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BIOLOGICAL
WATER QUALITY
MONITORING
W7F D0CUMEN7S COLLECTION
' W " 7 7003
MONTANA STATE LIBRARY
HELENA 7^n-,TANA 59r ;o
4
NORTHCENTRAL MONTANA
1977-1978
STATE OF MONTANA
WATER QUALITY BUREAU
ENVIRONMENTAL SCIENCES DIVISION
DEPARTMENT OF HEALTH AND ENVIRONMENTAL SCIENCES
HELENA, MONTANA 59601
MONTANA STATE LIBRARY
3 0864 1001 9840 0
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BIOLOGICAL WATER QUALITY MONITORING
NORTHCENTRAL MONTANA
1977-1978
by
Gary L. Ingman, Loren L. Bahls,
and Abraham A. Horpestad
March 1979
State of Montana
Water Quality Biareau
Environmental Sciences Division
Department of Health and Environmental Sciences
Helena, Montana 59601
#
#
ACKNOWLEDGEMENTS
Darryl Maunder assisted with field work. Peter Gorman performed
all statistical calculations relating to periphyton community structure.
Rob Greene and Keith Kramlick performed algal assays. Chemical analyses
were conducted by the Chemistry Laboratory Bxireau of the Department of
Health and Environmental Sciences. This report was funded by the U.S.
Environmental Protection Agency under Section 208 of the 1972 Federal
Water Pollution Control Act Amendments. Wendