(\ 0 ILLINOIS GEOLOGICAL
557
IL6of
1989-3 SURVEY LIBRARY
ENVIRONMENTAL IMPACTS OF OIL FIELD
BRINES IN SOUTHEASTERN CLAY COUNTY, ILLINOIS
Edited by;
Bruce R. Kensel and Dennis P. McKenna
with contributions by:
J. Roger Adams (2)^
Allison R. Brigham^-^)
Steven L. Burch(2)
Billy K. Cook(2)
Barbara R. Cline^^)
Paul C. Heigold(\)
Louis R. Iverson^-^)
Douglas E. Laymon^-^)
Edward A. Lisowski^-^)
Vickie L. Poole (^-)
Raman K. Raman (^)
Edward C. Smith (1)
John D. Steele(l)
Christopher J. Stohr(l)
Stephen Whitaker(^)
Illinois State Geological Survey
Champaign, Illinois
OPEN FILE SERIES 1989-3
(^*^ Illinois State Geological Survey
-^^lilinois State Water Survey
(■^H.llinois Natural History Survey
ILLINOIS STATE GEOLOGICAL SURVEY
3 3051 00006 9728
ENVIRONMENTAL IMPACTS OF OIL FIELD
BRINES IN SOUTHEASTERN CLAY COUNTY, ILLINOIS
Edited by:
Bruce R. Hensel and Dennis P. McKenna
with contributions by:
J. Roger Adams (2) ^
Allison R. Brighain(3) ^^y
Steven L. Burch^^) \P ^,
Billy K. Cook(2) (JC-' r^
Barbara R. Cline(l) .q"^ <^
Paul C. Heigold(l) o^ o^^^ ^
Louis R. Iverson(3) ^ <^^ _ <^^
Douglas E. Laymon^-^) ^v.
Edward A. Lisowski^-^) ^'^
Vickie L. Poole(l)
Raman K. Raman (2)
Edward C. Smith (1)
John D. Steele(l)
Christopher J. Stohr^^)
Stephen Whitaker^^)
Illinois State Geological Survey
Champaign, Illinois
OPEN FILE SERIES 1989-3
(-'-) Illinois State Geological Survey
(2) Illinois State Water Survey
(■^) Illinois Natural History Survey
PART ONE
OVERVIEW - EXECUTIVE SUMMARY
ABSTRACT
Brine waters, characterized by high concentrations of
dissolved minerals, can be found at depth throughout the oil
producing region of Illinois. Because petroleum traps commonly
contain both brines and petroleum, both liquids are commonly
pumped to the surface. When brine waters are allowed to come in
contact with the near-surface environment, degradation of that
environment occurs. The results of an investigation of the
environmental impacts of oil field brines in southeastern Clay
County, Illinois are presented in this report. This
investigation showed that: 1) Brine has been stored and
disposed in 384 holding ponds in the study area. Spillage and
leakage from these ponds has rendered hundreds of acres of farm
land unsuitable for crops. 2) High erosion from unvegetated
brine-damaged lands and high concentrations of dissolved
minerals in that runoff have increased sedimentation and caused
degradation of surface water quality. However, water from the
stream investigated for this study still satisfies drinking water
quality standards. 3) No evidence for wide-spread degradation
of groundwater resources was found. Although groundwater in the
vicinity of two filled-in brine holding ponds was highly
contaminated .
Table of Contents
page
Abstract 4
Section 1. Project Overview and Conclusions 6
Section 2. Description of Study Area 24
Section 3. Assessment of Groundwater Quality 44
Section 4. Assessment of Surface Water Quality 59
Section 5. Effects of Oil Brines Upon Benthic Communities
in Buck Creek 7 7
Section 6. Investigations at the Origin of Domestic Well
Water Contamination by Saline Waters 93
Section 7. Reclamation at Oil Brine Holding Ponds 119
Section 8. Remote Sensing 173
Section 9. Case Studies of Brine Contamination from
Holding Ponds 184
Section 10. Appendices 225
Appendix 2-A. Summary of Water Quality Data
Estimated from Southeastern Clay County
Electric Logs 226
Appendix 3 -A. Summary of Data from Water Well
Driller's Logs for Southeastern Clay County . . 231
Appendix 3-B. Results of Water Quality
Reconnaissance in Southeastern Clay County. . . 238
Appendix 3-C. Regression Analysis - Well Depth
and Proximity to Brine Holding Pond vs.
Conductance 255
Appendix 4-A. Water Quality Data for Buck
Creek 265
Appendix 5-A. Methods Used for Assessment of c^l
Brines Impacts on Aquatic Biota 270
Appendix 5-B. Benthic Macroinvertebrate,
Chloride, and Stream Order Data from Wabash
River Watershed, 1976 and 1977 276
Table of Contents (continued)
page
Appendix 5-C. Benthic Macroinvertebrates
(Except Diptera and Mollusca) Collected
in Buck Creek 288
Appendix 6-A. Methods Used During Investigation
of Origin of Domestic Well Contamination
by Saline Waters 292
Appendix 9-A. Brief Description of Analytical
Procedures Performed on Water Samples Taken
at Case Study Sites and Domestic Wells in
Southeastern Clay County 297
Appendix 9-B. Results of Chemical Analysis on
Groundwater Samples Collected at Clay County
Case Study Sites 299
SECTION 1 PROJECT OVERVIEW
compiled by
Bruce R. Hensel and Dennis P. McKenna
INTRODUCTION
The production of oil and gas has been a significant part of
the economy of Illinois since the discovery of oil in the
Illinois Basin in 1903. In 1984, the value of crude oil produced
was approximately 83 0 million dollars, with ten counties in
southeastern Illinois producing 70% of that total (Van Den Berg
et al., 1986). Direct employment by oil companies and suppliers,
as well as related service industries, is a major contributor to
the economic well being of this region.
Environmental problems from oil and gas production may occur
during drilling, production, or disposal of associated wastes.
If appropriate precautions are not taken, drilling fluids and
muds, acids used to increase the permeability of reservoir rocks,
and corrosion inhibitors and other additives are potential
sources of contamination to soils, surface water, and
ground-water (Collins, 1971) . Also, losses of crude oil to the
environment can occur during production, storage, and
transportation. However, the greatest potential for
environmental damage comes from brine waters that are produced as
a waste product with oil.
Brines are naturally occurring fluids, with extremely high
concentrations of total dissolved solids (> 100,000 ppm. Freeze
and Cherry, 1979) , which are present throughout most of the
stratigraphic column throughout the world. The composition of
brine varies both areally and with depth. In general, the
concentration of total dissolved solids, also referred to as
salinity, increases with depth. Meents et al., (1952) analyzed
hundreds of samples of brines from the oil reservoirs of the
Illinois Basin and found high concentrations of chloride (up to
95,000 ppm and commonly exceeding 50,000 ppm), sodium (up to
50,000 ppm), calcium (up to 18,000 ppm) and magnesium (up to 3400
ppm) .
Gas, oil, and brine waters are found in subsurface
stratigraphic traps. Gas, which has the lowest density of the
three fluids, will fill the pores near the top of the trap, oil
is typically found immediately below the gas, and the dense
brines occur below the oil and gas. Due to this close
association of brines and hydrocarbons, it is common to
encounter and produce both in an oil well. As oil and gas are
removed, the pore spaces formerly occupied by the hydrocarbons
are filled with water. Consequently, a well may initially
produce mostly oil; however, with increasing time, the ratio of
brine to oil will increase. The Illinois Environmental
Protection Agency (1978) has estimated that 973,000 barrels of
brine are disposed of daily in Illinois.
Brine waters, which are highly corrosive, may cause
environmental problems during (Figure 1-1) : 1) oil well
drilling, when brings mixed with drilling mud are brought to the
surface; 2) oil production, when the potential exists for brine
leakage from pipelines, oil-brine separation tank batteries,
waterflood injection wells, and when the potential exists that
reservoir pressures created by waterflood operations may force
brine waters to upwell through possible vertical conduits such as
unsealed, abandoned boreholes; and 3) disposal or storage, when
seepage can occur from holding ponds (unlined holding ponds have
been banned in Illinois) .
Disposal of brine waters has been a problem in Illinois
since the early years of oil production when they were treated as
an unwanted by-product and were commonly discharged directly into
streams and drainage ditches. During the 1940's, injection well
technology was developed. Still, the usual method of disposal
involved pumping brine into a holding pond for evaporation.
However, since the net precipitation rate in Illinois exceeds the
evaporation rate (Roberts and Stall, 1967) , brines stored in
these ponds were infiltrating to the subsurface rather than
evaporating. By the 1950 's most brine was being disposed by
injection (Bell, 1957); although many brine holding ponds
continued to be operated until they were phased out from
1980-1985. Currently all oil field brines must be injected, or
stored in corrosion resistant tanks until they can be injected.
The environmental consequences of improper brine disposal
can be severe. When allowed to mix with surface and
groundwaters, the high salinity of brines can make these valuable
resources unpotable. One barrel of brine with a chloride
concentration of 50,000 mg/L will raise the chloride content of
more than 150 barrels of deionized water above the maximum
recommended concentration for drinking water (250 mg/L) . The
environmental consequences of brine contamination in groundwater
are especially severe because the residence time is much greater
than in surface water and because chloride, the dominant ion
other than hydrogen and oxygen, is conservative.
When brine comes into contact with the soil, the excessive
sodium causes colloidal particles to disaggregate, thereby
destroying the soil structure (United States Salinity Laboratory,
1969) . Thus, the soil cannot support plant growth and is easily
eroded, which adds to the impact of brines on surface water
systems. An estimated 28,000 to 38,000 acres of land in Illinois
have been severely damaged by oil field brines (Coleman and
Crandal, 1981) .
8
Figure 1-1
Potential routes for oil field related brine
containination of the environment. None of these
occur -ences are likely if proper oil drilling and
brine disposal practices are used. A) Brine and mud
returned to the surface during drilling are spilled
on the ground surface, contaminating soils and
shallow groundwater. B) Brine leakage from a
separation tank. C) Brine infiltration from an
unlined holding pond (such ponds are now banned; but
were common prior to 1980) . D) Possible leakage
from brine injection/disposal v;ells. E) Reservoir
pressure caused by waterflood injection or brine
disposal forces brine up unplugged abandoned
borehole. F) Runoff of brines and
brine-contaminated sediments to streams causing
degredation of water quality and increased
sedimentation.
Eri-e C)i-br;r.e Oil
^lOCi"g separc'.icn pr:>curjc'i
pcr.i -.a.-.k well
^-e-r.:'.e
PURPOSE OF STUDY
The primary objective of this research was to assess the
impact of oil field brines on the soil, surface water and
groundwater resources, and aquatic biota of a study area in the
oil producing region of Illinois. An additional objective was
to assess the utility and cost-effectiveness of selected
geochemical, geophysical, and remote sensing techniques in
distinguishing between the various potential sources of brine
contamination .
This report describes this research, funded by the Illinois
Department of Energy and Natural Resources, and performed by the
State Geological, Natural History, and Water Surveys. The report
consists of three parts. This first part (Section 1) is a
summary of research conducted for the project. Final conclusions
and recommendations are presented at the end of this section.
The second part of the report (Sections 2-9) contains the
results of field investigations conducted for this project. The
geology of the study area is described in Section 2; brine
effects on groundwater, surface water, and aquatic biota are
described in Sections 3-5; and Investigative and remedial
techniques for brine contamination are discussed in Sections 6-9.
The third part of the report (Section 10) contains appendices.
DESCRIPTION OF STUDY AREA
The study area is located in the east-central portion of
southern Illinois (Figure 1-2) and includes that part of
southeastern Clay County bounded on the north and east by the
Little Wabash River, on the south by the Clay County line, and on
the west by the west edge of the Flora 15 minute topographic
quadrangle. Surface drainage is split by a divide which trends
northwest-southeast through the study area. North of the divide
drainage is toward the Little Wabash River, south of the divide
drainage is toward the Elm River in northern Wayne County. This
area was selected because 1) it has numerous, yet localized oil
fields; 2) geologic conditions, estimated from maps of bedrock
(Willman et al., 1967) and Quaternary (Lineback, 1979) geology,
are representative of other oil producing areas of southeast
Illinois; and 3) there was significant local interest and
support.
Geology
The principal unconsolidated deposit through the study area,
except in the valley of the Little Wabash River, is the Vandalia
Till Member of the Glasford Formation. The Vandalia Till, which
is generally overlain by a thin loess cover, is a compact, sandy
to silty till with thin, discontinuous beds of sand and gravel at
the base. The thickness of this unit is generally less than 50
feet. The valley of the Little Wabash River is underlain by
10
Figure 1-2.
Map of counties and oil fields in Illinois.
Southeastern Clay County study area is shown in
inset.
11
fine-grained lacustrine deposits of the Carmi Member of the
Equality Formation with a total thickness greater than 100 feet.
Immediately adjacent to the Little Wabash and its major
tributaries, the poorly sorted fluvial deposits of Cahokia
Alluvium overlie gl&cial till or lacustrine sediments. Locally,
the Cahokia contains sand and gravel deposits.
The uppermost bedrock unit is the Mattoon Formation of
Pennsylvanian age. This formation consists of sandstone, shale,
limestone, and coal. The average thickness of this formation in
southeast Clay County is about 3 00 to 4 00 feet. Total thickness
of the Pennsylvanian units is greater than 2 000 feet. Underlying
the Pennsylvanian units are Mississippian age formations.
Oil Resources
In southeastern Clay County, oil is produced from strata in
the Mississippian System. These units consist of limestone and
sandstone with some shale. The principal oil-producing
formations are the Tar Springs Sandstone, the Cypress Sandstone,
the Aux Vases Sandstone, and the McClosky Limestone. The Tar
Springs Sandstone is typically encountered below 2200 feet,
approximately. 1750 feet below mean sea level, and is the
uppermost oil-producing unit of the Mississippian System. The
Mississippian System has an approximate thickness of 2300 feet.
Commercial quantities of oil were first discovered in the
study area in May 1937, with the completion of the discovery well
for the Clay City Oil Field. This well, the Pure Oil Company
Bunyon Travis #1, established production in the oolitic McClosky
Limestone Member of the Ste. Genevieve Formation (Mississippian) .
This discovery, which was based on structural mapping from
seismic data, led to a tremendous increase in drilling activity
throughout the state.
The major oil field in the area is the Clay City Oil Field.
This oil field has been partially subjected to waterflood
projects for over 35 years. In 1984, oil production from the
field was approximately 3.22 million barrels from 2900 wells.
Total cumulative production through 1984 was 333 million barrels
(Van Den Berg et al., 1986). Of this total, one million barrels
were produced from waterflood projects in 1983, with cumulative
recovery from waterf looding totaling 67.5 million barrels through
1983.
Occurrence of Brine Waters
Brine waters occur throughout the entire thickness of the
Mississippian System as well as in the overlying Pennsylvanian
formations. The depth to the base of the fresh water (TDS > 2500
ppm) has been estimated throughout the study area, based on
electrical resistivity well logs. This depth varies from 150 to
12
250 feet (Figure 1-3) . The salinity of water increases with
depth, and below 300 to 350 feet total dissolved solids are
estimated to exceed 10,000 ppm.
Groundwater Resources
Most groundwater supplies for domestic and farm use are
obtained from either the surficial unconsolidated deposits or
from shallow sandstones in the Pennsylvanian bedrock. Wells in
the drift are typically large-diameter (24 to 36 inch) wells
which obtain water from thin, discontinuous sand layers within
the glacial till or alluvium or from fractures and joints within
these units. Other than along the Little Wabash River, few
significant unconsolidated sand and gravel deposits have been
located in the study area. However, the sandstone aquifer
appears to be continuous throughout much of the study area.
Wells finished in the bedrock seldom exceed 150 to 2 00 feet in
depth because the groundwater in this region rapidly becomes
saline as depth increases.
Surface Water Resources
At the present time, no public water supplies in
southeastern Clay County use groundwater. Fifty-one percent of
the population of Clay County is served by public water supplies
which are entirely dependent on surface water sources, primarily
the Little Wabash River. The quality of the local surface water
is equal to or better than that of the potable groundwater;
however, its quality is also more variable. The Little Wabash
River near Louisville has an average discharge of 575 cubic feet
per second (cfs) but stream flow can drop as low as 0.5 cfs
during periods of drought. During periods of low flow, the water
quality of the river degrades.
ASSESSMENT OF BRINE IMPACTS
Impacts on Aquifers
Water quality within the drift and bedrock aquifers in the
study area is generally fair (Figure 1-4) . Instances of elevated
salt levels in deeper bedrock wells can usually be attributed to
naturally saline groundwater which occurs at depth (Section 3).
However, localized shallow groundwater contamination does occur
in the vicinity of brine holding ponds (Section 9) .
Measurements of electrical conductance of water samples from
199 domestic water supply wells in and around the study area (see
Section 3) were used to estimate that 53 had calculated total
dissolved solids concentrations over 1000 mg/L and five of those
53 had calculated TDS concentrations greater than 2000 mg/L. All
of the wells with estimated TDS concentrations greater than 2000
13
Figure 1-3
Depth to the base of fresh water (TDS less than 2500
ppm) in southeastern Clay County. TDS
concentrations are from electric log data.
R 6 E
R 7 E
R 8 E
14
Figure 1-4
Comparison of regional water quality in southeastern
Clay County to water quality in the vicinity of a
brine holding pond.
100-
80-
o
-o
o
CO
05
o
E
c
a
o
q3
Q.
60-:
40-
20 -S
Domestic water wells in
southeastern Clay County
Monitoring wells within 1000 feet
of a brine holding pond
I I T**^ i'^ I 1 T"^^ i i
0 - TOGO 2001 ■ 3000 -iOOl - 5000 6001 - 7000 8001 • 9000 > 10,000
1001 - 2000 5001 - 4000 5001 - 6000 7001 - 6000 9001 - 10,000
IDS concentration (mg/L)
15
mg/L were finished at depths greater than 150 feet. The depth to
the base of the fresh water zone in Clay County is estimated to
be 150 to 250 feet (see Section 2) , which suggests that upconing
of naturally saline groundwater is the cause of the high TDS
concentrations in those five wells.
No apparent causes could be identified for the high salinity
in the 53 wells where TDS concentrations were between 1000 and
2000 mg/L. There were no significant correlations between TDS
and depth or TDS and proximity to brine holding ponds. Of the 14
wells located within an estimated distance of 500 feet to brine
holding ponds, none had an estimated total dissolved solids
concentration greater than 1500 mg/L.
Shallow, localized contamination of groundwater was noted
near two intensely studied brine holding ponds. Total dissolved
solids in groundwater below the two ponds were as high as 52,000
mg/L.
Impact on Surface Water
An assessment of the water quality in one perennial stream,
Buck Creek, indicated generally good water quality; however,
brine impacts were evident (see Section 4) . An increase in
suspended sediment was noted between the upstream and downstream
stations, indicating that runoff entering the stream between the
two stations carried almost twice the concentrations of suspended
solids as was measured at the upstream station. Concentrations
of several indicators of oil field brines, including chloride and
total dissolved solids, increased significantly between the two
stations, although the levels did not exceed Illinois water
quality standards. Also, grease and oil concentrations in this
stream were higher than those usually found in Illinois rivers.
The increased sediment load and elevated chloride and TDS
concentrations between the upstream and downstream stations at
Buck Creek, as well as the relatively high grease and oil
concentrations, indicate that Buck Creek has been affected by oil
field activities. The high suspended solids are a result of
increased runoff from areas where vegetation will not grow
because brines have damaged the soils. Concentrations of TDS and
chloride in runoff from one such area (not in the Buck Creek
watershed) were as high as 14,000 and 8,250 mg/L, respectively.
Impacts on Aquatic Ecosystems
Examination of aquatic biota in Buck Creek showed decreased
species diversity downstream from the area of heavy oil field
activity (see Section 5) . This decrease in diversity can
partially be attributed to degradation of water quality by oil
field brines. However, the absence of a variety of microhabitats
16
was considered to have a greater effect on the decrease in
species diversity.
No water quality variables were detected which might be
limiting or toxic to aquatic life. However, a limited
microhabitat diversity was apparent. Buck Creek has been
historically channelized. Rocky riffle areas are absent along
most of its downstream length, and the substrate consists
primarily of finer or softer sediments. Also, undercut banks,
log jams, and other micro-habitats are uncommon. For these
reasons, the absence of microhabitat diversity was deemed more
limiting to benthic macroinvertebrate diversity than degraded
water quality.
EVALUATION OF BRINE INVESTIGATIVE TECHNIQUES
As ssment of actual or potential environmental damage from
the production and disposal of oil field brines on a state- or
county-wide basis is hampered by 1) the widespread nature of oil
production in Illinois (47 counties produced oil or gas in 1983) ,
and 2) the large number of potential sources (more than 8600
brine holding ponds, over 77,000 active and abandoned oil wells,
and more than. 12,000 injection wells). Identification of
site-specific sources of contamination is difficult because 1)
saline water may be either natural or the result of oil field
brines, and 2) tracing of contaminant plumes in groundwater is
often expensive and time-consuming.
During this investigation, air photo interpretation proved
to be an efficient method of locating abandoned brine holding
ponds (Section 8). Three sets of photos were used (1953, 1966,
and 1983) to identify 384 holding ponds (Figure 1-5) in
southeastern Clay County.
Subsurface brine plumes were efficiently located using a
combined electrical resistivity survey and groundwater monitoring
program (Section 9) . The electrical resistivity survey can be
done relatively quickly and at little expense. The resistivity
data can be used to delineate the approximate depth, location,
and extent of the plume. Those data can aid in the efficient
placement of groundwater monitoring wells (Figure 1-6) .
Multivariate statistical analysis showed promise as a
technique to differentiate the origin of brine waters (Sec on
6). Ratios of Ca/Cl, Mg/Cl, Ca/Li, and Mg/Li can be used
differentiate shallow brines from oil field brines from fre^h
water (Figure 1-7) .
CONCLUSIONS
1) An assessment of the environmental impacts of oil field
brines in southeastern Clay County shows that both surface waters
17
Figure 1-5
Brine holding ponds in southeastern Clay County.
Identified using air photographs from 1953, 1966,
and 1983.
R
6 E
R 7 E
R 8 E
t"
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1
4
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N
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A
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.
-I 1
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(some also visible on 1953 photos)
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but not visible on 1966 photos
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A Ponds visible on 1983 photos only
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18
Figure 1-6
Comparison of two brine plume tracing techniques.
- plume mapped according to concentration of total
dissolved solids in groundwaxier. B - plume mapped
based on electrical resistivity values.
1027
550'
3861
C3 Unvegelated area
■ Elevation datum
H NHS test plot
Intermitlent drainage way
■ SWS surface water station
• 841 Data point, TDS concentration (mg/L)
Inferred limit of TDS plume
icon
Contour interval = 10,000 mg'L
(dashed where interred)
000 - - ■
'285
•■-. /
^Approximate boundary
of holding pond ■
■-■•■■7 '942
Tank battery
1570
TsoSy
"" V
/
/
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1029* ,
•949
19
Figure 1-7
Discriminant Analysis territorial map for oil field
brine, shallow brine, and fresh water.
•15.0
-20.0
20.0 +*"
15.0 ■■
10.0 ■•
0
000
.ssooo
5.0 -f sssooo.
sssoo
ssooo
sssooo
sssooo
. _ sssooo
0.0 + sssoo
ssooo
sssooo
sssooo
sssooo
sssoo
canonical Discriminant Function 1
-10.0 -5.0 0.0
-5.0 ••
•10.0 ■■
-15.0 ••
-20.0 •
-20
20.0
ssooo
sssooo
sssooo
Isssooo
sssoo
ssooo
sssooo
sssooo
SHALLOW BRINE
0 -15.0 -10.0 -5.0 0.0 5.0 10.0 15.0 20.0
* Group centrolds, # Unknown, 0 Oil Field Brine, S Shallow Brine, F Fresh Water
Unstandardlzed Canonical Discriminant Function Coefficients
log(Ca/Cl)
log((Ca+Hg+Sr)/Cl)
log((Nd-^Ca+M9+Sr-»-L1)/Cl)
log(Na/Ca)
log(Mg/L1)
log(Sr/L1
(constant)
FUNC 1
8.574445
26.38258
-27.94176
23.79036
8.225558
-3.403425
-5.930134
FUNC 2
21.62735
-1.057425
-23.43031
10.69833
-3.014662
1.823528
16.52935
20
(Section 4) and groundwaters (Sections 3 and 9) have been
affected. Increased concentrations of suspended solids,
chloride, bromide and sulfate were noted in surface water;
however, drinking water quality standards were not exceeded for
any of these parameters. Groundwater contamination has occurred
in localized areas where brine holding ponds once existed.
However, no water supply wells appeared to be contaminated by oil
field brines.
2) The most severe problem currently associated with oil
field brines may be damage of surficial soils caused by brine
spills. Hundreds of acres of land in the study area have soils
which have been damaged by oil field brines. Where the brine
spill has been recent, no vegetation has grown and erosion is
severe. With time, the salts are partially leached out of the
soils and salt tolerant plant species may be established (Section
7) .
3) Brine, which is more dense than fresh water, will tend
to sink within an aquifer until a relatively impermeable stratum
is encountered. In materials with low permeability, brine will
move along pathways of higher hydraulic conductivity. Because
many cases of. brine contamination of ground-water are caused by
leakage from holding ponds, mounding may have had a significant
affect on the direction(s) of brine migration (Section 9). Also,
brine contaminated fluids and sediments can be carried as surface
runoff to lowland areas. These waters may enter surface water
bodies or infiltrate into the groundwater system, in either case
degredation of water quality may occur.
4) Many of the conclusions noted in this investigation of
environmental affects of brine in southeast Clay County may also
apply to other oil producing regions of the State (particularly
the ten major oil producing counties, listed in order of oil
production in 1984; White, Wayne, Lawrence, Marion, Fayette,
Crawford, Edwards, Clay, Franklin and Wabash). The degree of
environmental damage caused by oil field brines will depend on
the disposal practices used in an area, the intensity of oil
development, and the regional geology. More information would be
needed to adequately describe potential impacts of oil field
brines in these areas.
RECOMMENDATIONS
1) Oil field brines can pose a significant threat to
groundwater resources in those counties where large scale oil
production has occurred. More than 8,600 brine holding ponds,
77,000 active and abandoned oil wells, and 12,000 brine
injection v/ells have been in use in Illinois. These features
should be mapped along with geology and surface water resources
for each oil producing county so that an assessment can be made
as to which counties face the greatest potential for groundwater
21
quality degredation due to oil field brines. Then, assessments
of the impacts of oil field brines should be conducted in a
manner similar to that described in Sections 3, 4, and 5 of this
report.
2) Additional research on brine movement through permeable
materials is needed. The case study sites described in this
report (Section 9) were both situated over geologic materials
with low hydraulic conductivity. Brine movement through
permeable materials should be more rapid; however, dilution will
be greater. The ramifications of this relationship should be
studied.
3) Research is needed on the potential for brine leakage
from injection/ disposal wells as well as upward brine migration
through abandoned and unsealed boreholes. Contamination from
these sources may be very difficult to detect unless a water
supply well is affected, in which case widespread contamination
of the aquifer may have already occurred. An inventory of
reported cases of contamination could be the first step in such a
study, followed by an assessment of possible techniques to detect
such contamination and finally by application of those
techniques.
22
REFERENCES
Bell, A. H. , 1957, Brine Disposal in Illinois Oil Fields:
Circular 244, Illinois State Geological Survey, 12 p.
Coleman, W. B. and D. A. Crandall, 1981, Illinois Oil Field Brine
Disposal Assessment - Phase II report: Illinois
Environmental Protection Agency, 47 p.
Collins, A. G. , 1971, Oil and Gas Wells - Potential Polluters of
the Environment?: Journal of Water Pollution Control
Federation, V. 43, No. 12, pp. 2383-2393.
Freeze, R. A. and J. A. Cherry, 1979, Groundwater: Prentice-Hall,
Inc. , 604 p.
Illinois Environmental Protection Agency, 1978, Illinois oil
field brine disposal assessment: lEPA Staff Report, 114 p.
Lineback, J. A., 1979, Quaternary deposits of Illinois: Illinois
State Geological Survey, 1:500,000 map.
Meents, W. F.., A. H. Bell, O. W. Rees, and W. G. Tilbury, 1952,
Illinois Oil Field Brines, Their Geologic Occurrence and
Chemical Composition: Illinois State Geological Survey
Illinois Petroleum Report No. 66, 38 p.
Roberts, W. J. and J. B. Stall, 1967, Lake Evaporation in
Illinois: Illinois State Water Survey Report of
Investigations 57, 44 p.
United States Salinity Laboratory Staff, 1969, Diagnosis and
Improvement of Saline and Alkali Soils: U.S.D.A.
Agricultural Handbook No. 60, U.S. Department of
Agriculture.
Van Den Berg, J., J. D. Treworgy, and J. R. Elyn, 1986, Petroleum
Industry in Illinois, 1984: Illinois Petroleum 127,
Illinois State Geological Survey, 140 p.
Willman, H. B. and others, 1967, Geologic Map of Illinois:
Illinois State Geological Survey, 1:500,000 map.
23
PART TWO
RESULTS OF FIELD INVESTIGATIONS
24
SECTION 2 DESCRIPTION OF STUDY AREA.
by
Vickie L. Poole, Stephen T. Whitaker, and Edward C. Smith
LOCATION
The study area is located in the east-central portion of
southern Illinois and includes the part of southeastern Clay
County bounded on the north and east by the Little Wabash River,
on the south by the Clay County line, and on the west by the west
edge of the Flora 15' topographic quadrangle (figure 2-1) . This
area was selected because of its numerous, yet localized, oil
fields within an area of limited groundwater resources. This
county also has both natural sodium-affected soils and soils
damaged by the high sodium content of oil field brines. Clay
County lies at the north edge of the Mt. Vernon Hill Country of
the Till Plains Section of the Central Lowland Physiographic
Province. This province is characterized by thin drift mantling
a bedrock surface of low relief; uplands are fairly level and
stream valleys generally have broad alluvial plains. Land
surface topography is strongly controlled by bedrock surface
topography (Leighton et al., 1948; Hunt, 1974).
Surface drainage is split by a divide which trends
northwest-southeast through the study area. Drainage of the
northern and eastern parts of the area is north and east towards
the Little Wabash River. Drainage in the southwest is toward the
south-southeastward flowing Elm River, 1/2 to 2 miles south of
the study area.
GENERAL GEOLOGY
The bedrock surface is overlain by Pleistocene deposits
which consist mainly of till, occasionally interbedded, with
thin, discontinuous sand and gravel deposits. Lake deposits,
loess and alluvium often overlie the till. The thickness of
these deposits varies from less than 5 feet on the uplands to
over 100 feet in the bedrock valley underlying the Little Wabash
River. In general, drift thickness is less than 50 feet.
Generalized drift thickness within the study area is shown in
figure 2-2. This map is based on work by Piskin and Bergstrom
(1975) and has been updated using recent well log information.
Reported locations of bedrock exposures were not field checked
for this study.
The till is Illinoian in age and is classified as the
Vandalia Till Member of the Glasford Formation; generally a hard,
gray silty till with scattered, thin sands and gravels (Willman
and Frye, 1970) . Wisconsinan-aged lake deposits (Carmi Member
25
Figure 2-1. Map of Study Area in southeastern Clay County
R 6 E
R 7 E
R 8 E
26
Figure 2-2.
Drift thickness in southeastern Clay County.
Updated and modified from Piskin & Bergstrom (1975)
R 6 E
R 7 E
R 8 E
27
of the Equality Formation) are concentrated along the Little
Wabash and Big Muddy Rivers. These deposits consist
predominantly of lacustrine silts and clays (Willman and Frye,
1970) . Loess overlies most of the glacial deposits and its
thickness ranges from 2 feet to a little more than 4 feet in the
study area (Willman "and Frye, 1970) . Loess is generally absent
in areas where alluvium is deposited. Cahokia Alluvium is
Wisconsinan and Holocene in age and usually consists of silty
deposits found in the channels and floodplains of present-day
streams and rivers (Willman and Frye, 1970) . Major alluvial
deposits occur along Elm Creek and Buck Creek.
The uppermost bedrock unit is the Mattoon Formation of
Pennsylvanian age which is a complex of sandstone, shale,
underclay, thin limestone and coal. Average thickness of the
Mattoon Formation in southeastern Clay County ranges from
slightly more than 300 feet to slightly more than 400 feet
(Willman et al., 1975). Lithologies present at the bedrock
surface, as determined from drillers' logs, are shown in figure
2-3. Shale is the dominant lithology; sandstones occur in the
west-central and southern portions of the area.
The top of the Mattoon Formation is an erosional surface.
Its topography reflects the drainage system that developed into
the Pennsylvanian rocks prior to glaciation (Horberg, 1950) .
Figure 2-4 is a generalized topographic map of the bedrock
surface. It is based on previous work by Horberg (1950) and was
updated using recent well log information. Elevation of the
bedrock surface ranges from over 4 50 feet above mean sea level
(m.s.l.) around Flora and just south of Clay City to less than
3 50 feet above m.s.l. in a tributary bedrock valley in the
south-central portion of the study area. A dominant feature of
the bedrock surface in this area is the Little Wabash Bedrock
Valley. This valley trends roughly north-south just east of the
study area.
Geologic cross sections through the study area, shown in
figures 2-5a and 2-5b, were constructed using electric logs from
oil test wells. Figure 2-6 shows the lines of section and
location of electric logs. Correlations of stratigraphic units
were made using previously published material for Wayne County
(DuBois and Siever, 1955; Sims et al., 1944). The uppermost
sandstone units shown on the cross sections are of the Mattoon
Formation and are the major source of domestic drinking water
supplies.
Underlying the Mattoon Formation are approximately 10,500 to
11,500 feet of other Pennsylvanian and older Paleozoic
formations, and the Pre-Cambrian basement rocks (Willman et al.,
1975) . The deepest oil-producing formations are Devonian
carbonates; major oil-producing formations are limestone,
dolomite and sandstone of Mississippian age. Figure 2-7 is a
28
Figure 2-3.
Lithology at the bedrock surface in southeastern
Clay County. Data are interpolated from drillers'
logs.
R 6 E
R 7 E
R 8 E
29
Figure 2-4.
Bedrock surface topography in southeastern Clay
County. Updated and modified from Horberg (1950)
R 6 E
R 7 E
R 8 E
30
Figure 2-5a. Cross-section A-A' , north-south, southeastern Clay
County.
500 ft
-500
- 500 ft
]50tl V
E = 52.8
1 mi
Till
Sand and gravel
Limestone
Shale
-^ Sandy shale
Sandstone
"^ -_-_-_--■- -I-r->"^-f~ ^ mean sea level
♦ E-logs used for
section compilation
- -500
31
Figure 2-5b. Cross-section B-B' , east-west, southeastern CI
County.
ay
500 t1
E
B-
Linle Wabash River
500 n
Jsofi VE = 52.8
1 mi
Till
■J Sand and gravel
Limestone
-:| Shale
~ Sandy shale
Sandstone
mean sea level
1 E-logs used for
section compilation
--500
32
Figure 2-6
Location of cross-sections A-A' and B-B' ,
southeastern Clay County.
R 6 E
R 7 E
R 8 E
33
Figure 2-7
Stratigraphic column illustrating a typical sequence
of lithologies in southeastern Clay County. Section
shows lithologies from Pennsylvanian Age formations
through major oil producing formations of
Mississippian Age.
SP
MillrvoHS
Resistivity
Olim-rTi^.ni
SP Resislivify
Millivofts Ohm-m'/m
SP
Millivolts
Resislivily
Onrn-m'/m
Shoal O Is
PENNSYLVANIAN
MISSISSIPPIAN
NO-7 Coal
No 6 Coal
CARBONDALE
HANEY
Lower Cypress Ss
;^~DOWNEYS BLUFF LS
AUX VASES
STE. GENEVIEVE
Rosiciare
McCiosky
ST LOUIS
BEECH CREEK
y (Barlow Ls)
SALEM
WARSAW
I; ] I Limestone
['••.'■■I Ooliies
|l ' I Dolomne
|v:-'| Chert
[ I Sanosione
t^-"^ Shaie
^H Coal
34
stratigraphic column illustrating a typical sequence of
lithologies in the study area from the Pennsylvanian through the
major Mississippian oil-producing formations.
GROUNDWATER OCCURRENCE
Aquifer Lithologies
Shallow Pennsylvanian sandstone is the principal aquifer of
southeastern Clay County. As shown in figure 2-3, the sandstones
are concentrated in the west-central and southern parts of the
study area. Of the 133 producing water wells with logs on file
at the State Geological Survey, 24 were completed in sandy clay,
sand, or sand and gravel, 105 were completed in sandstone, 2 were
completed in shale or slate, 1 was completed in sandstone and
limestone, and 1 was reportedly completed in shale and gravel.
Figure 2-8 illustrates the generalized domain of the predominant
aquifer types.
Depth to Saline Water
To delineate the average depth to natural saline water in
the study area, a method outlined by Pryor (1956) was used to
estimate the quality of ground-water from electric resistivity
logs. Water quality determinations were used to define two
zones: 1) the zone of potential domestic water supply in shallow
Pennsylvanian sandstone, and 2) a zone delineating water with TDS
concentration less than 10,000 ppm. A summary of the water
quality data estimated from electric logs of 78 wells in the
study area is presented in Appendix 2 -A.
Estimation of total dissolved solids (TDS) concentration
from electric logs is based on the concept that an empirical
relationship between TDS concentration and formation water
resistivity can be determined for particular geological and
hydrochemical settings. Pryor (1956) developed his empirical
relationship between NaCP-solution equivalents and measured TDS
concentrations from chemical analyses of groundwater from
Pennsylvanian sandstone in southern Illinois. He included data
from 2 wells in Clay County and 16 wells in neighboring Wayne and
Richland Counties in developing his empirical curve. Therefore,
his method is assumed to be applicable to water in shallow
Pennsylvanian sandstones in Clay County.
s Base of the Shallow Sandstone Aquifer. The criteria used in
defining a fresh water aquifer are: 1) electric logs indicate a
sandstone with sufficient permeability for domestic water
supplies to be developed; and 2) the estimated TDS concentration
of the water must be less than 2500 parts per million (ppm) .
Growth and development of livestock may be adversely affected by
water with TDS concentrations greater than 2500 ppm (Hem, 1985;
35
Figure 2-8.
Generalized map of aquifers utilized in southeastern
Clay County.
R 6 E
R 7 E
R 8 E
36
McKee and Wolf, 1963) . These criteria are satisfied in the
shallow Pennsylvanian sandstone unit. Estimated TDS
concentration was almost never the limiting factor in determining
the base of this fresh water aquifer; in nearly all cases the
base of the aquifer coincided with the base of the sandstone.
The aquifer appears continuous over the study area except for a
small region south of Clay City where the sandstone is absent.
Figure 2-9 shows the estimated depth to the base of the
fresh-water aquifer.
» Water Quality Relating to Injection. Deep well underground
injection in Illinois is prohibited in or above formations
containing water with less than 10,000 ppm TDS. Estimation of
water resistivity using electric logs depends on infiltration of
drilling mud into the saturated unit. Therefore, the method is
not applicable to shale, a formation in which infiltration is
negligible. This limitation is important in this study because
the 10,000 ppm TDS limit appears to occur within a 300- to
500-foot thick section predominantly consisting of shale.
Sandstone above and below this shale contains water with TDS
concentrations of less than- 10^000 ppm and greater than 10,000
ppm, respectively. Therefore, instead of defining a single
10,000 ppm TDS concentration surface, it was necessary to define
two surfaces that essentially represertt the top and base of the
shale unit. These surfaces divide the near-surface bedrock into
three zones related to water qualUty:
1) Upper Sandstone/Siltstone Unit - The top of this unit is
presumably the bedrock surface; however, the electric
logs start at the bottom of the drill hole casings;
i.e., 100 feet or more below the land surface. The
upper part of the recorded interval contains a
fresh-water sandstone that appears to be fairly
continuous over most of the study area. This sandstone
grades downward into fine-grained siltstone with
premeabilities that are probably too low and TDS
concentrations that may be too high for this part of the
unit to be used as a source of drinking water. However,
concentrations do not exceed 10,000 ppm.
2) Shale Unit - This unit consists of 300 to 500 feet of
shale with interbedded silty layers. Generally, the TDS
concentration of water within this unit cannot be
estimated using Pryor's (1956) method.
3) Lower Sandstone Unit - This unit consists of a
well-developed sandstone that occurs below the shale
unit over most of the study area. Only 4 of the
resistivity logs examined indicated that water in this
unit contains less than 10,000 ppm TDS. A spot check of
logs for additional drill holes , near these wells did not
confirm the presence of TDS concentrations of less than
37
Figure 2-9
Depth to the base of fresh water (TDS less than
2 500 ppm) in southeastern Clay County. TDS
concentrations are estimated from electric log data
R 6 E
R 7 E
R 8 E
38
10,000 ppm. However, the spot check did locate one
additional drill hole in Section 11, T. 2 N. , R. 6 E., with
an estimated TDS concentration less than 10,000 ppm. In
summary, most of the water in this unit has TDS
concentrations exceeding 10,000 ppm; however, it may locally
contain water with a slightly lower TDS concentration.
Oil industry records indicate that current brine-disposal
wells discharge into the lower sandstone unit. This is the
shallowest unit into which water disposal should be considered.
Two maps were compiled as part of this task:
1) Depth to the base of the upper sandstone/siltstone unit
(less than 10,000 ppm estimated TDS) (figure 2-10).
2) Depth to the top of the lower sandstone unit (greater
than 10,000 ppm estimated TDS) (figure 2-11).
General stratigraphic relationships of the units are clearly
illustrated by comparing the depths or elevations of figures 2-10
and 2-11 to the cross sections of figures 2-5 and 2-6.
OIL INDUSTRY ACTIVITY IN THE CLAY CITY AREA
History
Oil was discovered near Clay City on May 17, 1937 when the
Bunyan Travis #1 well, drilled by the Pure Oil Company,
encountered reservoir rock in the Mississippian McClosky oolite.
This discovery led to a dramatic increase in drilling activity in
the state, and by 1940 had established Illinois as the fourth
largest producer of oil. In the study area, oil was initially
recovered from Mississippian age reservoirs in the Cypress sands
(depth 2600'±) as well as the McClosky oolites (depth 3050'±).
Since then, additional pays have been found in the Mississippian
age Waltersburg (depth 2175'±), Tar Springs (depth 2560'±),
Bethel (depth 2800'±), Ohara (depth 3020'±) , Spar Mountain (depth
3030±) , Saint Louis (depth 3300'±), Salem (depth 3550'±), Ullin
(depth 3600'±) , Carper (3810'±) , and in Devonian age formations
(depth 4350'±) .
Through 1983 the combined fields of Clay City Consoi iated
and Sailor Springs, located in the study area, have injec d
approximately 1.122 billion barrels of water and produced 3
million barrels of oil. Annual production from the two fi ids
was approximately 1.2 million barrels of oil and 26 millio..
barrels of water in 1984.
39
Figure 2-10. Depth to the base of the upper sandstone/siltstone
unit in southeastern Clay County. Estimated TDS
concentrations in this unit are less than 10,000
ppm.
R 6 E
R 7 E
R 8 E
40
Figure 2-11. Depth to the top of the second sandstone unit in
southeastern Clay County. Estimated TDS con-
centrations in this unit are greater than 10,000
ppm.
R 6 E
R 7 E
R 8 E
41
Injection
The practice of water injection, or waterflooding,
typically requires the conversion of oil wells in downdip
structural positions to water injection wells, or the drilling of
wells solely for water injection. Water, usually brines produced
from neighboring oil wells, is forced down these injection wells
and into the particular reservoir being flooded. The influx of
water into the reservoir pushes the oil toward higher structural
positions where it is recovered. Reservoirs subject to
waterflooding in the study area are: Mississippian age Cypress,
Bethel, Aux Vases, Ohara, Spar Mountain (Rosiclare) , McClosky,
and Salem.
Reservoir pressures caused by injection are not sufficient
to force oil to the surface in the study area. Typical fluid
levels in waterflooded wells range from 2000' to 1200' below land
surface.
Brine Disposal
The disposal of brines from oil fields has long been a
problem. Transportation costs for salt water are prohibitive for
wells with high ratios of brine to oil. This problem was
alleviated by the use of brine holding ponds, salt water disposal
wells and waterflood injection wells.
The use of brine holding ponds was relatively common in the
study area until the 1960s when injection programs became more
viable. Figure 2-12 illustrates the distribution of brine
holding ponds in the study area as determined from aerial
photographs. In 1980, the state began a five-year, phase-out of
brine holding ponds.
42
Figure 2-12. Location of brine holding ponds in southeastern
Clay County. Ponds located by inspection of aerial
photographs from 1953, 1966, and 1983.
R 6 E
R 7 E
R 8 E
• Ponds visible on 1956 photos
some also visible on 1953 photos)
o Ponds visible on 1953 photos,
but not visible on 1966 photos
A. Ponds visible on 19&3 photos only
43
REFERENCES
Du Bois, E. P., and R. Siever, 1955, Structure of the Shoal Creek
Limestone and Herin (No. 6) Coal in Wayne County, Illinois:
Illinois State Geological Survey Report of Investigations
182, 7 p.
Hem, J. D. , 1985, Study and interpretation of the chemical
characteristics of natural water: U.S.G.S. Water Supply
Paper 2254, 263 p.
Horberg, L. , 1950, Bedrock topography of Illinois: Illinois
State Geological Survey Bulletin 73, 111 p.
Hunt, C. B. , 1967 (revised 1974) , Natural regions of the United
States and Canada: W. H. Freeman and Company, San
Francisco, 725 p.
Leighton, M. M. , G. E. Ekblaw, and L. Horberg, 1948, Physio-
graphic divisions of Illinois: Illinois State Geological
Survey Report of Investigations 129, 33 p.
McKee, J. E. ,. and H. W. Wolf, 1963, Water quality criteria:
California State Water quality Control Board Publication
3-4, 548 p.
Piskin, K. , and R. E. Bergstrom, 1975, Glacial drift in Illinois:
thickness and character: Illinois State Geological Survey
Circular 490, 36 p.
Pryor, W. A., 1956, quality of groundwater estimated from
electric resistivity logs: Illinois State Geological
Survey Circular 215, 15 p.
Sims, P. K. , J. N. Payne, and G. H. Cady, 1944, Pennsylvanian key
beds of Wayne County and the structure of the "Shoal Creek"
Limestone and the Herrin (No. 6) Coal bed: in Progress
Reports on Subsurface Studies of the Pennsylvanian System in
the Illinois Basin, p. 27-32.
Willman, H. B. , and J. C. Frye, 1970, Pleistocene stratigraphy of
Illinois: Illinois State Geological Survey Bulletin 94,
204 p.
Willman, H. B. , E. Atherton, T. C. Buschbach, C. Collinson, J. C.
Frye, M.E. Hopkins, J. Lineback, and J. A. Simon, 1975,
Handbook of Illinois Stratigraphy: Illinois State
Geological Survey Bulletin 95, 261 p.
44
SECTION 3 ASSESSMENT OF GROUNDWATER QUALITY
by
Vickie L. Poole and Stephen L. Burch
INTRODUCTION
The focus of this section is on groundwater quality within
the study area and the extent of possible oil field brine
contamination. The study was undertaken to address possible
impacts on groundwater resulting from regional oil field
activity. Residents of the area have expressed concern that
large-scale degradation of groundwater quality has been caused by
oil field activities such as brine disposal.
GROUNDWATER UTILIZATION
Drillers' logs of water wells in the study area were
examined to determine total depth, length of casing, static
water-level, top and base of the aquifer tapped, aquifer
lithology and. reported yield in gallons per minute (gpm) . A
total of 143 well logs were examined; 7 wells were reported as
dry, and 3 were reported plugged due to high salt content. The
plugged wells are located in 23-3N-7E (county ID numbers 26283
and N-17) and 28-3N-7E (county ID number 4 688) and were completed
at depths of 174, 160, and 169 feet, respectively.
In addition to examining well logs on file, a field
inventory of domestic water wells was performed. Location of
wells and electrical conductance measurements of water samples
were obtained for 238 wells at 227 locations in and around the
study area. Eleven landowners had two wells essentially in the
same location. Due to problems in reported locations of wells
and changes in ownership, most wells could not be matched to
drilling logs on file. One hundred and ninety-nine of the wells
inventoried were physically located within the study area.
Landowners reported estimated depths for 138 of these wells.
Figure 3-1 illustrates the depth-range distribution of water
wells in the study area as reported by the landowners and as
reported on drillers' logs. Discrepancies may be due in part to
a large number of shallow dug wells for which logs were never
submitted, and to deeper abandoned wells of which current owners
are unaware.
Shallow Pennsylvanian sandstone is the principal aquifer
lithology of southeastern Clay County. Of the 133 producing
water wells with logs, 24 were completed in sandy clay, sand, or
45
Figure 3-1. Depth-range distribution of water wells
38 -J
-
36-
34-
32-
30-
28-
26-
24-
o
o
22-
20-
o
S2
18-
16 —
■
-
:
b
Z
14-
12-
10-
8-
6-
,
•r.ry^,r.-\
4-
.
2-
■
_
;.•.■:■;.;-;-:■;■:■:■:
.. _ _ _-
'i-r^i-r^^-
x-x^i-xoxt;:::;::;;:,:::;:;:
1
26
51
76
101
126
151
175
' 201 ^ 226
251
to
10
10
10
10
10
10
10
10 10
10
25
50
75
100
125
150
175
200
225 250
275
Well depth ranges (ft)
owner reported (138 lolal)
drillers' log (133 tolsl)
46
sand and gravel, 105 were completed in sandstone, 2 were
completed in shale, 1 was completed in sandstone and limestone,
and 1 was reportedly completed in shale and gravel.
Yields have been reported on drillers' logs of 83 wells
completed in sandstone. These values range from 1 to 50 gpm and
average approximately 13 gpm.
Most of the shallow wells are completed in sandy clay, sand
and/or gravel. They are large-diameter bored or dug wells which
rely on seepage that is stored in the wellbore to meet peak water
demands.
METHODOLOGY
Electrical Conductance
During the field inventory of domestic water wells,
estimates of water quality were obtained from measurements of
electrical conductance. Electrical conductance is a measure of
the water's ionic strength and is directly related to the
concentration of total dissolved solids (TDS) in a water sample.
Because conductance is temperature dependent, an automatically
compensated conductivity meter (MYRON L. Co. , OS Meter, Model
532-Ml) was used in this study. Results of the reconnaissance of
water samples from 199 domestic water wells, including the name
of the owner/controller, well location and reported depth, and
conductance measurements, are shown in Appendix 3-B.
Samples for Chemical Analyses
A subset of the inventoried domestic water wells was
selected for detailed chemical analysis. Hydrogeologic and
conductivity data were used to:
- obtain a uniform distribution of sampling sites over
the study area
- sample wells that had drillers' logs on file and which
were cased to isolate a specific aquifer
- select sites having anomalously high values of
conductance so that they could be compared to sites
with lower values, presumably reflecting background
conditions.
A 2-mile separation of wells was sought where reliable
information was available. Wells were also chosen to represent
the three major sources of groundwater being utilized; shallow
glacial deposits (dug or bored wells) , deeper glacial deposits
(drilled wells, generally more than 70 feet deep), and
Pennsylvanian sandstone (drilled wells, generally more than 100
47
feet deep) . Twenty-two groundwater samples were collected for
analysis.
Laboratory determinations made for this study focused on the
major ionic species found in groundwater as well as selected
trace metals. Chemical analyses were performed by an EPA
Certified Laboratory located at the Illinois State Water Survey.
Determinations were made for the following constituents:
calcium (Ca) ; magnesium (Mg) , sodium (Na) , strontium (Sr) ,
lithium (Li), chloride (CI), sulfate (S04) , alkalinity as CaC03,
and total dissolved solids (TDS) . Specific conductance and
laboratory pH were also measured at the time of analysis.
Standardized analytical methods were used and are briefly
described in Appendix 9-A. Results of the analyses are shown in
table 3-1 (mg/L) and table 3-2 (meq) .
Strontium and lithium ordinarily occur as trace elements in
natural waters and are not usually reported in a normal domestic
water well analysis. However, interelement ratios including
these elements have been useful in helping to differentiate
brines. In Section 6, Ca/Li, Mg/Li, and (Na+Li)/ (Ca+Mg-Sr) are
among the ratios used to differentiate oil field brine, shallow
brine, and freshwater groups.
INTERPRETATION
Conductivity and Regional Estimates of Water Quality
Measurement of conductance and temperature were made in the
field at the time of sampling. These data, listed in table 3-3,
are shown in comparison with laboratory measurement of specific
conductance. Groundwater temperatures observed in this study
ranged from 14° to 18°C (57° to 64°F) . Field conductance values
were found to be approximately 93% that of lab derived values.
In order to estimate water quality on regional scale, an
empirical relationship between field conductance and TDS
concentration was developed. Figure 3-2 shows the relationship
between field conductance measured at the time of sampling and
the analytical concentration of TDS, based on 20 of the 22
analyzed samples. Accurate field conductance values were not
obtained for samples OFB-16 and OFB-17.
A least squares regression line of best fit through the data
is described by the following equation:
Y = 0.665 X + 80.41
where: X = measured field conductance (in microsiemens/cm)
Y = predicted average concentrations of TDS (in mg/L)
and the linear correlation coefficient (r^) is 0.97.
48
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Figure 3-2.
Field conductivity (microsiemens/cm) of water
samples vs analyzed TDS concentration (mg/L)
2000
400
800 1200 1500 2000
Field conductance (microsiemens/cm)
2400
,amO^S GEOIOGICA*-
SURVEV
'JUL.
8A993
52
Estimated TDS concentrations for 197 of the 199 measured
wells located within the study area range from 147 to 2940 mg/L.
Conductance measurements of the two remaining wells, OFB-16 and
OFB-17, were highly inaccurate due to difficulties with the
conductivity meter. Analytical TDS concentrations of these tv;o
wells were 3292 and 2935 mg/L, respectively. Only 53 of the 199
wells had an estimated (or measured) TDS concentration in excess
of 1000 mg/L. TDS concentrations of these 53 wells were divided
as follows:
# between 1000 and 1500 mg/L = 38
# between 1500 and 2000 mg/L = 10
# between 2000 and 3000 mg/L = 4
# greater than 3000 mg/L = 1
Although 500 mg/L is the public and food processing water
qaulity standard for TDS in Illinois (Illinois Environmental
Protection Agency, 1985) , several municipalities in Illinois use
waters with TDS concentrations of 1500 to 2000 mg/L and domestic
wells often have water with up to 1000 mg/L (Illinois State Water
Survey 1962) . Water with 1000 mg/L or less TDS is generally
considered fresh, from 1000 to 10,000 it is considered brackish,
and water with 10,000 to 100,000 mg/L is considered saline
(Fetter, 1980) .
The field inventory of conductance data indicates that only
5 of the 199 wells measured may have anomalously high values of
TDS. Sample OFB-16 is the only one with a laboratory derived TDS
concentration exceeding 3,000 mg/L. No driller's log is on file
for the well from which this sample was taken; however, the
owner-reported depth of this well is 253 feet. The approximate
depth to the base of fresh water in this area is 250 to 300 feet.
Therefore the poor water quality in this well probably reflects
the natural salinity which should be expected in groundwater at
this depth in this portion of the study area.
OFB-17 (2935 mg/L analytical TDS concentration) , located in
23-3N-7E (SW NW NW NW) , is known to have originally been an oil
well 3063 feet deep (owner reported depth at 2800 feet) . It was
plugged back to 310 feet (owner reported 280 feet) when it was
converted to a water supply well. The generalized depth to the
base of the freshwater aquifer (estimated 2500 mg/L TDS) is 150
to 200 feet. While naturally occurring brackish water may be
expected at this well depth in this area, poor water quality may
also be related to well construction, plugging, or past oil
production at the site.
None of the other three wells identified by the field
inventory as having TDS concentrations between 2000 and 3000 mg/L
were sampled for chemical analysis. (These wells are identified
in Appendix 3-B under the name Don Wigley (23-3N-7E) , Harold Good
(29-3N-8E) , and Bonnie Wrey (29-3N-8E) . )■ The wells are reported
53
to be 201, 150, and 185 feet in depth, respectively. All are
completed in Pennsylvanian sandstone. A comparison of the depth
of each of these wells with the electric-log estimated depth to
the base of the fresh water aquifer indicates that the Wigley and
Wrey wells are completed within 20 feet of the estimated base of
the 2 500 ppm TDS aquifer. Therefore, the estimated water
quality reflects a natural salinity which should be expected at
those depths and locations.
Electric-log derived water quality data is very sparse in
the area of the Harold Good well (see figure 2-10) . Depth to the
base of the fresh water aquifer (estimated 2500 ppm TDS) may be
as much as 250 feet or as shallow as 180 feet. Since the well is
completed at 150 feet, its estimated TDS concentration of 2541
mg/L may also be a result of naturally occurring brackish water.
Well Depth and Proximity to Brine Pit vs Conductivity
Regression analysis was used to determine whether a
relationship exists between conductance (as a measure of water
quality) , and depth of the well and/or conductance and distance
from the nearest brine pit existed. Two single and one multiple
regression analyses were performed on the groupings of wells;
shallow wells (> 50 feet deep) , deep wells (> 50 feet deep) , and
combined shallow and deep wells. A total of 149 wells with
reported depths, located in and around the study area, were
included in the analysis. In all cases, conductance was the
dependent variable and proximity to a brine pit and well depth
were the independent variables. Results of these analyses are
shown in Appendix 3-C.
No significant correlation between conductance and well
depth and/or distance from the nearest brine pit was observed.
The highest linear correlation coefficient (r^) obtained was 0.39
for two of the deep well (> 50 feet depth) groupings; depth vs
conductance and depth and proximity vs conductance. The data
indicate that no widespread degradation of water supplies has
occurred in this area due to disposal of brine in pits. The lack
of correlation may be an artifact of the data; i.e., only 14
wells were located within an estimated 500 feet of a brine pit.
However, none of these 14 wells had water with electrical
conductance greater than 2000 microsiemens/cm (estimated 1410
mg/L TDS) .
Chemical Analyses and Water Type Characterization
Results of the chemical analyses of the 22 domestic water
well samples are graphically presented in figure 3-3. Data used
in plotting the trilinear diagram are given in table 3-2.
Bicarbonate (HC03) values were calculated from alkalinity, and
potassium was considered negligible.
54
Figure 3-3.
Trilinear diagram of major groundwater quality
parameters for samples obtained from domestic wells
in southeastern Clay County.
Cstions Antons
Hydrogeochemical classification sysiem (or natural waters using the Inlinear diagram
Classified as fresh (section 6)
Classified as brine (section 6)
A
/ \
/ \
/ \
/ ^^' /■ \ y
\ Ji
o
\
\
\
:-X
Ca
L .
4,15,16.17.19.21
■4 ^5
CI
55
The water samples can be grouped into two types: fresh
water and shallow brine. Major cations of the fresh water type
(as subsequently described in Section 6) are a mix of sodium
(Na) , calcium (Ca) , and magnesium (Mg) . The predominant cation
of the shallow brine type is sodium. Anions of the fresh water
group are bicarbonate or no dominant type, while anions of the
shallow brine group are predominantly chloride or no dominant
type. One sample, OFB-22, plots in the bicarbonate domain but
its cation facies is over 90% sodium; it is still classified as a
shallow brine.
The samples with the highest conductances and TDS
concentrations, OFB-16 and OFB-17, also have the highest
percentages of sodium (98.9% for both wells) and chloride (81.0%
and 74.2%, respectively) as reacting cations and anions. In
general, the group of samples identified as shallow brines in
Section 6, appear to fall in a domain characterized by 90% or
greater sodium as reacting cation and 50% or greater sulfate and
chloride as reacting anions.
Figure 3-4 illustrates the relationship of the major ions
(calcium, magnesium, sodium, and chloride) with depth. Calcium
and magnesium, tend to decrease as sodium and chloride increase
significantly. Plots of relative sodium and chloride
concentrations with well bottom elevations (figure 3-5) indicate
that elevated sodium and chloride concentrations are common below
300 feet (referenced to mean sea level) .
CONCLUSIONS
Groundwater availability in the study area is limited;
however, wells completed in shallow bedrock aquifers do yield
potable water at rates adequate for domestic supply. Brackish
water commonly occurs at depths of 150 to 250 feet (figure 2-10,
Section 2) . This water has high, naturally-occurring
concentrations of sodium and chloride.
Other potable water is yielded by shallow, large-diameter,
bored or dug wells. In general, these wells have water with
lower TDS concentrations and better overall water quality than
wells finished in shallow bedrock aquifers.
Although shallow, bored or dug wells are susceptible to
contamination resulting from abandoned brine pits, it appears
that no wells sampled for this study have been affected by oil
field brine contamination.
No widespread degradation of groundwater resources related
to brine disposal practices has been observed in the study area.
All 5 wells with estimated or measured TDS concentrations greater
than 2 000 mg/L were completed at depths where brackish water
could be expected to occur.
56
Figure 3-4
Well depth (feet) vs concentration of major ions;
calcium (Ca) , magnesium (Mg) , sodium (Na) , and
chloride (CI) .
120 160
Well depth (ft)
240
280 320
57
Figure 3-5.
Concentration of chloride and sodium
(milliequivalents) vs elevation of well bottom
(feet) for samples obtained from domestic wells in
southeastern Clay County.
440-
30
Sodium (meq)
40
I
50
60
440-
20 30
Chloride fmfta^
58
REFERENCES
Illinois Environmental Protection Agency, 1985, State of Illinois
Rules and Regulations - Title 35: Environmental Protection
Subtitle C: Water Pollution Chapter 1; Pollution Control
Board; Illinois Environmental Protection Agency, 44 p.
Illinois State Water Survey, 1962, Potential water resources of
southern Illinois: Illinois State Water Survey Report of
Investigation 31, 97 p.
Fetter, C.W. , Jr., 1980, Applied hydrogeology: Charles E. Merril
Publishing Company, Columbus, Ohio, 488 p.
59
SECTION 4 ASSESSMENT OF SURFACE WATER QUALITY
by
J. Rodger Adams, Billy K. Cook, and Raman K. Raman
INTRODUCTION
The surface water investigation focused on two locations:
1) Buck Creek which flows into the Little Wabash River in Clay
County and passes through an area of oil production and 2) a
surface runoff site near an abandoned and filled brine holding
pond. Two sampling sites were selected along Buck Creek to
determine any change in water quality as it flows through an
area with numerous oil wells and brine disposal sites. Sampling
at the runoff site was concentrated in an extensive gully and
rill system which is developing in the bare soil at the site.
Sampling included measurement of water quality and sediment
concentration at each site. In addition, bed material samples
were collected from Buck Creek and analyzed for particle size.
Generally dry. conditions in the study area resulted in low
discharges in Buck Creek and only a few measurable runoff events
in the gullies. Precipitation at Flora totaled 22.06 inches, or
17.4% less than the normal precipitation of 26.72 inches for the
period. July was the only month with above average
precipitation. The average temperature for this period was 2 . 5°F
above normal, and August was the only month with below normal
temperature. The above normal temperature would cause above
normal evaporation and reduced stream flow.
SITE DESCRIPTIONS
Buck Creek has a drainage area of 2 6.8 square miles. It
flows into the Little Wabash River, 145.9 miles upstream from the
Wabash River. The main stem has a length of about 21 miles and
an average slope of about 5 feet per mile. The basin relief is
120 feet. The Little Wabash River has a drainage area of about
780 square miles at the mouth of Buck Creek. The long-term
runoff in the Little Wabash basin is about 0.86 feet per year
(USGS, 1986) . This is an average discharge of about 20 cfs for
Buck Creek. The average annual sediment load is about 3,500 tons
(Bhowmik et al., 1986). The surrounding watershed area contains
active as well as inactive oil fields including abandoned brine
holding ponds and injection wells.
Two sampling sites were selected on Buck Creek and are shown
on figure 4-1 with the site codes BCU for the upstream site and
BCD for the downstream site. The drainage area is 17.25 square
miles at BCU, or 64.4% of the water-shed area. The downstream
site has a drainage area of 23.42 square- miles, or 87.4% of the
60
Figure 4-1.
Location of Buck Creek water sampling stations
(BCU=upstream, BCD=Downstream) . Location of gully
and rill runoff measurement site is denoted by CSO,
R 6 E
R 7 E
R 8 E
BCD Buck Creek sampling stations
O CSO Sampling station near abandoned
brir>e holding porvd
61
watershed area. The contributing area between BCU and BCD is
6.17 square miles, or 23% of the total watershed area. This is
an increase of 35.8% over the area at BCU. However, this area
has many more oil wells and brine separation tanks than the area
upstream of BCU. The slope between the two sites is 4.1 feet per
mile. These stream sampling stations on Buck Creek have provided
the necessary data for comparison of the effects of oil field
runoff on surface water quality in the study area. The upstream
station was used to sample a portion of the creek largely
uneffected by oil field activities and the downstream station was
used to sample a portion of the creek which may have been heavily
effected by these activities. This particular creek is subject
to the Illinois General Use Standards which were used to
determine the percentage of violation rate for the sampling
period of this report at both upstream and downstream sampling
stations.
An abandened, filled-in, brine holding pond was selected as
a surface runoff site and is located on figure 4-1 by the code
CSO. Figure 4-2 shows this site in greater detail. The land
slopes down to the east at about 4 percent. Runoff from the
bare soil has eroded two gullies which coalesce and flow eastward
into a field swale which empties into a road ditch and then flows
east into Elm Creek. The total length of the gulley is about 700
feet. Elm Creek is about 1200 feet east of the site.
Runoff from storm events at the runoff site was included in
the water quality analysis in order to determine surface water
impacts caused by abandoned brine holding pond runoff.
SAMPLING METHODS
Water quality and suspended sediment samples were collected
at the Buck Creek sites using the US DH-59 depth-integrating
suspended sediment sampler. This sampler and its use are
described in detail by Guy and Norman (1970) . Water quality
samples were composited to make the required volume.
Preservation of the samples was carried out as per standard
methods (APHA, 1980) . The water quality samples were kept iced
and shipped to the Illinois State Water Survey laboratory in
Peoria for analysis. Suspended sediment samples were delivered
to the Inter-Survey Geotechnical Laboratory in Champaign for
analysis. Temperature, pH, and dissolved oxygen were measured in
the field.
Table 4-1 includes descriptions of methods and materials
used for each water quality analyis. Raw data for upstream and
downstream sampling stations is contained in Appendix 4-A.
Samples were collected at these two stations approximately every
two weeks from April through September. All metal analyses were
performed in duplicate with blank and control samples for each
62
Figure 4-2.
Location of single stage sampling devices (A and B)
and bed material sampling stations (A1-A3, B1-B3,
AB) at gully and rill runoff site.
C3 Unvegetated area
- Observation well (entire length slotted)
Piezometer (2.5 ft screen)
■ Elevation datum
H NHS test plot
• intermittent drainage way
• Single stage sampler
• Sediment sampling station
100 ti
I
— 1
/
\/
/
Approximate boundary
of holding pond
JV_/
i/
Tank battery
63
Table 4-1. Methods of Chemical Analysis
Parameter
Ammonia Nitrogen
Boron
Bromide
Chloride
Electrical Conductance
EDTA Hardness
Grease and Oil
Iodide
Metals
Nitrate & Nitrite
PH
Phosphate
SuLfate
Total Alkalinity
Total Dissolved Solids
Total Kjeldahl Nitrogen
Total Suspended Solids
Total Volatile Solids
Method
Steam Distillation/Phenate Method. AllC^
Boron, Total Recoverable ( : 01022) ^
Catalytic Ocidation ( : 71870)2
Argentometric Method. 4 07^
Metrohm Conductometer Model -^
EDTA Titrimetric Method. 3146^
Partition-Gravimetric Method. 503A-^
Leuco Crystal Violet Method. 414a1''^
Flame Atomic Absorption. 3 03-^
Chromotropic Acid Method. 418D-^
Metrohm pH Meter/Glass Electrode
Vanadomolybdo Phosphoric Acid Method. 424D-
Turbidimetric Method. 42 6C^
Titration to pH 4.5^
Total Filtrable Residue. 209B^
Steam Distillation/Macromethod. 420A^
Total Nonfiltrable Residue. 209d1
Total Volatile Residue. 209e1
^ American Public Health Association. 1980.
2 United States Geological Survey. 1979.
-ductivities compared well with total filtrable residue as did
-.i-dness and selected mineral concentrations.
^ Inference with the Leuco crystal violet method of iodine. analysis forced
the use of standard addition methods for this analysis.
64
analysis group. Likewsie, alkalinity, hardness, chloride, boron,
bromide and residue analyses were duplicated.
Bed material samples from Buck Creek and soil samples from
the runoff site were collected using a shovel and were placed in
plastic ziplock bags for shipment to the geotechincal laboratory
for particle size analysis. The methods for the laboratory
analysis of sediments are given by Guy (1969) .
The measurement of sediment on the open field site during
runoff events presented particular problems. Unless the field
technician was present during a storm, he could not sample the
runoff. The exposed nature of the site, which is surrounded by
actively cultivated farm fields, precluded the installation of an
automatic pumped sampler. Therefore, a device called a single
stage sampler (model US SS-59, described in "A study of methods
used in measurement and analysis of sediment loads in streams"
(Federal Inter-Agency Sedimentation Project, 1981 was used) .
Each of these samplers consists of a standard pint sample bottle
and a stopper with two formed copper tubes which allow the bottle
to fill and retain a sample during a flow event. The dimensions
of the single stage samplers which were used at this site are
given in figure 4-3. Two of these were mounted, one above the
other on a post driven into the bed of the gullies at the
locations shown in figure 4-2. Because of the shallow depth of
the flow, the bottom bottle was actually buried in the bed of the
gully.
RESULTS
Buck Creek
Suspended sediment sampling was performed on 16 dates
(table 4-2) . The gage readings are inches below a fixed
measuring point. At the downstream site (BCD) the top of the
bridge deck at the downstream center was the measuring point and
at the upstream site (BCU) the top of the concrete curb at the
downstream center of the bridge was the measuring point. Though
discharge was not measured, the observed flow rates were all low
and essentially zero for gage readings over 132 inches at BCU and
97.5 inches at BCD. This was the case on 11 of the 16 sampling
dates. The specific conductivity was measured in the lab at the
time of the suspended sediment concentration analysis. These
values are similar to those measured in the water quality
samples.
The suspended sediment concentrations ranged from 14 to 4 8
mg/L at BCU with an average of 30.6 and a standard deviation of
12.0. Suspended sediment concentrations at BCD ranged from 22 to
87 with an average of 42.9 and a standard deviation of 17.6. The
average suspended sediment concentrations and average discharges
based on the regional runoff rate were used to estimate that the
65
Table 4-2. Suspended Sediment Data For Buck Creek
Date
Upstream Station
Cone. Cond. Stage
inq/1 umbo inches
Downstream Station
Cone. Cond. Stage
na/1 umho inches
3/25/86
4/03/86
4/08/86
4/18/86
4/29/86
5/06/86
5/13/86
5/20/86
6/03/86
6/17/86
6/24/86
7/08/86
7/22/86
7/29/86
48
490
130.0
26
707
130.5
33
892
130.5
14
718
131.2
31
671
131.0
18
754
132. 0
18
777
132.8
47
730
133.0
29
760
133.8
27
729
134.0
-
-
136.5
-
-
137.0
-
-
136.2
46
295
131.5
87
25
47
23
46
47
22
51
35
53
37
42
673
1013
948
1224
897
1133
1346
1208
1388
1400
1228
638
8 7. 0
92 . 0
86. 5
92
88
94
97
97
99.0
100.0
101.5
106.0
101. 0
99.0
Table 4-3. Suspended Sediment Concentrations at Case Study 1 Site.
Date
Gully A
C-ullv B
5/20/86
7/08/86
7/29/86
8/26/86
100, 000
30, 000
28,500
71,300
46,900
66
runoff entering Buck Creek between the two sites would have an
average suspended sediment concentration of about 77 mg/L. This
is over twice the concentration of BCU. The increases in
conductance and total dissolved solids indicate a large influx of
soluble compounds between the two sites. The dissolved solids
may be a direct result of the brines on the surface or mixed with
the surface soils. The increased influx rate of suspended
sediment may be due to erosion of the soils resulting from brines
raising the soil salinity above the level at which most plants
can grow.
Runoff Site
Suspended sediment concentrations were determined on four
dates (table 4-3) . Low precipitation during the sampling period
resulted in infrequent runoff events and limited the number of
samples collected. The water quality analyses were also
considered to be of greater value than suspended sediment at
this location. Thus, when only a partial sample was obtained
water quality parameters were analyzed instead of suspended
sediment concentration.
PHYSICAL CHARACTERISTICS OF BED MATERIAL
Buck Creek
Samples of creek bed material were collected from the
thalwrrg (deepest point of a cross section) downstream of each
bridge across Buck Creek. The six sample sites are marked in
figure 4-1 with the same codes given in table 4-4. The two
downstream sites have the finest bed material, with over half in
the silt and clay size-fractions. These variations in material
size are probably local. Using a soil classification (Terzaghi
and Peck, 1967) based on the percentages of sand, silt, and clay
in a sample, the bed material at locations BKl to BK4 is either
sand or sandy-loam, BK5 is loam, and BK6 is silty-clay-loam.
Runoff Site
Seven surficial samples of bed material were taken at the
locations indicated in figure 4-2. The letters "A" and "B"
correspond to the gullies in which the single stage samplers were
placed. Gulley A and the upstream end of gulley B have bed
materials classified as loam or sandy-loam. The downstream sites
in gulley B and the site downstream of the junction of the two
gullies are classed as sandy-loam. The bed materials at this
site primarily consists of sand and silt with less than 20
percent clay (table 4-5) .
67
Figure 4-3
Sketch of US 55-59 single stage sampler (after
Federal Interagency Sedimentation Project, 1981)
Sample
container
68
WATER QUALITY
Buck Creek
The surface water quality in the Buck Creek study area is
generally good. Of the 16 General Use parameters studied, four
exhibited violations. Ammonia was the only parameter
experiencing frequent violations with copper, iron and manganese
concentrations near the maximum allowable levels. Of the
unregulated parameters, only grease and oil concentrations seem
to be slightly elevated from those normally found in Illinois
surface waters.
Heavy precipitation in the study area during late May and
early June (figure 4-4) may have contributed to the steadily
increasing ammonia and phosphate concentrations, as well as that
of other constituents analyzed in this study (figures 4-5 through
4-9) . Possible contributing factors to the high ammonia and
phosphate concentration are agriculture fertilizers in the Buck
Creek watershed area coupled with atmospheric sources of ammonia
and phosphate (Kothandaraman et al., 1977). Algal blooms
observed during the sampling period reflected the elevated
concentrations of ammonia and phosphorous.
On only one occasion did dissolved oxygen (DO) concentration
in Buck Creek fall below the General Use Standard. This event
occurred during a period of no flow and reflected the stagnation
of the stream water at the sampling site. During periods of
flow, the creek appears to be well aerated with DO levels being
slightly lower at the downstream station. This fact could
possibly be associated with grease and oil concentrations
observed in the creek.
Although grease and oil concentrations fluctuated between 4
and 10 mg/L in the Buck Creek samples, run-off from the Case
Study Site contained an order of magnitude more, averaging 7 0
mg/L. Grease and oil in surface waters may cause decreases in DO
sufficient for fish kills.
Locally high concentrations of chloride, total dissolved
solids and grease and oil indicates that infiltration of brines
from the surrounding watershed may have occurred. Although
chloride and TDS concentrations did not exceed General Use
Standards, their increase from upstream to downstream stations
supports this implication (figures 4-7 and 4-8).
Table 4-6 indicates that bromide and sulfate concentrations
increased from upstream to downstream stations. The presence of
these two constituents in oil field brines again points to oil
production practices in the watershed area as sources. The
concentrations of these analytes, however, are not of sufficient
magnitude to warrant concern.
69
Location
Code
Table 4-4. Bed Material Characteristics Along Buck Creek
Percentage Composition
Gravel Sand Silt Clay
M e d i an
Diameter
mm
BK 1 ,
BK2
BK3
BK4
BK5
BK6 ,
BCU
BCD
18
95
13
50
040
020
2.4
70.7
17.3
9. 6
44 .9
51.0
4 . 1
0.0
1 .3
53.7
28.8
16.1
51.1
30.3
10.8
7.8
4.9
36.2
41.2
17.7
2.8
13.9
57.5
25 .8
Table 4-5
Bed Material Characteristics at Runoff Site
Location
C ode
M ed i an
Diameter
mm
Percentage Composition
Gravel Sand Silt Clay
A1
A2
A3
B1
B2
B3
AB
024
045
040
029
30
, 17
,30
1 .1
27.9
55.2
15.8
1 .2
43.4
38. 1
17.3
4.4
33.2
45 .9
16.5
3. 1
29.9
54.3
12.7
4.1
53.4
27.7
14.8
7.4
51 .2
23.7
1 7.7
3.9
62.8
18.1
15.2
70
Figure 4-4. Precipitation on Flora, Illinois, April-August, 1986
1.5
c
o
15 1 H
.5-
A K cdl cA
i I i
li
April
May
June
Sampling date
July
August
Figure 4-5. Hardness concentrations in Buck Creek,
350
300-
-r 250-
O)
E
V)
200
a
c
•o
CO
X
150
100-
50-
• Hardness - Buck Creek upstream
■ Hardness - Buck Creek downstream
April
May
June
Sampling date
July
August
71
Figure 4-6. Conductivity values in Buck Creek,
14CX)
1200-
c
a
E 1000-
0)
\n
O
o
e 800 •
^ 600
•o
c
o
O
400
200
• Conductivity - Buck Creek upstream
■ Conductivity - Buck Creek downstream
April
May
June
Sampling date
July
August
Figure 4-7. Chloride concentrations in Buck Creek.
300-
250-
200-
E,
"^ 150-
;g
o
x:
^ 100-
50-
• Chloride - Buck Creek upstream
■ Chloride - Buck Creek downstream
April
May
June
Sampling date
July
August
72
Figure 4-8. Total dissolved solids concentrations in Buck Creek
900-
Q
700-
500-
300-
100
• TDS - Buck Creek upstream
■ TDS - Buck Creek downstream
April
May
June
Sampling date
July
August
Figure 4-9. Total grease and oil concentrations in Buck Creek
16'
12-
E
fO
o
O
4 -
Oil/grease - Buck Creek upstream
Oil'grease • Buck Creek downstream
April
May
June
Sampling date
July
August
73
Metal concentrations, on the whole, were not excessive.
Sodium, potassium, calcium and magnesium concentrations appeared
typical of Illinois streams with only slight increases from
upstream to downstream stations. This may be attributed to
natural geochemical processes and poses no health threat at the
concentrations observed. Minimal violations for iron, copper and
manganese were observed and are attributable largely to
background contributions.
Good compliance records for most of the metals appear to be
due to limited solubility under ambient water conditions. Those
metals which appear to be solubility limited include barium,
lead, nickel, copper and zinc.
CONCLUSIONS
Buck Creek complies well with General Use Water quality
Standards where compliance can be achieved. Frequent difficulty
in maintaining the iron standard is primarily due to natural
background concentrations. Non-point sources of ammonia and
phosphorous also make it difficult to maintain these standards.
In reference to those constituents normally associated with oil
field brines,. Buck Creek is not unaffected. It is clear that the
surrounding watershed area contributes to the increased levels of
dissolved solids including barium, bromide, and chloride, along
with grease and oil.
Run-off from the gully system at Case Study Site 2 (table 4-
7) did contain elevated levels of several salient parameters
including bromide, chloride, boron, sodium, barium and manganese.
These constituents, frequently found in oil field brines,
indicate that runoff from this site could have a negative impact
on water quality in the surrounding watershed. Further
implications of natural seepage from abandoned brine holding
ponds combined with run-off results observed in this study could
explain concentrations of these constituents in surrounding
surface waters.
74
Table 4-6. Water Quality Data for Buck Creek
*A11 concentrations expressed as mg/L unless otherwise noted.
Upstream Sta.
?4in . Max . Mean
Efcwnstream Sta.
Man . Kzx . Mean .
General Use
Standard
Boron
Brondde
Chloride
Conductance (microsieroens)
Dissolved Oxygen
Grease and Oil
Hardness (as CaC03)
Iodide
Nitrate & Nitrite
pH (unit less)
Phosphate
Sulfate
Total Alkalinity
Total Dissolved Solids
Total Kjeldahl Nitrogen
Total Suspended Solids
Total Volatile Solids
Na
(Tot.)
K
(Tot.)
Ca
(Tot.)
Mg
(Tot.)
3a
(Tot.)
5a
(Sol.)
Cd
(Tot.)
Cd
(Sol.)
Cu
(Tot.)
Cu
(Sol.)
Cr
(Tot.)
Cr
(Sol.)
Fe
(Tot.)
Fe
(Sol.)
Li
(Tot.)
U
(Sol.)
Hn
(Tot.)
!'^
(Sol.)
Ni
(Tot.)
Ni
(Sol.)
Fb
(Tot.)
Fb
(Sol.)
Sr
(Tot.)
Sr
(Sol.)
Zn
(Tot.)
Zn
(Sol.)
0.09
0.03
0.14
21
295
5.7
4.1
89
<0.10
0.09
(7.68-8
0.07
28
97
150
0.44
12
1
38
4.2
26
6.3
0.03
0.03
<0.01
<0.01
<0.01
<0.01
<0.01
<0.01
0.43
0.01
<0.01
<0.01
0.26
0.13
<0.05
<0.05
<0.05
<0.05
0.08
0.08
0.01
<0.01
12.4
0.12
0.70
155
831
22.0
14.0
196
<0.10
0.47
,79)
0.26
106
155
472
14.4
46
7
124
6.0
60
15
0.07
0.06
<0.01
<0.01
<0.02
0.02
<0.01
<0.01
2.0
0.12
<0.01
<0.01
1.7
1.6
<0.05
<0.05
<0.05
<0.05
0.22
0.22
0.02
0.02
3.
0.
0.
94
647
6,
6,
170
28
09
46
0.27
0.12
67
123
386
4.22
22
4.1
85
5.0
46
12
0.06
0.05
0.92
0.05
0.78
0.53
0.16
0.16
0.02
0.18
0.08
0.55
123
638
1.4
2.6
151
<0.10
0.05
(7.6-8
0.09
32
105
336
0.45
27
2
38
4.3
37
13
0.05
0.04
<0.01
<0.01
0.01
<0.01
<0.01
<0.01
0.82
0.01
<0.01
<0.01
0.44
0.22
<0.05
<0.05
<0.05
<0.05
0.15
0.15
0.02
<0.01
,37
,82
4.73
0.14
1.10
260
1321
10.5
10.0
310
<0.10
0.48
.0)
0.
169
201
858
5.
54
18
287
10.1
86
29
0.13
0.09
<0.01
<0.01
0.04
<0.01
<0.01
<0.01
1.9
0.32
<0.01
<0.01
3.6
3.1
<0.05
<0.05
<0.05
<0.05
0.34
0.32
0.04
0.02
1.60
0.11
0.
182
1035
11,
6,
252
77
0.18
107
141
640
2.63
39
6.4
145
6.1
65
21
0.10
0.07
0.02
1.3
0.07
1.8
1.5
0.25
0.25
0.03
1.5
1.0
500
>5.0
6.5-9.0
0.05
500
1000
5.0
0.05
0.02
1.0
1.0
1.0
0.1
1.0
75
Table 4-7. Water Quality Data for Case Study Site 1
*A11 concentrations expressed as mg/L unless otherwise noted.
7/8/86
7/29/86
8/26/86
CSOBO
CSOA
CSOB
CSOB
ISG
3.95
1.54
IS
IS
2.97
3.22
IS
2.8
12.5
17.5
3.6
765
8,
250
3<
860
975
IS
IS
IS
IS
IS
72
62
76
251
2,
120
1-
,140
634
<0.5
<0.5
<0.5
IS
0.57
0.88
1.68
0.9
IS
27.9
18.7
1.9
43
108
68
25
35
6.4
6.4
6.4
1,700
9
,300
14
,900
1,490
IS
IS
IS
IS
28,500
100
,000
71
,300
46,900
1,560
3
,870
2
,580
1,380
500
1
,360
800
210
12
50
36
28
105
580
330
140
69
490
270
IS
48
280
130
68
20
180
92
IS
2.0
10.4
5.6
1.3
0.13
1.3
0.79
IS
<0.01
0.04
0.02
0.0
<0.01
0.02
0.01
IS
0.64
4.5
2.9
3.0
0.10
0.46
0.11
IS
0.18
0.64
0.44
0.4
<0.01
<0.01
<0.01
IS
31
125
112
86
0.02
0.23
0.12
IS
0.09
0.54
0.44
0.2
<0.01
<0.01
<0.01
IS
5.6
37
17
5.2
0.79
17
6.2
IS
0.25
1.0
0.72
0.6
0.05
0.30
0.10
IS
0.26
1.5
0.98
0.5
0.09
0.20
0.08
IS
1.7
7.5
3.7
1.2
0.42
7.2
3.6
IS
0.78
1.9
1.1
0.8
0.05
0.36
0.14
IS
NH3-N
Boron
Bromide
Chloride
Conductance (microsiemens)
Grease and Oil
Hardness (as CaCo3)
Iodide
Nitrate & Nitrite
Phosphate
Sulfate
-Total Alkalinity
Total Dissolved Solids
Total Kjeldahl Nitrogen
Total Suspended Solids
Total Volatile Soldis
Na (Tot.)
K (Tot.)
Ca (
Tot.)
Ca (
Sol. )
Mg (
Tot.)
Mg (
Sol. )
Ba (
Tot.)
Ba (
Sol. )
Cd (
Tot.)
Cd (
Sol. )
Cu (
Tot.)
Cu (
Sol. )
Cr (
Tot.)
Cr (
'Sol.)
Fe (
'Tot.)
Fe (
'Sol.)
Li
[Tot. )
Li
;soi.)
Mn
[Tot. )
Mn
[Sol. )
Ni
[Tot. )
Ni
(Sol.)
Pb
(Tot. )
Pb
(Sol.)
Sr
(Tot.)
Sr
(Sol. )
Zn
(Tot.)
Zn
(Sol. )
G IS - Insufficient Sample.
+ CSOA and CSOB represent two gullies sampled at Case Study Site 1
76
REFERENCES
American Public Health Association, 1980, Standard methods for
the examination of water and wastewater: 15th ed.
Washington, D.C., 1134 p.
Bhowmik, Nani G. , J. Rodger Adams, Allen P. Bonini, Anne M.
Klock, and Misganaw Demissie, 1986, Sediment loads of
Illinois streams and rivers: Illinois State Water Survey
Report of Investigation 106, Champaign, Illinois.
Federal Inter-Agency Sedimentation Project, 1981, Catalog:
Instruments and reports for fluvial sediment investigations:
Minneapolis, Minnesota.
Guy, Harold P., 19 69, Laboratory theory and methods for sediment
analysis: Chapter CI, Book 5, Techniques of Water-
Resources Investigations of the United States Geological
Survey: U.S. Government Printing Office, Washington, D.C.
Guy, Harold P., and Vernon W. Norman, 1970, Field methods for
measurement of fluvial sediment: Chapter C2 , Book 3,
Techniques of Water-Resources Investigations of the United
State Geological Survey, U.S. Government Printing Office,
Washington, D.C.
Kothandaraman, V., R. L. Evans, N. G. Bhowmik, J. B. Stall, D. L.
Gross, J. A. Lineback, and G. R. Dreher, 1977, Fox Chain of
Lakes Investigation and Water quality Management Plan:
Cooperative Resources Report 5, Illinois State Water Survey
and Illinois State . Geological Survey, Urbana, IL, 200 p.
Terzaght, Karl, and Ralph B. Peck, 1967, Soil mechanics in
engineering practice: John Wiley & Sons, Inc., New York,
New York.
U.S. Geological Survey, 1986, Water resources data for Illinois,
Volume 1 Illinois except Illinois River Basin: Water Data
Report IL-86-1, Urbana, Illinois.
U.S. Geological Survey, 1979, Methods for Determination of
Inorganic Substances in Water: Book 5.
77
Section 5 EFFECTS OF OIL BRINES UPON
BENTHIC COMMUNITIES IN BUCK CREEK,
CLAY COUNTY, ILLLINOIS
by
Allison R. Brigham and Edward A. Lisowski
INTRODUCTION
In 1983, the Greater Egypt Regional Planning and
Development Commission concluded that the oil field brine problem
in Illinois affected 45 percent of the counties. At that time
only three counties had been surveyed to assess the extent and
nature of brine damage and its affect upon soil and water
(GERPDC, 1983) . To illustrate the potential for damage to
surface waters, data from Jefferson County revealed that 69
percent of sites with brine-damaged acreage occurred within 0.25
mi or less of a stream and 55 percent occurred within 500 ft or
less (GERPDC, 1982) . Such contamination by oil brines may add
boron, bromide, chloride, heavy metals, oil and grease, sodium,
sulfate, suspended and dissolved solids, to surface waters.
A method of assessing the impact of a particular pollutant
upon surface waters is to examine the biological communities.
Stream community structure integrates long-term environmental
factors and critical conditions of short duration. The structure
and composition of benthic macroinvertebrate communities are
sensitive to perturbations or alterations in the abiotic
environment and, in general, their response to environmental
stress is expressed as lower species diversity.
During 1976 and 1977, the benthic macroinvertebrate
communities of the Wabash River watershed were studied by the
Illinois Natural History Survey (Brigham 1979) . Biological and
associated chloride data from approximately 500 sites from that
study were reexamined to assess the potential for water quality
degradation resulting from oil brine contamination of streams.
As part of the present inter-Survey oil brine research, Buck
Creek, a tributary of the Little Wabash River in southeastern
Clay County, was selected for more detailed investigation. This
watershed typifies hydrologic conditions and the level of oil
field activities occurring throughout southeastern Illinois.
Specifically, there were known cases of brine contamination;
numerous, yet localized, oil fields; available shallow
groundwater; and the interest and support of the local community.
Six sites were sampled in Buck Creek during August and
October, 1986 (figure 5-1) . Station 1 corresponded to the
upstream surface water quality site monitored by the State Water
78
Figure 5-1.
Location of sampling stations in the Buck Creek
watershed Clay County, Illinois.
H 6 E
R 7 E
R 8 E
79
Survey (see Section 4) ; station 6 corresponded to their
downstream site. Since benthic macroinvertebrate communities may
vary greatly temporally and spatially in response to variables
other than water quality, four additional sites were included to
ensure reliability.
BENTHIC MACROINVERTEBRATES AND CHLORIDE IN THE WABASH RIVER BASIN
1976-1977
In 1976 and 1977, approximately 900 sites were sampled in
the Wabash River basin in southeastern Illinois to assess
existing stream quality conditions based upon the composition of
the benthic macroinvertebrate communities observed. The effects
of approximately 200 point sources, agricultural non point
sources of pollution, and the presence of oil fields in the basin
were assessed (Brigham 1979) .
These sites were evaluated using the Illinois Environmental
Protection Agency's (lEPA) station classification system (a
tolerance-status approach described in Appendix 5-A) . Water
samples from 477 stations were analyzed for chloride to assist in
determining what, if any, effect the presence of oil well
operations in. the watershed had upon stream quality. Major river
basins within the watershed and the number of sites sampled
within each are illustrated in figure 5-2; summary benthic
macroinvertebrate, chloride, and stream order data are included
in Appendix 5-B.
Sites having both benthic macroinvertebrate and chloride
concentration data were re-examined. Sites were assigned to one
of six categories based upon the chloride concentration, defined
in table 5-1.
The lEPA general water quality standard for chloride is 500
mg/L; 4 58 sites or 9 6 percent met this stream standard. In fact,
nearly 70 percent of all chloride concentrations observed were
less than or equal to 50 mg/L. Only 19 sites (4 percent)
exceeded the 500-mg/L stream standard.
When a stream is stressed, as might occur from exposure to
oil brine contamination through discharge or surface runoff, the
biological communities are affected and frequently altered.
Generally, the part of its fauna that cannot tolerate the stress
(intolerant species) disappears while species less sensitive to
the particular change (generally tolerant, but may include some
moderate and facultative) are favored or unaffected.
A number of biotic index or classification schemes have
been proposed to illustrate the results of such stress or
impacts. The one used by lEPA is based upon the percentages of
organisms assigned to each of the four tolerance status groups
80
Figure 5-2
Distribution of sites of sampled for chloride in the
Wabash River watershed in Illinois.
c:h[r wabasm river tributaries
135 samples
>;^
81
Table 5-1
Distribution of Sites Sampled for Benthic Macroinvertebrates
Within Six Categories of Chloride Concentrations
Number
Category Chloride Concentration of Sites Percent
333
69.8
64
13.4
44
9.2
17
3.6
1 CI < 50 mg/L
2 100 mg/L < CI > 50 mg/L
3 250 mg/L < CI > 100 mg/L
4 500 mg/L < CI > 250 mg/L
lEPA General Water quality Standard = 500 mg/L
5 1,000 mg/L < CI > 500 mg/L 8 1.7
6 CI > 1,000 mg/L 11 2.3
Total: 477 100.0
(intolerant, moderate, facultative, tolerant; defined in Appendix
5-A) . The corresponding benthic macroinvertebrate data from the
474 sites (biological data unavailable for three chloride
sampling sites) were examined to see if station classifications
were generally affected by increasing concentrations of chloride.
Results are summarized in table 5-2.
Stations classified as balanced or unbalanced are considered
to be less disturbed by adverse environmental impacts than those
classified as semi-polluted or polluted. Group 1 (sites with
chloride concentrations < 50 mg/L) appeared to have more diverse
benthic macroinvertebrate populations. This was reflected in its
having 67 percent of its sites classified as either balanced or
unbalanced rather than the 45 to 55 percent of sites in groups 2
through 6. From these data, the effect of chloride concentration
appeared to be at 50 mg/L rather than the 500 mg/L general water
quality standard (table 5-2) .
If increasing concentrations of chloride contribute to
degradation of water quality, one expected outcome might be a
significant reduction in the number of organisms classified as
intolerant among sites with increasing chloride concentration.
The mean numbers of organisms assigned to each of the four
tolerance status groups is summarized in table 5-3.
82
Table 5-2
Stream Classifications Derived from Benthic
Macroinvertebrate Data at Sites Sampled for Chloride
Balanced/ Semi-Polluted/
Chloride Number Unbalanced Polluted
Category of Sites (%) (%)
108 (33)
33 (53)
20 (45)
9 (53)
lEPA General Water Quality Standard = 500 mg/L
5 8 4 (50) 4 (50)
6 .11 5 (45) 6 (55)
Total: 474 294 (62) 180 (38)
1
332
224 (67)
2
62
29 (47)
3
44
24 (55)
4
17
8 (47)
Table 5-3
Distribution of Benthic Macroinvertebrates
Among Four Tolerance Status Groups
Within Six Categories of Chloride Concentrations
Chloride Number Mean Number of Individuals
Category of Sites Intolerant Moderate Facultative Tolerant Total
1 332 17 13 23
2 62 12 12 20
3 44 12 11 15
4 17 8 8 16
5 8 10 11 25
6 11 8 5 19
474 15 12 22 39 SS"
31
84
70
114
52
90
34
66
41
86
50
82
83
A linear regression with chloride as the independent
variable and the number of intolerant organisms as the dependent
variables was performed. The numbers of intolerant (or
sensitive) organisms decreased significantly (P > 0.001) with
increasing chloride concentration.
The presence or absence of a species can also be influenced
by factors other than the concentration of a particular
contaminant such as chloride (e.g., its presence or absence in
the species pool available for colonization, the season of
collection, flow conditions at the time of sampling, chance, the
availability of the appropriate microhabitat, and longitudinal
position in the stream continuum) .
One additional variable was determined for each site to
distinguish (partially) naturally occurring changes in community
structure from those occurring in response to the presence of
increasing chloride concentration.
This variable was stream order and ranged from 1 (extreme
headwaters) to 8 (Wabash River) . A linear regression with stream
order as the independent variable was significant (P > 0.0001)
for intolerant organisms.
To identify the contributions of chloride and stream order,
a linear regression with two independent variables (chloride
concentration and stream order) was performed. For intolerant
organisms both chloride concentration and stream order were
significant (P > 0.001):
# intolerant [In (X + 1) ] = - 0.15 [In (chloride cone + l) ] +
0.7 6 [In (stream order + 1)] + 1.7 4
Although fewer numbers of organisms classified as intolerant
occurred at sites having higher concentrations of chloride, the
importance of stream order in the equation illustrates the
environmental complexities that influence the kinds and numbers
of species which may occur at a given site. Tolerance-status
based biotic index schemes, as applied to these data, rely upon
the presumed knowledge of the sensitivities of individual species
to widely ranging environmental variables. The pool of species
for which such information is known is limited. Assumptions are
made which are frequently limited or erroneous.
The tolerance-status approach as a tool to describe
environmental impact may be more appropriate in regions of the
country where the basin lithology results in ion-depauperate,
weakly buffered streams and rivers. In such areas the
environmental impact of pollutants may be more pronounced.
However, it is inappropriate in Illinois where the greater
84
buffering capacity of the water and the apparent wide tolerance
of native Illinois species to considerable variations in water
quality affords some protection against degradation.
This suggests that, even in the presence of urban,
agricultural non-point pollution, or oil brine runoff, the
absence of suitable substrate might be more of a limiting factor
to invertebrate colonization than we suspect. Extensive
channelization of natural streams, agricultural practices which
reduce the water-storage capacity of floodplains and transport
large quantities of sediment to streams, and the use of streams
as conduits to transport stormwater and the wastes of urban areas
have either removed or covered much of the natural stream
substrates in Illinois.
WATER QUALITY IN BUCK CREEK
The State Water Survey analyzed surface water at 2 -week
intervals from 3 April through 29 July 1986 at two sites in Buck
Creek: station 1, upstream, and station 6, downstream (Section
4) . For this statistical analysis, one (8 July 1986) of their
nine collections was eliminated since the upstream site had no
flow.
Of 34 chemical variables that were monitored, nine showed
significant differences between upstream and downstream areas in
Buck Creek (table 5-4) . These variables include the major
anions and cations which constitute dis-solved solids: chloride
and sulfate, and sodium, calcium, and magnesium. Specific
conductance, a measure of the ability of water to carry an
electric current, is often frequently expressed as total
dissolved ionizable solids. In most aquatic systems, total
dissolved solids is roughly equivalent to total dissolved
ionizable solids. Although these concentrations did not exceed
any applicable lEPA general water quality standards, all nine
variables in table 5-5 reflected sizeable increases in
concentration from upstream to downstream, suggesting
contributions of runoff or groundwater that were brine-rich.
BENTHIC MACROINVERTEBRATE COMMUNITIES IN BUCK CREEK
Four thousand four hundred thirty-two individuals
representing 97 taxa were collected from the six sampling sites
in Buck Creek during August and October. Kinds and numbers of
benthic macroinvertebrates collected are summarized in Appendix
5-C. These results, in general, illustrate a diverse community
representative of an average, low-gradient, slowly flowing,
sand/gravel-to-silt substrate stream in central Illinois.
Three major groups of benthic macroinvertebrates were
collected: (1) aquatic worms and leeches (Annelida); (2) scuds,
85
Table 5-4
Surface Water Quality Variables Showing
Significant Differences Between Upstream and Downstream
Sites in Buck Creek
Station
Variablea.b
1
fupstream)
6
f downstream)
Chloride
93.5
174
Specific Conductance (umho/cm)
646
1,
,011
Hardness (as CaC03)
170
249
Sulfate (as S04)
66.8
117
Dissolved Solids
386
626
Suspended, Solids
22
40
Sodium
84.9
144
Calcium
46.1
63.6
Magnesium
11.9
20.4
^ as mg/L unless other units are indicated; data provided
by State Water Survey (see Section 4)
^ means significantly different at the 0.05 level
isopods, crayfishes and prawns (Crustacea) ; and (3) seven orders
of aquatic and semi-aquatic insects. Aquatic and semi-aquatic
insects predominated, both in number of taxa and individuals.
Among insects, water beetles were the most diverse (28 taxa) ,
followed by aquatic and semi-aquatic true bugs (17 taxa) and
dragon-flies and damselflies (13 taxa) . Aquatic worms were
especially diverse (19 taxa) .
Most species were not numerically abundant. Sixty-two
species (nearly 64 percent) were represented by 10 or fewer
individuals (table 5-5) . This numerical dominance of uncommon
species is not unusual, although it is often mistakenly believed
to be a feature of unimpacted or unaltered ecosystems only. In
most communities there are usually a few numerically dominant
86
species and a much larger number of uncommon ones. In an
investigation of the physical, chemical, and biological variables
of streams receiving mine drainage containing high concentrations
of total dissolved solids, Brigham and Stegner (1982) observed
that 142 of 271 species from 50 sampling sites were represented
by five or fewer individuals.
Table 5-5
The Number of Individuals of Each Species Collected
and Related Summary Statistics
Total
. Number of
Cumulat:
Lve
Percent
Cumulative
Individuals
Number of
Number
of
of
Percent of
- Collected^
Species
Species
Total
Total
1
23
23
23.7
23.7
2
5
28
5.2
28.9
3
11
39
11.3
40.2
4
3
42
3.0
43.2
5
6
48
6.2
49.4
6
to
10
14
62
14.4
63.8
11
to
20
13
75
13.4
77.2
21
to
30
6
81
6.2
83.4
31
to
40
0
81
-
-
41
to
50
1
82
1.0
84.4
51
to
100
5
87
5.2
89.6
101
to
150
2
89
2.1
91.7
151
to
200
2
91
2.. 1
93.8
201
to
250
2
93
2.1
95.9
>250
4
97
4.1
100.0
Benthic macroinvertebrate data are summarized in Appendix 5-C,
Twelve species were ubiquitous, occurring at all sites in
Buck Creek. These included the aquatic worms Dero diaitata. Dero
nivea . and Aulodrilus pigueti; the crustaceans Hyalella azteca
and Palaemonetes kadiakensis; the mayfly Caenis, the water
boatmen Sigara modesta and Trichocorixa calva; and the water
beetles Hydroporus sp. A. Dubiraphia Ouadrinotata , Peltodvtes
duodecimpunctatus . and Scirtes.
At the other extreme, 3 3 species occurred at only one of
the six sites. These were widely represented among all the major
taxonomic groups of organisms: six species of aquatic worms, one
leech, one crustacean, one mayfly, two dragonflies, eight aquatic
or semi-aquatic true bugs, one dobsonfly, two caddisflies, and 11
water beetles.
87
If these results were evaluated using the lEPA stream
classification system discussed above, Buck Creek would be
classified overall as unbalanced since more than 10 percent of
the 4432 individuals collected could be classified as intolerant.
The upstream site at station 1 was consistently classified as
unbalanced and stations 3, 4, and 5 as semi-polluted (both August
and October collections) . Stations 2 and 6 were classified as
semi-polluted in August and unbalanced in October.
Mean chloride concentrations in Buck Creek ranged from 93.5
mg/L upstream at station 1 to 174 mg/L downstream at station 6
(table 5-5) . These concentrations place Buck Creek in chloride
groups 2 and 3, respectively (table 5-1). These groups were
approximately one-quarter of the sites sampled in the Wabash
River watershed. In terms of stream classifications, conditions
in Buck Creek could be interpreted as being generally poorer than
reported for other group 2 and 3 sites in the Wabash River
watershed. In Buck Creek unbalanced stations were only 3 3
percent and semi-polluted 67 percent compared to 47 to 55 percent
unbalanced and 45 to 53 percent semi-polluted for the entire
watershed (table 5-2) .
Relationships. Among Benthic Macro invertebrate Communities
Patterns of similarity among the biological communities at
the various sampling stations in Buck Creek were examined using
cluster analysis. Results, illustrated by the dendrograms in
figure 5-3, are presented separately by date.
In cluster analysis, stations are grouped according to the
similarity of aquatic communities present, with lower values
indicating greater similarity. The strength of the similarity
of stations in a cluster is shown by the proximity of the
branching of the dendrogram, i. e., the nearer to 0 the vertical
bars joining sites or groups of sites together, the more similar
the biological communities. The advantage of the cluster
analysis is that it eliminates making value judgements upon
individual species by avoiding the ranking of one species as
inherently better than another, as in the tolerance-status
approach used in many biotic-index schemes. Cluster analysis
produces a less biased assessment of the relationships among
sampling sites and, therefore, a less biased evaluation of the
extent of impact of a particular activity in the watershed.
There were two major groups of stations in the dendrograms
illustrating the results of the August and October benthic
macroinvertebrate collections from Buck Creek: stations 2, 3,
and 5, and stations 4 and 6. The collections at station 1 varied
seasonally, clustering with stations 2, 3, and 5 in August and
with stations 4 and 6 in October. These results closely followed
the relationships demonstrated among stations for species
diversity (figure 5-3) . Expressing community structure as
88
species diversity condenses biological information into a single
numerical value. It assumes that greater diversity of aquatic
life implies greater structural and functional stability of the
ecosystem.
Species diversity indices and the cluster analyses
integrated all data for 97 species in 12 collections. Among
those data, eight taxa illustrate some important general species
differences among the two major clusters. Station 1 was shown
separately in table 5-6 since it was more closely allied to the
cluster of stations 2, 3, and 5 in August and stations 4 and 6 in
October.
Table 5-6
Differences in Species Composition Among Clusters
Taxa
2,3,5
STATIONS
4, 6
Dero diqitata
Hyalella azteca
Palaemonetes kadiakensis
Caenis
Ischnura posita
Corixidae
Haliplidae
Scirtes
uncommon/common
common
abundant
common/ abundant
common
uncommon/ common
common/abundant
common
very abundant
common
common
uncommon
common
very abundant
common
very abundant
uncommon
very abundant
very abundant
common/abundan
very abundant
uncommon
very abundant
uncommon
Benthic macroinvertebrate communities in Buck Creek were
more diverse than might otherwise be expected from such a small
stream. The total number of taxa observed ranged from 25 to 48.
Species diversity was similarly high, with only one station/date
below 3.4 (figure 5-3, Appendix 5-C) . In such small streams,
seasonality and water level, and the diversity of microhabitats
available for colonization frequently limit the number of
species.
Buck Creek experiences extreme fluctuations in water level.
During the summer the upper portions (upstream of station 1) were
dry or discontinuous, with flow absent and water reduced to small
pools. Downstream channelized portions of the stream were long,
stagnant pools with little observable flow. Benthic biological
communities in small streams like Buck Creek are composed
predominantly of species with wide ecological tolerances that
89
Figure 5-3.
Species diversity and dendrograms illustrating
clustering analyses of benthic macroinvertebrates in
Buck Creek.
Speci es
Site Diversity
Averaae Distance Between Clusters
Auijust
2
4.2
3
3.S
5
3.9
1
4.4
4
3.5
6
3.5
'1 0.34
U.61
0.73
1.20
October
2
3.5
5
3.5
3
2.5
1
3.3
4
3.9
A
3.4
0.50
0.58
0.79
0.93
90
function as "pioneers" (i.e., species that colonize quickly by
moving into areas recently modified and unoccupied by other
species) . Such species are widespread in Illinois and are common
components of small streams which occasionally become
discontinuous or dry and frequently have little or no
microhabitat diversity.
In general, proceeding from source to mouth with increasing
stream order, streams become more diverse as more microhabitats
become available for colonization and exploitation. In the
absence of a constituent in the water which would be toxic to
aquatic life, the physical nature of the stream may be of more
importance in determining the benthic macroinvertebrate
colonizers than the concentration of any water quality variable.
No water quality variables were detected that might be
limiting or toxic to aquatic life (i. e. , none exceeded the lEPA
general water quality standards) . The limited microhabitat
diversity, however, was apparent in Buck Creek. The stream had
been historically channelized, rocky riffle areas were absent
along most of its length (only apparent at station 1) , the
substrate was primarily composed of fine or soft sediments (e.g.,
sand, clay, silt) , and undercut banks, log jams, and other
microhabitats were uncommon.
The importance of microhabitat diversity was demonstrated in
a study of physical, chemical, and biological variables of
streams receiving mine drainage containing high total solids
concentrations (Brigham and Stegner 1982.) Although the
distribution and abundance of benthic macroinvertebrates
suggested strongly that the observed differences among benthic
communities were attributable to higher concentrations of total
dissolved solids, subsequent analysis using measurements of
microhabitat diversity showed that the distribution and abundance
of species was not governed solely by water quality. Instead
stream order and microhabitat development were significantly more
important than any water quality variable tested.
Water quality and Species Diversity
Water quality deteriorated from upstream to downstream in
Buck Creek. Chloride, sulfate, sodium, calcium, magnesium,
specific conductance, hardness, and dissolved and suspended
solids all reflected sizeable increases in concentration from
upstream (station 1) to downstream (station 6) , suggesting
contributions of runoff or groundwater to Buck Creek that were
brine-rich (table 5-4) .
The benthic macroinvertebrate community of station 1
differed from that observed downstream at station 6. Species
diversity decreased from upstream to downstream, declining from
4.4 to 3.5. This is especially apparent in the dendrogram
91
illustrating the August collections (figure 5-3). Although the
communities of stations 2, 3, and 5 were more similar to station
1 than either stations 4 or 6, station 1 was still rather
distinct. It occupied an intermediate position between the two
clusters of stations.
Since the diversity of microhabitats available for
colonization declined downstream in Buck Creek and no water
quality variable violated existing lEPA general water quality
standards, the absence of a variety of microhabitats was
considered to be more limiting to benthic macroinvertebrate
diversity than degraded water quality.
To verify that water quality was of more limited importance
in determining the kinds and numbers of benthic macro-
invertebrates observed at the upstream and downstream sites in
Buck Creek, a stepwise regression was performed. In this
analysis, species diversity for stations 1 and 6 in August was
used as the dependent variable. Only August biological data were
used because the available surface water quality data were
collected from April through July. Results are summarized in
table 5.7.
Table 5-7
Stepwise Regression Procedure for Species Diversitya
Variance
Step Variable f percent) Probability > F
1 Magnesium 51.4 0.0018
2 Suspended Solids 73.5 0.0058
Magnesium 0.0050
3 Ammonia 83.7 0.0179
Suspended Solids 0.0004
Magnesium 0.0080
^ Alpha level for entry and exit = 0.15. The model selected from
the 20 water quality variables described in Appendix 5-A;
species diversity from stations 1 and 6 in August.
In this analysis no variable that would be unambiguously
associated with contributions of brine was selected as an
important predictor of species diversity. Ammonia, suspended
solids, and magnesium would account for nearly 84 percent of the
variance in predicting species diversity. Although the
92
distribution and abundance of benthic macroinvertebrates
suggested that the observed differences among upstream and
downstream benthic communities were attributable to higher
concentrations of variables associated with oil brine, regression
analysis showed that the distribution and abundance of species
was not governed solely by water quality. Instead, another
variable such as microhabitat development was likely more
influential in Buck Creek.
LITERATURE CITED
Brigham, A. R. , 1979, An assessment of the water quality of the
Wabash River basin derived from a biological investigation:
Unpublished report to the Illinois Environmental Protection
Agency. vi + 297 pp.
Brigham, A. R. , W. U. Brigham, and A. Gnilka, 1982, Aquatic
insects and oligochaetes of North and South Carolina:
Midwest Aquatic Enterprises, Mahomet, Illinois. 837 pp.
Brigham, A. R. , and S. Stegner, 1982, Comparative study of
physical., chemical, and biological variables of streams and
lakes receiving mine drainage containing high total
dissolved solids: Unpublished report to the Mine-
Related Pollution Task Force. iv + 53 pp.
Greater Egypt Regional Planning and Development Commission, 1982,
An overview of oil field brine problems in three Illinois
counties: Publ . No. GERPDC-82-626. iii + 52 pp. +9
individually number appendices.
Greater Egypt Regional Planning and Development Commission, 1983,
Procedures for evaluation and reclamation of oil field
brine damage with recommendations for individual, local and
state actions: 1983 oil field brine special project
report. Publ. No. GERPDC-83-643 . 24 pp.
93
Secton 6 INVESTIGATIONS OF THE ORIGIN OF DOMESTIC
WELL WATER CONTAMINATION BY SALINE WATERS
by
John D. Steele and Barbara R. Cline
GEOCHEMICAL CHARACTERIZATION OF BRINES
Oil field brines are highly concentrated (total dissolved
solids reaching 160,000 mg/L or more) aqueous solutions which
also contain high concentrations of potassium, calcium, and
magnesium. The brines of the Illinois Basin have been
characterized as calcium chloride brines due to their relatively
high concentrations of calcium when compared to halite derived
brines or seawater.
Table 6-1 is a summary of data for major constituents (Na+K,
Ca, Mg, and CI) in oil field brines for various formations in
Clay County and the counties surrounding the study area
(Crawford, Edwards, Effingham, Fayette, Jasper, Lawrence, Marion,
Richland, Wabash, and Wayne) . The data are taken from Meents et
al. (1952) .
Observed differences in the compositions of brines from
various depths within the Illinois Basin are explained by Nesbitt
(1985) as reflecting the geochemical origin of the brines. The
chemical compositions of the brines, according to Nesbitt (1985) ,
are controlled by mineral transformations involving the
equilibrium of the brines with kaolinite, illite, a sodic clay
mineral, and calcite. As proposed by Graff et al., (1966), during
the concentration of the brines by ultrafiltration, kaolinite
and calcite are consumed while a sodic clay is produced,
resulting in a decreased Na/Ca ratio of the brine relative to the
precursor solution. When the brines are mixed with near-surface
waters and are diluted, calcite and kaolinite are produced while
the sodic clay is consumed, causing an increase in the Na/Ca
ratio of the brine. Evidence for this behavior can be seen in
table 6-2, which shows concentration ratios of Na/Cl, Ca/Cl,
Mg/Cl, and Na/Ca for the data from Meents et al. (1952).
The variations in composition of Clay County oil field
brines relative to the rest of the Illinois Basin can best be
explained by the correlation of composition with depth (both
within and between formations) and the nearness of Clay County to
the center or deepest part of the basin. The brines of Clay
County often have as much as 3 0 percent higher TDS concentrations
relative to the rest of the Illinois Basin although this pattern
varies from formation to formation. Tar Springs concentrations
are highest in Clay County and to the southwest, and become less
concentrated to the north and east. Cypress brines
94
Table 6-1
Summary of Brine Data from Meents et al
Formation and
Location
Na & K
(mg/L)
Ca
(mg/L)
(1952)
Mg
(mg/L)
CI
(mg/L)
Pennsylvanian
Clay Co.
Othersl(8)
Mississippian
Tar Spring
Clay Co. (2)
Others (4)
mean
std. dev,
mean
std. dev,
mean
std. dev,
9290
5079
42691
163
32446
3428
331
236
3876
1
3177
482
All data
mean
std. dev.
40324
4791
5449
1197
201
116
1189
45
626
414
1863
519
^Crawford, Edwards, Effingham, Fayette, Jasper, Lawrence, Marion,
Richland, Wabash, and Wayne Counties.
14251
8989
75896
437
56468
6600
All data
mean
35861
3410
813
62944
std.
dev.
5920
519
434
11262
Cyress
Clay Co. (7)
mean
38187
3060
1216
68467
std.
dev.
5007
1148
143
9504
Others (30)
mean
36565
3975
1260
66890
std.
dev.
4136
831
365
7720
All data
mean
36872
3801
1251
67188
std.
dev.
4286
953
333
7866
Aux Vases
Clay Co. (5)
mean
43610
4871
1317
79155
std.
dev.
3461
622
183
5746
Others (13)
mean
44044
5877
1475
81692
std.
dev.
4847
715
378
8522
All data
mean
43924
5598
1431
80987
std.
dev.
4410
817
338
7772
Ste. Genevieve
Clay Co. (17)
mean
44334
5657
1535
82753
std.
dev.
3547
1251
624
5703
Others (38)
mean
38531
5356
2008
73697
std.
dev.
4167
1177
392
7335
76496
8021
0.685
0.0246
0.0166
175.2
0.575
0.0526
0.0135
11.1
0.555
0.0559
0.0189
10.4
0.547
0.0680
0.0175
8.2
0.527
0.0714
0.0247
7.8
95
Table 6-2
Concentration Raios of Selected Constituents
in Oil Field Brines
(Meents et al., 1952)
Formation Na/cl Ca/Cl Mg/Cl Na/Ca
Pennsylvanian
Tar Springs
Cypress
Aux Vases
Ste. Genevieve
concentrations are highest west of Clay County and the
concentration decreases from west to east. Aux Vases brines
concentrations are highest in central Clay County and to the
south and west, and show a decrease to the northwest, north, and
east. Ste. Genevieve brines are more concentrated in southern
Clay County and to the south, and are less concentrated to the
west, north, and east.
It can be seen from table 6^1 that, for each constituent,
there is a general increase in concentration with increasing
depth (age) of formation. This trend is most obvious between the
Pennsylvanian and Mississippian formations where the mean
concentrations of the major constituents are significantly lower
in the Pennsylvanian brines than they are in the Mississippian
brines. These differences in composition between formations will
be used to differentiate between brines from different sources.
There are numerous examples in the literature of the
application of geochemical methods to differentiate brines from
different sources. Collins (1978) studied the geochemical
relationships between high iodide brines and the geologic strata
of Oklahoma. Rittenhouse (1967) used the relationship between
bromide and total dissolved solids to subdivide oil field brines
into at least five groups based on their origins. More
recently, Whittemore (1984a and 1984b) used bromide/chloride and
iodide/chloride ratios to identify sources of contamination in
aquifers of Kansas.
SAMPLE LOCATIONS AND DATA PRESENTATION
Thirty-one samples of oil field brines were collected from
sites shown in figure 6-1. The samples were collected from
producing oil wells from the following formations: Tar Springs,
Cypress, Aux Vases, McClosky, and Salem. Two samples consisted
96
almost entirely of oil with insufficient brine volume for
analysis. The producing zone of one brine sample could not be
identified. The analytical data for the brines for which there
was sufficient sample volume are shown in table 6-Al of Appendix
6-A.
INTERELEMENT RELATIONSHIPS
In order to examine the interelement patterns associated
with these brines, a matrix of correlation coefficients between
each element was produced and used to group the elements into
clusters with similar patterns of behavior using cluster analysis
(see figure 6-2) . In the cluster analysis procedure, each
constituent is grouped or clustered with those remaining
constituents with which they show a similar pattern of behavior.
Each remaining constituent is either assigned to an already
existing group with which it most closely resembles or it forms
its own group. This procedure is continued until all the
constituents are assigned to groups.
As expected, sodium and chloride, comprising 9 5 percent of
the brine, were significantly correlated (0.85). The minor
constituents <:alcium, magnesium, and strontium also showed
significant, although lower, correlations with chloride. Sodium
showed only one other significant correlation, that with calcium.
Calcium, magnesium, potassium, and lithium as a group showed
relatively high interelement correlations, with potassium and
lithium showing the highest correlation of any of the elements
(0.95). Strontium correlates weakly with magnesium and chloride
but not with calcium. Iron does not show any significant
correlations.
The cluster dendrogram shown in figure 6-2 combines the
elements into mutually correlated groups. The measure of
similarity decreases from left to right so that clusters shown to
form to the left in the dendrogram possess greater similarity
than those clusters which form to the right. The clustering of
the elements shown in Figure 6-2 appears to follow basic
chemical principles. The Na-Cl cluster reflects their dominant
influence in the composition of the brines. The alkali elements,
K and Li, form a cluster, and the alkaline earth elements, Ca and
Mg, form a cluster. These three clusters then form a large six
element cluster. Strontium and iron, which show the weakest
interelement correlations do not fall into any particular
grouping, although strontium does correlate weakly with
magnesium and chloride.
Another method of looking at the interelement relationships
is with factor analysis, a statistical technique which tries to
identify a relatively small number of underlying factors which
explain relationships among a large number of variables. A
discussion of factor analysis is beyond the scope of this report
97
Figure 6-1.
Location of Mississippian Age Formation Water
Sample Sites.
R 6 E
R 7 E
R 8 E
Wayne Co.
98
Figure 6-2
Cluster analysis of Clay County oil field brine
constituents .
A. INTER-ELEMENT CORRELATION MATRIX
Na
Ca
Mg
Li
Sr
Fe
CL
Na
1.0000
.3144
.6355**
.4053
.1028
.3809
-.0627
.8531**
K
.3144
1.0000
.5562**
.5991**
.9499**
-.0905
.2903
.3804
Ca
.5355**
.6662**
1.0000
.7648**
.5083*
.1828
.3362
.7744**
Mq
.4063
.6991**
.7648**
1.0000
.6413**
.4333*
.4107
.5202**
Li
.1028
. 9499**
.5083*
.5413**
1.0000
-.1428
.3133
.1711
Sr
.3809
-.0905
.1828
.4333*
-.1428
1.0000
.1997
.4257*
Fe
-.0627
.2903
.3362
.4107
.3133
.1997
1.0000
.1122
CI
.8531**
.3804
.7744**
.5202**
.1711
.4267*
.1122
1.0000
1 -tai 1 ed Signi f :
01
- .001
B. CLUSTER DENDROGRAM
Decreasing Similarity
Element
0
+
10
- + ■
15
— + _,
20
25
K
Li
J
Ca
Mg
Na
CI
Fe
Sr
99
and the reader is referred to Davis (1973) , Korth (1975) , or
Tabachnick and Fidell (1983) .
The results of the factor analysis are shown in table 6-3.
The right hand portion of the upper table shows that three
factors were extracted which account for 88 percent of the
variance in the data. The column labeled communal ity in the
upper table shows the proportion of the variance for each
constituent which can be accounted for in the three factor model.
The lower table of coefficients shows the factor loadings
of the three factors for each constituent. In this analysis, the
coefficients can be thought of as the correlations between the
factors and the constituents. Factors with high loadings (in
absolute value) therefore indicate a close relationship between
that factor and the constituent. The first factor, which
accounts for 50 percent of the variance, shows high loadings for
CI, Na, Sr, and Ca. The second factor, which shows high loadings
for K, Li, and Mg, accounts for an additional 25 percent of the
variance. The final factor shows a high loading for Fe only, and
it accounts for an additional 13 percent of the variance. The
first factor most likely reflects the metal-chloride
interrelationship found in the brines for the elements loaded for
this factor, while the second factor most likely reflects the
elements which are not as strongly associated with chloride. The
third factor probably reflects the low correlation which iron has
with all the other elements.
PRELIMINARY ANALYSIS
Mississippian Brine Groupings by Formation
A summary of mean concentrations of the major, constituents
by formation for the Clay County oil field brine data are shown
in table 6-4. The concentration trends with depth, as discussed
for the Meents et al. (1952) data are much less pronounced for
the current data. Analysis of variance reveals that the same
trends, although fairly subtle and with considerable overlap, are
still in effect. The lowest concentrations for the constituents
shown are found in the Tar Springs and Cypress brines while the
highest concentrations are found in the Aux Vases, McClosky, and
Salem brines.
In the previous discussion, cluster analysis was used to
examine inter element relationships and to cluster the elements
into groups with similar patterns of behavior. The resulting
cluster dendrogram is shown in figure 6-3, where the individual
samples are identified by the formation of the producing zone.
It can be seen that the clustering process is only partially
successful. One relatively distinct cluster consists of seven of
the eight Salem brines and one Cypress brine. A second cluster
is composed of five of the six Cypress brines and one McClosky
100
Table 6-3
Factor Analysis of Oil Field Brines
Variable Communal ity Factor
Eigenvalue
Pet of Var
Cm Pet
4.00989
50.1
50.1
2.01574
25.2
75.3
1.02343
12.8
88.1
log(Na) .87504 1
log(K) .96943 2
log(Li) .94363 3
log(Ca) .84485
log(Mg) .83333
log(Sr) .74506
'(Fe) .92054
log(Cl) .91720
Varimax Rotated Factor Loading Matrix
Factor 1 Factory 2 Factor 3
log(Cl) .91948 .25264 -.08902
log(Na) .87542 .15219 -.29242
log(Sr) .80090 -.21806 .23678
log(Ca) .70651 .58605 .04734
log(K) .15697 .97170 .02054
log(Li) -.10369 .96287 .07586
log(Mg) .51422 .72506 .20783
log(Fe) -.04766 .14241 .94762
101
Table 6-4
Summary Means of Clay County Oil Field Brine Data^
FORMATION
Na
K
Ca
Mg
Li
Sr Fe
CI
Tar Springs
Cypress
Aux Vases
McClosky
Sal em
(2)
(6)
(3)
(H)
(8)
45900 b
38660a
48280 b
45550 b
46950 b
91a
188a
176a
180a
418 b
3625a
3632a
Slllab
4309ab
5498 b
1230a
1378ab
1347ab
1510ab
1950 b
2.2a
9.1 b
5. lab
6. Sab
16.8 c
168a
96a
222a
282a
139a
22a
15a
6a
15a
44a
78070 b
65890a
84170 b
78370 b
81170 b
Grand Mean (30) 44880 239 4525 1503 9.4 193 23 77180
^ For each element, means with the same letter are not
significantly different at the 95 % confidence level
using Duncan's Multiple Range Test.
102
brine. The remaining clusters consist of a mix of the formations
with no dominating single formation.
In the preceding cluster analysis, the samples were grouped
into clusters based on similar patterns of behavior of their
measured constituents. No prior assumptions were made about the
grouping of the samples by formation. If the prior knowledge of
the groupings by formation is used, then canonical discriminant
analysis can be used to arrive at a grouping scheme.
Discriminant analysis derives a linear combination of the best
predictor variables so that differences among the groups is
maxir.- 3d. Based on the derived function or functions, new
samples may be assigned to their respective groups. A discussion
of discriminant analysis may be found in Tabachnick and Fidell
(1983), Norusis (1986), or Sanathanan (1975).
It should be emphasized that the applications of
discriminant analysis which are to follow cannot be considered
statistically rigorous. The major deficiency is the limited
number of samples which can be used to define each group. The
minimum number of samples in the smallest group should be about
twenty if multivariate normality is to be expected.
In applying the method of discriminant analysis to the oil
field brine data, interelement ratios were used instead of the
individual elements so that factors such as dilution would not
affect the groupings. The results of the discriminant analysis
for the brine data from the five Mississippian formations is
shown in figure 6-4. Effective grouping of all of the brines was
achieved using two functions. The calculated discriminant scores
for each brine, plotted as upper case letters, fall within the
zones established by the discriminant analysis. Based on this
grouping scheme, the one brine sample of unknown origin was
classified as coming from the Aux Vases, although it should be
noted that this sample does not plot very close to the class
centroid for the Aux Vases group.
Mississippian Versus Pennsylvanian Grouping
The above discussion has dealt with the grouping of the
brines collected from various Mississippian formations. The goal
of this project required only that differentiation be made
between the shallow Pennsylvanian brines and those Mississippian
brines being generated as a result of oil production activity. A
major difficulty arose, though, which prevented or at least
severely limited the successful completion of this part of the
task. We initially anticipated that the shallow brine samples
would be collected from Pennsylvanian source water wells used to
produce injection water for water flood operations. However the
poor economy in the oil industry during the study period resulted
in the shut-down of many oil wells and the shallow Pennsylvanian
source water wells in the study area.
103
Figure 6-3.
Cluster dendrogram, brines from Mississippian
formations in southeastern Clay County.
Formation
0
+ --
Decreasing Similarity
5 10 15
^
20
25
\.
- - +
SALEM
SALEM
SALEM
SALEM
SALEM
SALEM
SALEM
CYPRESS
MCCLOSKY
MCCLOSKY
MCCLOSKY
CYPRESS
CYPRESS
CYPRESS
CYPRESS
MCCLOSKY
CYPRESS
TAR SPRINGS
MCCLOSKY
TAR SPRINGS
MCCLOSKY
SALEM
MCCLOSKY
MCCLOSKY
UNKNOWN
AUX VASES
MCCLOSKY
AUX VASES
MCCLOSKY
MCCLOSKY
AUX VASES
J
n
J
J"
J
104
Figure 6-4
Discriminant analysis, brines from Mississippian
formations in southeastern Clay County.
-16.0
15.0 t*
12.0 ■■
8.0 ■■
4.0 •■
0.0 ■■
-4.0
-8.0
-12.0 ■■
16.0
-15. O'
■12.0
, Canonical Discriminant Function 1
-£..0 -4.0 0.0 4.0
8.0
12.0
15.0
ssstt
sstt
sst
ss
s
tt
ctt
scttt
sccctt
sccccc
ssc c
sc
sec
ssc
sc
sec
ssc
sc
sec
ssc
sc
sc
sc
ss
s
s
s
TAR SPRINGS
t
ttt
cctt
ccttt
cccttt
cccttt
ccctt
ecttt
eeettt
cccttttt
cniitiiiitttttt
T •!
CYPRESS
crrm iiiiiiiiiiiiitttttt
s s
s
SALEM
c
c
c
cc
sc
sc cc
sec
ssc
sc
sec
ssc
sc
sec
ssc
sc
sec
ssc
sc
sec
ssc
sc
sec
ssc
sc
sec
ssc
sc
C C
ccm
an
em
em
em
em
cm
cm
cm
ci
ccm
cm
iiiirirmiitttttt
imiiiiiiiiitttttt tttt
TTTTTTTTTTVtUttt tttttttadfl
i;i;i!i:iTTntttocacaaa
rrTicoca
rrr.sa
mrrriaa
rmaaa
M
mm M
H
M *M
M MM
HCCLCSKY
cm
cm
cm
em
cm
cm
em
cmm riTTTTiaa
ccmrmaaa
cnrnaa
eemaa
caaa
cea
ceaa
eaa
cea
ceaa
mTTfaa
nrnaaa
iiiiiiiaa
rrnaaa
rrrr.aa
mmaa
rrmaaa
i!iiiiiaa
rrmaaa
mrrmaa
riT^aa
AUX VASES
-12.0
-8.0
-4.0
secccaa
ssecaa
scca
-H h-
0.0
4.0
8.0
12.0
i6.0
* Group Centroids, f Unknown, T Tar Springs, C Cypress. A Aux Vases, M HcC'.osky, S Salem
Unstandardized Canonical Discriminant Function Coefficients
FUNC 1
FUNC 2
Ca/Cl
-1584.745
-548.4712
Li/Cl
138351.8
205969.1
Ka/K
.1054185E-
■01
-.7259851E-01
Na/Mg
-2.005153
1.827889
Na/Li
-.5055750E-
■02
-.2747752E-02
Ka/Sr
-.8309050E-
■01
-.2530177E-01
K/Mg
95.93858
21.35844
K/Li
-.5850196
-.9188802
Ca/Hg
45.30396
-3.323473
Ca/Sr
-.2340535
.5590730
Hg/Li
.2425754
.2356895
Kg/Sr
3.356902
.7418412
Li/Sr
-238.9912
-247.4514
(Ka+Li
)/Cl
119.9517
53.34898
( Na+L 1
)/(Ca+Hg+Sr)
3.8S1433
-2.554487
(constant)
-95.12807
-35.79255
105
Because of our inability to collect samples of shallow
Pennsylvanian brines, the data from Meents et al. (1952) for
Pennsylvanian waters were used to construct a preliminary
differentiation scheme. The use of these brine data introduced
considerable uncertainty into the analysis which follows because
none of the samples came from Clay County, the number of
analyses performed on these samples is limited, and the data are
extremely variable. The data for these Pennsylvanian brines are
reproduced in table 6-A4 of Appendix 6-A and summary statistics
are shown in table 6-1.
The previous discussion of the differences between the
Pennsylvanian and Mississippian brine data of Meents et al.
(1952) has the same relevance for the current set of
Mississippian brine samples. T-tests performed on the two sets
of data (current Mississippian brines and Meents et al. (1952)
Pennsylvanian brines) show that the means of the two groups for
the following constituents and constituent ratios are
significantly different at the 95 percent confidence level: Na,
Ca, Mg, CI, Na/Cl, Ca/Cl , Ca/Mg, and Na/Mg.
Cluster analysis was performed on the current brine samples
and the Pennsylvanian brines from Meents et al. (1952) using the
following interelement ratios: Na/Cl, Ca/Cl, Mg/Cl, Na/Ca,
Na/Mg, Ca/Mg, (Ca+Mg)/Cl, and Na/(Ca+Mg). Figure 6-5 shows
that the two major clusters, both of which form relatively tight
groups, consist entirely of the Mississippian samples in one
group, and the Pennsylvanian samples in the other.
The results of the discriminant analysis using the same
ratios as those used in the cluster analysis are shown in figure
6-6. A single discriminant function is derived and the resulting
discriminant scores for each sample are plotted as a histogram.
Figure 6-6 shows that there are two relatively distinct groups
representing the two brine types. The current Mississippian
brines form a much tighter group than the Pennsylvanian brines
and one of the Pennsylvanian brines is classified incorrectly as
Mississippian.
EVALUATION OF DOMESTIC WELL WATERS
Mississippian, Pennsylvanian, Fresh Water Groupings
The next step in evaluating the discrimination procedure
involves the incorporation of a fresh water group into the
process. The domestic well water samples collected for the
study of domestic well water quality (Section 3) provide the
members for this group. Of the 22 well water samples collected,
eight samples with specific conductance values of less than 1000
microseimen/cm were selected as representing the fresh water
group. The remaining fourteen domestic well water samples were
considered as unknowns.
106
Figure 6-5
Cluster dendrogram, brines from Mississippian and
Pennsylvanian formations in southeastern Clay
County.
Formation
Decreasing Similarity >
5 10 15 20 25
PENN
PENN
PENN
PENN
PENN
PENN
PENN
PENN
PENN
MCCLOSKY
MCCLOSKY
MCCLOSKY
SALEM
SALEM
SALEM
SALEM
SALEM
AUX VASES
MCCLOSKY
MCCLOSKY
SALEM
SALEM
CYPRESS
CYPRESS
MCCLOSKY
CY' .S
MCCLOSKY
CYPRESS
CYPRESS
CYPRESS
UNKNOWN
AUX VASE
MCCLOSKY
MCCLOSKY
SALEM
TAR SPRINGS
TAR SPRINGS
MCCLOSKY
MCCLOSKY
AUX VASE
107
Figure 6-6
Discriminant analysis of brines from Mississippian
and Pennsylvanian formation in southeastern Clay
County.
Canonical Discriminant Function 1
8 + +
Mississippian MM
Pennsyl vani an
MM
MMMM
MMMM
MMMM
5 +
4 +
MMMMM
MMMMM
2 + MMMMMM P " +
MMMMMM P
MMMMMMMM PP PP P P P
MMMMMMMM PP PP P P P
X + 4- + + + + + X
Out -5.0 -4.0 -2.0 0.0 2.0 4.0 6.0 Out
MMMMMMMMMMMMMMMMMMMMMMMM PPPPPPPPPPPPPPPPP
Class
Centroids
-0.85
3.294
■60. 663 (Ca/Cl)+352. 50 (Mg/Cl)-0. 60324 (Na/Ca)+0. 16941 (Na/Mg) -9. 5688
108
Table 6-5. Classification results - discriminant analysis of
brines from Mississippian and Pennsylvanian
formations and water from shallow deposits in
southeastern Clay County.
MISS.
& PENN.
BRINES
DOMESTIC
WATER
WELLS
PREDICTED^
PREDICTED^
ISGS
MEMBERSHIP
ISWS
MEMBERSHIP
SAMPLE r
# ASSIGNED^
Pl
P&S2
S3
#
ASSIGNED-
> pl
P&S2
S3
6-51^8
0
0
0
0
OFB-2
:
F
F
:
B-5165
0
0
0
0
OFB-3
-
F
F
■
B-5165
0
0
0
0
OFB-4
■
F
F
■
B-5144
0
0
0
0
OFB-5
•
F
'
B-5145
0
0
0
0
OFB-7
•
F
p
■
B-5152
0
0
0
0
OFB-8
-
F
F
"
B-5153
0
0
0
0
OFB-10
■
F
F
■
3-5155
0
0
0
0
OFB-11
-
F
F
-
3-5161
0
0
0
0
—
3-5140
0
0
0
0
OFB-1
F
F
3-5141
0
0
0
0
OFB-6
F
F
3-5168
0
0
0
0
OFB-9
F
F
3-5142
0
0
0
0
OFB-12
F
F
3-5147
0
0
0
0
OFB-13
F
F
3-5154
0
0
0
0
OFB-20
F
F
3-5156
0.
0
0
0
OFB-21
0
0
3-5157
0
0
0
0
—
3-5162
0
0
0
0
OFB-15
s
P
S
s
3-5163
0
0
0
0
OFB-17
s
P
s
s
3-5164
0
0
0
0
—
3-5167
0
0
0
0
OFB-14
3
S
s
3-5170
0
0
0
0
■■ OFB-15
3
s
s
3-5171
0
0
0
0
OFB-19
3
s
s
3-5143
0
0
0
0
OFB-22
3
s
s
3-5149
0
0
0
0
3-5150
0
0
0
0
OFB-18
P
p
0
3-5151
0
0
0
0
3-5158
0
0
0
0
3-5159
0
0
0
0
'
3-5160
0
0
0
0
3-5169
0
0
0
0
p
)
P
3-56
p
)
p
3-55
p
3
p
3-54
p
3
p
,
3-57
p
0
0
,
3-647
p
3
p
3-441
p
3
p
B-379
p
0
0
1 Analysis using known Pennsylvanian brines. Variables
used in analysis: Na, Ca, Mg, and CI.
^ Analysis using known Pennsylvanian brines & Shallow
brines. Variables used in analysis: Na, Ca, Mg, and CI
Analysis using shallow brines. Variables used in
analysis: Na, Ca, Mg, Sr, Li, and CI.
Group categories: 0=Oilfield brine, P=Pennsyl vanian
Brine, S=Snailow Brine, and F=Fresn water.
^ Defining group assignments
109
Table 6-6. Sumraary of constituent ratios from discriminant
analysis using known Pennsylvanian brines.
D-^p2 # Na/Cl Ca/Cl Mg/Cl Sr/Cl Li/Cl AEVcI CATVcI Na/Ca Na/Mg
Known 0 0 31 .5844 .0580 .0205 .0025 .00012 .081 .565 10.5 30.0
Unkn. 0 1 .7360 .3640 .1560 .0012 .00008 .521 1.257 2.0 4.7
Known P P 6 .6858 .0178 .0141 228.3 63.5
Known P 0 2 .6825 .0450 .0243 15.5 34.4
Unkn. P 5 1.2966 .0172 .0095 .0004 .00005 .027 1.323 163.1 329.1
Known S P 2 .8245 .0041 .0025 .0002 .00003 .006 .831 198.9 323.0
Known F F 8 2.8757 3.0583 1.3959 .0110 .00099 4.465 7.342 1.9 4.2
Unkn. F 6 4.0283 2.7142 1.4391 .0115 .00079 4.164 8.194 3.8 4.0
Grp
D P # Na/Sr Na/Li Ca/Mg Ca/Sr Ca/Li Mg/Sr Mg/Li Sr/Li ALK^AE
Known 0 0 31 304- 7134 2.894 30.2 658 10.5 227 31.08 7.4
Unkn. 0 1 513 9200 2.333 303.3 4550 130.0 1950 15.00 1.4
Known P P 6 1.212
Known P 0 2 2.109
Unkn. P 5 4201 22793 1.995 41.3 283 21.3 153 6.00 105.7
Known S P 2 4740 28860 1.525 23.7 145 15.0 90 5.50 119.5
Known F F 8 307 5034 2.148 258.3 3375 123.3 1585 16.55 1.3
Unkn. F 6 585 8298 1.677 222.5 4122 133.2 2293 17.50 1.8
^ - Defining group category.
^ - Predicted membership group.
^ - Group categories:
0=Oil Field Brine, P=Pennsyl vanian Brine
S=Shallow Brine, F=Fresh water.
^ - Ca+Mg+Sr
^ - Na+Li+Ca+Mg+Sr
^ - Na+Li
110
The results of a preliminary three-group discriminant
analysis using the Pennsylvanian data of Meents et al. (1952) are
shown in table 6-5, column heading P and table 6-6. All of the
oil field brines (O) , six of the eight Pennsylvanian brines (P) ,
and all of the fresh water samples (F) were classified correctly.
The two incorrectly classified Pennsylvanian brines were grouped
with the oil field brines. From table 6-6, it appears that the
oil field brines are characterized by low Na/Cl and intermediate
Ca/Cl, Mg/Cl, and Na/Ca ratios. The Pennsylvanian brines are
characterized by low Ca/Cl and Mg/Cl, intermediate Na/Cl, and
high Na/Ca ratios. The fresh waters are characterized by low
Na/Ca and high Na/Cl, Ca/Cl, and Mg/Cl ratios. The unknown
samples show constituent ratio patterns which result in the
following groupings: one sample with oil field brine
characteristics, seven samples with Pennsylvanian brine
characteristics, and six samples with fresh water
characteristics .
MISSISSIPPIAN, PENNSYLVANIAN, SHALLOW, AND FRESH WATER GROUPING
The relevance of the above analysis remains suspect due to
the inadequacy of the Pennsylvanian data previously discussed. A
solution to this problem may be found by a closer examination of
those unknown domestic well water samples classified as
Pennsylvanian in character. Two samples in particular, OFB-16
and OFB-17 offer promise. Both samples have specific conductance
values greater than 5000 microseimen/cm, and both samples come
from wells with depths greater than 250 feet (i.e. into the
Pennsylvanian) . For the next analysis, these two samples were
considered as a fourth group, shallow (S) Pennsylvanian, in an
attempt to introduce a more appropriate shallow brine group into
the analysis.
By incorporating two of the unknown samples into the
analysis as shallow brines, the number of unknown samples is
reduced from fourteen to twelve while the remaining defining
groups remain unchanged. The results of this four-group
discriminant analysis are shown in column heading P&S of table
6-5 and in table 6-7. The results for this analysis are nearly
identical to the previous one with the assignments to the
defining groups remaining unchanged, and with the successful
assignment of the two shallow brines. The assignments of unknown
samples into groups is also unchanged for the one sample
characterized as showing oil field brine patterns and for the six
samples characterized as showing fresh water patterns. The only
difference in assignments are for those samples which showed
Pennsylvanian patterns from before. Four of these samples were
characterized as showing shallow brine patterns, while the fifth
sample remained assigned to the Pennsylvanian group.
Ill
Table 6-7.
Summary of constituent ratios from discriminant
analysis using known Pennsylvanian brines and
shallow brines.
Dlp2 # Na/Cl Ca/Cl Mg/Cl Sr/Cl Li/Cl AE'^/Cl CAT^Cl Na/Ca Na/Mg
.655 10.5 30.0
1.257 2.0 4.7
228.3 53.6
15.6 34.4
1.274 23.3 38.2
Known
Unkn.
0 0
0
31
1
.5844
.7360
.0580
.3640
.0205
.1560
.0025
.0012
.00012
.00008
.081
.521
Known
Known
Unkn.
P P
P 0
P
6
2
1
.6858
.6825
1.1911
.0178
.0450
.0511
.0141
.0243
.0311
.0007
.00007
.082
Known S S 2 .8246 .0041 .0026 .0002 .00003 .006
Unkn. S 4 1.3229 .0087 .0041 .0003 .00005 .013
.831 198.9 323.0
1.336 198.1 401.8
Known F F 8 2.8757 3.0583 1.3959 .0110 .00099 4.465 - 7.342 1.9 4.2
Unkn. F 6 4.0283 2.7142 1.4391 .0115 .00079 4.164 8.194 3.8 4.0
Grp
D P # Na/Sr Na/Li Ca/Mg Ca/Sr Ca/Li Mg/Sr Mg/Li Sr/Li ALK^AE
Known 0 0 31 304 7134 2.894 30.2 668 10.5 227 31.08 7.4
Unkn. 0 1 613 9200 2.333 303.3 4550 130.0 1950 15.00 1.4
Known P P
Known P 0
Unkn. P
5 1.212
2 2.109
1 1785 17865 1.642
76.6 766 45.5 466 10.00 14.3
Known S S 2 4740 28860 1.525 23.7 145 15.0 90 5.50 119.5
Unkn. S 4 4805 24025 2.083 32.5 162 15.0 75 5.00 128.5
Known F F 8 307 5034 2.148 258.3 3376 123.3 1586 15.55 1.3
Unkn. F 6 586 8298 1.577 222.5 4122 133.2 2293 17.50 1.8
Defining group category.
Predicted membership group.
Group categories:
0=Oil Field Brine, P=Pennsylvanian Brine
S=Shallow Brine, F=Fresh water.
Ca+Mg+Sr
Na+Li+Ca+Mg+Sr
Na+Li
112
Figure 6-7
Discriminent analysis territorial map for oil field
brines from Mississippian formations, shallow brines
from Pennsylvanian formations, fresh water from
surficial deposits, and unknown samples.
20
•15.0
Canonical Discriminant Function 1
■10.0 -5.0 0.0 5.0
10.0
15.0
?0.0
15.0 ■■
10.0 •■
5.0 ■■
0.0 ••
-5.0
■10.0 ■•
■15.0 •■
-20,
0
ooo
ssooo
sssooo
sssoo
ssooo
sssooo
sssooo
sssooo
sssoo
ssooo
sssooo
sssooo
sssooo
sssoo
OIL FIELD BRINE
^1
ssooo
sssooo
SfSOOO
f sssooo
SSSOO
ssooo
SSSOOO
SSSOOO
SSSOOO
SSSOOO
ssoo
SHALLOW BRINE
0 -15.0 -10.0 -5.0 0.0 5.0 10.0 15.0 20.0
* Group centrolds, # Unknown, 0 Oil Field Brine, S Shallow Brine. F Fresh Vater
Unstandardlzed Canonical Discriminant Function Coefficients
loa(Ca/Cl)
log((Cdt-Hg-fSr)/Cl)
logifNa-^Ca-^Wg-'Sr-^LO/Cl)
log(Na/Ca)
log(Mg/Li)
log(Sr/L1)
(constant)
FUNG 1
8.574<<5
25.38258
-27.94176
23.79035
8.225558
-3.'! 03425
-5.930134
FUNC 2
21.52735
-1.067425
-23.43031
10.69833
-3.014662
1.823528
15.52935
113
Mississippian, Shallow, and Fresh Water Grouping
The incorporation of the shallow brine group into the
analysis represents an improvement over the first analysis, since
the shallow brine group is indigenous to the study area but this
analysis does have its problems. The deficiencies of the second
analysis are two-fold. The first problem is that there are only
two shallow brine samples used to define this group, they are not
especially saline, and they still may not be representative of
the shallow Pennsylvanian brines of the study area. The second
problem involves the inclusion of the Pennsylvanian data of
Meents et al. (1952). The limited number of constituents
reported for Pennsylvanian brines is the limiting factor in the
number of constituents used in the discriminant analysis.
The first problem cannot be overcome until the economic
situation of the oil industry improves, but the second problem
can easily be solved by using the shallow brine group as the only
representatives of the Pennsylvanian, thus permitting the
inclusion of additional constituents in the analysis.
The results of the final three-group discriminant analysis
are shown under column heading S of table 6-5, table 6-8, and
figure 6-7. The members of the defining groups are all correctly
classified. The constituent ratio patterns f or Na/Cl , Ca/Cl,
Mg/Cl, and Na/Ca are the same for this analysis as they are for
the previous two. In addition, the oil field brine group is
characterized by intermediate Li/Cl, Ca/Li, Ca/Sr, Mg/Li,
AE(Ca+Mg+Sr)/Cl, Na/Mg, and ALK(Na+Li) /AE ratios. The shallow
brine group is characterized by low Li/Cl, Ca/Li, Ca/Sr, Mg/Li,
and AE/Cl ratios and high Na/Mg and ALK/AE ratios. The fresh
water group is characterized by high Li/Cl, Ca/Li,. Ca/Sr, Mg/Li,
and AE/Cl ratios and low Na/Mg and ALK/AE ratios. The grouping
of the unknown samples again remains mostly unchanged although
there are a few exceptions. The four samples grouped with
shallov/ brines are the same ones as before. The six samples
grouped as fresh in the prior analyses remain classified as fresh
with the addition of a seventh sample previously classified as
the only unknown showing oil field brine characteristics. The
single unknown sample (OFB-18) classified as having Pennsylvanian
characteristics from the previous analysis is now grouped as
exhibiting oil field brine characteristics. Although sample
OFB-18 shows good agreement with the oil field brine group for
the following constituent ratios: Ca/Cl, Mg/Cl, (Ca+Mg+Sr)/Cl,
Na/Ca, Na/Mg, Ca/Li, and Mg/Li, its classification is hard to
explain from a physical standpoint. The well is not located near
any oil wells and its depth is only 140 feet.
The Effect of Mixing on Classification
It should be understood that the classification of the
unknowns in the above analyses does not mean that the unknowns
114
are pure representatives of the groups to which they have been
assigned. The only inference which should be made from the
classifications is that based on the techniques used in this
study, the unknowns show interelement patterns similar to those
of their assigned groups and that the "contaminated" unknowns
most likely represent mixtures of the brines and fresh water.
The simplest way to look at the mechanism of domestic well
water contamination is to view the process as one of mixing of
waters from three different sources (oil field brine, shallow
brine, and fresh water) where no chemical reactions occur. In
order to evaluate the effect of mixing on unknown classification,
mathematical mixtures of waters from the three different sources
were computed and evaluated. The mean composition of each
constituent for each of the three basic water types is shown in
table 6-9a. Using these compositions, ternary mixtures were
computed and the composition of each mixture was used as input
for Fisher's linear discriminant functions where each mixture is
assigned to the group for which the function produces the largest
discriminant score. The coefficients derived for the oil field
brine-shallow brine-fresh water discriminant analysis are shown
in table 6-9b. The use of Fisher's linear discriminant functions
produces the same classification results as the canonical
discriminant functions.
The results of this mixing exercise are shown in table 6-9c
which show the boundaries for each predicted group as delineated
by three end-member compositions of ternary mixtures of oil field
brine, shallow brine, and fresh water. Due to the exceptionally
high salinity of the oil field brine end-member relative to the
shallow brine and fresh water end-members, the discrimination
procedure is very sensitive to the proportion of oil field brine
in the mixture. For a mixture to be assigned to the shallow
brine group, it must consist of at least 77 percent shallow brine
with no oil field brine and can have no more than 0.9 percent oil
field brine if no fresh water is present. Mixtures containing
greater than 0.9 percent oil field brine will be assigned to the
oil field brine group. This sensitivity becomes even more
extreme for the fresh water group. A mixture must contain at
least 92.4 percent fresh water if no oil field brine is present
and can have no more than 0.04 percent oil field brine if no
shallow brine is present. All mixtures not meeting the above
criteria are assigned to the oil field brine group.
It should be noted that within the oil field brine group
there is a range of binary mixtures of fresh water and shallow
brine where no oil field brine is present. The compositions of
these mixtures ranges from greater than 2 3 percent to less than
92.4 percent fresh water. This anomaly, which represents a major
deficiency in the discrimination model used in this study, most
likely reflects the lack of an adequate definition of the shallow
brine population. This situation may be a possible explanation
115
Table 6-8. Summary of constituent ratios from discriminant
analysis using shallow brines.
Grp3
D-^p2 # Na/Cl Ca/Cl Mg/Cl Sr/Cl Li/Cl AEVcI CAtVcI Na/Ca Na/Mg
Known 0 0 31 .5844 .0580 .0205 .0025 .00012 .081 .655 10.5 30.0
Unkn. 0 1 1.1911 .0511 .0311 .0007 .00007 .082 1.274 23.3 38.2
Known S S 2 .8245 .0041 .0026 .0002 .00003 .005 .831 198.9 323.0
Unkn. S 4 1.3229 .0087 .0041 .0003 .00005 .013 1.336 198.1 401.8
Known F F 8 2.8757 3.0583 1.3959 .0110 .00099 4.465 7.342 1.9 4.2
Unkn. F 7 3.5579 2.3784 1.2558 .0101 .00069 3.644 7.203 3.6 4.1
Grp
D P # Na/Sr Na/Li Ca/Mg Ca/Sr Ca/Li Mg/Sr MgAi Sr/Li ALKVAE
Known 0 0 31 304 7134 2.894 30.2 668 10.6 227 31.08 7.4
Unkn. 0 1 1786 17865 1.642 76.6 766 46.6 465 10.00 14.3
Known S S 2 4740 28860 1.625 23.7 145 15.0 90 5.50 119.5
Unkn. S 4 4805 24025 2.083 32.5 162 15.0 75 5.00 128.6
Known F F 8 307 5034 2.148 258.3 3375 123.3 1586 16.56 1.3
Unkn. F 7 590 8427 1.770 234.0 4183 132.7 2244 17.14 1.8
^ - Defining group category.
^ - Predicted membership group.
^ - Group categories:
0=Oil Field Brine, P=Pennsylvanian Brine
S=Sha11ow Brine, F=Fresh water.
^ - Ca+Mg+Sr
I - Na+Li+Ca+Mg+Sr
^ - Na+Li
116
Table 6-9. The effects of mixing of oil field brine, shallow
brines, and fresh water on classification results
A. PURE END-MEMBER COMPOSITIONS
PURE END-MEMBERS Na Ca Mg Sr Li CI
Oil Field Brine 44880 4525 1503 193.5 9.37 77180
Shallow Brine 1292 6.5 3.8 0.3 0.05 1575
Fresh Water 81.1 64.8 30.8 0.3 0.02 34.8
B. FISHER'S LINEAR DISCRIMINANT FUNCTION COEFFICIENTS
COEFFICIENTS
RATIO OIL FIELD BRINE SHALLOW BRINE FRESH WATER
log(Ca/Cl) -292.3922 -643.0253 -245.1665
log(AE^/Cl) 185.6781 -89.66165 556.8124
1og(CAT^)/Cl) 112.3093 696.5027 -198.0292
log(Na/Ca) 10.59133 -337.0043 305.5829
log(Mg/Li) 175.13 120.8049 299.4482
log(Sr/Li) -81.68469 -56.04589 -135.0388
(constant) -223.2602 -494.2072 -428.3567
1 (Ca+Mg+Sr); 2 (Na+Ca+Mg+Sr+Li)
C. COMPOSITION BOUNDARIES FOR PREDICTED GROUPS
END MEMBER COMPOSITIONS
PREDICTED GROUP OFB^ SHB^ FRESH
{%) (%) (%)
0 0 100
FRESH WATER 0 7.6 92.4
0.04 0 99.95
0 100 0
SHALLOW BRINE 0-77 23
0.9 99.1 0
OIL FIELD BRINE ALL OTHERS
^ Oil field brine; ^ Shallow brine
117
for the classification of sample OFB-18 as showing oil field
brine characteristics. A mixture of approximately 4 5 percent
shallow brine and 55 percent fresh water produces Ca/Cl,
(Ca+Mg+Sr)/Cl, (Na+Ca+Mg+Sr+Li)/Cl, and Na/Ca ratios which are
very similar to those found for sample OFB-18, and it is these
ratios which carry the greatest weight in determining the group
assignments.
SUMMARY AND CONCLUSIONS
This study has shown that there are significant differences
in composition between brines of the oil producing formations of
the Mississippian and the shallow brines of the Pennsylvanian.
It has also been demonstrated that based on these differences in
composition, criteria (such as Ca/Cl, (Ca+Mg+Sr)/Cl, Na/Ca, and
Mg/Li ratios) can be established which can allow the
differentiation between brines from these two basic sources and a
third fresh water source. The major limitation in the current
study is the lack of available data for brines of the shallow
Pennsylvanian. Because of this limitation, the classification
results obtained in this study can only be considered
preliminary.
BIBLIOGRAPHY
Bower, C. A. and L. V. Wilcox, 1965, Chapter 62, Soluble Salts:
in Methods of soil analysis^ Agronomy Series #9, (C. A.
Black, ed.), Amer. Soc. Agron. , Madison, p. 933-940.
Collins, A. G. , 1978, Geochemistry of anomalous lithium in
oil-field bines: Oklahoma Geological Survey, Circular 79,
p95-98.
Davis, J. C. , 1973, Statistics and data analysis in geology: John
Wiley & Sons, Inc., New York, 550 p.
Fletcher, G. E. and A. G. Collins, 1974, Atomic absorption
methods of analysis of oilfield brines - barium, calcium,
copper, iron, lead, lithium, magnesium, potassium, sodium,
strontium, and zinc: U.S. Bureau of Mines Report of
Investigations 7861, 14p.
Graff, D. L. , W. F. Meents, I. Friedman, and N. F. Sh mp, 1966,
The origin of saline formationw Waters, III - calcium
chloride waters: Illinois Geological Survey, Circular 397,
60 p.
Korth, B. , 1975, Exploratory factor analysis, in introductory
multivariate analysis: (D. J. Amick and H. J. Walberg,
eds.), McCutchan Pub. Co., Berkeley, pll3-146.
118
Meents, W. F. , A. H. Bell, O. W. Rees , and W. G. Tilbury, 1952,
Illinois oil-field brine - their occurrence and chemical
composition: Illinois Petroleum No. 66, 39p.
Nesbitt, H. W. , 1985, A chemical equilibrium model for the
Illinois basin formation waters: Amer. Jour. Sci., v. 285,
p. 436-458.
Norusis, M. J., 1986, SPSS/PC+, Advanced Statistics: SPSS Inc.,
Chicago, 3 3 Op.
Rittenhouse, G. , 1967, Bromide in oil-field waters and its use in
determining possibilities of origin of these waters: Bull.
Amer. Assoc. Petrol. Geol., v. 51, no. 12, p. 2430-2440.
Sanathanan, L. , 1975, Discriminant analysis, in introductory
multivariate analysis: (D. J. Amick and H. J. Walberg,
eds.), McCutchan Pub. Co., Berkeley, p236-256.
Tabachnick, B. G. and L. S. Fidell, 1983, Using multivariate
statistics: Harper & Row, Pub., New York, 509p.
U.S. EPA, 197.9, Chloride, Method 3 2 5.3 (Titrimetric, Mercuric
Nitrate) : methods for chemical analysis of water and
wastes: U.S. Environmental Protection Agency, Cincinnati.
Whittemore, D. O. , 1984a, Geochemical identification of the
source of salinity in groundwaters of southeastern Seward
County, Kansas: Kansas Geological Survey: Open-File Report
84-3, 15p.
Whittemore, D. O. , 1984b, Initial report on the geochemical
identification of the source of salinity in groundwaters in
northwestern Harvey County, Kansas Geological Survey:
Open-File Report 84-6, lip.
119
SECTION 7 RECLAMATION OF OIL BRINE HOLDING PONDS
by
Louis R. Iverson
INTRODUCTION
A survey conducted by lEPA in 1980 estimated that between 28
and 38 thousand acres in Illinois have been severely damaged by
oil field brines (Coleman and Crandall, 1981) . Surveys via
aerial photographs of Hamilton and White Counties revealed the
existence of considerably greater amounts of devegetated land.
These barren lands are considered to have critical soils by the
Soil Conservation Service because of the potential for severe
erosion. Calculations made in Hamilton County estimated that an
acre of brine damaged soils will annually lose, on average, 113
tons of material, compared with 7 tons for an acre of similar
soil which has not been contaminated (Coleman and Crandall,
1981) . The importance of reclaiming these brine contaminated
soils cannot be understated, as erosional runoff from just a few
acres can severely degrade adjacent water courses.
The excessive sodium in brine-affected soils readily enters
into cation exchange reactions and disperses colloidal particles,
thereby destroying the soil structure. This disaggregation
leads to a highly impermeable soil which erodes excessively as
water and soil move laterally rather than vertically during rain
events (United States Salinity Laboratory Staff, 1969) . These
soils are considered saline-sodic.
To reclaim saline-sodic soils, the sodium ions must be
leached from the soil particles. Two criteria need to be met for
this process to occur; (1) sufficient water must be applied so
that precipitation plus irrigation exceeds consumptive use, and
(2) infiltration rather than runoff must occur. In Illinois,
precipitation generally exceeds consumptive use in contrast to
locations in the West. To increase percolation in these sites, a
vegetative cover of any kind (even dead, mulch material) is
needed to reduce runoff and increase infiltration capacity.
The addition of calcium-rich substances, like lime or
gypsum, also can aid in the recovery of sodium-rich soils, with
the excess calcium replacing sodium on soil exchange sites. The
sodium ions then disassociate and become very water soluble for
rapid leaching.
Several methods have been utilized to hasten recovery of
brine-contaminated soils. One which has been successful in
southern Illinois is the "Wayne County Method" which uses a
combination of tile drainage, lime or gypsum, mulch, and
120
chiseling to help hasten the process of leaching (Townsend,
1982). The disadvantages of this method are that tiling is an
expensive procedure and that the site needs to be left
undisturbed for two years while sodium is leached from the soil.
The Soil Conservation Service (1986) has developed a set of
standards and specifications for establishing a vegetative
cover on high sodium and salt-damaged soils. It includes the
planting of some salt-tolerant grasses.
The purpose of this study was to further assess whether the
use of salt-tolerant species Would allow a more rapid
establishment of vegetative cover, which in turn, can hasten
infiltration of water and leaching of sodium. Most of the
selected species were obtained from western sources where
naturally salinized soils are common.
MATERIALS AND METHODS
Plant Species Selection
A total of 17 species were selected to test for survival and
growth on the brine contaminated soils (table 7-1) : seven shrubs
(1 from Fabaceae, 1 from Elaeagnaceae, and 5 from
Chenopodiaceae) , two leguminous forbs, and 8 grasses. Selection
of species was based on the author's personal experience during
doctoral and post-doctoral research in North Dakota (Iverson and
Wali, 1982) , discussions with experts in the field, and a review
of the literature (Redente et al., 1982; Thornburg, 1982;
Fulbright et al. 1982; Kies and Depuit, 1984; Monsen and Plummer,
1978; Best et al., 1971, Vogel, 1981).
Plant materials were purchased from Native Plants, Inc., in
Salt Lake City, Utah. The first five species listed in table 7-1
were purchased or grown and planted as containerized seedlings,
the remainder were sown as seeds. All species were planted at
the rates given in table 7-1. Quantities of seed sown varied
according to seed distributor's recommendations for sowing in
pure stands, quantity of seed, and tested germination
percentage. Seeds of Hedysarum boreale were scarified with
sandpaper prior to planting to enhance its germination
percentage.
Test Plot Preparation
A test plot was established during the period April 14-24,
1986. It measured 17m by 17.5m and was located in the area of an
abandoned brine holding pond in the northeast corner of Section
33, T3N R7E (figure 7-1). A randomized block design was
constructed within the plot with three replicates of four
treatments for each of the 17 plant species tested (figure 7-2).
The treatments were: (1) control - no amendments, (2)
fertilizer - addition of lOOkg/ha nitrate, lOOkg/ha phosphorus.
121
Table 7-1.
Plant materials selected
seeding in the test plot
density also given (PLS =
Robinia neomexicana -
(locust shrub)
Atriplex gardneri -
(Gardner's saltbush)
Atriplex confertifolia -
(shadscale)
Atriplex canescens -
(four wing saltbush)
Shepherdia arqentea -
(Silver buf faloberry)
Agropyron elongatum -
(Jose tall wheatgrass)
Trifolium subterranean -
(Mt. Barker subterranean clover)
Sporobolus airoides -
(Alkalai Sacaton)
Puccinellia distans -
(Fults alkalai grass)
10) Elymus triticoides -
(Creeping wildeye 'shoshone')
11) Atriplex cuneata -
(Castle Valley saltbush)
12) Hedysarum boreale -
(Utah sweetbetch)
13) Elymus iunceus -
(Russian wildrye)
14) Ceratoides lanata -
(winter fat)
15) Agropyron trachycaulum -
(slender wheatgrass)
16) Eragrostis curvula -
(weeping lovegrass)
17) Panicum virgatum -
(switch grass)
for transplanting or
Seed or transplant
= pure live seed) given,
4 transplants in-2
6 transplants m-2
4 transplants in-2
(poor condition)
4 transplants m-2
4 transplants m-2
6.0g (280 PLS) m-2
5.0g (1500 PLS) m-2
0.8g (1040 PLS) m-2
6.0g (15,600 PLS) m-2
5.0g (175 PLS) m-2
3.4g (50 PLS) m-2
10. Ig (12 PLS) m-2
3.0g (360 PLS) m-2
3.4g (56 PLS) m-2
5.0g (250 PLS) m-2
0.7g (330 PLS) m-2
5.0g (550 PLS) m-2
122
Figure 7-1
Location of test plot. Case study site B, Section
33, T. 3 N., R. 7 E., Clay County.
C3 Unvegetated area
- Observation well (entire length slotted)
Piezometer (2.5 fl screen)
■ Elevation oatum
0 NHS test plot
■ Intermittent drainage way
■ SWS surlace water station
100 tt
.^proximate boundary
■-ij i|^0 ':■:•:■;•:■:•; of holding pond
y
Tank battery
123
Figure 7-2.
Plot layout. Numbers in subplots equate to
designation given in table 7-1 for plant species,
Four treatments with three replicates were used.
. I G = Gypsum Treatmenl
N F = Fertilizer
7
9
12
14
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124
lOOkg/ha potassium; (3) gypsum - addition of 44 81 kg/ha (2
tons/acre) ; and (4) fertilizer plus gypsum - addition as in (2)
and (3). The plot consisted of 204 randomly distributed
subplots, Im X Im in size with 50cm buffer strips between each
treatment block (figure 7-2) .
The plot area was disked repeatedly to a depth of 2 0 cm on
April 14, 1986. The area was staked out into subplots, and
fertilizer and gypsum treatments were then applied to the
specific subplots and raked into the soil to a depth of
approximately 8cm. Approximately one liter of dilute 'Miracle
Grow' (a solution of 2.25 g 20N, 20P, 20K fertilizer per liter
water) was applied to each seedling at the time of transplanting.
Seeds were broadcast by hand and incorporated to varying depths
depending on the size of the seed. All subplots were mulched
with a layer of wheat straw to increase moisture retention.
Some additional Atriplex canescens (15 plants) and Atriplex
qardneri (8 plants) were transplanted around the plot to assess
survival under low care conditions. These plants were placed in
the ground by opening up the soil with a spade and packing the
soil around the transplant soil tubes; no water, fertilizer, or
mulch was applied. The overall appearance of the plot is
presented in figure 7-3, a photo taken one month after the plot
was established. The area surrounding the plot continued to be
completely barren for the entire year.
Plot Monitoring
Site visits were made at monthly intervals throughout the
growing season. For five monthly site visits, transplant
survival and height were recorded for the five transplanted
shrubs. The sown species were subjectively evaluated, on a 0-10
rating scheme, for germination, vigor, and growth at each site
visit. A rating of 0 indicated no germination whereas a rating
of 10 indicated 100% cover and vigorous growth.
Rainfall measurements were recorded daily at the Klein farm,
about 2 km west of the site.
At the end of the growing season (mid-October) , the eight
grass species were sampled for biomass by clipping two 25cm x
2 5cm quadrats from each subplot. Weeds and planted materials
were separated into different bags, the contents were then oven
dried at 65 C and weighed. A total of 96 subplots were clipped.
Soil samples were collected on: April 14 (before planting) ,
July 16 mid-season) , and October 18 (end of season) . Samples
were collected from 2 depths (0-15cm, 15-30cm) from all subplots
for two species. This amounted to 144 samples (3 dates x 2
depths X 2 species x 4 treatments x 3 replicates) .
125
Figure 7-3.
Test plot asit appeared at the time of planting,
April 14, 1986.
' ' r" V ■ !' ■■
126
Laboratory Analysis
The 96 harvested plant biomass samples (weed and planted)
were dried and weighed. A subset of these samples from six grass
species were selected for further tissue analysis. The harvested
plant material from 72 plots was sent to A & L Agricultural
Laboratories of Memphis, Inc. for wet digestion and analysis of
chloride (CI) , phosphorus (P) , potassium (K) , magnesium (Mg) ,
calcium (Ca) , sodium (Na) , aluminum (Al) , manganese (Mn) , copper
(Cu) , and zinc (Zn) .
Soil samples were dried, ground, and passed through a 2mm
screen. Electrical conductivity was performed on the samples by
extracting 1 part soil with 2 parts water, filtering the
suspension through Whatman No. 1 filter paper and reading
conductivity values on the solutions with a Yellow Springs
Instruments electrical conductivity meter. Soil samples were
also sent to A & L Agricultural Laboratories of Memphis, Inc.,
for analysis of pH, organic matter (OM) , available phosphorus,
exchangeable potassium, magnesium, calcium, calculated cation
exchange capacity (CEC) , soluble salts, and sodium (Na) .
Statistics utilized for comparisons among treatments and
among species with plant and soil chemical data included the
ANOVA and GLM procedures in SAS. The Duncan test was used for
multiple comparisons among means if the F statisticic was
significant at the 0.05 level.
RESULTS AND DISCUSSION
Environmental Conditions On Site
Rainfall measurements were recorded daily at the Klein farm,
about 2 km west of the site. Overall, 23.6 inches of rain fell
in the vicinity of the plot during the growing season (mid-April
to late-September, 1986) . This is about normal for that area.
Rainfall was not evenly distributed throughout the growing
season, however. Weekly rainfall totals show a dry period in
late April (just after transplanting) and a very dry two-week
period in late June (Fig. 7-4) . These two dry periods were
harmful to at least some of the transplants and seedlings, as can
be seen in the seasonal assessments of the species.
Species Success
a. Aqropyron elonqatum (Poaceae)
Tall wheatgrass is native to Siberia; it was introduced to
this continent in 1929 by the University of Saskatchewan (Best et
al., 1971). It is a perennial grass not recorded in the Illinois
flora (Mohlenbrock, 1986) . It is considered the most salt
tolerant of all cultivated grasses, excellent for hayfields and
127
Figure 7-4.
Weekly rainfall amounts at the plot during the 1986
growing season.
5.0
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R o I n •? o 1 1
128
pastures on saline soil (Best et al. 1971). It is also
considered excellent cover for upland game birds (Thornburg,
1982) .
Our first year data concur with these assessments. Rating
values for this species were above 8 for all treatments for
nearly the entire growing season (figure 7-5) . There tended to
be higher vigor in the non-control subplots, with the gypsum
treated subplots best in August and September (figure
7-5) . Productivity data from the tall wheatgrass subplots also
show significantly increased yields due to gypsum, it was the
only species which showed significant benefits from the addition
of calcium sulphate (figure 7-6) . The bar graphs like that of
figure 7-6 are constructed with planted material biomass on the
bottom and weed biomass on the top of each bar? the four bars on
the left represent the means of three replicates for each
individual treatment with the four bars on the right representing
the means of six replicates, with and without fertilizer or
gypsum treatment}. Fertilizer-treated subplots showed dramatic
and significant increases in both planted and weedy biomass,
although even the control plots did relatively well providing
cover, forage material, and erosion control.
b. Aaropyron trachvcaulum (Poaceae)
Slender wheatgrass is native to and has a wide distribution
within North America and the northern part of Illinois. It is
reported to be tolerant of alkali and is useful as a short-lived
species in reclamation plantings and range seeding, primarily in
the West (Thornburg, 1982) . It persists in rocky areas, but is
easily destroyed by cultivation or prolonged grazing (Dore and
McNeill, 1980) . It was also found to be tolerant of a salinized
roadside environment in Maine (Pitelka and Kellogg, 1979) . This
species was observed on mined lands in North Dakota; it persists
well for about three years and then gives way to other species
invasions (Iverson and Wall, 1982) . This may be the desired
effect in reclaiming salt brine contaminated areas.
The rating values for A^ trachvcaulum are high for the
fertilizer-treated subplots, but rapidly diminish for e control
and gypsum treatments (figure 7-7) . Biomass values al. show
significant increases due to fertilizer and significant- "
decreased yields due to gypsum treatments (figure 7-8). ""he
gypsum treatment even caused significant depressions in y eld
when compared against the control. Addition of fertilize alone
benefitted yields two-fold over the fertilizer plus gypsu..
treatment and three-fold over the controls (figure 7-8).
c. Atriplex canescens (Chenopodiaceae)
Four-wing saltbush, as the name implies, is tolerant of
considerable alkalinity. It is also very drought resistant and
129
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survives and grows well on dry sites (Blauer et al., 1975). It
is a dioecious shrub which occurs widely on desert and foothill
ranges in the western United States. It does not occur naturally
in Illinois. It persists well in association with other shrubs
and grasses, and is a fair to good browse species for deer
(Ostyina et al., 1984).
A. canescens was the most successful transplanted species in
this study. It had 100% survival in the subplots (figure 7-9) ,
and even 100% in the low-effort transplants which were placed
around the plot. It also grew well in all treatments, about 4 5
cm in non-fertilized subplots and 55 cm in fertilized subplots
(figure 7-10) .
d. Atriplex conferti folia (Chenopodioceae)
Shadscale is another fairly alkaline-tolerant shrub native
to dry alkaline plains and hills in the western United States; it
is not found naturally in Illinois (Rydberg, 1954, Martin and
Hutchins, 1980) . In this study, no transplants survived the full
season. However, this is attributed primarily to the poor
condition of the transplants upon arrival from Utah.
The low vigor, transplants were then subjected to abnormally dry,
hot southerly winds in the first three days following
transplantation. By June, no live A. confertifolia plants
existed on the site.
e. Atriplex cuneata (Chenopodiaceae)
This species, called Castle Valley saltbush, is native to
the southwestern United States and does not occur naturally in
Illinois. It was the only Atriplex species which was sown,
rather than transplanted on the site. Direct seeding of shrubs
like these is commonly done on western mined lands, but often
only about 1 seedling is established per 100 pure live seed
sown (Luke and Monsen, 1984) .
In this experiment, A_i. cuneata had very low germination and
hence, few seedlings established. The rating assessments were
low throughout the year, but were especially low in the early and
late parts of the season (figure 7-11) . The seeding rate was
grossly underestimated for this species. Some seedlings did
emerge by June, seemingly slightly better in the non-fertilized
plots; the added competition from increased weed growth may have
contributed to this. By September, most of the seedlings
appeared dead or dying.
f. Atriplex gardneri (Chenopodiaceae)
Gardner's saltbush is native to Wyoming and Colorado, and is
not found naturally in Illinois. It appears to prefer alkaline
flats or dry lake beds (Rydberg, 1954) . It is a low growing,
134
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persistent shrub which has been shown to be successfully
established on western mined lands by transplanting
(Frischknecht and Ferguson, 1984) or by direct seeding (Luke and
Monsen, 1984) . In one experiment, 94% of transplants were still
surviving after five years of growing on processed oil shale
(Frischknecht and Ferguson, 1984).
In this study, four transplants purchased from the Utah
nursery were placed in each subplot; additionally, 2 plants grown
from seed in the Illinois Natural History Survey greenhouses were
transplanted in each subplot. Overall, survival during the first
year was 87%, with no significant differences in survival for
different treatments (figure 7-9) . By the time of the last
assessment on September 26, 1986, many previously vigorous A.
qardneri plants were showing signs of reduced vigor - some
appeared dead. Apparently, these plants were entering season-end
scenescence on that date. Growth for this species was only half
that of A_i. canescens, with slightly more growth on nongypsum
treated subplots (figure 7-10) .
g. Ceratoides lanata (Chenopodiaceae)
Winterfat is a long-lived, low-statured, C3 shrub native to
dry, sandy or shallow clay loam soils of western North America
(Springfield, 1979) . It has been shown to survive very well as
transplants into harsh spoil material (Iverson et al., 1984) and
can thrive in salinized, droughty environments (Iverson, 1986) .
However, it is not very competitive against weeds during the
seedling establishment phase (Iverson, 1986) .
In this study, seedling establishment was sparse; the direct
seeding rate was insufficient for adequate seedling establishment
(as was the case with Atriplex gardneri. Luke and Monsen, 1984) .
A few seedlings emerged in May, but the June drought and
competition from weeds may have contributed to its poor
perform.ance in the summer and fall (figure 7-12) . The fertilized
plants survived slightly better than non-fertilized plants.
Previous studies indicate this species would survive well from
transplants into salinized environments (Iverson et al., 1984).
This species needs further investigation.
h. Elymus junceus (Poaceae)
Russian wildrye was introduced from Siberia. It is used for
pasture in the northern parts of the Great Plains and in the
western intermountain area (Thornburg, 1982) . It is not found in
Illinois. Wildrye is slow to establish but is very persistent
(Best et al. , 1971) .
In this first year of the study, we confirmed that it is
slow to establish. The assessment ratings show medium levels
were achieved throughout the season for this species (figure
138
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7-13). It is also important to note that the fertilizer
treatment was beneficial to the vigor and survival of the
species. The data show a tremendous increase in biomass,
especially weed biomass, in the fertilizer treated plots (figure
7-14) . A noticeable depression in wildrye growth was evident in
the gypsum treated plots. The total planted yields were much
lower relative to most other grass species. But, it is yet to be
seen whether this species will become more established and become
more productive in the second year.
i. Elymus triticoides (Poaceae)
This species, creeping wildrye, also is not native to
Illinois but is native to the western states. It is a species
highly tolerant to salt and alkali, and is adapted to a wide
range of soil textures (Thornburg, 1982) .
The subjective ratings for this species indicated relatively
poor establishment and growth, especially on non-fertilized
subplots (figure 7-15) . Yet its vigor did not decrease during
the season as some species did. Total wildrye biomass was
extremely low, with some benefits apparent from the addition of
fertilizer (figure 7-16) . The proportion of weed biomass to
planted biomass was higher with this species than any other.
Fertilizer increased weed biomass 2.5 fold, and doubled wildrye
biomass. We believe that this species will improve in the second
year, since the species was healthy, though sparse, in its first
year of growth, and since weeds commonly decrease in biomass
after the first year (Iverson and Wali, 1982) .
j. Eraqrostis curvula (Poaceae)
Weeping lovegrass was introduced into this country from
South Africa in 1927 (Kucera, 1961) . It is a warm-season
perennial found occassionaly throughout the southern United
States, and has been seen in Morgan County, Illinois
(Mohlenbrock, 1986) . It is useful for controlling erosion and in
the revegetation of grasslands because it provides a quick cover
(Hitchcock and Chase, 1951) . It is relatively short lived (2 to
4 years) unless foliage is removed by mowing, burning, or grazing
(Vogel, 1981) .
In our experiment, weeping lovegrass did not quickly
establish in April and May, but substantially increased in
prominence during the warm season (figure 7-17) . There was a
marked difference in assessment rating among treatments.
Fertilizer was beneficial and gypsum was detrimental in estab-
lishment rate, amount of vigor and survival, and total biomass of
the species (figures 7-17, 7-18). Its yield on the fertilized
subplots exceeded that of any other species, with 395 g/m2
produced. The gypsum treatment yield, on the other hand, was
only 7% that of the fertilized subplots.- This species, not
140
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being strictly a western species, apparently cannot tolerate
calcareous conditions which resulted from the addition of calcium
sulfate.
k. Hedysarum boreale (Fabaceae)
Northern sweetvetch is native to the northern Great Plains
in the United States and Canada; it is not found naturally in
Illinois. As a legume, it is capable of nitrogen fixation and
has been suggested as a potential species for stressful sites.
It did very poorly in our study. Some germination occurred
early; but by September, little or no live activity was apparent
(figure 7-19) . Part of the problem is the hard seed coat on the
seed and apparently the seeds were not adequately scarified prior
to planting.
1. Panicum vircfatum (Poaceae)
Switchgrass is a widely distributed native, warm-season
grass which ranges throughout the United States except for the
west coast (Hitchcock and Chase, 1951) . In Illinois, it is
rather common, throughout the state, and is found in prairies,
fields, wasteground, rocky stream beds, and woods (Mohlenbrock,
1986) . Plants are tall, large-stemmed, and spread by short
rhizomes and seed. Stands usually require 2 to 4 years to
develop good cover on mine spoils, but once established, require
little maintenance (Vogel, 1981) . Of the several cultivars
available, the one planted in this study, 'Blackwell', has been
shown by Soil Conservation Service trials to be the superior
grass tested for survival and growth on brine contaminated soils
(Soil Conservation Service, 1986) . The species also produces
excellent wildlife cover and the seeds are eaten by song and game
birds (Thornburg, 1982) .
In this study, switchgrass established moderately well in
the first year of study, with variations in assessment ratings
prevalent temporally and across treatments (figure 7-20) . The
final rating showed an advantage to fertilized subplots. Biomass
data revealed a somewhat surprising result in that the control
subplots did equally as well as fertilized subplots (figure
7-21) , although variation was high among replicates. Addition of
gypsum was noticeably detrimental.
m. Puccinellia distans (Poaceae)
This species, Fults alkalai grass, is an exotic, perennial
grass introduced from Eurasia. It was introduced to western and
northern U.S. and adjacent Canada (Hitchcock and Chase, 1951) .
In Illinois, it is occasionally found in the northeastern
counties on disturbed soil (Mohlenbrock, 1986) . It has been
observed that along highways, P^ distans- encroaches closer to the
147
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paved surface than other weed species, presumably because of its
greater salt tolerance; it also may become more prevalent in
years to come (Dore and McNeill, 1980). The species is also
common on saltflats in the northern Great Plains.
In this experiment P^ distans established very quickly from
its dense sowing of very small seeds (table 7-1) . A division in
growth pattern occurred as the season progressed as the non-
fertilized subplots appeared to degenerate with time (figure
7-22) . With biomass, substantial benefits occurred from the
addition of fertilizer (figure 7-23) , with no changes resulting
from the gypsum treatments. The quick cover and high salt
tolerance of this species makes it a desirable candidate for
reclaiming brine contaminated soils.
n. Robinia neomexicana (Fabaceae)
This species, a locust shrub with thorns, is native to the
Southwest (Colorado, New Mexico, Arizona, Utah, Nevada) and is
not in the Illinois flora. It will form thickets and it spreads
freely from stumps and roots; in fact, it can be difficult to
eradicate (Thornburg, 1982) . Its habitat naturally is in moist
soils along streams at elevations of 4000 to 8500 feet, quite
different from conditions in southern Illinois.
In this experiment R. neomexicana proved to be only
marginally successful. Survival rates during the first year
ranged from 8 percent on gypsum plots to 42 percent on fertilized
plots (figure 7-9) . Most of the surviving plants lacked vigor;
they averaged about 2 0cm growth from time of transplanting to
season end (figure 7-10) .
o. Sheperdia arqentea (Eleagnaceae)
Silver buffaloberry is native to Kansas, New Mexico,
Nevada, and Utah, north to Saskatchewan and Alberta (Hitchcock
and Chase, 1951) ; it is not reported in the Illinois flora
(Mohlenbrock, 1986) . It is most common on sandy soils but also
grows on moist soils; it is the author's experience to see it
growing in swales of higher moisture content in pastures of North
Dakota. It produces excellent wildlife food and cover. It is
also used as an ornamental plant and in windbreak plantings. It
has considerable promise for use on mined lands in the northern
Great Plains (Thornberry, 1982) , although it is not particularly
salt tolerant. Apparently, the salinity was excessive for this
species as all of the buffaloberry plants perished in the first
year, even though they were highly vigorous when transplanted.
p. Sporobolus airoides (Poaceae)
Alkalai sacoton is native to the western half of North
America, it occurs as far east as northwestern Missouri on dry
151
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hill prairies (Hitchcock and Chase, 1951; Kucera, 1961). It is
not known in the Illinois flora (Mohlenbrock, 1986) . It is a
perennial grass which naturally occurs in meadows and valleys,
especially in moderately alkaline soil. It has been used in
species mixes for mined land reclamation in the West.
In this experiment, alkalai sacaton was slow to establish,
being found to steadily increase in assessment rankings,
especially after July 1 (figure 7-24) . Biomass estimates
revealed a large increase in yield due to the addition of
fertilizer (figure 7-25).
q. Trifolium subterranean (Fabaceae)
Subterranean clover is a winter annual legume which was
introduced to the United States from Europe via Australia. It
also is not known in the Illinois flora (Mohlenbrock, 1986) . It
grows best on well-drained, fertile loam soils in areas with a
mean annual precipitation of more than 18-20 inches.
In our experiment, there was a very good rate of
germination in all plots by early May (figure 7-26) . However,
the dry period in June was critically damaging to this species,
and by the end of the year, most plants were dead.
Overall Species And Treatment Evaluation
Several groups of species emerged upon comparison of the
first year results (table 7-2) . Aqropvron elonaatum was the most
successful species both in production and rating (table 7-2) . A^
trachycaulum was next in rating, followed by Puccinellia distans.
These three species appear to rate the best of the seeded species
for their first year overall performance. The next five species,
S. airoides. P. virgatum, E_j. curvula, E_j. triticoides, and E.
iunceus. all clump together as similar in rating. The two
species of Elymus were low in stature. Each of these species may
or may not become firmly established and highly productive in the
second year after seeding. The third group of species, T.
subterranean. A. cuneata, C_^ lanata, and H_j. boreale, did very
poorly in the first year of the experiment. T_^ subterranean
germinated well but died off in the later part of the season
after the June dry spell. For the other three species, poor
geirmination resulted in very sparse stands of seedlings. C.
lanata and A^ cuneata should have been planted at a much heavier
rate (Luke and Moran, 1984) . Apparently H_^ boreale was not
sufficiently scarified for adequate germination.
Of the Transplants, Atriplex canescens came out as clearly
the most successful species (table 7-2) , with 100% survival and
49 cm growth in 1986. A^ gardneri also performed well; it is a
lower growing shrub which is indicated in the growth data.
154
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Table 7-2.
157
Overall assessments of plant species according to the
subjective assessment rating in September, biomass
estimate in October and overall growth during 1986.
Different letters within a column indicate
significant differences at the .05 level.
Seeded Species
Species
September
Rating
Biomass
g/m2
Growth
cm
Acfropyron elonaatum
9.2
a
206.3 a
2 6.9 be
Aaropyron trachycaulum
6.7
b
142.2 ab
22.0 cd
Puccinellia distans
5.9
be
88.5 ab
19.9 cd
SDorobolus airoides
4.8
c
131.3 ab
34.6 b
Panicum viraatum
4.8
c
193.1 a
50.1 a
Eracrrostis curvula
4.6
c
188.6 a
32.5 b
Elymus triticoides
4.4
c
32.0 b
2 0.3 cd
Elymus iunceus
4.3
C-
46.6 b
16.4 de
Trifolium subterranean
1.1
d
*
5.0 f
Atriplex cuneata
0.8
d
*
11.2 ef
Ceratoides lanata
0.6
d
*
9.6 ef
Hedysarum boreale
0.1
d
*
5.2 f
Transplants
Atriplex canescens
Atriplex qardneri
Robinia neomexidana
Atriplex confertifolia
Sheperdia arqentea
*no data available
%
Survival
100
a
87
a
25
b
0
c
0
c
Growth .
cm
49
a
21
b
26
b
0
c
0
c
158
Robinia neomexicana had only 25% survival with 26 cm growth on
thesurviving plants. A^ confertifolia and S_^ argentea did not
survive the 1986 growing season. A^. confertifolia plants were in
very poor condition upon planting and none survived the season.
S. argentea were in good condition when transplanted but
apparently could not tolerate the elevated salt concentrations.
In evaluating the treatment effects, it is clear that
fertilizer amendments are highly desirable for growth and
production of seeded species (table 7-3) . Soil analysis revealed
phosphorus deficiencies on these brine soils, and, although
nitrogen was not tested, the low organic matter along with other
evidence indicated nitrogen to be severely deficient as well.
The addition of gypsum was not helpful in the first year growth.
The addition of calcium sulphate added osmotic potential to the
soils which may have been detrimental initially during the
critical establishment phase. It would have been better to
apply gypsum several weeks prior to seeding.
Weed Invasion And Growth
Weed invasion was very prevalent in the plot, as indicated
by final biomass estimates (figures 7-6, 7-8, 7-14, 7-16, 7-18,
7-21, 7-23, 7-25). The weed species found growing on the plot in
October, 1986 are given in table 7-4. It appears likely that of
the 12 species found, the seeds of 11 of them were brought in by
the straw used for mulch. Only Atriplex patula, a known salt
tolerant species in Illinois, appeared to have existed on or near
the plot prior to 1986. Most of the other species are common
field/barnyard weeds which are characterized by phenotypic
plasticity such that they can grow over a wide range of site
conditions. Biomass amounts of weeds were even more sensitive
to the treatments, especially fertilizer, than were the biomass
estimates for planted species. Of the eight species analyzed for
weed biomass, five showed a significant fertilizer effect and
three showed a significant gypsum effect. In many cases,
especially the Elvmus species (figures 7-14, 7-16), the weed
biomass outstripped the planted biomass. This is a common
phenomenon in the first year growth on any restoration attempt
(Iverson and Wali, 1982) . In the second year of growth, weed
production is expected to be much less than planted species
production.
Soil Physical And Chemical Characteristics
Soil electrical conductivity (EC) showed a trend in which
the upper soil horizon EC (0-15cm) dramatically decreased between
the April and July sampling dates (figure 7-27) . On the other
159
Table 7-3.
Overall assessments of treatments according to the
subjective assessment rating in September, biomass
estimate in October, and overall growth in 1986.
Different letters within a column indicate significant
dif fences at the .05 level.
Seeded Species
Treatment
Control
Fertilizer
Gypsum
Gypsum & fertilizer
Control
Fertilizer
Gypsum
Gypsum & fertilizer
September
Ratincf
Biomass
a/m2
Growth
cm
3.0 b
97.5 be
19.0 c
5.1 a
208.6 a
31.4 a
3.2 b
61.3 c
18.0 c
4.4 a
Tran
146.9 ab
splants
23.6 b
% Survival
3
Growth-^
cm
44- a
30.
9
a
44 a
36.
1
a
39 a
29,
6
a
37 a
31.
0
a
1 mean of 12 species
2 mean of 8 species
3 mean of 5 species
4 mean of 3 species
160
hand, in the lower sampled horizon there was a gradual increase
in EC throughout the season (figure 7-27) . The lower soil
layers had significantly higher EC levels, overall, with a mean
of 1.9 mmhos/cm vs. 1.4 mmhos/cm on the upper horizon. Since
these measurements were taken on a 1 part soil to 2 part water
soil suspension, values should be considered quite high for plant
growth. EC values between 1.2 and 2.4 can cause severe
restrictions on plant growth. Only very tolerant species are
able to grow satisfactorily in the range, 2.4-4.8. All species
are seriously impaired at levels above 4.8 mmhos/cm (Bradshaw and
Chadwick, 1980) . The range of EC values for the plot was from
0.31 in the upper horizon beneath Puccinelia distans in July to
5.1 mmhos/cm in the upper horizon beneath Atriplex cuneata in
April.
The seasonal decrease in surface EC is advantageous for
plant growth; levels at the surface generally fell to a range
tolerable by many plant species. If low levels could be
maintained at the surface in future years, additional species
could invade (or be planted) which would increase diversity
and stability of the ecosystem. Yet, there is a possibility that
elevated winter moisture levels will allow capillary action to
bring the salts from the lower horizon back to the surface. It
is hoped that the additional roots and moisture retention in the
vegetated plots will contribute to leaching salt and permanent
reduction in surface EC and therefore progress towards the
reclamation of the site. It is also hoped that leaching will
continue to deeper horizons in the future and that the EC values
at 15-30 cm will decrease further. We will be able to follow
this by continued sampling in future years.
Additional soil analyses were conducted by a commercial firm
for the following parameters: EC (on a paste rather than a 1:2
soil: water suspension as was used the INHS laboratory) , organic
matter percentage (OM) , a weak Bray extraction for phosphorus
(PI) , a strong Bray (more acidic) extraction for phosphorus (P2) ,
ammonium acetate extractable potassium (K) , magnesium (Mg) ,
calcium (Ca) , and sodium (Na) , pH, and buffered pH. The data
were analyzed by date (table 7-5) , by treatment (table 7-6) , and
by layer and date (table 7-7) .
Several parameters showed significant trends with time
during the 1986 growing season. Most notable was the decrease in
EC and the cations Na, Mg, and Ca as the season progressed (table
7-5) . This trend can be attributed to leaching. It is hoped
that Na levels will continue to decrease in the coming years.
There was also an apparent increase in pH with time, possibly due
to the influence of gypsum.
Treatment effects were apparent on chemical parameters and
can be attributed to the amendments to the soils (table 7-6) .
For example, increases of EC, PI, P2 , K,' and the decrease in pH
161
Table 7-4. Weed-species located on brine plots.
Scientific Name
Melilotus officinalis
Setaria faberi
Lepidium virqinicum
Sida spinosa
Rum ex crispus
Ipomoea hederacea
Panicum dichotomif lorum
Echinochloa muricata
Polygonum pennsylvanicum
Trifolium hybridum
Atriplex patula
Chenopodium sp.
Common Name
Yellow sweet clover
Foxtail
Field peppergrass
Prickley sida
Curley dock
Ivy-leaved morning glory
Fall panicum
Barnyard grass
Smartweed
Alsike clover
Spear scale
Goosefoot
162
Figure 7-27. Soil electrical
conductivity at two soil depths
taken on three dates in 1986.
3.0
Soil Electrical Conductivity
By soil d«pth and date
1 soil : 2 water extracts
163
Table 7-5. Chemical attributes of soils summarized by date.
All estimated parameters differed significantly (P <
.05) among sampling dates. Columns followed by
differing letters are significantly different (P <
.05) .
Date, 198 6
April July October
EC, mmhos/cm 6.44a 3.77b 3.53 b
O.M., % 0.96 b 1.19 a 0.91 b
PI, ppm 11.40 b 15.21 a 10.02 b
P2, ppm 14.69 b 19 . 15 a 13.98 b
K, ppm 108.1 b 116.6 a 115.8 a
Mg, ppm 220.4 a 200.4 ab 174.1 b
Ca, ppm 875.6 a 902.3 a 779.2 b
Na, ppm 1844.4 a 1185.4 b 212.5 b
pH 5.13 b 5.35 a 5.28 a
Buf-pH 6.25 b 6.44 a 6.44 a
164
Table 7-6.
Soil concentrations of certain chemical characteristics
tabulated by treatment. Values represent means over thre
dates. Columns followed by differing letters are
significantly different (P < .05).
EC, mmhos/cm
O.M., %
PI , ppm
P2 , ppm
K, ppm
Mg , ppm
Ca , ppm
Na , ppm
PH
Buf-pH
Control
3.60 a
1.03
8.22 a
11.69 a
108.9 a
202.1 ab
766.9 b
1375.6
5.4 a
6.48 a
Treatment
Fertilizer
4.36 b
0.98
14.56 b
16.78 b
120.7 b
225.7 a
779.7 b
1438.6
5.13 b
6.29 b
Gypsum
5.08 b
0.99
9.08 a
12.50 ab
113.3 ab
195.6 ab
977.8 a
1430.8
5.23 b
6.36 b
Fertilizer &
& Gypsum
5.27 b
1.09
16.97 b
22.78 c
111.2 a
169.8 b
885.0 a
1411.4
5.25 b
6.37 b
165
Table 7-7.
Chemical attributes of soils summarized by sampling date and laye
sampling.
Date,
1986
Apri
J,
October
UDDer
Lower
UDper
Lower
1
Sianif icance
EC, mmhos/cm
8.24
4.63
1.98
5.09
***
O.M., %
1.01
0.91
1.07
0.75
*
^1 , ppm
16.72
6.17
13.04
7.00
*
20.00
0.38
17.63
10.33
NS
K, ppm
111.29
04.92
118.04
113.58
NS
Mg , ppm
239.3
201.5
179.8
168.3
NS
Ca , ppm
1016.3
735.0
852.9
705.4
NS
Na , ppm
2136.7
1552.1
812.9
1612.1
***
PH
5.13
5.13
5.54
5.01
***
Buf-pH
6.15
6.35
6.61
6.27
***
+ = P < .05, *** = P < .001.
166
can be attributed to the addition of fertilizer. Additionally,
increases in EC and Ca can be related to the addition of gypsum
in those treatments.
When one examines the more detailed data reflecting date and
layer interactions, temporal trends become more apparent (table
7-7) . Most importantly, Na levels in the surface horizon fell
from 2137 ppm in April to 813 ppm in October. This 62% reduction
in Na brings an excessive and toxic Na level to a tolerable level
for most non-halophytic plants. Concurrently Na levels in the
lower horizon showed slight increases (table 7-7) , again
reflecting movements of salts into lower horizons. Mirroring
the trend in Na was the changes in EC, a measurement of total
salts. Again, an EC level of 8 mmhos/cm or higher at the
beginning of the season was excessive for proper growth of most
plants (Saturated paste extract - Bradshaw and Chadwick, 1980) ;
by October, the EC level at the surface was sufficiently low for
almost any plant species to germinate. The lower horizon salt
level tended to be fairly high, however, such that deeper root
growth of plants would be somewhat inhibited, and therefore
problematic for plants during periods of dry weather. With
continued leaching, salt levels in the lower horizons should
eventually be. reduced. pH also had significant interactions
between date of sampling and depth of sampling. The surface pH
tended to increase with time, whereas the lower horizon pH
decreased slightly (table 7-7) . The gypsum treatment is the
probable factor controlling the increase in pH as the Ca replaced
Na on the exchange sites. The reduction in pH in the deeper
horizon can be related to influx of anions and acidity from the
leaching phenomena.
Plant Tissue Analysis
Six harvested plant species were chosen for wet digestion
and chemical analysis, and the data are reported according to
treatment (Table 7-8) and species (table 7-9) . Chemical
characteristics analyzed included P, K, Mg, Ca, Na, aluminum
(Al) , manganese (Mn) , copper (Cu) , zinc (Zn) , and chloride (CI) .
No significant differences were apparent among treatments
for any of the plant tissue elements (table 7-8) . Evidently,
differences in the soils were not sufficient for them to become
apparent statistically after uptake into the aboveground plant
tissue. There was also a high variation in tissue concentrations
among species, which apparently overwhelms any treatment
differences.
When considering differences in tissue concentrations by
species, there were significant differences found in nine the ten
elements studied (table 7-9) . Many of the trends can be
interpreted as resulting from the dilution effect, i.e., plants
with lower biomass tend to have higher nutrient concentrations
167
per unit dry weight than those with high biomass. For example,
Elymus triticoides had very low production and exhibited the
highest concentrations for Cu and Zn, where Panicum virqatum had
high biomass production and the lowest concentrations for P, K,
Al, Cu, and Zn. Still, real differences exist among species for
their capacity to take up (or exclude) elements. Aaropvron
elonqatum had 50% higher CI concentration than the next highest
species. It can apparently tolerate high levels of CI
internally, whereas species like Puccinellia distans and Elymus
triticoides do not uptake CI readily and possibly exclude it
before uptake. These latter examples are more characteristic of
resistance, rather than tolerance, phenomena.
After one year of testing the most promising species for
reclamation of brine damaged soils in Illinois are 3 grasses and
2 chenopod shrubs: A^. elongatum. A. trachvcaulum. P. distans. A.
canescens, and A_s_ gardneri.
CONCLUSIONS AND RECOMMENDATIONS
1. Five species show great promise for growth on salinized
soils resulting from oil brine contamination: Aqropyron
elongatum. Aqropyron trachycaulum . Puccinellia distans,
Atriplex canescens. and Atriplex qardneri. After one year,
these species provided excellent vegetative cover for
erosion control and wildlife habitat.
2. An additional five species survived well and provided
adequate cover by the end of the first growing season.
These species may be even more successful during future
years: Sporobolus airoides. Elvmus triticoides. Elymus
iunceus. Eraqrostis curvula. and Panicum virqatum.
3. Another seven species were classified as unsatisfactory for
reclaiming salt brine soils under the conditions and
treatments of this experiment: Robinia neomexicana.
Atriplex confertifolia. Shepherdia arqentea. Trifolium
subterranean. Atriplex cuneata. Hedysarum boreale, and
Ceratoides lanata. Some of these species would be
acceptable if different conditions had been present (e.g.,
A. confertifolia transplants had arrived in better
condition, C_5_ lanata and A^ cuneata had been planted at
much higher densities or as transplants) .
4. Fertilizer proved to be advantageous to the growth of most
of the seeded (and weedy) species. Gypsum was only
beneficial for two species during the 1986 growing season.
Perhaps gypsum would have been of greater benefit if it had
been applied several weeks prior to seeding rather than at
the same time of planting.
168
Table 7-8. Plant tissue concentrations for selected species,
summarized by treatment. No elements showed
significant differences among treatments. Value
represents mean of six grass species.
Treatment
Fertilizer
Control
Fertilizer
Gypsum
& GvDsum
p,
%
.127
.148
.158
.148
K,
%
.842
.980
1.009
.993
Mg,
%
.107
.100
.116
.102
Ca,
%
.294
.244
.331
.277
Na,
%
.147
.202
.172
.138
Al,
ppm
650.6
520.6
642.4
527.6
Mn,
ppm
313.6
282.8
236.4
284.7
Cu,
ppm
9.50
11.61
10.00
8.18
Zn,
ppm
15.50
15.06
17.65
14.29
CI,
%
.682
.737
.686
.618
169
Table 7-9. Plant tissue concentrations for selected species, summarized b
Columns followed by differing letters are significantly differ
(P<.05) .
Species
Agropyron Sporobolus Puccinellia Elymus Eragrostis
elongatum airoides distans triticoides curvula
P, % .190 a .108 b .195 a .168 a .132 b
K, % 1.38 a .82 c .98 bc 1.21 ab .79 c
Mg, % .088 b .105 b .095 b .115 ab .089 b
.266 ab .195 b .385 a .286 ab .214 b
i^ia, 'i .203 b .386 a .162 bc .123 cd .046 d
Al, ppm 770.8 b 286.4 c 1066.7 a 790.8 b 326.7 c
Mn, ppm 318.4 b. 150.4 c 185.6 c 325.1 b 205.2 c
Cu, ppm 8.83 12.64 7.50 14.25 11.42
Zn, ppm 15.83 a 15.46 a 19.50 a 21.92 a 14.33 a
CI, % 1.28 a .84 b .36 c .40 c .45 c
170
5. Mulching the plots was valuable in retaining moisture,
especially during the dry spells in April and June.
6. Electrical conductivity in general and sodium concentration
in particular declined in the surface zone during the summer
of 1986. EC also increased in the lower horizon during that
same period, indicating a leaching of salts into the lower
zone.
7. It is recommended that one or more of the species mentioned
as promising be planted on brine damaged areas. Fertilizer
and mulching are also highly recommended. Then, a plant
cover may be established, and leaching of salts and organic
matter rejuvenation may occur so that the land can return to
meaningful production again, and at a relatively low cost.
ACKNOWLEDGEMENTS
I am indebted to David Ketzner, Ron Ehman, Jean Karnes,
Kristin Goltry, Dimond, and Sharon Baum for field and laboratory
assistance for this Lisaect. Special thanks to Jake and Henry
Klein for their efforts in preparing the seed bed, providing
mulch, and recording rainfall during the period of 1986. Thanks
also to Ms. Charlene Miles for typing the report. Thanks also
to my colleagues in the scientific surveys, especially Dennis
McKenna and Bruce Hensel, and to Tom Heavisides, Doug Wagner, and
John Marshall of the Department of Energy and Natural Resources
for their support.
LITERATURE CITED
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identified and described by vegetative characters: Canada
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disposal assessment-phase II report: Illinois Environmental
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Biosystematics Research Institute. Ottawa, Ontario, 566 p.
171
Frischknecht, N. C. and R. B. Ferguson, 1984, Performance of
Chenopodiaceae species on processed oil shale: Proceedings -
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Colorado plants from seed - a state-of-the-art:
FWS/DBS-82/29 Western Energy Land Use Team, USDI Fish and
Wildlife Service, Washington, D.C. 113 p.
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lands: the role of Kochia scoparia and other pioneers.
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relationships of winterfat fCeratoides lanata) in western
North Dakota: Proceedings of the Ninth North American
Prairie Conference, Clambey, G. and Pemble, R. , editors,
Tri-College Press, Fargo, ND, pp. 25-31.
Iverson, L. R. , D. Jordan, M. K. Nunna, 1984, Transplanting
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reclamation: Bulletin of the Ecological Society of America
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land. Journal of Soil and Water Conservation 39:26-29.
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Missouri Press, Columbia, 241 p.
Luke, F. and S. B. Monsen, 1986, Methods and costs for
establishing shrubs on mined lands in southwestern Wymoing:
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related chenopods, A. R. Tiedeman, E. McArthur, H. C.
Stutz, R. Stevens, and L. Kendall compilers. Gen. Tech. Rep.
INT-172, Intermountain forest and Range Experiment Station,
Ogden, UT, pp. 286-292.
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2 Volumes, J. Cramer, Germany, 2 591 p.
Monsen, S. B. and A. P. Plummer, 1978, Plants and treatment for
revegetation of disturbed sites in the intermountain area:
The reclamation of disturbed arid lands. University of New
Mexico Press, Albuquerque, pp. 155-173.
Mohlenbrock, R. H. , 1986, Guide to the vascular flora of
Illinois: Southern Illinois Univeristy Press, Carbondale,
507 p.
172
Ostyina, R. M. , C. M. McKell, J. M. Malecheck, and G. A. Van
Epps, 1984, Potential of Atriplex and other chenopod shrubs
for increasing range productivity and fall and winter
grazing use: Proceedings - symposium on the biology of
Atriclex and related chenopods, A. R. Tiedeman, E. McArthur,
H. C. Stutz, R. Stevens, and L. Kendall compilers. Gen.
Tech. Rep. INT-172, Intermountain Forest and Range
Experiment Station, Ogden, UT, pp. 215-219.
Pitelka, L. F. and D. L. Kellogg. 1979. Salt tolerance in
roadside populations of two herbacious perennials: Bulletin
of the Torry Botanical Club 2, pp. 131-134.
Redente, H. F. , P. R. Ogle, and N. E. Horgis, 1982, Growing
Colorado plants from seed - a state-of-the-art: Western
Energy Land Use Team FWS/OBS-8320 USDI Fish and Wildlife
Service, Washington, D.C. Vol. Ill, 141 p.
Rydberg, P. A., 1954, Flora of the Rocky Mountains and adjacent
plains: 2nd ed. Hafner Publishing Co. , New York. 1143 p.
Soil Conservation Service, 1986, Critical area planting oil well
salt damaged areas and high sodium areas: Interim Standards
and Specifications Technical Guide Section IV, Champaign, IL
pp. 1-4.
Springfield, H. W. , 1974, Eurotia lanata (Pursh) Mog. Winterfat,
Seeds of woody plants in the United States: Forest Service,
United States Department of Agriculture Handbook, 4 50 p.
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surface-mined lands in arid and semi-arid regions: USDA
SCS-IP-157, EPA600/7-79-134.
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Professional Paper. 2 p.
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improvement of saline and alkali soils: USDA Agriculture
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173
SECTION 8 REMOTE SENSING
by
Christopher J. Stohr and Edward C. Smith
INTRODUCTION
Two techniques were used to identify possible sources of
brine contamination of groundwater. Aerial photograph
reconnaissance was successfully used to locate brine holding
ponds which had been historically located in the study area.
Thermal infrared imagery was also used in an unsuccessful
attempt to locate underground sources of oil field brine
contamination .
AERIAL PHOTOGRAPH RECONNAISSANCE
One of the first tasks which must be undertaken when
assessing the potential for a brine problem over a given area is
location of all brine holding ponds, past and present which have
existed in that area. Physically searching the area would be
time consuming, labor intensive, and would not guarantee that all
holding ponds would be located, especially if holding ponds are
located on posted private property. Another problem which might
be encountered if an area were to be searched manually would be
locating abandoned holding ponds which may have been buried and
re-vegetated .
To overcome these problems, a time series of aerial photos
was used to locate all brine holding ponds in the study area. It
was found that holding ponds are easily recognizable, when using
stereo images, by their berms and by the surrounding vegetation
kill areas. Photos from 1953, 1966, and 1983 were used for this
task. The holding ponds identified on these images were then
located on U.S.G.S. 7.5' topographic quadrangles, which were
then used to compile figure 8-1.
The aerial photo reconnaissance was a time and cost
efficient method of locating brine ponds. Using this method,
both recent ponds and past ponds, no longer evident at the ground
surface, were located.
A total of 384 holding ponds were located in the study area.
Forty-four of the ponds noted in 1953 had been buried and
revegetated by 1966 (figure 8-1). The aerial photo
reconnaissance was also used to determine that very few (18)
holding ponds were constructed in the 17 years from 1966 to 1983,
indicating that injection for waterf looding and disposal have
become the dominant forms of brine disposal, and the usage of
174
Figure 8-1.
Brine holding ponds in southeast Clay County.
Locations from aerial photos taken in 1953, 1966,
and 1983. Also shown are locations A, B, C, and D
with wei^e investigate with Thermal Infrared
techniques.
R 6 E
R 7 E
R 8 E
Ponds visible on 1966 photos
(some also visible on 1953 photos)
Ponds visible on 1953 photos,
but not visible on 1966 photos
Ponds visible on 1983 photos only
175
brine holding ponds has been curtailed. These holding ponds were
concentrated throughout the eastern portion of the study area in
general and in particular, around the Camp Travis and Clay City
areas. Groundwater in these areas may be subject to
contamination due to leakage from these ponds. Further
discussion of this topic is given in Section 9.
THERMAL INFRARED SURVEY
Thermal Infrared (TIR) imagery is a nonphotographic method
of observing the long wavelength thermal infrared energy radiated
from any object with a temperature above 0° Kelvin (-273°C or
-459. 4°F). A TIR image is a black and white representation of
the relative amount of thermal energy (heat) radiating from a
given object. When the assessment of environmental affects of
oil field brines was proposed, it was envisioned that the TIR
imagery might be used to locate sites where brine was being
forced to the near-surface through leaky abandoned or inactive
wells and unsealed boreholes. It was theorized that this
procedure would be possible because the brine water which would
have been upwelling would be warmer than ambient near-surface
ground-water. However, no locations could be found within the
study area where brine migration of this type was occurring and
budgetary limitations precluded a search outside the study area.
Therefore, there was no control with which to test the ability of
TIR as a method of locating areas where brine water would be
upwelling. A secondary goal was. to observe differences between
brine-effected soils and nonaffected soils and compare the
results with black and white photographs of the area to determine
which type of imagery was best suited for identification of
brine-spoiled sites.
The theoretical and technical aspect of TIR imagery are
discussed by Sabins (1978) and Estes (1983) . In general,
materials absorb thermal energy from the sun at different rates
dependent on their composition, conductance, heat capacity, and
density. Water, for instance, absorbs thermal energy slowly and
radiates it slowly in contrast to most earth materials which
absorb and radiate the energy quickly. A TIR image, or
thermograph, shows the differences in radiant heat of materials
so that interpretations can be made of the types of materials
present based on their thermal properties. Areas which radiate
high thermal energy (i.e., warm areas) will be represented as
light-colored areas on the TIR image; areas of low thermal
energy (i.e., cold areas) will be represented by darker areas on
the image.
In order to obtain the best TIR imagery, some
considerations must be made regarding the time of day, season ,
and surface and atmospheric conditions. TIR imagery is best
taken at night, preferably in the predawn hours, so that the
effects of shadows and differential heating of surface
176
topography, which occur during daylight hours are minimized. The
season of the year was important to this study because green
vegetative cover can obscure the features of the ground surface.
The optimum time of the year is after leaf-fall in the winter.
During this season, colder temperatures of the ground
surface contrasting with relatively warm groundwater. This
contrast can allow observation of groundwater movement into
gullies and streams or possibly the presence of shallow aquifers.
Surface conditions are ideal if the ground is dry. Complete snow
cover would be unacceptable for most TIR surveys since the snow
would obscure the thermal energy radiated from the underlying
earth materials. Atmospheric conditions are ideal if it is not
hazy, cloudy or windy.
Site Selection
Four sites were selected for the TIR survey (figure 8-1) .
Sites A and B are the brine holding pond study sites discussed in
Section 9. These sites were selected for the comparison of TIR
versus black and white and color infrared imagery for use in
identification of brine spoiled sites.
Sites C and D were selected as possible locations of brine
water upwelling. The reconnaissance of groundwater quality
(Section 3) identified wells with total dissolved solids
concentrations greater than 2500 mg/L at these sites.
Results
The TIR survey was conducted during late evening of February
23, 1987. A helicopter, furnished by the Illinois Department of
Transportation - Division of Aeronautics, carried two
instruments; a FLIR Systems thermal scanner mounted on the
helicopter and an Inframetrics portable thermal scanner. The
imagery was recorded on videocassette recorders for later
interpretation of the data. Prior to the aerial survey, flashing
road hazard lights had been placed at the four sites to aid in
navigation.
Much of the area to be surveyed was moist due to recent rain
and melting snow. A few small areas were still covered by snow.
Also, a low fog affected several isolated areas and dew began to
form on the grass and field stubbles before and during collection
of the imagery.
The time of day and weather conditions may have hindered the
acquisition and interpretation of the TIR imagery. The flight
should have been made in the fall just after leaf-fall when the
ground was dry and dew formation was at a minimum.
177
= Site A Section 33 Study Site (figure 8-2)
The TIR imagery thermogram from this site shows that the
brine affected-areas have a higher thermal radiance than the
non-affected areas. The higher thermal radiance may indicate
higher moisture being held by salts and saline soils. The area
of the filled-in brine pond does not appear to have a
significantly higher thermal radiance than the surrounding
area. The warmest areas are the bases of the numerous erosional
gullies that dissect the area. The heat in these areas is likely
due to groundwater seepage into the gullies from the soil. The
presence of brine salts in the gullies may have added to the
thermal radiance seen on the imagery. The areas of the heaviest
brine salt accumulations downgradient from the brine pit have a
high thermal radiance.
s Site B Section 21 Study Site (figure 8-4)
Drainage patterns are enhanced at this site. Brine affected
areas appear warm. A bright spot (indicating relatively high
temperature) on the imagery appears near the center of the
abandoned pit area (figure 8-5) . The spot is located in a
depression which has remained continually moist even when air
temperatures were below freezing. The reasons for the high
thermal radiance at this spot are not known.
A ground TIR Survey of this- area made several weeks after
the aerial survey indicated slight variances (figure 8-3) in the
thermal radiance. The center of the depression had the highest
reading but that was only slightly higher than the surrounding
area. There may be an unreported abandoned well at this site;
however, none is recorded in ISGS files. Without excavation or
detection by some other means there is no conclusive evidence
that the high temperature "hot spot" is an abandoned well or
upwelling brine waters.
= Site C High TDS in abandoned well NE-1/4 NW-1/4 Section 23,
T. 3 N. , R. 7 E.
No evidence of surficial brine damage or upwelling brine
waters from abandoned wells was observed.
= Site D High TDS in old well SE-1/4 SE-1/4 , T. 3 N. , R. 7 E.
No evidence of surficial brine damage or upwelling brine
waters from abandoned wells was observed.
Conclusions
The airborne thermal infrared imagery proved useful in
observing differences in thermal radiance at the study sites.
Brine-affected areas were especially noticeable. However,
178
Figure 8-2
Sketch of thermograph for site A. Large light
colored areas indicate brine affected soils. White,
rectangular patch in lower right corner is NHS test
plot (section 7) .
179
Figure 8-3. Traverse across "hot spot" at Site B.
180
Figure 8-4
Sketch of thermograph for Site B study site. Light
colored areas are brine affected soils. Thin light
area at lower right edge shows groundwater
discharge to creek. Ground survey traverse line is
indicated.
181
Figure 8-5.
Postsunset, airborne thermal infrared imagery
(thermograph) of Site B, Clay Co., IL. Light areas
represent relatively high temperatures (thermal
radiance) ; dark areas represent relatively low
temperatures. A stream appears in the lower right
of the image, U.S. 50 is in the upper right, and a
dirt access road makes an S-shaped curve from the
upper left to the lower center of the image.
Brine-affected soils which probably hold more
moisture and therefore appear relatively light
(warm) . The unusual bright spot near the center of
the image is a thermal anomaly.
182
brine-affected areas are also observable on large to medium
scale aerial and color infrared photographs. Thermal infrared
imagery had to be flown especially for this project, and
consequently was more expensive than the photography which was
borrowed locally.
Groundwater flow into stream and gullies could be discerned
from thermal infrared imagery. This may prove useful for
identifying areas of aquifer discharge, groundwater flow along
near-surface joints, and groundwater flow into surface water
bodies. As expected, no evidence of leaky wells could be
identified by airborne thermal infrared imagery.
Imagery collected at Site B shows an abrupt change (a hot
spot) in radiance. The increase in radiance could possibly come
from an underground source such as an abandoned, unplugged well.
Other evidence supports the hypothesis:
a) The TIR imagery shows an abrupt increase in temperature
at the muddy depression indicating a restricted heat
source.
b) There was a continuous presence of water in the
depression where the change in radiance was recorded.
c) Nearby oil production is being actively promoted by
injecting water into deep (about 3000 to 3500 feet)
bedrock formations. At this depth groundwater
temperatures rise to about 90 degrees F (Whitaker, 1987)
which would contrast sharply with the below freezing air
temperature (daily maximum was 47 F; minimum was 2 8.2 F
as recorded at the Flora weather observation station on
February 23, 1987).
However, there are no records of a well being drilled at
thi .. .-.:e. Although the thermal IR data suggest the existence of
a ^i^aKy well, there has been no confirmation by other methods.
183
REFERENCES
Estes, J. E. , E. J. Hajic, and L. R. Tinney, 1983, Chapter 24,
Fundamentals of Image Analysis: Analysis of Visible and
Thermal Infrared Data: in Manual of Remote Sensing, 2nd
ed. , Robert N. Colwell, editor. Am. Soc. of Photogramm,
2440 p.
Sabins, F. S., Jr., 1978, Remote Sensing: Principles and
Interpretation: W. H. Freeman and Company, San Francisco,
CA. , 426 p.
Stohr, C. H., 1974, Delineation of Sinkholes and the Topographic
Effects on Multispectral Response, M.S. Thesis, Purdue
Univ., Lafayette, IN., 132 p.
Whitaker, S., 1987, personal communication. Geologist, Oil and
Gas Section, Illinois State Geological Survey.
184
TASK 9 CASE STUDIES OF GROUNDWATER CONTAMINATION
ORIGINATING FROM BRINE HOLDING PONDS
by
Bruce R. Hensel, Dennis P. McKenna, Stephen L. Burch,
Paul C. Heigold, and Douglas E. Laymon
INTRODUCTION
Brine water produced in association with oil pumpage in Clay
County, Illinois typically has high concentrations of chloride
(55000 - 89000 ppm) , sulfate (28 - 2100 ppm) , sodium (32000 -
48000 ppm), calcium (2300 - 8900 ppm), and magnesium (100 - 2800
ppm) (from Meents et al., 1952). Total dissolved solids
concentrations of brines produced in this county are typically
three to four times higher than that of sea water.
Disposal of oil field brines has been a problem since the
1930 's when the brines from the first oil wells in the state were
allowed to spill onto the land surface and into rivers and
streams. Beginning in the 1940 's brines were stored in holding
or 'evaporation' ponds. However, since the average precipitation
rate in Illi.-iois exceeds the average evaporation rate (Roberts
and Stall, 1967) , large quantities of brines may have been
infiltrating into local aquifers from these ponds (Reed et al.,
1981) . Unlined brine holding ponds were phased out during the
1980 's and have been banned since 1985.
It has been estimated that over 8600 brine holding ponds
have been in recent use in Illinois (Illinois Department of Mines
and Minerals, Division of Oil and Gas, 1985) . All of these
holding ponds should now be closed; however, the brine which has
seeped into the earth beneath these ponds still remains as a
potential source of groundwater contamination.
The first objective of the case study was to investigate the
movement of brines through the subsurface. The second objective
was to investigate the use of a cost- and time-efficient
geophysical method to trace subsurface brine plumes.
Two sites were chosen for study and are labeled A and B on
figure 9-1. Site A was chosen because the holding pond at this
site is isolated from other potential sources of brine
contamination (other holding ponds, oil wells, abandoned wells,
and injection wells) , and because a study had previously been
conducted at this site (Reed et al., 1981). That study provided
background data and information on the shape of the plume in
1978, as determined by geophysical techniques. Site B was
selected because of its isolation from other possible sources of
185
Figure 9-1
Location of case study sites A and B, southeastern
Clay County.
R 6 E
R 7 E
R 8 E
Wayne Co.
186
brine. Also, since a large portion of this site was not to be
used as cropland, sufficient area was available for surface water
and plant reclamation investigations (see sections 4 and 7) as
well as for the groundwater investigation.
METHODS OF GROUNDWATER MONITORING
Installation of Groundwater Observation Wells
Fifteen observation wells were installed at the two study
sites (7 at site A, 8 at site B; figures 9-9 and 9-16) . The
wells were placed in locations most suitable for measuring the
elevation of the water table at or near the study sites. Thus,
these wells were not necessarily located in areas of suspected
brine plumes.
The borings for these wells were made with 4-inch, solid-
stem auger driven by the Illinois State Geological Survey Mobile
B-3 0 trailer-mounted drilling rig. The wells were constructed of
2-inch diameter PVC pipe which was hand slotted from 2 feet below
ground surface to total depth of 12 to 24 feet (figure 9-2) . The
entire slotted interval was back-filled with washed, crushed
limestone and a bentonite seal, 1-foot thick, was placed at the
top of the bore hole. Because the crushed limestone may have
affected the chemical composition of groundwater samples, the
results of chemical analysis on samples obtained from these wells
were used only as gross indicators of the presence of brine.
Installation of Piezometers
Forty-one piezometers were installed at the two sites (19 at
site A, 22 at site B) for the purpose of obtaining groundwater
samples. Most of the piezometers were located in nests of two or
three wells which were finished at different depths. A total of
9 monitoring stations were established at site A (figure 9-9)
and 11 stations at site B (figure 9-16) . The stations were
located in places where data from the geophysical survey
indicated a plume should exist as well as in places where no
plume was detected.
All piezometers were drilled with 6-inch hollow-stem auger
driven by the Illinois State Geological Survey Mobile B-30
trailer- mounted drill rig. Samples of the earth material were
collected from the deepest borings at each well nest. Soil tubes
were pushed to collect a continuous sequence of samples of the
surficial materials, usually to a depth of between 5 and 10
feet. After the maximum penetration of the soil tube, the
borehole was advanced with the hollow stem-auger and split-spoon
samples were collected at 5-foot intervals.
187
Figure 9-2.
Schematic drawing of typical piezometer (I) and
observation well (II) used at case study sites A and
B.
Natural pack
Bentonite seal *=^
greater than 1 ft
2 in. ID threaded, flush
joint PVC
Natural pack
. Locked cap
Hole diameter 6 in
Bentonite seal
greater than 2 ft
Sand pack
0.01 in. slot screen
Bottom cap
Natural pack
Bentonite seal
greater than 1 ft
2 in. ID PVC,
hand slotted
Crushed limestone
backfill
Hole diameter 4 in.
No bottom cap
188
The piezometers were constructed of 2-inch diameter,
threaded, flush-joint PVC pipe. Each well was completed with a
2.5 foot, 0.01 inch slotted screen at the base. The annulus of
the borehole was filled with; 1) silica sand to the top of the
screen, 2) a bentonite seal of at least 2 feet overlying the
sand pack, 3) cuttings from the lower seal to near surface, and
4) another foot of bentonite at the surface (figure 9-2) .
Samples collected during drilling were described using
standard soil survey nomenclature. Characteristics described
included color, texture, structure, root occurrence, presence of
carbonates, concretion occurrence, jointing and mottling. The
pres€- -e of clay skins, siltans, iron or other deposits on joint
faces ere noted, as well as laminations and other sedimentary
structures. Selected samples were analyzed for grain-size
distribution and clay-mineral composition by the Inter-Survey
Geotechnical Lab This lab work was done to facilitate
determination of stratigraphic relationships. Grain-size
analysis followed the standard hydrometer procedure (ASTM
D-422) : clay is less than 4 microns. Clay-mineral composition
was determined by X-ray diffraction procedures described by
Killey (1982) and Hallberg, Lucas and Goodmen (1978) .
Groundwater Sampling Methods
Preliminary field measurements of the electrical conductance
of water samples from all of the. wells were made during the
summer of 1986. The preliminary electrical conductance data were
used to determine the order in which water samples would be taken
from the wells for detailed chemical analysis of common ion
concentrations (Ca, Li, Mg, Na, Sr, CI, S04 , and alkalinity).
Wells with water of low electrical conductivity were sampled
first to reduce the possibility of cross-contaminating samples.
Sampling of water for detailed chemical analysis was
conducted in the fall of 1986. All wells were first purged of
standing water with a teflon/-PVC diaphragm pump. The majority
of the wells recovered comparatively slowly and were pumped until
dry. Those wells which recovered more rapidly were pumped until
at least two (three in the case of the shallow wells) well
volumes had been extracted. Water samples were then taken from
all of the piezometers and some of the observation wells, using a
teflon bailer, while water was still recharging to the wells.
The water samples were filtered in the field with either a
peristaltic pump and 142mm diameter, 0.45um membrane filter or a
pressurized tank and 47mm diameter, 0.45um filter. The filtered
samples were split into acidized and non-acidized high-density
polyethylene containers, and stored on ice until returned to labs
of the State Water and Geological Surveys for analysis of ion
concentrations. The procedures and results of the chemical
analyses are listed in Appendix 9-A.
189
Collection of Hydrogeologic Data
Water levels in both the observation wells and the
piezometers were recorded at approximately three-week intervals.
Slug testing was performed at five piezometer stations to
determine the hydraulic conductivity of the sediments underlying
the sites. The results of the slug tests were analyzed using
the method of Horslev (1951). The relative recovery of water
levels in the piezometers, after sample purging, was noted.
These recovery rates may be indicative of the ability of the
materials near the piezometers to transmit water. Recovery to
within 10% of pre-purge levels, after 24 hours, was considered
high. A 24 hour recovery of less than 50% was considered low.
Some piezometers did not recover at all, recovery rates for these
wells are very low. Figure 9-3 shows the relationship of the
observed piezometer recovery rates to slug test derived valves of
hydraulic conductivity at those piezometers. Even though the
correlation is not strong, the relationship is significant.
GEOPHYSICAL METHODS.
The geophysical surveying consisted of a number of shallow
seismic refraction profiles and vertical electrical soundings
(VES) . The purpose of the geophysical surveys were to: 1)
determine the depth to bedrock at the study areas; and 2) map the
configuration of the subsurface brine plumes.
Shallow Seismic Refraction Profiling
The shallow seismic refraction surveying at the two holding
ponds was conducted with an EG&G multichannel, signal enhancement
seismograph, model ES 2415 F, owned by the Illinois State
Geological Survey. This instrument is commonly used by the ISGS
in studies to determine seismic properties of subsurface
materials and to estimate the depth to the bedrock surface.
At each of the two brine ponds, four 600-foot reversed
profiles, oriented in north-south and east-west directions
(figure 9-4) provided information about the depth to the bedrock
surface as well as the seismic properties of the drift and
bedrock.
Vertical Electrical Sounding
The vertical electrical sounding surveying at the two brine
ponds was conducted with an ABEM Terrameter, model SAS 3 00 B,
owned by the Illinois State Geological Survey. This instrument,
which has an alternating current power source, is commonly used
by the ISGS to characterize the glacial drift when searching for
domestic, community, and industrial groundwater supplies. In
recent years the VES method has been successfully used to locate
190
Figure 9-3
Semi-log plot of % recovery vs hydraulic
conductivity at the Clay County study sites.
Correlation is significant at the 95% level.
.58.
r2 is
100 T
10
10"* 10-=*
Hydraulic conductivity (cm/s)
191
and monitor the migration of contaminant plumes within the
glacial drift.
A number of vertical electrical soundings were made in the
vicinity of each brine holding pond. The distribution of the
soundings is shown on figures 9-13, and 9-19 . In all of these
soundings the electrode spacings were expanded to a distance that
assured that the corresponding VES curves adequately represented
the resistivity of the near surface deposits and groundwater
within those deposits.
The Schlumberger electrode configuration was employed in
this study (figure 9-5) . In this configuration, four electrodes
are placed along a straight line on the earth surface. The two
outer electrodes, the current electrodes {li and I2)/ are
located at a distance, L, from the center of the array, while
the two inner electrodes, the potential electrodes (P^^ and P2)/
are located a distance a/2 from the center of the array. For
this electrode configuration, the resistivity (Pn) of ^
homogeneous and isotropic medium, in which the electrodes are
inserted, is given by:
(P2-P1) (a) l2 1
I 2 a 4
where a = the distance between the potential electrodes
L = the distance from the center of the array to
either current electrode
P2 - Pi = the difference in potential between
electrodes P^ and P2
I = the current flowing between electrodes I^ and
l2-
When the medium into which the electrodes are inserted is
not homogeneous, the resistivity given by the above equation is
an apparent resistivity (Pa) — a weighted average of whatever
resistivities may exist in the region between the potential
surfaces (P]_ and P2) that intersect the ground surface at the
potential electrodes.
As the electrode spacings, a/2 and L, are increased (in this
study, the ratio of L to a/2 was kept at a constant value of 10) ,
the resistivities of deeper materials have an effect on the
measured apparent resistivity. The method of expanding the
electrode configuration systematically around the center point,
measuring current and potential differences, and calculating
apparent resistivity values is called vertical electrical
sounding (VES) . A plot of apparent resistivity values versus
electrode spacings is a vertical electrical sounding (VES) curve.
192
Figure 9-4
Location of seismic lines at Clay County case study
sites A (5-8) and B (1-4).
193
Qualitative information about near surface materials can be
obtained from the maxima, minima, inflection points, and apparent
resistivity values of a VES curve. However, the types of
information most often desired are the layering parameters, that
is, the "true" thicknesses and the "true" resistivities of the
strata immediately below the center of the VES profile. Several
quantitative interpretation or inversion techniques can be used
to determine the layering parameters from VES curves. The
technique developed by Zohdy (197 3) was used in this study.
However, this technique, like most of the others available,
provides only one of many geoelectrically equivalent layering
parameter solutions for a given VES curve. Prior knowledge of
the geologic conditions in the study area helped to compensate
for this shortcoming.
A typical vertical electrical sounding (VES) curve
corresponding to a vertical electrical sounding (made using the
Schlumberger electrode array) near the north brine pond (site B)
is shown in figure 9-6. In this particular sounding the distance
from the center of the array to an outside current electrode was
expanded to 4 6 meters (150 ft) . The layering parameter solution
for this sounding, using the Zohdy inversion technique, is shown
in figure 9-7,. As can be qualitatively surmised from the
inspection of the VES curve, the unconsolidated materials near
the earth's surface are a series of low resistivity layers
overlying materials of considerably higher resistivity.
The electrical resistivity of a material is inversely
proportional to the conductance of the material. Consequently,
materials with a high electrical conductance will have a low
resistivity. The measured electrical resistivity of an earth
material will be affected by two factors, the conductance of the
material and the conductance of the fluids in the void spaces of
that material. Water is more conductive than most earth
materials, hence it has a strong effect on the resistivity values
of saturated earth materials. As the mineral content (ion
concentration) of the pore water increases, so does its
conductivity. Thus materials saturated with brine waters, which
have high mineral content, are more conductive and have lower
resistivity than similar materials saturated with fresh '"*^^^*,
The low resistivity value or 12 oKm-ino-terti ^tigure 9-7) probably
represents materials containing brine water.
In order to determine the configuration of a plume which has
migrated away from a given brine pond, the following scheme was
employed: first, data from all vertical electrical soundings
around a brine pond were inverted so that a set of layering
parameters (layer thicknesses and resistivities) was obtained
194
Figure 9-5
Basic elements of an earth resistivity meter and the
Schlumberger electrode configuration.
Battery
<^
■(T tP^im.-^-^f.
Volt meter
7^
p, Pj
n
a
Current meter
<2>
^M ■• ^'^
195
Figure 9-6
Vertical electrical sounding (VES) curve from data
gathered at a resistivity station near piezometer
P3 , case study site B (figure 9-15).
^0
30
Q.
C
<
■•= 20
10
J_
_L
1 10
Distance (L) !rom center ol array to either current electrode in meters
100
196
Figure 9-7.
Layering parameter solution for VES curve presented
on figure 9-6.
12
23
12
"True" resistivity values
in ohm-meiers
10
112
Q.
0)
Q
15
70
20
197
for each discrete VES point; next, at each VES point the "true"
resistivity values associated with depths of 3 and 6 meters were
recorded; then, these "true" resistivity values were plotted and
contoured. Low "true" resistivity values (more specifically,
"true" resistivity values lower than those that would be expected
for the observed lithology saturated with fresh water) were of
special interest. These exceptionally low "true" resistivity
values are most likely indicative of brine contamination. The
expected or normal "true" resistivity values at a given depth
would likely occur in areas distant from the brine pond where
earth materials are more likely to be saturated with fresh water.
The interpretation and evaluation of the resistivity results
was hampered by imprecise mapping of VES stations. The VES grid
was laid out according to taped measurements and markers were
left at each VES station. However, when the sites were surveyed,
many of these markers were missing; thus the location of those
stations represented by the missing markers had to be
interpolated based on taped measurements. Because more than half
of the VES stations are mapped imprecisely, direct comparison of
resistivity values with data on ion concentrations (obtained at
precisely located piezometers) was not attempted.
RESULTS
Site A (NORTH SITE)
Site A is located on a nearly level upland in sections 21
and 28, T. 3 N. , R. 7 E. , Clay County. Surface drainage is south
to a road ditch along U.S. Route 50 and west to an intermittent
channel which is a tributary of the Elm River (also the discharge
point of the road ditch) . A brine holding pond had been in
operation at this site for more than 20 years (Reed et al . , 1981)
and was filled in 1984 (Klein, personal communication, 1986) .
At the time of this investigation there was no vegetation growing
in the area of the former holding pond or along a wash which
drains into the tributary (figure 9-8) .
- Site Geology
This site is underlain by moderately well to somewhat poorly
drained soils formed in Wisconsinan age loess and loamy diamicton
of the Glasford Formation of Illinoian age. The soils are
strongly developed with thin silt loam A horizons and clay loam B
horizons that have moderately slow to slow permeability. The
underlying diamicton is generally uniform in texture in the upper
25 feet. Evidence of oxidation along vertical and horizontal
joint faces within the generally massive material of the
diamicton and the presence of oil stains along vertical joints at
depths of up to 31 feet in core samples below the holding pond
suggests that there is preferential flow through the diamicton
along the joints. Below 2 5 feet, the materials become
Figure 9-8
198
Location of observation wells, piezometers, and
cultural features at site A.
G3 Unvegetated area
■ Elevation datum
• Piezometer (2.5 tt screen)
•^ Observation well (entire length slotted)
199
stratified, consisting of fine to coarse sand, diamicton, and
bedded silts. Bedrock was not encountered during drilling.
The seismic refraction data show that the bedrock surface at
this site generally slopes down to the southeast. The depth to
bedrock immediately below the area of the filled-in pond is
approximately 94 feet.
» Previous Investigation
Reed et al. (1981) conducted an investigation at this site
in 1978. Four piezometers were installed (one nest, two single
wells) and a VES survey was conducted to determine the extent of
brine migration. The results of that study are shown on figure
9-9. Groundwater at the site was determined to be flowing in a
radial pattern away from the holding pond, which was still in
use. The radial flow pattern indicated leakage of brine from the
holding pond into the subsurface. The plume detected in the VES
survey had extensions to the northeast, south and west. Air
photo interpretation indicated that from 1966 to 1978 the
unvegetated area surrounding the holding pond had expanded
(figure 9-9) .
« Groundwater Flow Direction and Hydraulic Conductivity at
Near-Surface Materials
The relative elevation of the water table, as measured in
the observation wells, is shown on figure 9-10. In general, the
horizontal component of shallow groundwater flow is toward the
southwest and is controlled by the tributary to Elm Creek as well
as by the drainage ditch. Horizontal gradients range from 0.02
to 0.03. The vertical component of groundwater flow is generally
downward. Downward vertical gradients, measured at the
piezometer nests, range from 0.38 to 0.02 (table 9-1). However,
the gradients measured between the shallow and intermediate wells
at station P4 and between the intermediate and deep wells at
station P3 indicated groundwater flow in an upward direction.
The upward flow at station P4 is believed to have been a result
of seepage toward the adjacent gully, which is probably a local
groundwater discharge area. The upward flow at station P3 could
be upward seepage toward the relatively high permeability
sediments overlying the inteirmediate well (the shallow well is
finished in these sediments) . This effect is probably local and
not typical of groundwater flow conditions for most of the site.
Slug tests were conducted at piezometer stations P3 and P5.
Hydraulic conductivity for the four wells tested ranged from 3 x
10~2 to 8 X 10"^ cm/s.
200
Figure. 9-9. Resistivity contours and extent of unvegetated area
in 1978 at site A (from Reed et al., 1981).
Approximate SE corner
-j- of section 21
300 ft
I
^^- Contour showing apparent resistivity; interval 5 ohm-nneters
■-45Q -- Elevation contour (ft)
• Resistivity station (numbered stations shown on fig. 7)
1978
'T966"
Approximate limit of unvegetated area
N
201
Figure 9-10. Relative water table elevation (in feet), site A,
October 1986.
Approximate extent of
brine damaged area
C3 Unvegetated area
■ Elevation datum
Contour interval = 2 tt
(dashed where inferred)
Water table
.8 October, 1986
202
= Groundwater Chemistry
The results of the chemical analyses of groundwater samples
from this site are tabulated in Appendix 9-B. In general, the
chloride concentrations were very high (up to 32,000 mg/L) in
areas affected by the brine. Water samples from the two
piezometer stations outside of the brine plume had higher
concentrations of sulfate (134-329 mg/L) than chloride (21-27
mg/L). The concentration of sodium is very high (630-15,000
mg/L) in waters sampled toward the central part of the plume.
At the fringe and outside of the plume, the concentration of
calcium and sodium are roughly equivalent (87-310 and 55-590
mg/L, respectively) .
Because chloride is a highly mobile and conservative anion,
as well as the major constituent of Illinois oil brines (Meents
et al., 1952), it was chosen as an indicator of brine impacts on
groundwater. The extent of the chloride plume, as interpreted
from chloride concentrations in water samples taken from the
piezometers, is shown on figure 9-11. This figure only shows
data from wells less than 20 feet deep. With the exception of
three wells near the center of the plume, the chloride
concentration, in the wells greater than 20 feet deep is less than
250 mg/L.
Two lobes of high chloride concentration are apparent on
figure 9-11. One lobe of high concentration extends from the
area of the holding ponds south beneath highway 50. The second
lobe extends northwest from the holding pond area. This plume
has a similar configuration to that mapped by Reed et al.,
(Figure 9-9) except that the northeast lobe is absent. Data for
other ions, including strontium (figure 9-12) , suggest a similar
plume configuration.
- Vertical Electrical Sounding Survey
Two VES surveys were conducted at site A. Resistivity
values for the entire site were measured during the first survey.
A second, less extensive, survey was conducted to better define
the extent of the plume's south lobe. Figure 9-13 shows the
distribution of the "true" resistivity values at a depth of 3
meters in the vicinity of the north brine pond. The area within
the 10 ohm-meter contour represents an area at a depth of 3
meters that is likely contaminated with brine.
The selection of the 10 ohm-meter value as an indicator of
brine contamination was based on comparison of resistivity vs.
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204
Figure 9-11
Chloride concentrations in groundwater at site A.
Concentrations at nested piezometer stations are
from shallow well only. Samples taken in November,
1986.
Approximate e)ctent of
-, /brine damaged area
G3 Unvegetated area
Inferred limit of chloride plume
8530 Data point, chlonde concentration (rngt)
Contour interval = 10,000 mg/L
(dashed where inferred)
205
Figure 9-12. Strontium concentration in groundwater at site A.
Concentrations at nested piezometer stations are
from shallow well only. Samples taken in November,
1986.
Approximate extent
brine damaged
G3 Unvegetated area
Inferred limit of strontium plume
• 9.1 Data point, strontium concentration (mg/L)
Contour interval = 10 mg/L
(dashed where inferred)
206
Table 9-2.
Chloride concentrations and total dissolved solids
compared to resistivity, site A. Underlined values
indicate data for observation wells.
Resistivity
(ohm-meters)
Chloride
Concentrations (mg/L)
Average
0-10
11-20
21-30
8530, 8770, 32000, 12690. 14950
4400, 9800
21, 27, 36, 1510. 1730, 2500
15,388
7,100
970
Resistivity
(ohm-meters)
TDS (mg/L)
Average
0-10
11-20
21-30
12, 817, 13182, 52006, 19827, 23809
8928, 21054
560, 894, 959, 2589, 2893, 5206
24,328
14,991
2,183
207
chloride concentration and resistivity vs total dissolved solids
(table 9-2) . For both comparisons, the wells within the 20
ohm-meter resistivity contour have water contaminated with brine.
However, wells outside of the 2 0 ohm-meter contour may or may not
be contaminated. Therefore, the conclusion may be made that the
area within the 2 0 ohm-meter contour is likely contaminated by
brine. However, the more conservative value of 10 ohm-meters was
used because only two data points lie within the 11 to 20
ohm-meter range (table 9-2) . Figure 9-14 shows the resistivity
values at a depth of 6 meters. At the 6-meter depth only two
rather small, discrete areas in the vicinity of the brine pond
are enclosed by the 10 ohm-meter contour. Since the low "true"
resistivity values at the 6 meter depth may be an artifact of the
inversion technique caused by low "true" resistivity values at
shallower depths, it appears that the earth materials and
groundwater at, and possibly above 3 meters has a greater
concentration of brine ions than at the 6-meter depth.
- Site A Summary
A brine plume exists at site A with lobes extending south,
northwest, and northeast. This plume configuration is similar to
that mapped by Reed et al. (1981) . However, it does not follow
current groundwater flow patterns at the site which are generally
south and east (figure 9-10) . The existence of lobes in
directions currently upgradient of the location of the holding
pond is explained by the observed groundwater mounding beneath
the pond in 1978, before it had been filled in (Reed et al.,
1981) . Mounding would have caused a groundwater gradient away
from the pond in all directions.
Recovery rates, a gross indicator the ability, of the soil to
transmit water were high at shallow wells where brine
concentrations were high and low to moderate where brine
concentrations were lower. This relationship suggests that brine
migration at this site was principally through the more permeable
materials. Downward migration at this site may have been
restricted because the deeper materials are generally less
permeable than those near the surface.
SITE B (SOUTH SITE)
Site B is located in sections 33 and 34, T. 3 N. , R. 7 E. ,
Clay County. The holding pond at this site was in existence for
approximately 10 years and was filled in 1984 (Klein, personal
communication, 1986) . The holding pond was situated on top of a
hill. Surface relief across the entire study site is about 15
feet. Surface drainage is primarily east toward Elm Creek
(figure 9-15) along a gully which has cut one to two feet into
the unvegetated soil of the brine damaged portion of the site.
Headward erosion of the gully exceeded twenty feet during the
summer of 1986.
208
Figure 9-13. "True" resistivity contours at site A,
depth is 3 meters.
Approximate
I '
150 ft
—I
• Resistivity station
Approximate boundary of brine holding pond
True" resistivity value « 10 ohm -m
Contour interval = 20.0 ohm -m
209
Figure 9-14. "True" resistivity contours at site A.
depth is 6 meters.
Approximate
N
150 tt
—I
• Resistivity station
Approximate boundary of brine holding pond
Cii} True" resistivity value « 10 ohm -m
Contour interval = 20.0 ohm -m
210
Site Geology
The soils at site B range from moderately well to well
drained soils on the convex sideslopes to poorly drained soils on
the concave toe slope positions and on the flood plain of Elm
Creek (east of the site) . Somewhat poorly drained soils occur on
the nearly level upland west of the holding pond area.
The upland soils formed in thin loess (10 to 40 inches) and
the underlying silty diamicton of the Glasford Formation. The
poorly drained soils formed in up to seven feet of loess and
silty alluvial and colluvial sediments. These soils are less
well developed than soils which formed in the more stable upland
positions.
The diamicton at site B is generally finer-textured and less
variable than at site A. This unit also exhibits less evidence
of secondary structures, such as root channels and voids. The
finer texture and lack of pedologic features which would increase
permeability in this unit suggest that it would have lower
hydraulic conductivities than the diamicton at site A.
On the uplands, weathered sandstone and shaly sandstone of
the Pennsylvanian age Mattoon Formation were encountered at
depths of 25 to 45 feet below ground surface. The seismic
refraction data indicate that the bedrock surface generally
slopes downward toward the northeast.
= Groundwater Flow Direction and Hydraulic Conductivity of
Near-Surface Materials
The relative elevation of the water table was, contoured
based on data from late October (before water samples had been
collected (figure 9-16). Groundwater flow at this site reflects
surface topography, with a horizontal component of flow primarily
to the east. Horizontal gradients range from 0.01 to 0.03.
Vertical gradients measured at the piezometer nests are generally
downward (table 9-3). These gradients range from 0.01 to 0.45.
Station P6 did not have a deep well) . These upward gradients are
believed to be due to seepage toward the adjacent gully. Also,
station P4 had a slight upward gradient (0.04) which is believed
to be seasonal. Measurements at station P4 , taken in January of
1987 after a snow-melt, indicated a downward gradient of 0.36.
Slug tests were performed at piezometer stations PI, P6, and
P8 . The hydraulic conductivities calculated at these stations
range from 2x10"^ to 5x10"^ cm/s (table 9-3) .
211
Figure 9-15. Location of observation wells, piezometers, and
cultural features at site B.
2
a-b
10a
CD Unvegetated area
- Observation well (entire length slotted)
• Piezometer (2.5 tt screen)
■ Elevation datum
Q NHS test plot
■ Intermitlenl drainage way
■ SWS surface water station
100 ft
ki^i^iiin:
2 /
/
/
::|s|i/ipproximate boundary
\\- W^ C' y/'vyy. of holding pond
li./
lit
/
11a
a*
Tank battery
8^
212
Figure 9-16. Relative water table elevation, site B, October
1986.
G3 Unvegetated area
■ Elevation datum
0 NHS test plot
Intermitlent drainage way
■ SWS surlace water station
Contour interval = 2 tt
100 n
Water table
October, 1986
Datum is lower outlet pipe on
west tank ot tank batlery
Tank banery
-14
•-15.4
213
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214
Groundwater Chemistry
The results of chemical analyses of groundwater samples from
this site are tabulated in Appendix 9-B. The concentration of
chloride in groundwater in areas affected by the plume is as high
as 11,000 mg/L. Away from the plume, the concentration of
sulfate (35-650 mg/L) is higher than the other anions including
chloride (11-57 mg/L). Sodium (56-3900 mg/L) and calcium
(62-1760 mg/L) are the cations with highest concentrations.
The configuration of the chloride plume at site B, as
detected by concentrations in groundwater samples, is shown on
figure 9-17. Only two stations, both near the area of the
filled-in pond (piezometer stations 1 and 3) , showed evidence of
elevated levels of chloride in groundwater at a depth greater
than 20 feet. Total dissolved solids concentrations were also
mapped and show a similar plume configuration (figure 9-18).
The presence of a plume in the lowland area east of the
filled-in pond and the area of low chloride concentrations
between the lowland and the holding pond area may indicate that
processes other than migration through groundwater are
responsible for brine movement at this site. There are two
mechanisms of brine transport which may explain the lowland
(east) plume. One possible mechanism is saline runoff waters
from the holding pond area flowing downhill along the gully and
seeping into the ground at the base of the hill. Another
possible mechanism may be groundwater seepage from the pond
area to the sandstone which occurs 4 5 feet below ground surface.
If the brine water entered the sandstone and then moved
downgradient toward the creek, it may have discharged at the
lowland. However, the general shape of the plumes, as determined
from the map of chloride concentration and the VES survey,
indicate that overland and transport of sediments flow along the
drainage way is the primary transport mechanism. Also, the
likelihood of migration through the sandstone and toward the
lowland is low because the concentrations of brine indicators are
lower in the deepest well in the area of the holding pond (88
mg/L chloride at well Pla, depth 42.5-45 feet) than in the
lowland plume (about 400 mg/L chloride) . If transport through
the sandstone were the cause of the lowland plume, the chloride
concentration at piezometer Pla would be expected to be higher
than that measured. Furthermore, the vertical hydraulic gradient
measured at station P9 , which is within the lowland plume, is
strongly downward (table 9-3) , indicating that groundwater
discharge does not occur in this area.
= Vertical Electrical Sounding Survey
Figure 9-19a shows the distribution of the "true"
resistivity values at a depth of 3 meters at this site. The
areas enclosed by the 10 ohm-meter contours, one in the immediate
215
Figure 9-17.
Chloride concentrations in groundwater at site
B. Concentrations at nested piezometer stations
are from shallow wells only. Samples taken in
November, 1986.
Cj) Unvegelated area
■ Elevation datum
Q NHS test plot
Intermittent drainage way
• SWS surface water station
• 408 Data point, chlonde concentration (mg/L)
Inferred limit ot chloride plume
100 ft
Contour interval is variable
(dasl^ed where inferred)
216
Figure 9-18
Total dissolved solids concentrations in
groundwater at site B. Concentrations at nested
piezometer stations are from shallow wells only.
Samples taken in November, 1986.
E3 Unvegeiated area
■ Elevation datum
Q NHS test plot
Intermitlent drainage way
■ SWS surface water station
• 841 Data point, TDS concentration (mg/L)
Inferred limit of TDS plume
100 n
Contour interval = 10,000 mg/L
(dashed where inferred)
550
<3861
1027
w
••18 887. jN^
^Approximate tx)undary
of holding pond <
lOOO-----..^
•285 ''^
'^ 2505y
/
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//'
//■
1 029" :"
'949
--■•"7 '942
Tank battery
1570-
217
vicinity of the brine pond and a smaller one in the eastern
(lowland) portion of the site, represent areas at a 3-meter
depth that are likely to be contaminated by brine. Table 9-4
shows chloride and total dissolved solids values for wells within
the VES survey grid for various ranges of resistivity values.
Those wells within the 10 ohm-meter range are clearly within the
confines of the brine plume. However, some of the wells in areas
with electrical resistivity values greater than 10 ohm-meters
have elevated chloride concentrations while others do not.
Therefore, only those areas with resistivity values of 10
ohm-meters or less can be mapped, with confidence, as a part of
the brine plume.
Figure 9-19b shows the distribution of the "true"
resistivity values at a depth of 6 meters. Areas of possible
brine contamination at the 6 meter depth are indicated by three
small, discrete areas in the immediate vicinity of the filled-in
brine pond which have "true" resistivity values less than or
equal to 10 ohm-meters. The reasons for these low "true"
resistivity areas at the 6 meter depth are similar to those given
in the discussion of the pond at site A.
= Site B Summary
The migration of brine at this site has been strongly
influenced by two factors, surface water runoff and groundwater
mounding. The extension of the plume west and upgradient of the
filled-in holding pond (figures 9-17 and 9-19a) is evidence of
groundwater mounding. The presence of a second plume of lower
ion concentration in the lowland area east of the holding pond
may be a result of brine transport by overland flow. This
transport may have been drainage from the pond while it was still
in use, or the result of erosion and transport of sediments with
high salt content from the area of the filled-in pond.
The VES method was successfully used to locate areas of high
brine concentration in the groundwater. However, definition of
the fringe areas of the plume was poor because of uncertainties
in interpreting the resistivity data in areas where the brine
concentration was relatively low.
The VES method was useful for delineating the plume
boundaries in the areas south and west of the site where there
were few piezometers. In other areas, the plume traced with the
VES method generally coincided with that mapped based on chloride
concentrations .
SUMMARY & CONCLUSIONS
The first objective of this task was to evaluate brine
migration in the subsurface. The typical conceptualization of
contaminant migration is that of a plume- with a single lobe
218
Table 9-4.
Chloride concentration and total dissolved solids
compared to resistivity, site B. Underlined values
indicate data for observation wells.
Resistivity
(ohm-meters)
Chloride
Concentration (mg/L)
Average
0-10
11-20
21-30
7545, 11680, 15420, 17150
12, 43, 402, 827, 2440
22, 513
12,949
745
268
Resistivity
(ohm-meters)
TDS (mg/L)
Average
0-10
11-20
21-30
13755, 18887, 23837. 26885
732, 637, 854, 1935, 3861
841, 1029
20,841
1,604
935
219
Figure 9-19. "True" resistivity contours at site B.
depths are 3 and 6 meters.
Approximate
300 tt
• Resistivity station
Approximate boundary ot brine holding pond
C22) 'T"''ue" resistivity value « 10 ohm -m
Contour interval = 10. 0 ohm -m
220
migrating steadily in a direction downgradient from the source.
However, groundwater mounding below brine holding ponds may
change local groundwater gradients so that brine migration can
occur radially. Once the pond is abandoned and filled in, the
mounding effect will eventually diminish and unidirectional
groundwater flow will probably resume. The pathway of brine
migration will also be influenced by the hydraulic conductivity
of the earth materials.
Another important factor affecting the movement of a brine
plume in groundwater is density. Brine waters are more dense
than fresh water (Hoskins, 1947; Jeffords, 1948), therefore they
will tend to migrate downward in the aquifer until they have
thoroughly mixed with aquifer waters or a less permeable stratum
is reached (Van Diersel, 1985). This effect was not apparent at
the sites studied for this project because of the generally low
hydraulic conductivity of the earth materials below a depth of 3
to 6 meters. However, in an area of highly permeable, coarse
grained deposits, density differences may have significant
effects on the flow of brine in the subsurface.
Brine contaminated water and sediments may also be
transported by surface runoff from a holding pond to an area of
lower elevation where the sediments will settle and the water
will pond and infiltrate. Depending upon the concentration of
brine and volume of runoff, significant degradation of the
quality of groundwater may occur some distance from the holding
pond. This degradation may occur at greater distances than if
groundwater were the only mechanism of groundwater transport.
The second objective of this task was to test the accuracy
and effectiveness of the vertical electrical sounding (VES)
method for tracing brine plumes. This method was used to map the
general shapes of brine plumes at two sites. The advantages of
VES are:
1) Delineation of the extent of the brine plumes was more
detailed than that possible by interpretation of groundwater
chemistry data along. Lobes of the plume which would not have
been detected by the groundwater monitoring were identified with
the VES results.
2) The method is quicker and less expensive (table 9-5) than
groundwater monitoring. A complete VES survey can be implemented
at a site in less than one week. Installation of piezometers may
take two or more weeks plus time for well development and
sampling. Processing of the VES data can be done on a desktop
computer. Chemical analyses of water samples may require
expensive laboratory procedures.
221
Table 9-5. Estimated costs for brine plume investigation, Clay
County case study sites A and B.
Time
Cost
6 days
$2,500
5 days
10,000
Vertical electrical sounding
Groundwater monitoring study
(field only, does not include sampling and chemical analyses)
3) Vertical electrical sounding stations can be placed where
piezometers can not, such as the middle of a farm field or
woodland. Also, because of the lower costs, more VES stations
than piezometers may be used at a site, thus providing greater
areal coverage.
However, there are several limitations to this method:
1) Resistivity values may be affected by factors other than
the conductivity of the groundwater. Some of these factors are
lithologic changes, soil moisture differences, and/or cultural
features such- as overhead power lines, wire fences, and buried
conductors.
2) Vertical electrical sounding results may be difficult to
interpret, especially if no groundwater quality data are
available. At both case study sites, the determination of
significant low resistivity values was dependant on groundwater
quality data. Also, lithology will have an affect on resistivity
values. A coarse-grained material saturated with fresh water
will have a higher resistivity than a f ine-grained. material
saturated with fresh water. However, when both materials are
saturated with brine, the coarse-grained material will have lower
resistivity. Therefore, data on lithology and the ion
concentrations of local groundwater are needed for dependable
interpretation of observed resistivity values.
3) Vertical electrical sounding data can not be used to
interpret parameters affecting plume migration, particularly
groundwater gradients and hydraulic conductivity. While the rate
and direction of migration may be estimated from the size and
configuration of the plume, complexities in plume configurations,
such as at site A, may cause estimates of this type to be in
serious error.
4) Electrical resistivity is a measure of the conductance of
the soil and water. Thus, it is comparable to a measurement of
the concentration of total dissolved solids in groundwater and
yields no data on individual chemical species.
222
The optimal method of evaluating the extent and source of
possible brine contamination of groundwater should include both a
VES survey and groundwater monitoring. The VES survey should be
conducted first. The distance between stations should by small,
preferably 100 feet or less. If, after processing the data,
areas of anomalously low resistivity are found to extend past the
boundaries of the VES grid, additional surveying should be
conducted in those areas. After the VES data are complete, a
limited number of piezometer nests should be installed. These
wells should be finished in areas of very low resistivity as
well as areas of high resistivity, so that ion concentrations
may be obtained for both brine contaminated and ambient
groundwater. Also, an attempt should be made to locate the
piezometer nests at VES stations so that resistivity values can
be directly compared to ion concentrations. Observation wells
should be installed prior to installation of piezometer nests to
allow determination of the direction of groundwater flow.
REFERENCES
Hallberg, G. R. , J. R. Lucas and C. M. Goodmen, 1978, Part I.
Semi-quantitive analysis of clay mineralogy: in Standard
Procedures for Evaluation of quaternary Materials in Iowa:
Iowa Geological Survey Technical Information Series 8, p.
5-21.
Hoskins, H.A. , 1947, Analysis of West Virginia brines: West
Virgin Geological Survey Report of Investigations 1, 22 p.
Hvorslev, M. J., 1951, Time log and soil permeability in
groundwater observations: U.S. Army Corps of Engineers
Bulletin 36, 50 p.
Illinois Division of Oil and Gas, 1985, Mid-Year review FY '85
SDWA Section 1425 Class II Underground Injection Control
Program: 11 p.
Jeffords, R.M. , 1948, Graphic Representation of oil field brines
in Kansas: State Geological Survey of Kansas Bulletin 76,
Part 1, :.2 p.
Killey, 1982, The Dwight mineralogic zone of the Yorkville Till
Member, northeastern Illinois: Illinois State Geological
Survey Circular 526, 25 p.
Klein, J., 1986, Personal communication. Clay County Soil and
Water Conservation District.
Meents, W.F., A.H. Bell, O.W. Rees, and W.G. Tilbury, 1952,
Illinois oil field brines, their geologic occurrence and
223
chemical composition: Illinois State Geological Survey
Illinois Petroleum Report No. 66, 38 p.
Reed, P.C., K. Cartwright, and D. Osby, 1981, Electrical earth
resistivity surveys near brine holding ponds in Illinois:
Illinois State Geological Survey Environmental Geology Notes
95, 30 p.
Roberts, W. J. , and J.B. Stall, 1967, Lake evaporation in
Illinois: Illinois State Water Survey Report of
Investigations 57, 44 p.
Van Diersel, T.P.V., 1985, Hydrogeology and chemistry of an
oil-field brine plume within a shallow aquifer system in
southern Bond County, Illinois: Unpublished M.S. Thesis,
Southern Illinois University, 162 p.
Zohdy, A.A.R. , 1973, A computer program for the automatic
interpretation of Schlumberger sounding curves over
horizontally stratified media: U.S. NTIS PB-232 703.
224
PART THREE
APPENDICES
225
Section 10 APPENDICES
226
Appendix 2-A. Depth to base of fresh water estimated from
southeastern Clay County electric logs.
227
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238
Appendix 3-B. Results of water quality reconnaissance in
southeastern Clay County.
239
Appendix 3-B. List of domestic wells sampled during reconnaissance of the
study area.
Owner/Controller Well Depth Location
(ft) Township-Range-Section
(Given in quarters)
Field Conductivity
( micros iemen)
JAKE KLEIN (OFB-1)
16
T.3N, R.7E, Sec. 32
NW NW SE NW
1225
JAKE KLEIN
150
T.3N, R.7E, Sec. 32
NW NW SE NW
1100
CANDY PAYNE
T.3N, R.7E, Sec. 33
NW NW SW NW
900
jt home
T.2N, R.7E, Sec. 05
NW SE NW NW
2775
ARTHUR SNELL
DUG
T.3N, R.7E, Sec. 34
SW NW NW SW
625
CHARLES HEMFHILL • DRILLED
T.2N, R.7E, Sec. 03
NW NW NW NW
1000
STEVE MILLER
195
T.3N, R.7E, Sec. 34
SW NW SW SE
900
^TAN HOARD
128
T.3N, R.7E, Sec. 34
SW NW NW NW
950
VIVIAN HOARD
20
T.3N, R.7E, Sec. 34
SW NW NW NW
1300
PENNY PYIE
18
T.3N, R.7E, Sec. 26
SE SW SE SW
1050
FRED GIFFORD (OFB-18) 140
T.3N, R.7E, SEC. 26
SW NW SW SE
2450
BERNICE MISENHEIMER 20
T.3N, R.7E, Sec. 23
SW SW SE SE
1600
ELANOR HALE
T.3N, R.7E, Sec. 26
SE NW SE SE
1900
GLENDA WILEY
75
T.3N, R.7E, Sec. 35
SE NW SE NW
1050
MAXINE STAFFORD
20
T.3N, R.7E, Sec. 36
SW NW SW SW
1350
240
^pendix 3-B (continued)
Owner/ Controller
Well Depth Location
( ft) Township-Range-Section
(Given in quarters)
Field Conductivity
(microsiemen)
EARL EAYLDR
100
T.2N, R. 7E, Sec. 02
NW NW SW SE
700
HARLEY MIX
135
T.2N, R.7E, Sec. 10
NW SE NW NW
800
RON GIBBS
125
T.2N, R.7E, Sec. 10
NW NW SW NW
1050
NANCY PIERCE
DEEP
T.2N, R.7E, Sec. 10
NW SE NW NW
800
RICH RUDY
100
T.3N, R.7E, Sec. 33
NW NW SE NW
500
ROBERT SNELL
93
T.3N, R.7E, Sec. 33
NW NW SW NW
600
IDUIS WICKEY
70
T.3N, R.7E, Sec. 33
SE SE NW NW
1400
DOIAN BAYIDR
100
T.2N, R.7E, Sec. 03
NW NW SE SE
1100
IVAN COLCIASURE
14
T.2N, R.7E, Sec. 03
NW NW SW SE
300
MARGE MCALLISTER
85
T.2N, R.7E, Sec. 04
NW SE NW SE
700
EDWIN PEARCE
144
T.2N, R.7E, Sec. 08
SE SE SE NW
750
LOWELL AYRES
T.2N, R.7E, Sec. 08
SE NW SE NW
800
BECKY KOHN
T.2N, R.7E, Sec. 05
SE NW SE SE
950
NOT HOME
T.2N, R.7E, Sec. 04
NW SW NW SW
1400
JERRY STANFORD
DUG
T.2N, R.7E, Sec. 05
NW NW NW SE
1150
241
Owner/Control ler
Appendix 3-B (continued)
Well Depth Location
(ft) Township-Range-Section
;. (Given in cfuarters)
Field Conductivity
(microsiemen)
HAROLD STANFORD
150
T.2N, R.7E, Sec. 05
SE SE SE NW
900
JAMES DAVIS
T.2N, R.7E, Sec. 04
NW SW SW NW
950
WIT ,T JAM KLINE (OFB-2) 160
T.2N, R.7E, SEC. 05
NW NW NW NW
1000
BIUL msK
100
T.2N, R.7E, Sec. 06
NW SE NW NW
700
FRANK BURT
160
T.3N, R.7E, Sec. 31
NW SW SW SW
600
DON lUSK
90
T.2N, R.7E, Sec. 06
NW NW SW NW
650
MARK KRESCH
100
T.2N, R.7E, Sec. 06
NW NW NW NW
600
NOT HOME
80-120? T.2N, R.7E, Sec. 06
NW SW SW NW
800
SUSAN STRANGE
102
T.2N, R.7E, Sec. 05
NW NW NW SW
850
BILL PEARCE
100
T.2N, R.7E, Sec. 06
NW SE SE SW
700
DON WILLIAMS
110
T.2N, R.7E, Sec. 07
NW NW NW NW
650
SHARON GREENWOOD
DEEP
T.2N, R.7E, Sec. 08
SW SW SW NW
800
DON UJSK
SHALLOW T.2N, R.7E, Sec. 07
SE SW SW NW
1000
DON UJSK
DEEP
T.2N, R.7E, Sec. 07
SE SW SW NW
700
LARRY HENDERSON
DEEP
T.2N, R.6E, Sec. 12
NW NW NW NW
800
242
Owner/Control ler
i^pendix 3-B (continued)
Well Depth Location
(ft) Township-Range-Section
(Given in quarters)
Field Conductivity
( micros iemen)
THE CURIUSS'S
T.2N, R.6E, Sec. 11
NW NW NW NW
2600
FIDSSY RITTER
T.2N, R.6E, Sec. 11
NW SE NW NW
850
BARNEY STEELE
DRILLED T.2N, R.6E, SEC. 02
NW SE SE SE
900
ILENE PARISH
75
T.2N, R.6E, Sec. 02
SE NW NW SE
900
BERNICE DENTON
35
T.2N, R.6E, Sec. 01
NW SW SW NW
600
BOB GRAHAM
120
T.2N, R.6E, Sec. 01
NW NW SW NW
800
DONALD MOORE
T.3N, R.6E, Sec. 36
NW NW SW SW
600
ALAN MCKNELLY
SHALLDW T.3N, R.6 E, SEC. 35
SE NW SE NW
300
CARL ECKART
40
T.3N, R.7E, Sec. 29
SE NW SW NW
1350
RON MCGEE
100
T.3N, R.7E, Sec. 29
NW NW SE NW
500
SHIRLYE MARKHAM
90
T.3N, R.7E, Sec. 29
NW NW SE NW
800
DON DEIANEY
90
T.3N, R.7E, Sec. 29
SW SE SE NW
650
RAY SHARP
T.3N, R.7E, Sec. 28
NW SW NW SW
650
THE KITLEYS
T.3N, R.7E, Sec. 28
SE NW SW SW
1000
MORRIS DUNAHEE
(OFB-15)
234
T.3N, R.7E, Sec. 16
SE SW SW NW
2300
243
Owner/ Controller
Appendix 3-B (continued)
Well Depth Location
(ft) Township-Range-Section
(Given in quarters)
Field Conductivity
(micros iemen)
RANDY HARDEE
265
T.3N, R.7E, SEC. 16
SE SW SE NW
1700
WALTER HARRY
180
T.3N, R.7E, Sec. 16
NW SE NW SE
1100
THE DUNIGANS
195
T.3N, R.7E, Sec. 15
NW NW NW SW
1700
KATHY CROY
180
T.3N, R.7E, Sec. 15
SW SE SE NW
1000
JIM OOSTNER
T.3N, R.7E, Sec. 22
SW NW NW NW
2000
TAMMY MONICAL
110-120 T.3N, R.7E, Sec. 22
SW NW NW NW
1500
CARL CASH (OFB-17)
310
T.3N, R.7E, SEC. 23
SW NW NW NW
3500
NOT HCME
T.3N, R.7E, Sec. 14
SW NW SE SW
1200
THE KELLYS
T.3N, R.7E, Sec. 23
NW NW SE NW
850
PALFH PAYNE
15
T.3N, R.7E, Sec. 23
SW SW NW SE
200
GENEVA HOHLBAUCH
22
T.3N, R.7E, Sec. 14
NW NW SE NW
1400
DAVIE CAILTEUX
22
T.3N, R.7E, Sec. 11
NW SW SW SE
1550
RON COLEMAN
POND T.3N, R.7E, Sec. 11
SW SW SE SW
200
GEORGE HARRISON
(OFB-16)
253
T.3N, R.7E, SEC. 10
SE SW SE SE
3300
GEORGE HARRISON
23
T.3N, R.7E, Sec. 10
SE SW SE SE
300
244
Appendix 3-B (continued)
Owner/Control ler
Well Depth Docation
( ft) Township-Range-Section
(Given in c(uarters)
Field Conductivity
(microsiemen)
B. SEHIE
22
T.3N, R.7E, Sec. 16
NW NW NW NW
2800
GLEN BURK
35
T.3N, R.6E, Sec. 24
SE NW SE SE
1300
WILMA MERRITT
T.3N, R.6E, Sec. 19
NW NW SW SW
650
JOHN COX (OFB-14)
235
T.3N, R.7E, Sec. 16
SE SW NW NW
1750
SAM THay[PSON
14
T.3N, R.7E, Sec. 09
SE SE NW SW
750
RALEY GALEN
POND
T.3N, R.7E, Sec. 09
NW SW NW SE
100
NORMAN SMITH
60-70
T.3N, R.7E, Sec. 05
NW NW SE SW
2300
NOT HOME
T.3N, R.7E, Sec. 06
SE SE NW SE
1150
DEBRA HOGAN
CISTERN
T.3N, R.7E, Sec. 06
NW SE NW SE
800
BILL HENSON
T.3N, R.7E, Sec. 06
NW NW NW SW
1400
BILL HARNED
15
T.3N, R.7E, Sec. 06
SW SW SE NW
650
NYAL DICKEY
25
T.3N, R.6E, Sec. 01
SE SW SW NW
800
BURLIN BATEMAN
(OFB-13)
23
T.3N, R.6E, Sec. 01
SW SW SW NW
1150
FRANK ZIMMERMAN
T.4N, R.6 E, Sec. 36
SE SW NW SW
500
LEE MATANICH
T.3N, R.6E, Sec. 11
SE NW NW NW
1500
Owner/Controller
245
Appendix 3-B (continued)
Well Oepth Location
(ft) Township-Range-Section
(Given in quarters)
Field Conductivity
(inicrosiemen)
ROIIA GREENWOOD
(OFB-12)
KAREN BEARD
CHARLES STOCKON
HERB BROWN
AUCAN PRATER
GENEVA FISK
WEDDON MCVAY
(OFB-11)
DON CASEY
JOE BEHNKE
LEIAND GUINN
LEIAND GUINN
BOB BRISCOE
KENT WARREN
BOB GIIZSOTROiyi
RON KECK
31
35
35
26
92
20
93
115
15
100
80
30
100
T.3N, R.6E, Sec. 12
SW SW SW SW
T.3N, R.6E, Sec. 13
NW NW NW NW
T.3N, R.6E, SEC. 12
SE SW SW SE
T.3N, R.7E, Sec. 18
NW NW NW NW
T.3N, R.6E, Sec. 24
NW SW SW NW
T.3N, R.6E, Sec. 13
SE SE NW SW
T.3N, R.6E, SEC. 13
SW SE SW NW
T.3N, R.6E, Sec. 12
SW SE SE SW
T.3N, R.6E, Sec. 14
SE NW SE NW
T.3N, R.7E, Sec. 17
SW SE NW SE
T.3N, R.7E, Sec. 17
SW SE NW SE
T.3N, R.7E, Sec. 17
NW SE NW SE
T.3N, R.7E, Sec. 16
NW SE SE SW
T.3N, R.7E, Sec. 08
NW SW SE SE
T.3N, R.7E, Sec. 17
NW NW NW NW
750
1100
500
2200
1000
700
800
550
800
600
200
600
650
2300
1300
246
Owner/Control ler
Appendix 3-B (continued)
Well Depth Location
( ft) Township-Range-Section
(Given in quarters)
Field Conductivity
(microsiemen)
NOT HOME
T.3N, R.7E, Sec. 18
NW NW NW NW
1200
JOHN LEWIS
20-25
T.3N, R.7E, SEC. 07
SE NW NW SE
1500
STEVE RUDY
T.3N, R.6E, Sec. 12
SE NW SE SE
700
JOHN RASTOVSKI
30
T.3N, R.7E, Sec. 27
NW SE NW NW
850
JAN BURT
T.3N, R.7E, Sec. 28
SE SE NW WN
450
JAN BURT
T.3N, R.7E, Sec. 28
SW SE NW NW
600
EDAG BRYAN
127
T.2N, R.6E, Sec. 13
NW SW NW SW
700
REX VAN MEDER
120
T.2N, R.6E, Sec. 14
SE SE NW SE
700
EARL SIDVER
136
T.2N, R.6E, Sec. 13
SE SW SE NW
1800
JOHN IIJSK (OFB-3)
100
T.2N, R.7E, Sec. 07
NW NW SW SW
700
FRED GLASFORD
95-100
T.2N, R.7E, Sec. 07
NW NW NW SW
1600
LAURENCE AUVIL
95-100
T.2N, R.6E, Sec. 12
SE SE NW SE
800
BOB HALE
110
T.2N, R.6E, Sec. 24
SE NW NW NW
950
BOB HALE
20
T.2N, R.6E, Sec. 24
SE NW NW NW
400
r^YRON WOOMER
90
T.2N, R.7E, Sec. 18
SE SW SE NW
1900
247
Owner/Control ler
T^pendix 3-B (continued)
Well Depth Ijocation
( ft) Township-Range-Section
(Given in quarters)
Field Conductivity
(microsiemen)
JOSEPHINE WIIUAMS
112
T.2N, R.7E, Sec. 18
NW NW SE NW
700
CHARLES PEARCE
129
T.2N, R.7E, Sec. 07
SW SW SE SE
600
lAUREEN WILLIAMS
100
T.2N, R.7E, Sec. 17
SW SW NW NW
650
CARL MOGREW
119
T.2N, R.7E, Sec. 17
SE SE NW NW
700
WATER ANDERSON
120
T.2N, R.7E, Sec. 17
NW SE NW NW
600
SAM HOWELL (OFB-5)
82
T.2N, R.7E, Sec. 09
NW NW SW SW
750
SAM HOWELL (OFB-6)
100
T.2N, R.7E, Sec. 09
NW NW SW SW
900
MARK DAWKmS
100
T.2N, R.7E, Sec. 08
NW SE SE NW
700
HENRY SKELTON
110
T.2N, R.7E, SEC. 17
SE NW SE SE
1000
:LrFF HURD
103
T.2N, R.7E, Sec. 21
NW NW NW NW
800
RON JURD
97
T.2N, R.7E, Sec. 16
SE SE SE SE
1100
HUGH BUFFINGTON
117
T.2N, R.7E, Sec. 22
NW NW NW NW
2400
JIM BQFFINGTON
35
T.2N, R.7E, Sec. 22
NW NW NW NW
900
GEORGE HENDERSON
137
T.2N, R.7E, SEC. 23
NW NW NW NW
3800
FRED SHELTON
35
T.2N, R.7E, SEC. 23
SW NW NW NW
1000
248
Appendix 3-B (continued)
Owner/Control ler
Well Depth Location
(ft) Township-Range-Section
(Given in quarters)
Field Conductivity
( micros iemen)
Min^RED SHELIDN
130
T.2N, R.7E, Sec. 14
SE NW SE SE
850
GILBERT HALE
120
T.2N, R.7E, Sec. 14
NW NW SE NW
850
EVERT LEWIS
100
T.2N, R. 7E, Sec. 10
SW SE SW SW
800
DAVID LEWIS
100
T.2N, R.7E, SEC. 09
SW SE SW SE
900
ROY YOUNG
140
T.2N, R.7E, Sec. 09
NW NW NW SE
800
ROY KLTLEY (OFB-4)
32
T.2N, R.7E, Sec. 09
SW NW NW SW
900
DAVID DUKE
40
T.3N, R.6E, Sec. 02
NW SW NW SW
850
ANDREY KAMPSCHRADER 82
T.3N, R.6E, Sec. 02
SW NW NW SW
3500
ALICE MCKNEELY
14-18
T.3N, R.6E, Sec. 02
SW SW SW NW
450
KEITH WILLISON
80
T.3N, R.6E, Sec. 02
NW NW NW SW
1500
DONALD KEMMER
34
T.4N, R.6E, Sec. 34
SE NW NW SE
1000
GENE REDDISH
T.3N, R.6E, Sec. 03
SE NW NW SE
900
ROBERT BUTE
110
T.3N, R.6E, Sec. 03
SW NW SE SE
1800
ROBERI BUTE
60
T.3N, R.6E, Sec. 03
SW NW SE SE
1600
EARL PHILLIPS
115
T.3N, R.6E, Sec. 11
SW SW SW SW
1500
249
/^pendix 3-B (continued)
Owner/Controller
Well Depth Location
( ft) Township-Range-Section
(Given in quarters)
Field Conductivity
(microsiemen)
WENDEUL PHIIlxIPS
18
T.3N, R.6E, Sec. 11
NW SE SW SW
550
E. B. JENNINGS
100
T.3N, R.6E, Sec. 15
SE NW NW SE
700
RAY RUTLAND
T.3N, R.6E, Sec. 15
SE SE SE SE
1300
WTTJ.TAM TOIiJVER 80
80
T.3N, R.6E, SEC. 23
NW NW NW NW
700
DOROTHY ENGELMEIER
120
T.3N, R.6E, Sec. 14
SW SE SW SW
1000
DOROTHY ENGELMEIER
80
T.3N, R.6E, Sec. 14
SW SE SW SW
600
OREN DENNIS
90
T.3N, R.6E, Sec. 23
NW NW NW NW
750
ROBERT GREENWOOD
80
T.3N, R.6E, Sec. 23
NW NW SW NW
850
BOB RUTLAND
190
T.3N, R.6E, Sec. 23
SW SE SW NW
1100
D. L. POWEKL
T.3N, R.6E, Sec. 23
SW SW SW NW
850
LLDYD WATSON
18
T.3N, R.6E, Sec. 26
NW SW NW NW
450
GARNET HALL
24
T.3N, R.6E, SEc. 26
SW SW NW SW
500
NOT HOME
T.3N, R.6E, Sec. 35
NW NW NW NW
1000
DAVE PEl'i'lT
30
T.3N, R.6E, Sec. 35
SW SW SW NW
800
DAVE PETTIT
20
T.3N, R.6E, Sec. 34
NW SE NW SE
1000
250
Appendix 3-B (continued)
Owner/Controller
Well Depth Location
( ft) Township-Range-Section
(Given in quarters)
Field Conductivity
( micros iemen)
RANDY STANFORD
DUG
T.2N, R.6E, Sec. 03
NW NW NW NW
1300
DON LEWIS
90
T.2N, R.6E, Sec. 02
NW SW SW NW
900
MILDRED PERRINE
100
T.2N, R.6E, Sec. 03
SE SE SE SE
950
MIKE PERRINE
103
T.2N, R.6E, Sec. 11
NW NW NW NW
850
CARL BURNS
162
T.3N, R7E, Sec. 27
NW NW NW NW NW
1600
RICH WIGEL
12
T.3N, R.7E, Sec. 26
NW NW NW NW
1800
DON WIGLEY
201
T.3N, R.7E, Sec. 23
NW SW SW SE
4300
M. D. WATSON
14
T.3N, R.7E, Sec. 24
NW SW SW SE
200
JERRY MAYO
SHALLOW
T.3N, R.8E, Sec. 30
NW NW NW NW
100
CAROL WOLF
T.3N, R.8E, Sec. 30
NW SE SW NW
1300
DEBBIE PARRISH
T.3N, R.8E, Sec. 30
NW NW SE SW
900
ED CRAIG
196
T.3N, R.8E, Sec. 30
NW NW SE SE
2500
RICH SNIPPER
T.3N, R.8E, Sec. 31
SW SW SW NW
1800
CLIFFORD PIERCE
190
T.3N, R.7E, Sec. 36
NW NW NW SE
1800
GENE CARPENTER
T.2N, R.7E, Sec. 01
NW NW SW SE
1100
Owner/Controller
251
Appendix 3-B (continued)
Well Depth Location
(ft) Township-Range-Section
(Given in quarters)
Field Conductivity
(microsiemen)
VANCIL ULUDN (OFB-7) 18
VANCIL ULLCM (OFB-8) 100
T.2N, R.7E, Sec. 13
SE NW NW NW
T.2N, R.7E, Sec. 13
SE NW NW NW
500
700
HAROLD GIBBS
22
T.2N, R.8E, Sec. 18
SW NW SW NW
800
DON SMITH
SHAIUDW
T.2N, R.8E, Sec. 06
NW NW SE NW
900
JOHN THOMAS
132
T.2N, R.8E, Sec. 05
SW NW NW NW
1000
HERBERT BURT (OFB-19) 190
(OFB-20) ?
HAROLD GOOD 150
T.3N, R.8E, Sec. 32
SW SE NW SW
T.3N, R.8E, Sec. 29
NW NW SW SW
1700
3700
FPmCES MORRIS
168-180 T.3N, R.8E, SEC. 32
SE NW SW NW
2400
TOM MITCHELL
96
T.2N, R.8E, Sec. 05
SE NW SE SE
600
OWEN HENRY
90
T.2N, R.8E, Sec. 08
SE SE NW NW
700
KENT HENRY
80
T.2N, R.8E, Sec. 09
NW NW NW SW
500
REXFORD GILL
25
T.2N, R.8E, Sec. 17
SE NW NW NW
1000
WAYNE PRUITT
DUG
T.2N, R.8E, Sec. 17
SE SE SE SE
1000
HUGH LYNN
24
T.2N, R.8E, Sec. 15
NW SW NW SW
1100
HIGH LYITN
70
T.2N, R.8E, Sec. 15
NW SW NW SW
1000
252
Owner/Controller
^pendix 3-B (continued)
Well Depth Location
( ft) Township)-Range-Section
(Given in quarters)
Field Conductivity
(micros iemen)
KEN HASSEKTON
35-40
T.2N, R.8E, Sec. 22
NW NW NW NW
1000
JUDY SCHOFIEID
T.2N, R.8E, Sec. 15
SW SE SE SE
750
RAY PIERCE
190
T.2N, R.8E, Sec. 14
NW SW SW SE
1000
BARBARA MTT.T.FR
T.2N, R.8E, Sec. 14
NW NW SE NW
950
DARRELL CURTIS
(OFB-9)
120
T.2N, R.8E, SEC. 14
SE NW NW NW
1200
MAURICE HERMAN
90
T.2N, R.8E, Sec. 11
SE SE SW SE
900
HUBERT EVANS
85
T.2N, R.8E, Sec. 15
SE SE NW SE
900
BEN SHARP
18
T.2N, R.8E, Sec. 15
SW NW NW NW
1100
WIIIZAM PIERCE
100
T.2N, R.8E, Sec. 10
SE NW SE SE
700
JIM BROWN
30
T.2N, R.8E, Sec. 10
NW NW SE NW
1400
DDUIE mSK
80
T.2N, R.8E, Sec. 10
SW NW SW NW
700
JANICE SMITH
6-8
T.2N, R.8E, Sec. 09
NW SE NW SE
450
SHERMAN THOyiAS
115
T.2N, R.8E, Sec. 04
NW NW NW NW
700
MARIE WEIIER
DEEP
T.2N, R.8E, Sec. 04
NW NW NW NW
700
ROY SHARP
142
T.3N, R.8E, Sec. 34
NW NW SW SW
900
253
Owner/Control ler
Appendix 3-B (continued)
Well Depth Location
( ft) Township-Range-Section
(Given in cpaarters)
Field Conductivity
(microsiemen)
ROY SHARP
12
T.3N, R.8E, Sec. 34
SW SW SW SW
800
ATRERT ABBOTT
160
T.2N, R.8E, Sec. 03
NW SW NW NW
1100
KEN WYATT
DEEP T.2N, R.8E, Sec. 03
NW NW SW SW
1650
'mE LYNNS
T.2N, R.8E, Sec. 10
NW NW SW NW
600
rONY STANDLER
T.3N, R.8E, Sec. 34
NW SW SW NW
100
BILL YOUNG
167
T.3N, R.8E, Sec. 27
SW SW SW SW
1500
BILL SMITH (OFB-22)
160
T.3N, R.8E, Sec. 27
SW SE SW SW
1500
JIM THmAS (OFB-21)
23
T.3N, R.8E, Sec. 28
SW SW SW SE
1400
DEAN TRAVIS
132
T.3N, R.8E, Sec. 33
SW NW NW NW
1050
W. W. WEATHERFORD
150
T.3N, R.8E, Sec. 33
NW NW NW NW
1500
CARROLL MURBARGER
75-90
T.3N, R.8E, Sec. 33
NW SW SW NW
750
ART HENDERSON
90
T.3N, R.8E, Sec. 33
NW NW NW SW
900
KERN DOERNER
CITY WIR T.3N, R.8E, Sec. 20
NW SE SW SE
500
BONNIE ULREY
185
T.3N, R.8E, Sec. 29
NW SE NW SE
3100
T.3N, R.8E, Sec. 28
SW NW SW SW
2000
254
Owner/Control ler
Appendix 3-B (continued)
Well Depth Location
(ft) Township-Range-Section
(Given in cpjarters)
Field Conductivity
( micros iemen)
CANDY RAY
T.3N, R.8E, Sec. 28
NW SW SW SW
2000
JOY HUDSON
133
T.3N, R.8E, Sec. 29
NW SE SE SE
1850
NORMA ?
165
T.3N, R18E, Sec. 29
NW SE SE SE
2100
LYNNE THOyLPSON
T.3N, R.8E, Sec. 29
SE SE SE SE
1950
JOE DENTON
135
T.3N, R.8E, Sec. 29
SW SE SW SE
1450
JOE DENTON
185
T.3N, R.8E, SEC. 32
NW NW NW NW
1100
•^OEL WYATT
30
T.3N, R.8E, Sec. 29
SE SW SW SE
400
NOEL WYATT
160
T.3N, R.8E, Sec. 29
SE SW SW SE
300
MARVIN SHARP
30
T.3N, R.8E, Sec. 16
SE NW SE SW
1400
FLDYD WELLS
20
T.3N, R.7E, SEC. 13
SW NW NW NW
1400
DDWELL FERRIS
DEEP
T.4N, R.6E, SEC. 26
NW SW NW SW
1850
MIIDRED GUFFY
30
T.4N, R.6E, SEc. 26
NW NW NW SW
1200
TXM CARPENTER
SHALDDW T.4N, R.6E, Sec. 26
SW SW SW NW
800
ALVIN HARRIS
T.4N, R.6E, Sec. 35
SW NW NW NW
1700
255
Appendix 3-C. Regression analysis - well depth and proximity
to brine holding pond vs conductance.
256
REGRESSION ANALYSIS
ADEH DATA FOR: B: SHALLOW LABEL: Shallow Wells < 50' Clay County Brines
MBBR OF CASES: 46 NUMBER OF VARIABLES: 4
nductivity vs Proximity Shallow Wells Clay County Brine Study
DEX
NAME
MEAN
1
well
111.89
2
depth
23.28
3
proximi t
2085.87
P. VAR.:
conduct
988.59
STD.DEV,
65.30
7.88
1793.84
545.53
IPBNDENT VARIABLE: conduct
VR. REGRESSION COBFFICIBNT
oximit -2.68B-02
)NSTANT 1044.42
STD. ERROR
4.567E-02
T(DF= 44)
-.586
PROB.
.56077
^D. ERROR OF EST. = 549.55
r SQUARED = .01
r = -.09
ANALYSIS OF VARIANCE TABLE
50URCE
SUM OF SQUARES
D.F.
MEAN SQUARE
JGRBSSION
103759.24
1
103759.24
JSIDUAL
13288373.91
44
302008.50
)TAL
13392133.15
45
F RATIO PROB
.344 .5608
257
REGRESSION ANALYSIS
\DBR DATA FOR: B:SHALLOW LABEL: Shallow Wells < 50' Clay County Brines
"fBBR OF CASES: 46 NUMBER OF VARIABLES: 4
Conductivity vs Depth Shallow Wells Clay County Brine Study
)EX NAME
|l well
p depth
i proximit
f . VAR. : conduct
MEAN
111.89
23.28
2085.87
988.59
STD.DEV
65.30
7.88
1793.84
545.53
^EWCKNT VARIABLE: conduct
II. REGRESSION COEFFICIENT
>th 11.98
LJSTANT 709.57
STD. ERROR T(DF= 44) PROB .
10.27 1.167 .24969
'). ERROR OF EST. = 543.36
r SQUARED = . 03
r = .17
ANALYSIS OF VARIANCE TABLE
)URCE
SUM OF SQUARES
D.F.
MEAN SQUARE
iRESSION
401746.62
1
401746.62
'-"AL
12990386.53
44
295236.06
^u
13392133.15
45
F RATIO PROB
1.361 .2497
258
REGRESSION ANALYSIS
VDBR DATA FOR: B: SHALLOW LABEL: Shallow Wells < 50' Clay County Brines
1BER OF CASES: 46 NUMBER OF VARIABLES: 4
xonductivty vs Depth and Proximity Shallow Wells Clay County
)EX
L
VAR
NAME
well
depth
proximit
conduct
MEAN
111.89
23.28
2085.87
988.59
STD.DEV.
65.30
7.88
1793.84
545.53
^ENDENT VARIABLE: conduct
1. REGRESSION COEFFICIENT
12.56
xjiit -3.13E-02
iSTANT 761.29
STD
ERROR
10.37
4.558B-02
T(DF= 43)
1.211
-.686
PROB.
.23232
.49642
PARTIAL r'"2
.0330
.0108
3. ERROR OF EST. =
JUSTED R SQUARED
R SQUARED
MULTIPLE R
DURCE
jRESSION
^TDUAL
SUM
= 546.66
= -.00
= .04 *
= .20
ANALYSIS OF
VARIANCE
TABLE
OF SQUARES
D.F.
MEAN SQUARE
F RATIO
PROB.
542359.34
2
271179.67
.907
.4111
12849773.81
43
298831.95
13392133.15
45
259
REGRESSION ANALYSIS
ADER DATA FOR: B:DEEP LABEL: CLAY COUNTY BRINES STUDY DEEP WELLS
MBER OF CASES: 103 NUMBER OF VARIABLES: 4
CONDUCTVITY VS PROXIMITY CLAY COUNTY DEEP > 50' WELLS
DEX
NAME
MEAN
STD.DBV
1
WELL
109.90
67.49
2
DEPTH
125.82
41.69
3
PROXIMIT
2098.54
1954.50
P. VAR.:
CONDUCT
1445.63
3215.75
PENDENT VARIABLE: CONDUCT
R. REGRESSION COEFFICIENT
"ViMIT -.14
NT 1738.30
STD. ERROR
.16
T(DF= 101)
-.855
PROB.
39461
D. iiRROR OF EST. = 3220.00
r SQUARED = .01
r = -.08
ANALYSIS OF
VARIANCE
TABLE
OURCE
GRESSION
SIDUAL
TAL
SUM OF SQUARES
7578409.92
1047207124.06
1054785533.98
D.F.
1
101
102
MEAN SQUARE
7578409.92
10368387.37
F RATIO
.731
PROB
.3946
260
REGRESSION ANALYSIS
[KADER DATA FOR: B:DBBP LABEL: CLAY COUNTY BRINES STUDY DEEP WELLS
fUMBER OF CASES: 103 NUMBER OF VARIABLES: 4
CONUCTVITY VS DEPTH CLAY COUNTY DEEP > 50' WELLS
NDEX
NAME
MEAN
STD.DEV
1
WELL
109.90
67.49
2
DEPTH
125.82
41.69
3
PROXIMIT
2098.54
1954.50
)EP.
VAR. :
CONDUCT
1445.63
3215.75
)EPENDENT VARIABLE: CONDUCT
'AR. REGRESSION COEFFICIENT
)EPTH 30.00
:ONSTANT -2329.33
STD. ERROR
7.07
T(DF= 101)
4.243
PROB.
.00005
;TD. ERROR OF EST. = 2977.16
r SQUARED = .15
r = .39
ANALYSIS OF VARIANCE TABLE
SOURCE
DEGRESSION
IBSIDUAL
^OTAL
SUM OF SQUARES D.F.
159572076.57 1
895213457.41 101
1054785533.98 102
MEAN SQUARE
159572076.57
8863499.58
F RATIO PROB.
18.003 4.900E-05
261
REGRESSION ANALYSIS
ADER DATA FOR: B:DEEP LABEL: CLAY COUNTY BRINES STUDY DEEP WELLS
MBER OF CASES: 103 NUMBER OF VARIABLES: 4
NDUCTIVTY VS DEPTH AND PROXIMITY CLAY COUNTY DEEP > 50' WELLS
DEX
NAME
MEAN
STD.DBV
1
WELL
109.90
67.49
2
DEPTH
125.82
41.69
3
PROXIMIT
2098.54
1954.50
P. VAR.:
CONDUCT
1445.63
3215.75
PENDENT VARIABLE: CONDUCT
R. REGRESSION COEFFICIENT
PTH 29.68
lOXIMIT -4.77E-02
INSTANT -2188.48
STD.
ERROR
7.18
.15
T(DF= 100)
4. 134
-.311
PROB. PARTIAL r"2
.00007 .1460
.75613 9.68884B-04
D. ERROR OF EST. = 2990.56
JUSTED R SQUARED = .14
R SQUARED = .15
MULTIPLE R = .39
ANALYSIS OF VARIANCE TABLE
OURCE
SUM OF SQUARES
D.F.
MEAN SQUARE
GRESSION
160439434.13
2
80219717.07
SIDUAL
894346099.85
100
8943461.00
TAL
1054785533.98
102
F RATIO PROB.
8.970 2.613E-04
262
REGRESSION ANALYSIS
,DER DATA FOR: BrBRINES LABEL: CLAY COUNTY BRINE STUDY
!BER OF CASES: 149 NUMBER OF VARIABLES: 4
Conductivity vs Proximity Clay County Brine Study
EX
NAME
WELL
DEPTH
PROXIMIT
MEAN
111.86
94.16
2094.63
STD.DEV.
66.40
58.95
1900.31
. VAR.i
: CONDUCT
1304.53
2694.87
INDENT
VARIABLE:
CONDUCT
REGRESSION COEFFICIENT STD.
ERROR
T(DF= 147)
PROB.
XIMIT
-.11
.12
-.931
.35334
). ERROR OF EST. = 2696.08
r SQUARED = .01
r = -.08
ANALYSIS OF VARIANCE TABLE
OURCE
SUM OF SQUARES
D.F.
MEAN SQUARE
F RATIO
PROB
3RESSI0N
6301337.29
1
6301337.29
.867
.3533
3IDUAL
1068518729.82
147
7268834.90
TAL
1074820067.11
148
263
REGRESSION ANALYSIS
ER DATA FOR: BrBRINES LABEL: CLAY COUNTY BRINE STUDY
ER OF CASES: 149 NUMBER OF VARIABLES: 4
Conductivity vs Depth Clay County Brines Study
: NAME MEAN STD.DEV
WELL 111.86 66.40
DEPTH 94.16 58.95
PROXIMIT 2094.63 1900.31
VAR.: CONDUCT 1304.53 2694.87
NDENT VARIABLE: CONDUCT
REGRESSION COEFFICIENT STD. ERROR T(DF= 147) PROB.
H 13.30 3.61 3.688 .00032
TANT 51.98
ERROR OF EST. = 2587.00
r SQUARED - .08
r = .29
ANALYSIS OF VARIANCE TABLE
RCE
SUM OF SQUARES
D.F.
MEAN SQUARE
ESSION
91014551.50
1
91014551.50
DUAL
983805515.61
147
6692554.53
1074820067.11
148
F RATIO PROB.
13.599 3.177E-04
264
REGRESSION ANALYSIS
,DER DATA FOR: BrBRINES LABEL: CLAY COUNTY BRINE STUDY
1BER OF CASES: 149 NUMBER OF VARIABLES: 4
Conductivity vs Depth and Proximity Clay County Brine Study
)EX
NAME
MEAN
STD.DEV.
[
WELL
111.86
66.40
1
DEPTH
94.16
58.95
5
PROXIMIT
2094.63
1900.31
\ VAR.:
CONDUCT
1304.53
2694.87
^ENDENT VARIABLE: CONDUCT
1. REGRESSION COEFFICIENT STD. ERROR T(DF= 146) PROB. PARTIAL r"2
TH 13.13 3.62 3.625 .00040 .0826
XIMlf -8.13E-02 .11 -.724 .47052 .0036
^ISTANT 238.77
1. ERROR OF EST. = 2591.20
JUSTED R SQUARED = .08
R SQUARED - .09
MULTIPLE R = .30
ANALYSIS OF VARIANCE TABLE
F RATIO PROB.
7.039 1.206E-03
)URCE
SUM OF SQUARES
D.F.
MEAN SQUARE
3RESSI0N
94529359.61
2
47264679.81
3IDUAL
980290707.50
146
6714319.91
TAL
1074820067.11
148
265
Appendix 4 -A. Water quality data for Buck Creek,
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267
Appendix 4-A. Complete Water quality Data for Buck Creek (Continue)
6/
17/86
7/8/86
7/29/86
BCU
BCD
BCU BCD
BCU
BCD
NH3-N
9.56
3.48
0.58
12.4
1.02
Boron
0.09
0.12
0.10
0.03
0.09
Bromide
0.61
0.95
0.99
0.14
0.55
Chloride
108
260
N
245
21
123
Cond. (umho)
700
1321
0
1228
295
638
Dissolved Oxygen
11.6
2.5
1.4
5.7
6.0
Grease and Oil
4.2
6.8
F
7.2
6.0
9.6
Hardness
187
310
L
278
89
151
Iodide
<0.1
<0.1
0
<0.1
<0.1
<0.1
Nitrate & Nitrite
0.30
0.29
W
0.35
0.42
0.48
PH
8.09
7.68
7.89
7.78
7.92
Phosphate-P
0.17
0.21
0.37
0.26
0.34
Sulfate
28
109
32
32
39
Temperature (oC)
22
21
25
29
28
Total Alkalinity
150
176
201
106
118
~otal Diss. Solids
440
858
753
150
336
Total Kjel. Nit.
11.0
5.11
2.30
14.4
2.9
Total Sus. Solids .
20
50
37
46
42
Total Vol. Solids
2
4
2
4
18
Na (Tot.)
124
287
155
38
38
K (Tot.)
4.7
6.3
7.9
6.0
10.1
Ca (Tot.)
50
77
72
26
37
Mg (Tot.)
14
28
25
6.3
13
+ BCU - Buck Creek Upstream; BCD - Buck Creek Downstream
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269
Appendix 4 -A,
Complete Water quality Data for Buck Creek (Continue;
6/17/86 7/8/86 7/29/86
BCU BCD BCU BCD BCU BCD
Ba (
Tot. ]
0.06
0.10
0.13
0.07
0.10
Ba (
Sol. ]
0.03
0.08
N
0.09
0.04
0.09
Cd (
Tot. ]
<0.01
<0.01
0
<0.01
<0.01
<0.01
Cd (
Sol.]
<0.01
<0.01
<0.01
<0.01
<0.01
Cu (
Tot. ]
0.01
0.02
F
0.02
0.01
0.01
Cu (
Sol. ;
<0.01
<0.01
L
0.01
0.01
0.01
Cr (
'Tot. ;
<0.01
<0.01
0
<0.01
<0.01
<0.01
Cr (
'Sol.;
<0.01
<0.01
W
<0.01
<0.01
<0.01
Fe (
'Tot.;
1.1
1.7
1.7
2.0
1.9
Fe (
'Sol. ;
0.03
0.04
0.04
0.12
0.05
Li (
[Tot. ;
<0.01
<0.01
<0.01
<0.01
<0.01
Li
[Sol. ;
<0.01
<0.01
<0.01
<0.01
<0.01
^■!n
[Tot.;
I 1.7
3.6
3.1
0.65
1.7
Mn
;soi.'
) 1.6
3.1
3.0
0.40
1.4
Ni
[Tot.
) <0.05
<0.05
<0.05
<0.05
<0.05
Ni
[Sol.
) <0.05
<0.05
<0.05
<0.05
<0.05
Pb
[Tot.
) <0.05
<0.05
<0.05
<0.05
<0.05
Pb
[Sol.
) <0.05
<0.05
<0.05
<0.05
<0.05
Sr
[Tot.
) • 0.17
0.29
0.28
0.08
0.15
Sr
[Sol.
) 0.17
0.29
0.28
0.08
0.15
Zn
[Tot.
) 0.02
0.03
0.03
0.02
0.02
Zn
[Sol.
) 0.01
0.02
0.01
0.02
0.02
+ BCU - Buck Creek Upstream; BCD - Buck Creek Downstream.
270
Appendix 5-A. Methods used for assessment of oil brines
impacts on aquatic biota.
271
Appendix 5-A. Methods used for assessment of oil brines impacts
on aquatic biota.
Selection and General Description of Stations. Six stations were
chosen to characterize the benthic macroinvertebrate communities
along Buck Creek, Clay County, Illinois, from source to mouth.
Sites were sampled on 22, 24, 31 August and 2, 24 October 1986.
These sites, illustrated in figure 5-1, are located on the Flora,
Illinois 1.5' quadrangle map, 1970 edition, as follows:
Station 1 - Buck Creek, 5.3 km (3.3 mi) N Flora 3rd P M:
T13N, R6E. E/2, NE/4 SE/4. NE/4 , Sec. 11 T M:
Zone 16, ^70^0^^E, 4286250m ^ width 0.5 to 5 m;
depth 0.05 to 0.4 m; substrate primarily sand
with some clay, silt, and gravel; few rocks;
water turbid, with a slight oil film on water;
banks steeply sloping; stream completely shaded
Station 2 - Buck Creek, 4.3 km (2.6 mi) NNE Flora 3rd P M:
T3N, R6E, S/2, SW/4 , SE/4. SE/4 , Sec. 12 U T M:
Zone 16, 37i800m g^ 4285lJ0mf^ width 1 to 5 m;
depth 0.1 to 1 m; substrate primarily sand with
some silt/detritus and clay; water moderately
turbid; solid mat of duckweed on water; little
flow; banks steeply sloping; stream shaded
approximately 50 percent
Station 3 - Buck Creek, 4.1 km (2.5 mi) NE Flora 3rd P M:
T3N, R7E, W/2. SW/4, NE/4, NW/4 , Sec. 18 U T M:
Zone 16, 372130m ^^ 4284790m ^ width 1 to 4 m;
depth 0.2 to 0.8 m; substrate primarily sand,
with gravel, silt, and detritus; water
moderately turbid; logjam present; duckweed
present in small accumulations in quiet areas;
little flow; banks steeply sloping; stream
completely shaded
Station 4 - Buck Creek, 4.5 km (2.8 mi) NE Flora 3rd P M:
T3N, R7E, NW/4, NW/4, SW/4, NW/4, Sec. 17 U T
M: Zone 16, 373300m g^ 4284620m ^ width 1 to 4
m; depth to 0.4 m; substrate primarily sand,
with some silt and gravel; water clear; duckweed
present; little flow; banks steeply sloping;
stream shaded approximately 50 percent
Station 5 - Buck Creek, 5.1 km (3.1 mi) NE Flora 3rd P M:
T3N, R7E, SE/4. SE/4, SW/4, SW/4, Sec. 8 U T M:
Zone 16, 373670m g^ 4285090m ^ width 1 to 5 m;
depth to 0.4 m; shallow riffle area present;
substrate primarily sand and silt; water
272
moderately turbid; duckweed present; banks
steeply sloping; stream unshaded
Station 6 - Buck Creek, 7.0 km (4.4 mi) NE Flora 3rd P M:
T3N, R7E, SW/4, NE/4, SE/4. NW/4 , Sec. 9 U T M:
Zone 16, 375620m E^ 4286030m ^ width 1 to 4 m;
depth <0.25 m; substrate primarily sand and
silt; water moderately turbid; duckweed present;
banks steeply sloping; stream 8 0 percent shaded
Benthic Macroinvertebrates . Benthic macroinvertebrate samples
consisted of semi-quantitative, hand-picked collections from the
six sites, distributed among the microhabitats at each station to
characterize riffle and pool areas, predominantly, and beds of
aquatic vegetation, undercut banks, exposed roots, leaf packets,
where present. Sampling continued until the return of usable
data no longer justified further collecting (about 2 to 2.5
man-hours) . Sufficient buffered formalin was added to algal and
detrital samples to produce a 10 to 15 percent final con-
centration. All other material was preserved in 95 percent
ethanol.
All samples were sorted under stereoscopic microscopes at a
magnification of lOX. Identifications to generic or species
level were performed by taxonomists specializing in each of the
major groups of aquatic organisms. Nomenclature follows Brigham,
Brigham, and Gnilka (1982) . Mollusca and aquatic Diptera were
excluded from further treatment since species-level identi-
fication of aquatic forms is uncertain. Summarized numbers
represent actual numbers of individuals taken. These techniques
were designed to secure a thorough representation of species and
an idea of the relative abundance of each.
Specialists providing identification of various invertebrate
groups included Dr. Allison R. Brigham (Lepidoptera) , Dr. Warren
U. Brigham (Coleoptera, Megaloptera) , Mr. Donald G. Huggins of
the Kansas Biological Survey (Odonata) , Dr. Lawrence M. Page
(Crustacea) , Dr. Milton W. Sanderson, retired, (Heteroptera) ,
Dr. John D. Unzicker (Ephemeroptera, Trichoptera) , and Mr. Mark
J. Wetzel (Annelida) . All are staff of the Illinois Natural
History Survey unless otherwise indicated.
lEPA Station Classifications. The review of historic benthic
macroinvertebrate data from the Wabash River watershed in
Illinois is presented in the stream evaluation system used by the
Illinois Environmental Protection Agency (lEPA) . Their system
includes assignment of identified species to one of four
categories based upon their "tolerance" to pollution. These
categories, summarized below include:
273
intolerant - organisms whose life cycles are dependent upon
a narrow range of ideal environmental conditions.
moderate - organisms without the extreme sensitivities to
environmental stresses of intolerant species, but unable
to adapt to severe environmental degradation.
facultative - organisms able to survive over a wide range of
environmental conditions and possessing a greater degree
of tolerance to adverse conditions than either
intolerant or moderate species. Some of the
macroinvertebrates which utilize surface air for
respiration are classified as facultative.
tolerant - organisms able to survive over a wide range of
environmental extremes, including water of extremely poor
quality.
Station classifications followed the system utilized by
lEPA:
balanced, environment (B) - intolerant species numerically
important in both number and diversity. For a station to
be classified as balanced, intolerant species represent
more than 50 percent of the specimens collected at a site
while moderate, facultative, and tolerant species
comprise less than 50 percent.
unbalanced environment (UB) - intolerant species numerically
less important than other forms combined, but combined
with moderate forms, usually outnumber tol^erant forms.
For a station to be classified as unbalanced, species
classified as moderate, facultative, and tolerant
comprise more than 50 percent of the sample while
intolerant species comprise more than 10 percent but
less than 50 percent of the sample.
semi-polluted environment (SP) - intolerant species few or
absent with moderate, facultative, and tolerant species
predominating. For a station to be classified as
semi-polluted, intolerant species comprise 10 percent or
less of the individuals collected while moderate,
facultative, and tolerant organisms combined comprise 90
percent or more of the sample.
polluted environment (P) - generally only tolerant species
present although some facultative forms may be observed.
For a station to be classified as polluted, either all or
virtually all organisms collected are classified as
tolerant, or no organisms are present.
274
State Water Survey Water quality Data. The State Water Survey
analyzed surface water at 2-week intervals from 3 April through
29 July 1986 at two sites in Buck Creek: station 1, upstream,
and station 6, downstream. For this statistical analysis, one (8
July 1986) of their nine collections was eliminated since the
upstream site had no flow.
Thirty- four chemical variables were analyzed. After
examining the means and variances of these data, variables
exhibiting little or no variance were eliminated from further
treatment. In addition, examination of the mean con-
centration relative to the observed detection limits eliminated
several other variables from consideration. Twenty variables
were retained following this preliminary selection.
Variables eliminated included boron, bromide, iodide,
nitrate + nitrite, pH, phosphorus, and the heavy metals barium
(total, soluble), cadmium (total, soluble), chromium (total,
soluble), copper (total, soluble), iron (soluble), lead (total,
soluble), lithium (total, soluble), nickel (total, soluble),
strontium (total, soluble), and zinc (total, soluble).
A one-way analysis of variance with the chemical variables
as depedent variables eliminated 11 additional variables that
demonstrated no significant differences between the upstream and
downstream sampling sites. Variables eliminated included
ammonia, dissolved oxygen, iron ^total) , manganese (total,
soluble) , oil and grease, organic nitrogen potassium,
temperature, total alkalinity, and total volatile solids.
Other Statistical Analyses. Species diversity was calculated
using the Shannon-Weaver function:
D = 3.3219 [log%lN - (1/N) n%2 . %010 %0i]
where N = total number of individuals and n%l= number of
individuals of the ith species. The Shannon-Weaver index is
commonly used because of its relative insensitivity to sample
size; it is preferred when samples from a community rather than
the complete community are being analyzed.
All data were transformed [In (X + 1)] for statistical
analyses. The SAS linear regression model with one and two
independent variables (chloride concentration and stream order)
was performed with the number of intolerant organisms as the
dependent variable.
The SAS stepwise regression procedure with the stepwise
technique was performed on 20 transformed, standardized (zero
mean, unit standard deviation) water quality variables.
275
The SAS cluster procedure with the unweighted pair-group
method with arithmetic averages was used to find hierarchical
clusters of benthic macroinvertebrates at the six sampling
stations in August and October. Actual numbers of individuals
were used.
276
Appendix 5-B. Benthic Macroinvertebrate, chloride, and stream
order data from Wabash River watershed, 1976 and
1977.
277
Hierarchical Ranking of Stations with Benthic Macroinvertebrate and
Chloride Data in the Wabash River Basin by (1) Chloride Group and
(20) Chloride Concentration
Station
Chloride
Group rtn/L
<
Station (^)
Class
Strpam
Number
Total
Int
Mod
Fac
Tol
Order
1
CAYZ-10
1
4
26
5
0
10
11
UB
2
2
CZR-11
1
4
89
16
1
58
14
UB
3
3
BEZA-11
1
5
91
21
32
28
10
UB
2
4
BJBZ-10
1
5
88
11
2
52
23
UB
2
5
CA-20
1
5
71
2
6
55
8
SP
2
6
CANBB-10
1
5
31
3
0
3
25
SP
2
7
CAWD-10
1
5
138
48
18
53
19
UB
2
8
CJC-10
1.
5
74
1
2
25
46
SP
3
9
COA-11
1
5
53
5
5
20
23
SP
2
10
RFIAZ-IG
1
6
130
13
5
38
74
UB
1
11
CA-19
1
6
33
5
1
21
6
UB
2
12
CANB-11
1
6
143
6
5
105
27
SP
3
13
CARB-10
1
6
115
21
55
15
24
UB
3
14
CAV-11
1
6
128
6
5
43
74
SP
2
15
CAW-14
1
6
36
9
1
16
10
UB
3
16
CAW-15
1
6
12
3
1
2
6
UB
2
17
CAZBZ-10
1
6
42
8
0
22
12
UB
2
18
GJDA-10
1
6
110
29
38
25
18
UB
2
19
OOA-10
1
6
113
1
3
31
78
SP
2
20
CQ-11
1
6
37
0
1
31
5
SP
4
21
CZR-10
1
6
62
6
0
37
19
SP
3
22
BEZZAA-10
1
7
142
32
30
69
11
UB
2
23
CAKZ-12
1
7
20
7
8
4
1
UB
1
24
GJ-16
1
7
24
11
1
7
, 5
UB
3
25
GJC-11
1
7
33
4
0
17
12
UB
2
26
GJE-11
1
7
71
16
0
27
28
UB
3
27
GJEC-10
1
7
63
11
15
22
15
UB
1
28
CM-12
1
7
71
14
4
26
27
UB
3
29
CZQ-10
1
7
61
3
1
34
23
SP
3
30
BBGA-10
1
8
48
25
13
4
6
B
3
31
BEZA-12
1
8
85
25
21
5
34
UB
2
32
RE7,ZA-11
1
8
100
3
5
78
14
SP
3
33
BHZ-10
1
8
107
3
1
44
59
SP
3
34
CAGBZ-13
1
8
168
0
4
160
4
SP
1
35
CAGC-14
1
8
93
4
11
17
61
SP
4
36
CAKZ-10
1
8
127
0
0
106
21
SP
1
37
CAV-10
1
8
71
3
1
19
48
SP
3
38
CA.WZ-10
1
8
78
8
12
17
41
UB
2
39
CDFZ-10
1
8
33
9
11
7
6
UB
1
40
CHB-10
1
8
16
3
2
2
9
UB
3
41
CHH-11
1
3
56
1
7
31
17
SP
3
42
GJ-14
1
8
107
27
25
42
13
UB
4
(^) lEPA station classification defined in Appendix 5.1
278
Station
Chloride
Group inq/L
Station (^)
Class
Stream
Number
Total
Int
Mod
Fac
Tol
Order
43
GJ-15
1
8
44
9
2
15
18
UB
3
44
GJEC-11
1
8
39
1
1
11
26
SP
2
45
OQ-10
1
8
42
1
4
33
4
SP
4
46
OQ-12
1
8
72
17
5
15
35
UB
3
47
CZF-10
1
8
127
31
38
41
17
UB
1
48
RR^A-ll
1
9
91
39
1
12
39
UB
3
49
RRGA-12
1
9
39
13
0
21
5
UB
2
50
BEZA-10
1
9
115
17
15
37
46
UB
3
51
RKZZA-IO
1
9
138
50
37
24
27
UB
3
52
BFA-11
1
9
51
25
1
15
10
UB
1
53
BFB-10
1
9
117
21
40
22
34
UB
4
54
BH-10
1
9
74
41
0
4
29
B
5
55
BH-17
1
9
54
25
3
16
10
UB
2
56
EfOlO
1
9
47
18
0
14
15
UB
3
57
BJBB-11
1
9
68
4
0
8
56
SP
2
58
BK-11
1
9
70
21
10
13
26
UB
3
59
CANB-12
1
9
49
1
8
8
32
SP
3
60
CANB-13 .
1
9
21
9
0
12
0
UB
2
61
CF-10
1
9
117
3
12
80
22
SP
2
62
CHEA-11
1
9
38
2
0
27
9
SP
3
63
CHEAZ-10
1
9
1
0
1
0
0
P
1
64
GJDB-IO
1
9
63
10
0
25
28
UB
1
65
GJEA-10
1
9
100
18
13
39
30
UB
2
66
CZZDA-11
1
9
36
12
3
19
2
UB
3
67
Rh;h'l>10
1
10
34
23
2
4
5
B
2
68
Rhlh'N-lOB
1
10
73
37
23
5
8
B
3
69
BG-12
1
10
46
10
0
27
.9
UB
3
70
BH-15
1
10
48
19
0
10
19
UB
4
71
BHA-10
1
10
60
9
2
7
42
UB
2
72
BHCA-10
1
10
29
6
2
15
6
UB
3
73
BHD-10
1
10
131
34
9
37
48
UB
2
74
BHG-10
1
10
43
6
4
6
27
UB
2
75
C-33
1
10
75
15
27
31
2
UB
4
76
CAGBZ-10
1
10
97
5
33
48
11
SP
2
77
CAGC-15
1
10
103
53
14
14
22
B
4
78
CAK-14
1
10
58
3
2
35
18
SP
3
79
CR-10
1
10
64
6
1
41
16
SP
3
80
CZG-11
1
10
47
14
3
22
8
UB
3
81
CZQ-11
1
10
46
2
0
32
12
SP
2
82
BFA-10
1
11
159
43
30
31
55
UB
1
83
BH-16
1
11
41
20
2
6
13
UB
3
84
BIB-10
1
11
164
6
0
103
55
SP
2
85
BJB-11
1
11
57
37
1
7
12
B
4
86
BJB-12
1
11
26
10
5
4
7
UB
3
87
BJBB-10
1
11
37
3
0
21
13
SP
3
88
BJD-10
1
11
51
8
0
37
6
UB
2
(a)
lEPA station classification defined in i^pendix 5.1
279
Station
Chloride
Group mcf/L
Station (a)
Class
Strpam
Nuinber
Total
Int
Mod
Fac
Tol
Order
89
CAGB-12
1
11
24
16
4
4
0
B
3
90
CAUA-10
1
11
73
2
17
12
42
SP
2
91
CAWB-10
1
11
213
30
10
20
153
UB
2
92
GJB-lOA
1
11
128
2
34
21
71
SP
3
93
GJKB-10
1
11
57
2
0
7
48
SP
3
94
CZ-14
1
11
47
0
1
38
8
SP
1
95
( r/,M-io
1
11
131
6
13
22
90
SP
3
96
RKFA-12B
1
12
53
24
1
9
19
UB
3
97
RKFA-13
1
12
35
6
2
2
25
UB
3
98
HhlhAA-lO
1
12
45
25
3
3
14
B
3
99
BHC-12
1
12
57
13
1
17
26
UB
3
100
BHCB-10
1
12
152
1
0
41
110
SP
2
101
BJ-12
1
12
32
6
2
5
19
UB
3
102
BJC-12
1
12
42
10
3
14
15
UB
3
103
OG-13
1
12
46
5
1
32
8
UB
3
104
BEZC-10
1
13
117
3
23
19
72
SP
3
105
BG-13
1
13
49
31
0
16
2
B
2
106
BGA-10
1
13
46
18
0
7
21
UB
3
107
BH-11
1
13
89
52
1
22
14
B
5
108
BH-12
1
13
134
62
30
16
26
UB
5
109
BHC-11
1
13
29
4
2
6
17
UB
3
110
BIB-11
1
13
67
22
0
41
4
UB
2
111
BJ-11
1
13
112
35
22
32
23
UB
4
112
BJB-10
1
13
26
15
2
3
6
B
4
113
BJC-10
1
13
108
38
43
14
13
UB
4
114
BK-10
1
13
204
0
0
0
204
SP
3
115
BZT-10
1
13
71
11
1
18
41
UB
2
116
C-10
1
13
50
6
4
35
5
UB
5
117
C-27
1
13
203
20
140
31
12
SP
5
118
C-34
1
13
70
27
12
15
16
UB
4
119
GAGB-ll
1
13
14
2
1
10
1
UB
4
120
CFA-IO
1
13
50
1
9
26
14
SP
3
121
CFA-11
1
13
57
0
7
37
13
SP
3
122
GJE-IO
1
13
134
16
8
27
83
UB
3
123
CPA-10
1
13
73
6
0
5
62
SP
3
124
BH-13
1
14
88
56
3
14
15
B
5
125
BHFZ-13
1
14
37
17
1
0
19
UB
3
126
BJ-10
1
14
67
37
17
2
11
B
4
127
BZ-15
1
14
130
3
0
6
121
SP
2
128
C-28
1
14
36
10
0
5
21
UB
5
129
CAWA-10
1
14
75
10
8
34
23
UB
1
130
CHE-10
1
14
86
3
14
34
35
SP
2
131
CHEA-10
1
14
52
10
4
14
24
UB
3
132
CPC-10
1
14
102
1
2
6
93
SP
2
133
CPC-11
1
14
74
8
15
21
30
UB
2
134
CPZ-10
1
14
76
4
10
17
45
SP
3
(a]
lEPA station classification defined in Appendix 5.1
280
Station
Chloride
Group mcf/L,
Station (a)
Class
Stream
Number
Total
Int
Mod
Fac
Tol
Order
135
BFBZ-10
1
" 15
155
7
54
31
63
SP
1
136
EH-OIB
1
15
59
20
22
12
5
UB
4
137
BH-14
1
15
102
34
24
19
25
UB
5
138
BHH-10
1
15
55
16
2
11
26
UB
2
139
BZV-10
1
15
134
5
17
87
25
SP
1
140
C-29
1
15
100
34
13
48
5
UB
5
141
C-30
1
15
185
49
88
4
44
UB
5
142
CANBZ-11
1
15
75
8
4
11
52
UB
2
143
CAU-10
1
15
51
0
0
50
1
SP
3
144
CAZB-10
1
15
74
5
20
30
19
SP
3
145
CAZBA-10
1
15
24
3
0
17
4
UB
1
146
GJ-17
1
15
66
0
0
29
37
SP
3
147
GJD-10
1
15
67
26
3
32
6
UB
3
148
CO-11
1
15
55
4
17
7
27
SP
3
149
CR-13
1
15
264
53
102
19
90
UB
2
150
Rh;h'l-10
1
16
73
12
0
13
48
UB
3
151
BH-OIA
1
16
70
25
1
17
27
UB
4
152
BHCA-11 .
1
16
74
9
0
34
31
UB
2
153
BJ-01
1
16
115
75
7
2
31
B
4
154
BZN-11
1
16
51
4
31
11
5
SP
2
155
BZS-10
1
16
47
20
5
16
6
UB
2
156
CA-04
1
16
48
11
13
19
5
UB
5
157
CDB-11
1
16
42
4
12
8
18
SP
2
158
CDBZ-12
1
16
40
7
0
21
12
UB
2
159
CS-10
1
16
48
21
1
16
10
UB
3
160
RFAC-lOB
1
17
133
3
78
30
22
SP
2
161
RFr .1
1
17
48
36
2
3
7
B
3
162
KHlh'J-lO
1
17
103
31
0
30
42
UB
3
163
BF.7,-18
1
17
92
15
22
29
26
UB
1
164
BFB-13
1
17
126
52
6
35
33
UB
2
165
BG-11
1
17
59
5
1
20
33
SP
4
166
BJB-13
1
17
63
15
5
13
30
UB
3
167
BI/-10
1
17
84
50
1
7
26
B
4
168
BL-11
1
17
86
21
6
19
40
UB
4
169
BL-12
1
17
27
5
1
6
15
UB
3
170
BLB-10
1
17
51
12
0
27
12
UB
3
171
C-31
1
17
84
33
2
42
7
UB
5
172
CAGBZ-15
1
17
35
7
2
26
0
UB
3
173
c:agc-12
1
17
92
0
3
63
26
SP
4
174
CAU-11
1
17
73
14
3
7
49
UB
2
175
CUH-10
1
17
53
5
16
21
11
SP
1
176
CFAA-10
1
17
86
2
47
11
26
SP
1
177
CZZE-11
1
17
50
8
7
33
2
UB
3
178
BC-11
1
18
75
12
33
22
8
UB
4
179
BE-44
1
18
308
101
128
32
47
UB
6
180
Rh;h'AAA-10
1
18
73
9
5
21
38
UB
2
(a)
lEPA station classification defined in Appendix 5.1
281
Station
Chloride
Group mcf/L
Station (a)
Class
Stream
Nuinber
Total
Int
Mod
Fac
Tol
Order
181
REFAB-10
1
18
42
13
0
24
5
UB
3
182
BJB-14
1
18
48
18
0
6
24
UB
3
183
BJC-11
1
18
46
9
5
16
16
UB
4
184
BJZ-11
1
18
206
3
23
61
119
SP
1
185
BZN-10
1
18
115
8
102
2
3
SP
2
186
BZO-11
1
18
108
51
2
11
44
UB
3
187
C-32
1
18
66
26
10
10
20
UB
4
188
CE-11
1
18
79
1
16
38
24
SP
3
189
GJ-18
1
18
38
9
0
10
19
UB
3
190
BJ-13
1
19
106
5
19
28
54
SP
3
191
C-35
1
19
77
49
0
23
5
B
3
192
cr-10
1
19
50
27
0
22
1
B
4
193
BC-12
1
20
127
23
32
53
19
UB
4
194
BCF-10
1
20
76
5
7
23
41
SP
2
195
BL-13
1
20
110
40
30
22
18
UB
3
196
BZU-10
1
20
64
17
20
6
21
UB
3
197
BZUZ-10
1
20
57
6
12
20
19
UB
2
198
C-06
1
20
146
61
53
12
20
UB
3
199
CAR-10
1
20
188
76
14
82
16
UB
4
200
CO-10
1
20
38
0
3
13
22
SP
3
201
CS-11
1
20
131
19
2
30
80
UB
2
202
CT-ll
1
20
50
12
0
21
17
UB
3
203
BLB-11
1
21
41
6
0
17
18
UB
2
204
BZO-10
1
21
30
0
0
9
21
SP
3
205
CAE-10
1
21
62
14
6
29
13
UB
3
206
CTC-IO
1
21
55
14
0
26
15
UB
3
207
CZW-10
1
21
92
5
8
24
55>
SP
2
208
BEZZAB-IO
1
22
74
51
0
21
2
B
3
209
BJC-13
1
22
109
25
1
16
67
UB
3
210
BJZ-10
1
22
104
15
13
72
4
UB
1
211
BZ-14
1
22
69
12
4
40
13
UB
3
212
BZU-11
1
22
31
12
8
5
6
UB
2
213
CAGBZ-16
1
22
16
2
5
3
6
UB
1
214
CFAB-11
1
22
31
1
11
13
6
SP
2
215
CR-11
1
22
111
8
9
21
73
SP
2
216
CT-12
1
22
29
8
4
9
8
UB
2
217
CAGB-10
1
23
13
1
0
9
3
SP
4
218
CANBZ-10
1
23
52
3
2
17
30
SP
2
219
CPA-11
1
23
48
2
2
10
34
SP
3
220
CPD-10
1
23
112
3
0
73
36
SP
3
221
BB-10
1
24
99
5
28
37
29
SP
1
222
BCE- 10
1
24
108
28
42
27
11
UB
4
223
R?;-40
1
24
111
37
11
36
27
UB
6
224
BEt'A-15
1
24
79
37
4
13
25
UB
1
225
BEFAAA-11
1
24
52
4
12
15
21
SP
2
226
BEGB-10
1
24
75
36
6
3
30
UB
3
(a]
lEPA station classification defined in Appendix 5.1
282
Station
Chloride
Group mq/L
Station fa)
Class
Stream
Number
Total
Int
Mod
Fac
Tol
Order
227
BEZB-10
1
24
134
2
1
13
118
SP
4
228
BFZ-14
1
24
29
5
0
12
12
UB
2
229
CAK-15
1
24
212
13
157
22
20
SP
2
230
CAKZ-11
1
24
18
12
0
4
2
B
1
231
Ci'B-10
1
24
86
26
2
43
15
UB
3
232
BE-01
1
25
144
27
21
31
65
UB
6
233
REFO-10
1
25
69
27
21
15
6
UB
1
234
RFGB-ll
1
25
98
31
1
12
54
UB
3
235
BG-10
1
25
99
35
0
30
34
UB
4
236
BJB-15
1
25
73
11
1
18
43
UB
2
237
BZO-12
1
25
44
11
0
20
13
UB
3
238
CE-10
1
25
50
1
5
41
3
SP
4
239
CHE-11
1
25
83
11
14
41
17
UB
2
240
GJ-19
1
25
140
24
15
37
64
UB
3
241
BEJ?'ir'-10
1
26
79
74
0
3
2
B
3
242
RHlhG-ll
1
26
55
38
1
1
15
B
2
243
BFB-11
1
26
100
25
23
26
26
UB
4
244
CDFB-10
1
26
96
20
6
34
36
UB
4
245
OGZ-11
1
26
116
0
47
32
37
SP
2
246
CZM-10
1
26
40
7
5
25
3
UB
2
247
BE-37
1
27
99
35
9
19
36
UB
6
248
RFABA-10
1
27
102
21
5
41
35
UB
2
249
BZA-10
1
27
62
7
22
27
6
UB
1
250
C-24
1
27
116
20
43
52
1
UB
6
251
CDF-12
1
27
153
17
27
37
72
UB
3
252
BZS-11
1
28
125
15
10
20
80
UB
2
253
C-25
1
28
182
33
67
64
18.
UB
6
254
CAB-10
1
28
30
4
5
14
7
UB
3
255
RKF-23
1
29
75
31
2
8
34
UB
3
256
BHF-10
1
29
89
10
0
8
71
UB
4
257
C-37
1
29
58
26
1
9
22
UB
3
258
CH-03
1
29
46
5
5
24
12
UB
4
259
CR-12
1
29
211
14
2
38
157
SP
2
260
B-20
1
30
95
0
1
0
94
SP
8
261
BE-43
1
30
258
55
102
13
88
UB
6
262
RH;hH-10
1
30
37
23
0
0
14
B
1
263
BEZJ-10
1
30
73
0
0
0
73
P
3
264
BFB-12
1
30
96
26
28
16
26
UB
3
265
BFZ-17
1
30
52
15
0
2
35
UB
1
266
BL-14
1
30
58
15
0
8
35
UB
2
267
BZ-10
1
30
173
32
79
56
6
UB
3
268
CAZA-10
1
30
84
10
3
65
6
UB
3
269
C3GAB-11
1
30
28
3
9
13
3
UB
1
270
CP-01
1
30
33
8
4
11
10
UB
4
271
CRB-10
1
30
204
6
0
18
180
SP
1
272
BEA-11
1
31
200
36
103
27
34
UB
4
(a)
lEPA station classification defined in Appendix 5.1
283
Station
Chloride
Group mcf/L
Station (a)
Class
Stream
Number
Total
Int
Mod
Fac
Tol
Order
273
CAGC-16
1
31
38
4
9
2
23
UB
3
274
CFAB-10
1
31
165
53
1
80
31
UB
2
275
CHEAZ-12
1
31
56
6
2
15
33
UB
1
276
CPZ-12
1
31
114
1
0
0
113
P
1
277
B-16
1
32
169
1
1
0
167
SP
8
278
B-17
1
32
155
0
1
2
152
SP
8
279
B-19
1
32
58
1
28
1
28
SP
8
280
B-22
1
32
67
1
6
28
30
SP
8
281
BE-42
1
32
239
105
105
24
5
UB
6
282
REAC-lOA
1
32
73
0
3
15
55
SP
2
283
BFBZ-11
1
32
137
5
100
18
14
SP
2
284
C-38
1
32
94
43
14
17
20
UB
2
285
CANBAA-IO
1
32
50
21
5
16
8
UB
1
286
CHH-10
1
32
123
22
17
44
40
UB
3
287
CZZB-10
1
32
89
7
11
66
5
SP
2
288
B-18
1
33
236
1
15
0
220
SP
8
289
BE-41
1
33
180
36
9
34
101
UB
6
290
BHlr'Z-12 .
1
33
51
6
1
11
33
UB
2
291
CZZA-10
1
33
97
0
1
43
53
SP
1
292
B-04
1
34
190
8
38
3
141
SP
8
293
BE-38
1
34
268
138
79
41
10
B
6
294
RF,-39
1
34
89
45
5
23
16
B
6
295
BE-45
1
34
112
26
11
15
60
UB
6
296
CH-13
1
34
79
9
2
33
35
UB
4
297
CN-10
1
34
74
18
14
33
9
UB
2
298
B-21
1
35
51
3
11
7
29
SP
8
299
BZS-12
1
35
54
12
0
30
12.
UB
2
300
BED2
1
36
113
13
5
2
93
UB
3
301
BFZ-16
1
36
29
15
0
1
13
B
2
302
BFZ-18
1
36
13
2
0
2
9
UB
1
303
BE-02
1
37
153
82
44
14
13
B
6
304
BLB-12
1
37
84
50
0
21
13
B
2
305
BFBZ-12
1
38
81
61
3
9
7
B
1
306
BEZB-11
1
39
111
7
0
1
103
SP
4
307
CAGC-12
1
39
57
15
14
23
5
UB
4
308
C-07
1
40
107
17
7
27
56
UB
5
309
CDF-10
1
40
79
14
4
55
6
UB
4
310
CK-10
1
40
123
39
23
46
15
UB
3
311
CUA-10
1
40
90
12
2
14
62
UB
2
312
BF-12
1
41
46
3
0
26
17
SP
1
313
OG-12
1
41
125
9
16
74
26
SP
3
314
CO-12
1
41
67
0
20
21
26
SP
2
315
BEG-lOB
1
42
24
4
11
0
9
UB
4
316
GAGBA-10
1
42
131
8
43
65
15
SP
2
317
QT-ll
1
42
26
0
0
2
24
SP
2
318
BE-36
1
43
127
42
6
35
44
UB
6
(a)
lEPA station classification defined in i^pendix 5.1
284
Station
Chloride
Group inq/L
Station (a)
Class
Strpam
Number
Total
Int
Mod
Fac
Tol
Order
319
RKhSZ-10
1
43
68
7
7
12
42
UB
2
320
CHZ-11
1
43
77
2
1
10
64
SP
1
321
GJB-lOB
1
43
153
0
9
16
128
SP
3
322
CP-14
1
43
72
17
10
23
22
UB
3
323
C-26
1
46
26
1
1
24
0
SP
5
324
CP-11
1
46
22
8
0
8
6
UB
4
325
CANB-10
1
47
77
19
4
24
30
UB
3
326
CD-16
1
47
138
5
18
11
104
SP
2
327
CAVA-10
1
48
150
0
5
40
105
SP
2
328
BEA-10
1
49
71
5
17
21
28
SP
2
329
CA-14A
1
49
-
-
-
-
-
-
6
330
CAJA-10
1
49
99
21
14
24
40
UB
2
331
C-23
1
50
135
21
54
53
7
UB
6
332
C-36
1
50
83
43
7
27
6
B
3
333
CD-14
1
50
96
6
47
38
5
SP
4
334
CAK-11
2
52
32
3
5
19
5
SP
3
335
CANZ-10
2
52
12
3
1
5
3
UB
2
336
BJAZ-11
2
54
52
0
0
0
52
P
1
337
CAK-12
2
54
59
15
17
16
11
UB
3
338
C3G-10
2
54
41
1
3
32
5
SP
4
339
CM-11
2
54
75
-18
0
29
28
UB
3
340
BFZ-19
2
55
302
0
0
0
302
P
1
341
CAK-13
2
56
92
58
12
10
12
B
3
342
CAA-10
2
57
13
1
4
6
2
SP
2
343
CAG-10
2
57
33
0
2
30
1
SP
5
344
BHir'Z-11
2
58
28
0
0
2
26.
SP
1
345
CDG-12
2
58
113
4
0
9
100
SP
1
346
BHJr"Z-10
2
59
1000
0
0
0
1000
P
1
347
CP-12
2
59
184
2
0
12
170
SP
3
348
CAJB-10
2
60
42
7
9
26
0
UB
2
349
CDB-10
2
60
16
0
11
2
3
SP
3
350
OG-11
2
60
77
11
26
29
11
UB
4
351
OGZ-10
2
61
41
4
5
28
4
SP
1
352
CRZ-11
2
61
122
3
2
1
116
SP
1
353
C3GAB-10
2
63
64
4
13
23
24
SP
1
354
CB-10
2
64
97
4
17
62
14
SP
4
355
CBBZ-10
2
64
78
0
5
39
34
SP
2
356
CJA-13
2
64
66
6
16
32
12
SP
2
357
BFZ-15
2
67
65
50
0
13
2
B
2
358
CD-13
2
67
40
2
13
22
3
SP
4
359
CA-14B
2
69
-
-
-
-
-
-
6
360
BFZ-13
2
71
91
19
0
34
38
UB
2
361
CAJ-13
2
75
15
0
2
4
8
UB
4
362
CDG-10
2
75
39
6
6
13
14
UB
2
363
cx:-io
2
77
44
0
15
20
9
SP
3
(a)
lEPA station classification defined in i^pendix 5.1
285
Station
Chloride
Group ixf/L
Station (a)
Class
Stream
Number
Total
Int
Mod
Fac
Tol
Order
364
CC-11
2
77
92
2
41
23
26
SP
3
365
CD-15
2
77
53
3
45
3
2
SP
3
366
CZXZ-11
2
77
124
26
1
39
58
UB
1
367
CZB-10
2
78
75
1
3
58
13
SP
3
368
BJA-10
2
79
63
21
11
10
21
UB
2
369
CH-15
2
79
72
18
13
25
16
UB
3
370
CP-13
2
80
161
4
5
8
144
SP
3
371
GJ-04
2
81
89
8
11
46
24
SP
4
372
CZ-10
2
81
129
0
33
9
87
SP
3
373
BFZ-20
2
82
17
3
0
1
13
UB
1
374
REB-10
2
83
203
53
37
31
82
UB
4
375
CDBZ-10
2
83
36
8
3
13
12
UB
2
376
BCZ-10
2
85
268
63
152
48
5
UB
3
377
CZXZ-10
2
87
215
0
2
2
211
SP
1
378
RETlA-ll
2
88
66
28
8
10
20
UB
1
"9
CH-14
2
88
140
30
5
31
74
UB
4
380
RHh'i;-ll
2
90
87
44
2
8
33
B
3
381
GAGBZ-12 .
2
90
8
0
1
6
1
SP
2
382
cx:a-ii
2
90
237
1
0
1
235
P
2
383
CCZ-11
2
90
-
-
-
-
-
-
-
384
RKF-25B
2
92
94
11
14
26
43
UB
3
385
CZX-10
2
92
69
16
2
36
15
UB
2
386
CAGBZ-11
2
93
16
0
1
1
14
SP
2
387
CAK-10
2
93
125
70
38
6
11
B
3
388
RH;h'-15
2
95
81
24
35
13
9
UB
5
389
CDBA-11
2
95
109
6
1
65
26
SP
3
390
CDZ-11
2
97
83
2
25
41
15.,
SP
2
391
GJA-12
2
97
53
1
19
10
23
SP
2
392
RER-12
2
98
44
16
8
7
13
UB
4
393
CDF-11
2
98
126
50
22
45
9
UB
3
394
CD-17
2
99
57
11
19
8
19
UB
2
395
BEZG-10
2
100
76
17
9
30
20
UB
3
396
CAKA-10
2
100
72
2
12
35
23
UB
2
397
CDG-11
2
100
1009
0
0
2
1007
P
1
398
GAGC-17
3
104
20
12
2
0
6
B
2
399
CZA-11
3
108
22
0
7
14
1
SP
3
400
RER-11
3
110
139
27
33
36
43
UB
4
401
rf:r-i3a
3
110
43
2
17
5
19
SP
2
402
BEJ?'-16
3
110
102
36
34
21
11
UB
5
403
BZK-lOA
3
110
12
4
1
6
1
UB
4
404
CAJ-11
3
110
89
14
44
20
11
UB
4
405
CM-01
3
110
69
14
13
27
15
UB
3
406
RKRB-IOB
3
112
23
1
14
0
8
SP
3
407
CD-11
3
116
131
21
20
69
21
UB
4
408
RER-13B
3
118
68
3
28
9
28
SP
2
409
BEX3-10A
3
120
115
89
11
3
12
B
4
(a)
lEPA station classification defined in Appendix 5.1
286
Station
Chloride
Group mq/L
Station (a)
Class
Strpam
Nuinber
Total
Int
Mod
Fac
Tol
Order
410
C-39
3
120
111
3
5
2
101
SP
2
411
CDD-10
3
120
37
1
0
9
27
SP
3
412
CHEAZ-11
3
120
100
3
1
1
95
SP
1
413
BZK-lOB
3
122
20
17
2
1
0
B
4
414
OOB-10
3
126
80
4
17
36
23
SP
2
415
RKFEZ-IO
3
130
106
0
0
0
106
P
1
416
CAJC-ll
3
130
39
8
6
2
23
UB
3
417
CDBA-10
3
138
70
15
30
12
13
UB
2
418
Rh;h'-03
3
140
42
19
4
9
10
UB
4
419
RKF-19
3
140
26
7
3
1
15
UB
4
420
BGB-10
3
140
54
5
0
30
19
SP
3
421
GJA-IO
3
145
86
38
12
19
17
UB
3
422
RFDB-ll
3
150
209
4
0
5
200
SP
3
423
CAJ-14A
3
150
28
10
3
9
6
UB
3
424
CPZ-13
3
150
49
4
5
16
24
SP
1
425
CD-12
3
151
71
4
2
22
43
SP
4
426
CGA-10
3
152
53
9
10
28
6
UB
3
427
CPZ-11
3
160
107
0
0
1
106
P
1
428
CH-16
3
163
122
2
8
0
112
SP
3
429
GJA-11
3
176
17
2
0
9
6
UB
3
430
BEC-10
3
180
33
16
4
7
6
UB
3
431
RH;h'-17
3
180
139
36
59
20
24
UB
5
432
CAN-IO
3
184
101
10
68
2
21
SP
4
433
BJAZ-10
3
190
1000
0
0
0
1000
P
1
434
CAL-10
3
190
82
1
1
44
36
SP
2
435
GAZCZ-10
3
190
44
5
1
27
11
UB
4
436
RED-IO
3
200
42
14
8
20
0.
UB
3
437
CDZ-12
3
212
61
6
22
19
14
SP
1
438
BF-13
3
220
45
9
0
21
15
UB
1
439
BZK-11
3
220
86
5
1
36
44
SP
4
440
RKDB-IO
3
230
54
23
12
18
1
UB
2
441
Hh;h'C-ll
3
240
27
8
0
7
12
UB
2
442
CZA-10
4
256
52
0
21
17
14
SP
4
443
RED-ll
4
260
21
12
5
0
4
B
3
444
BDZ-10
4
264
61
33
0
17
11
UB
3
445
CAJ-12
4
270
30
3
5
16
6
UB
4
446
REnC-10
4
280
69
15
21
25
8
UB
2
447
BF-llB
4
288
128
0
13
14
101
SP
3
448
C-lOB
4
290
80
3
16
23
38
SP
2
449
CBC-10
4
297
91
2
13
53
23
SP
3
450
RERB-lOA
4
370
31
1
9
8
13
SP
3
451
BFZ-IO
4
390
36
0
0
3
33
SP
3
452
BCA-10
4
406
76
9
16
27
24
UB
3
453
BFZ-llA
4
430
26
0
0
0
26
P
3
454
BFZ-llB
4
430
127
0
0
6
121
SP
3
455
CCZ-10
4
430
68
25
6
17
20
UB
1
(^) lEPA station classification defined in i^pendix 5.1
287
Station
Chloride
Group mcr/L
Station (a)
Class
Stream
Number
Total
Int
Mod
Fac
Tol
Order
456
CAC-11
4
450
24
7
1
7
9
UB
3
457
BEBZ-10
4
470
111
21
12
34
44
UB
2
458
BF-llA
4
500
88
0
0
2
86
SP
3
459
CAJC-10
5
510
41
5
2
10
24
UB
3
460
BEBZ-11
5
520
73
14
13
40
6
UB
2
461
BZ-13
5
520
40
20
11
5
4
B
2
462
CZH-10
5
525
54
3
28
12
11
SP
2
463
CZ-15
5
540
73
6
1
54
12
SP
3
464
BF-01
5
550
97
0
0
0
97
P
3
465
BZKA-10
5
550
179
15
25
49
90
SP
3
466
BZJZ-10
5
580
132
17
6
26
83
UB
2
467
BEZB-12
6
1100
91
5
6
11
69
SP
3
468
GANBA-10
6
1150
170
0
0
3
167
SP
1
469
CBA-10
6
1170
94
1
11
44
38
SP
3
470
BEZE-10
6
1200
126
5
14
35
72
SP
2
471
BZJZ-llB
6
1350
20
3
0
0
17
UB
2
472
CHD-10
6
1500
23
2
0
20
1
SP
4
473
RFTA-10 •
6
1600
36
25
3
3
5
B
2
474
CU-IO
6
1600
108
24
0
55
29
UB
3
475
BZJZ-llA
6
1940
56
11
5
26
14
UB
2
476
RFA-10
6
3700
129
14
2
7
106
UB
5
477
CAJ-14B
6
4900
48
0
10
3
35
SP
3
(a)
lEPA station classification defined in Appendix 5.1
288
Appendic 5-C. Benthic Macroinvertebrates (Except Diptera and
Mollusca) Collected in Buck Creek, Clay County,
Illinois, August and October, 1986
289
STATIONS ^__
Tolerence 1 2 3 4 S
Status^ Aug Oct Aug Oct Aug Cct Aug Oct Aug Oct
vjg uct
TOTAL
K'orrs , Leeches
ss[li:a
dljgdchaeta
Hip lot an da
Enchvt rjei ide
Ni i a 1 d J e T
rX:etOfceter cvcpKcnue ( Grui thu1 sen)
CHaetopceter sp.
"ero (/ uIopJio— ^p) .'urccta (Kuller)
re TO (/ ulcphprrje) icpa (Leldy)
"eT-o [Dero] dicita'.a i^jller)
Te-'O (Der-o) r.ivea Alyer
Tero ( Pcro) oituea fl'Udekeni
Zs-ro sp,
.■r'cencnai* Lx:I<fuoceIi Eretscher
Scie ccTrrjr.ie Piguet
,V2t8 j-'^r-daliB Picuet
Scie \xiT-iabilie Piouet
p-r-iitirTji leidyi (Smitti)
Pr-iffJr.3 pluraeeta Turner
Slcvl-nc cppendiculcta (d'UdeVem)
5rylcr-va tacnetris { f) (Llnnaeus)Tt
Tubif icidae
/nlocVilue lirmobi'^e Eretscher
Aulocr-ll-jB pia-^eti KiwjlewSki
Jl'-ocT-^luB terrpietc-.i (Southern)
lirr-xxiT-ilus clcpoTedicKue Ratrel
LirmodTilus hcffne\ster-i Cliparede
lirT^od-rilue sp.§
•UIW/OCC (prir.anly Tubi f ic idae)
**l'-7CC (primarily TubifldCae)
HIPUOINU
GTosslphonI 1 dae
?laecbdella pc-rcBiiica (Say)
HI rudi ni dae
UHROPOOA
CRUSTACEA
/Vipm poda
Talitridae
H-^alella azteca (Saussure)
IscpoCa
Asellidae
Ccecidatea fcrbeei (Willlarrs)
Decapoca
AstacTdae
Cc-ricr-^e dioger.cB Glrard
Crccr.ec'.ea vir-.lie (Hacen)
Pal aemonidae
Palae'V>r,e:eB Vad-lcVene-le RathSun
37
31
3
- 39
1
3
1
1 1
8 14
23
32
6
1
3
5
7
12
9
6
3
5
21 -JS
24 29
2
A
-
-
'0
1
73
13
-
9
-
23
-
A
-
-
-
1
-
-
18 c-2
26
22 s9
.
.
12
2
37
47
-
:a
.
-
1
-
1
-
2
1
2
,
3
_
-
2
.
1
8
49
36
S2
1
4
6
5
1
62 41
5 31
33 5
24 8
3 -
-
-
;
;
;
2
11
7
A
-
1
7
-
-
'8
11
16
1
-
3
'vTiphlpods, Isopods, Crayfishes, Prawns
n 20
1 1
3 2
6 46
1
! 2
20 1
1 11
13 17
S 3
5 7
- 9
1 6 2
30 10 74 16
16 9S
2 -
70 5
Aquatic and Semi-Aquatic Insects
N'SEC'A
Cpne->erop'.era (ray(lies)
C a e 1 1 d a e
Cullibcefle fer—.icir.eue (-'alsh)
Caenicae
Ccer.\B spp.
';'"e-ic" r;c
.Vfz^per::c :v~ia£a (Serville)
i^ezaner:;c sp.
6 16
15 37
2 1
I 3 7
24
SI 31
6
28
30 111
' ■ -ndiviouals '.deniifed as "'.■aididae- .-prearea primarily to t)e anterior portions of Per-c spp.
' • '. ) --Cters to the fcF£j:cT-:f fom cf .rr^lar-in Iccuoir-ie.
'. - cevelopinq penis sneaths -ere present in these inaivifluals.
• jnicent 1 ( lioie inr.ature <pecir.er« »?tnout capilliforn chaetae.
• unicent 1 ; licie specmens -iih capilli'orm criaetae.
2
371
6
1
A
62
261
103
29
12
5
10
3
2
23
8
1
9
7
105
15
1
13
4
2S4
63
1
1
5
2A8
13
1
16
239
51
369
7
1«
290
STATIONS
Tolerjnce 1 2 3 i S t".
Jixt^ Stilus^ Aug Oct Au9 Gel Aug Gel Aug Oct Aug uci Aug Gel TOTAL
Hepliceni Mte
Ste-\2crcn ir-.tcryuncictum (5^y) I -1 -1 -- -1 1', -- S
rtenc-ieTO femomium {Sty) 1 -1 -- -- -- -- -- 1
leplcphl eb1 i die
ieptcphlebia spp. 1 -2 -4 -1 -- •- -- 7
OOOSATA
Z'GOPTCSA (iiPielfnes)
Coenjcr 1 onl<;«e
A'fia <.p. H 2 1 - - 1 - < 1 1 - 5 ? 17
rnallcf-ti anttr.niti^Ti (Say) H -- 1- -- 2- -2 -- 5
rrv2llcc~a ci-jagcr.t SelyS M -- -1 -- -- -- -2 3
I>^:icc.-t3 ficr^tu.-s (Higen) M 1) 1- -- -- .- -. 3
■>^llcc-a spp. M 2 2 - - S 1 :0
Jecr.y.x.'n pofita (Haoen) 1 33 67 4 14 1 20 - - - - - 27 176
AN'ISC?T[RA (craconflies)
Aeshni dae
Kceicefchnc pentaccntha (Rimbur) M 11 -- -- 41 4- 2 - 13
CorOul 1 1 dee
Sc-ctochlcT^i ;p. M -- -- -1 -- 1- -- 2
Tat n:eor.eu»-ia sp. H 2- -4 -- -- •- -- 6
Gonph- eae
Cory.h-uB nr cnllie SelyS T -- 1- -1 -- 1- -- 3
Llbellul icae
lilellula p-ulchella Drury H -3 -- -- -- -- -- 3
Libellulc sp. M 3......-.1.. <
Fachvciplc^ Icnciperjnie ( Burmel 5 ter) H -- -4 -- -- -- -1 S
Ter-i-.her.-iB tene'-ra (Say) M .... 1 ... 8 - 5 - 14
?Icr>-.e-:8 li/^Cc (Drury) I 6- -- -- -- -- -- 6
Heteropierj (true bugs)
Eelosior.ancae
Belcetcna sp. F 1........... ]
Corixicae
Ccricella edulie (Chanplon) F -- -- -1 -- -- -- 1
Pclnccor-:.za buenoi Abboll F 6 - 2 1 - - - - 1 - 7 ! '.9
5-;pcra clterrv^ta (Say) F 6 - - - 6 - 22 2 14 3 !3 1 7 7
1
-
7
e
s
3
!3
1
3
7
128
12
7
6
24
10
Sigarv rcdeeta (Abbott) F 21 2 29 3 13 1 104 23 23 7 128 12 3S6
rTichc-.o-rizn oalva (Say) F 1 1 20 - 8 2 12 4 7 6 24 10 55
Gerrldae
Cerris rc-rginaiuB Say F -- -- -- -- 1- -- 1
Cerrie r^bular-ie Orake and Hottes F -- 1- -- -- -- -- 1
Cerr-ie reTT:icie Say F 17- -- -- -- -- -- 17
CerKs spp.' F 1 1 - - - - 9 - 1 - 1 - 13
Rheunctcbctee pclcei Elatchley F 11- -- 4-26- 3- 2- 46
Ty-epobctee pietut ( Herri ch-Sch2ef fer ) F 5- -- 1- 1- -- -- 7
Hydrometndae
Hydrortetrxi mrtini Kirkaldy F -- -- -- 1- -- -- I
Mesovel 1 1 dae
Meeovelia rulccr.ti White F -- 33 22 -- 1- 63 20
Nepidae
Fcnctr^ b-jenoi Huncerford F -- -- -- -- -- 2- 2
Notonectldae
Kotcr.ec'.a irrc^tc Uhler F -- -- 4- 1- J. 2- 8
Pleldae
Secplea etn'oZalF'. eber) F -- -- .1 -. .- -- 1
Vel 1 idae
Microvel\a c-r.er-iccna (Uhler) F 1- 1- -- 1- .. .. 3
Meoa loptera
Corycalidae (dcbsonf 1 les )
Chciilicdee T^efricor-r.ie Rambur M -. 1- .. .. .. .. \
Si«l idae (alderf I les)
SialiB sp. M 12---. I-.... 4
Trichopiera (caddl sf 1 i es )
Hyorppsychidae
Cheii-ctcpcuche sp. H .] .. .. __ __ __ j
Leplocer idae
CeeeiiB xnccnepicua (Walker) F -- .. .. .1 .. .7 "^
Cerac'.ta sp. H -. .. .. 1. .. .. 1
Colcoptera (beetles)
Orycpidae
.Helich-^K foBl\nial\jD (Say)
):elich..B 'i.i:\ophil.je (Gernar)
^e'lic'r-e .t—.r.Z'je leConte
Oytlsc-dae
iaccophil-ue faeciatuB mfuB Melsheiner F 16- 1- 4- 1- .. .- 27
iccccrh-.lue -.. -y^culceua Say F S- .. .. ._ .. .. 5
■'■^aT-^a Icc^-itr-io 'Say) F -. ..■.'. .. j. .. 1
F
.
H
-
F
1
F
2
F
1
F
16
F
S
F
.
291
STATIONS
Tolersnce 1 2 3 i
Stilus^ AuQ Oct Aug Ott Aug Oct Aug Oct
T
T
Aug Oct Aug Oct
•OTAL
Dyt'.scfdie (ccncluclto)
Hvdroporinl (larvje)
H)jdT-cpc—je SP. A
HudrcpOT-jB ip. B
HudrcpCJB sp. C
Agab\jB sp.
[ "i m i i e e
5J*neZrrie sp.
Gyri nICie
Cyr-lnuB sp.
HillpllCse
Feltodytoe du-ria-jcr-.i Young
reltodytee duoceci'rpvnclatuB (Siy)
Feltcdutee edentulua (LeConte)
Fe'.todutes KtcvKs Kstheson
FeltocLtea rut-.cue (LeConie)
peltody'eB ecr-aculctuB Roberts
Feltodu'.ee spp.
Hvflropni 1 1 cae
TT-cp-ieterTL/e collnr-is Btr-lclctus (LeConte)
"-crif tcrnua lateralis r.irtbatuB (Sjy)
-•-Ptem-js nztatcr a'Orchynont
; ■e7~.uB spp.
.;'-ce mcuiicollie flulsant
.-ceue aculeatue LeConte
EeroeuB pcegrir^s (Herbst) .
Be-roeuB spp.
Helcphcr-jB sp.
rydroch-^e sp.
Sci mcse
Sci-rtee SP.
Leplcopterj (moths)
Pyral iCae
Sync'.ita oblite-ralie (Walker)
- n - 3 - 13 - 7 - 31 - ?5
11 1 - 3 - - 2 5 - 10 -
< - 1 - 1
2 5 3 - - i 9 7 :0 6 10 9
11 1 - - - 1 . - 1 - - -
8S 8 10 - 32 1 IS 3 17 8 2 -
3 2 1 1 - - -
3 2 5 - 1 - - - - 1 - -
1 - - 1 1 - - - 1 - - -
S 2 2 - 1 - - 1 3 1 - -
2 1
1
10 4 - - 1
12 2
3 5 - - - 1 - - 2 - - -
1
i 14 3 121 3 197 - 2 - 79 9 31
12
90
24
1
3
6
es
1
5
181
7
12
4
15
4
3
1
15
14
1
3
3
11
1
1
463
22
otal S'urSer of 'axa
48 39 32 37 26 33 29 25 ':i 30 17 28
97
'otal N'jnber of InClvlCuals by
■ '- Status:
. : erenl
■'ocerate
■•' i c u 1 1 a 1 1 V e
Tolerant
rotal Number of InClviCuals
"ercent Ir,tc:erant
57 108 ■ 14 68 2 33 37 19 13 10 18 132 511
13 11 23 10 7 4 44 18 SB 28 £7 11 3i4
246 114 94 175 90 245 277 94 114 173 258 207 2087
100 146 100 179 111 167 167 78 SS 106 94 154 1490
416 379 231 432 210 4i9 525 209 :-03 317 <57 504
4432
14 23 6 :6 17 7 9 4 3 4 26
:rPA Station CI ass 1 f 1 ca 1 1 on =
secies Civersttv
SP L'B s? SP SP SP s? SP :p us
4.4 3.8 4.2 3.5 3.3 2.5 3.6 3.9 3.9 3.6 3.5 3.4
= [ntrie5 represent actual number collected In semi -quant U at We '.a-ple. Site Iccancis are lllullraiea '. n noure 5.1
descnpea m Appenoix 5.1.
-tolerance status • intolerant {]], moderate (f). 'acultative (T). ;clerant (T); defined In Appenc'x 5.1.
^:CPA station classification scheme Oeflneo 1n Appencix 5.1.
292
Appendix 6-A. Methods used during investigation of origin of
domestic well contamination by saline waters
Sample Collection
Brine samples were collected at the well head in 500 mL acid
washed high density polyethylene bottles and stored on ice until
the samples were returned to the laboratory for further
processing. The brine-oil mixture was transferred to a
separatory funnel and the brine was allowed to separate from
the oil. The brine was drawn off, filtered, and one split for
metal analysis was acidified with 50 percent (v/v) HN03 to a
final acid content of 1 percent and stored in acid washed high
density polyethylene bottles. Another split for chloride was
stored in acid washed high density polyethylene bottles and
refrigerated until the analyses could be performed.
Chemical Analysis
A. Metals
All metal constituents reported in this report were
determined using an atomic absorption spectrophotometric method
adapted from Fletcher and Collins (1974) . The spectrometer used
was a Perkin-Elmer Model 3 06 Atomic Absorption Spectrophotometer
and signals were recorded with a Perkin-Elmer Model 056 strip
chart recorder.
Due to the high dissolved solids content of the brine
samples and the potential for matrix interferences, all metals
except barium were determined by the method of standard
additions. Barium could not be determined by standard additions
because added Ba precipitates with the SO4 in the sample.
Calibration parameters and sample dilutions are shown in table
6-A2.
The instrumental conditions used for the metal
determinations are shown in table 6-A3.
B. Chloride.
Chloride was determined by mercuric nitrate titration, U.S.
EPA (1979). Unacidified brine samples, diluted 0.1 mL to 50 mL
were made slightly acidic with 0.036M HN03 and 5 drops of a mixed
diphenylcarbazone-bromphenol blue indicator was added. The
sample was titrated in duplicate against standardized 0.141N
Hg(N03)H20 titrant. The mercuric nitrate titrant was
standardized daily against 0.087N NaCl. The mean of the
duplicate determinations was reported.
293
TABLE 6-Al.
VJKi CdJ.ny OIL FIELD BRINE SAMPLES (mg/L)
SA'IPLE
rOR:-V\Tia^
LX
N'a
K
Ca
'■'9
Li
Sr
Ba
Fe
CI
3-51^
Un'r-vHaAfi
2N-7E- 9 mUhl
49470
165
5281
1332
5.2
277
<7
4
84520
B-5165
Tar Springs
3N-7E-J6 SES.6E
44600
104
3730
1240
2.3
174
<5
6
73080
B-5I&6
"^ar Springs
3N-7E-16 N2S;':SE
47200
79
3520
1220
2.1
163
<5
39
78060
B-5K4
Cypress
3!f8E-34 SVS'^JE
36720
ISO
2700
1353
12.0
84
<7
31
60490
3-5146
CvTDress
3N-8E- 3 C mi'l
35000
193
2370
1350
11.9
85
<7
5
59800
B-5152
Cypress
2!s'-8E- 8 NE!WSE
38670
177
3956
1325
7.3
103
<7
14
65830
B-5153
Cypress
2N-8E- 8 NEIsESa'
39190
159
3215
1153
7.5
94
<10
0
61730
B-5155
Cypi-^ss
2N-8E- 8 WU€
36460
130
2551
970
5.2
90
<10
15
57240
B-5161
Cypress
2N-7E-35 I\f>'«WESE
45900
289
7000
2120
10.9
125
<10
24
90220
3-5140
A'jx Vases
3[^SE-i8 Sv!Sv!.£
50500
178
4940
1170
4.7
211
<7
6
&;400
B-5141
A;^ Vases
3N-8E-21 SESE9,'J
48550
l&S
6174
16S3
5.4
231
<7
6
83370
3-5163
A!jx Vases
3N-7E-18 NESESE
45800
183
4220
1190
5.4
226
<5
7
84750
3-5142
f-'cClosky
3N-8E-28 NENESl'J
35700
137
3603
1353
6.3
110
<7
11
62940
3-5147
[•'cClosky
3N-8E-32 E2?a'SE
42540
124
2995
1221
6.7
170
<7
<3
66210
3-5154
[•'cClosky
2N-8E-15 NESi'.^C
49270
186
4568
1422
6.7
150
<10
2
776S0
B-5155
KcClosky
2N-8E- 6 W2NBs'E
44070
143
4064
1253
4.8
135
<10
7
69480
B-5157
!''cClosky
2:^7E- 1 Sw^CSE
52020
221
4534
2121
8.8
750
<iO
4
84100
3-5162
KcClosky
3N-7E-33 ?,'^'ENE
45800
214
6050
2290
6.3
537
<10
113
85170
3-5163
KcClosky
3N-7E-22 S2f.V.^JE
48900
23.9
5020
2000
7.3
167
xlO
1
84430
3-5164
KcClosky
3N-7E- 9 SESESi.-i
46000
224
4070
2130
8.9
576
<5
6
88620
B-5167
[■'cClosky
3N-7E-15 N2?a'SE
45100
184
3600
1050
6.7
149
<5
7
79520
B-5170
[•'cClosky
3I\'-7E-17 NESV.'SaI
44400
91
3440
1160
2.6
176
<5
4
75110
3-5171
!''cC1osky
3:';-2E-14 C SESE
47400
217
5460
1710
6.9
132
<5
7
38780
3-5143
Sal en
3N'-8E-34 fWJEl'W
43830
378
5299
2392
17.7
289
<7
183
82230
E-5149
Sale-n
2N-7E-n nes\'^:e
46560
489
56S4
1948
19.6
114
<7
10
30370
3-5150
Salffn
2['J-7E-11 Sr.^JE:W
46300
139
3157
1163
4.7
115
<7
16
74330
3-5151
Salem
2N-7E-12 KVa^'W
47900
520
5700
1950
19.5
115
<7
7
77790
B-51S3
Salem
2N'-7E- 1 SENESl-J
50000
475
6287
1974
20.0
126
<10
16
83210
3-5159
Sal em
2^^7E-:2 \UUh!
45900
503
5530
1820
19.2
107
<10
115
30080
3-5160
Sal em
2'!-7E- 1 Sl-S^W
4S000
417
5620
2000
18.6
119
<10
82950
3-5169
Sal en
3'^7E-17 S2!W€
47100
421
5610
2340
15.3
130
<5
8
33330
294
TABLE 6-A2.
ATOMIC ABSORPTION CALIBRATION PARAMETERS
Element
stock
1st
2nd
sampl G
solution
add.
add.
dilution
mq/L
mg/L
;ng/L
Na
500
50
100
0.1 to 50
K
10
1
2
0.1 to 50
Ca
100
10
20
0.1 to 50
Mg
30
3
6
0.1 to 50
Li
10
1
2
5 to 50
Fe
10
1
2
5 to 50
Sr
200
20
40
5 to 50
Bal
100
10
20
5 to 50
^ barium determined using conventional calibration,
calibration standard matrix 45 g/1 Na, 59.8 g/1 CI,
and 4 g/1 Ca.
295
TABLE 5-A3.
ATOMIC ABSORPTION INSTRUMENTAL CONDITIONS
Parameter Na K Li Ca Mg Sr Ba Fe
Wavelength, nm 330.2 755.5 570.8 422.7 285.2 460.7 553.6 302.1
Slit, nm 0.7 1.4 1.4 0.7 0.7 0.4 0.4 0.2
Flame oxidant air air air N^O N2O N2O N2O air
Burner^ 5 5 5 90 30 90 0 0
^ orientation of burner in degrees from parallel
296
TABLE 6-A4
PENNSYLVANIAN 5RINES; KEENTS ET AL
195;
SaT.pl e
':a-K
Ca
C1
4572
212
^ "" r "^
B- 56
5673
5
53
7096
3- 55
70S6
59
87
10354
B- 54
7023
174
94
10372
3- 57
4505
340
220
6200
3-647
14553
552
283
24106
3-441
19643
648
431
32349
3-379
11101
612
229
173S3
297
Appendix 9-A. Brief description of analytical procedures
performed on water samples taken at case study
sites and domestic water wells in southeastern
Clay County.
298
Conductivity
pH
Alkalinity-
taken in the lab, with an instrument that was
appropriately standardized beforehand. Sample
was allowed to come to room temperature and
scraped and shaken.
-Taken with a standardized pH meter in the lab
Again, sample was allowed to come to room
temperature and shaken.
After the pH was established on a 25 ml.
sample, it was titrated to a pH of 4.3 with
0.02N H2S04.
Residue (TDS)
A filtered portion of the unpreserved sample
was evaporated from a glass dish, of which the
before and after weights were subtracted to
give the TDS.
Chlorides and
Sulfates
These were determined by Ion Chromatography
Known standards are compared with the
unpreserved sample.
Calcium,
Magnesium,
Sodium,
Strontium,
Lithium
These were determined by Flame Atomic
Adsorption. The HNO3 preserved portion of the
sample was used.
299
Appendix 9-B. Results of chemical analysis on groundwater
samples collected at Clay County case study
sites.
300
CLAY COUNTY
BRINE STUDY
CHEMICAL
ANALYSIS
■-
CALCIUM
MAGNESIUM
STRONTIUM
SODIUM
LITHIUM
SITE
WELL
INTERVAL
(CA)
(MG)
(SR)
(NA)
(LI)
A
1-A
26.5-
29.0
112.0
53.2
0.30
82.0
0.03
A
1-B
16.5-
19.0
1750.0
480.0
3.70
650.0
0.11
A
1-C
7.5-
10.0
3110.0
1070.0
9.10
1380.0
0.20
A
2-A
22.5-
25.0
87.0
37.0
0.20
55.0
0.01
A
2-B
9.5-
12.0
307.0
134.0
1.30
514.0
0.05
A
3-A
32.5-
35.0
346.0
186.0
2.30
778.0
0.14
A
3-B
17.5-
20.0
416.0
205.0
1.90
1144.0
0.21
A
3-C
7.5-
10.0
2040.0
979.0
9.06
1200.0
0.18
A
4-A
26.5-
29.0
470.0
150.0
1.60
570.0
0.08
A
4-B
17.5-
20.0
1640.0
600.0
20.20
6880.0
0.24
A
4-C
7.5-
10.0
2350.0
550.0
36.30
11840.0
0.35
A
5-A
42.5-
45.0
100.0
48.8
0.30
122.0
0.03
A
5-B
24.5-
27.0
370.0
120.0
9.90
530.0
0.12
A
5-C
7.5-
10.0
3600.0
1120.0
44.70
15280.0
0.44
A
6-A
27.5-
30.0
106.0
50.0
0.40
224.0
0.05
A
6-B
12.5-
15.0
255.0
122.0
0.80
588.0
0.07
A
7-A
21.5-
24.0
115.0
50.0
0.30
110.0
0.02
A
8-A
19.5-
22.0
0.0
0.0
0.00
0.0
0.00
A
9-A
7.5-
10.0
1640.0
.. 800.0
5.18
1960.0
0.12
A
OB-4
2.0-
18.0
212.0
90.0
0.09
613.0
0.01
A
OB-5
2.0-
18.0
3200.0
1520.0
15.10
1080.0
0.25
A
OB-6
2.0-
23.0
2200.0
880.0
15.90
4960.0
0.23
301
CHLORIDE
SULFATE
ALKALINITY
TOTAL DISS
SPECIFIC
PH
SITE
WELL
(CD
(SO)
AS CAC03
MINERALS
COND
(IN LAB)
A
1-A
150.0
64.0
322
711
1152
7.6
A
1-B
4400.0
27.0
166
8928
12040
7.2
A
1-C
9800.0
32.0
119
21054
24600
7.1
A
2-A
35.0
102.0
343
560
900
7.7
A
2-B
1730.0
75.0
90
2893
5400
7.0
A
3-A
1940.0
427.0
293
4196
6530
7.9
A
3-B
2500.0
720.0
266
5206
8630
7.7
A
3-C
8530.0
58.0
156
12817
23600
7.0
A
4-A
1800.0
160.0
358
3189
5650
7.5
A
4-B
15850.0
480.0
240
26667
42200
7.3
A
4-C
22000.0
283.0
168
37282
57900
7.2
A
5-A
75.0
81.0
460
684
1144
7.9
A
5-B
1050.0
746.0
367
3238
4820
7.7
A
5-C
32000.0
376.0
165
52006
80500
6.7
A
6-A
225.0
161.0
525
1129
1778
7.6
A
6-B
1288.0
230.0
179
2646
4300
7.5
A
7-A
21.0
329.0
395
894
1273
7.6
A
8-A
27.0
134.0
342
959
893
7.8
A
9-A
8770.0
9.0
84
13182
24300
6.7
A
OB-4
1.510.0
70.0
164
2589
4830
7.4
A
OB-5
12690.0
300.0
180
19827
32800
7.4
A
OB-6
14950.0
50.0
141
23809
41000
7.0
302
CALCIUM
MAGNESIUM
STRONTIUM
SODIUM
LITHIUM
SITE
WELL
INTERVAL
(CA)
(MG)
(SR)
(NA)
(LI)
B
1-A
42.5-
45.0
97.0
40.0
0.39
96.0
0.01
B
1-B
27.5-
30.0
243.0
98.0
0.90
392.0
0.03
B
1-C
12.5-
15.0
1760.0
680.0
12.40
4240.0
0.27
B
2-A
24.5-
27.0
62.4
20.0
0.10
98.0
0.01
B
2-B
12.5-
15.0
69.0
26.4
0.20
250.0
0.01
6
3-A
29.5-
32.0
563.0
205.0
4.90
2160.0
0.11
B
3-B
17.5-
20.0
760.0
280.0
5.40
3920.0
0.22
B
3-C
9.5-
12.0
435.0
198.0
1.78
543.0
0.04
B
4-A
30.5-
33.0
154.0
66.0
0.40
247.0
0.02
B
4-B
12.5-
15.0
113.0
53.0
0.30
98.0
0.02
B
5-A
31.5-
34.0
109.0
50.0
0.40
123.0
0.01
B
5-B
22.5-
25.0
104.0
45.0
0.03
84.0
0.01
B
5-C
9.5-
12.0
71.0
29.6
0.02
110.0
0.02
B
6-A
22.5-
25.0
80.0
34.4
0.30
225.0
0.04
B
6-B
10.5-
13.0
275.0
115.0
0.89
218.0
0.06
B
7-A
22.5-
25.0
214.0
103.0
0.86
456.0
0.06
B
8-A
22.5-
25.0
137.0
70.0
0.05
192.0
0.02
B
8-B
9.5-
12.0
154.0
90.0
0.50
140.0
0.05
B
9-A
27.5-
30.0
79.0
36.0
0.40
311.0
0.02
B
9-B
12.5-
15.0
81.0
30.4
0.41
97.0
0.01
B
10-A
17.5-
20.0
85.0
28.8
0.20
56.8
0.03
B
11-A
L2.5-
15.0
131.0
65.0
0.04
117.0
0.03
B
OB-1
2.0-
13.0
112.0
38.0
0.60
147.0
0.01
B
OB-3
2.0-
21.0
3160.0
1480.0
13.50
960.0
0.24
B
OB-6
2.0-
24.0
3520.0
1520.0
15.50
3560.0
0.27
B
OB-8
2.0-
13.0
159.0
84.0
0.30
130.0
0.01
303
CHLORIDE
SULFATE
ALKALINITY
TOTAL DISS
SPECIFIC
PH
SITE
WELL
(CD
(SO)
AS CAC03
MINERALS
COND
(IN LAB)
B
1-A
88.0
3.5
526
669
1028
7.7
B
1-B
550.0
635.0
480
2270
3520
7.7
B
1-C
11680.0
490.0
208
18887
33100
7.3
B
2-A
5.1
35.0
438
522
815
7.5
B
2-B
37.0
310.0
535
1027
1480
7.5
B
3-A
4440.0
668.0
361
8163
14070
7.8
B
3-B
7545.0
185.0
230
13755
25200
7.8
B
3-C
2440.0
23.0
79
3861
7120
6.8
B
4-A
22.0
650.0
544
1546
1970
7.6
B
4-B
22.0
229.0
485
841
1270
7.2
B
5-A
29.0
105.0
480
893
1342
7.2
B
5-B
12.0
158.0
486
732
1090
7.5
3
5-C
43.0
129.0
361
637
1004
7.7
B
6-A
14.0
353.0
541
1043
1495
7.6
B
6-B
827.0
220.0
352
1935
3430
7.5
B
7-A
402.0
854.0
581
2505
3580
7.7
B
8-A
57.0
410.0
506
1250
1775
7.5
B
8-B
14.0
444.0
646
1285
1748
7.3
B
9-A
182.0
185.0
579
1161
1822
8.2
B
9-B
408.0
132.0
126
949
1553
6.7
B
10-A
. 11.0
161.0
373
550
828
7.3
B
11-A
334.0
63.0
356
942
1700
7.4
B
OB-1
513.0
20.0
82
1029
1732
6.3
B
OB-3
15420.0
83.0
149
23837
40300
5.8
B
OB-6
17150.0
50.0
. 160
26885
44800
5.7
B
OB-8
33.0
910.0
244
1670
1917
7.2
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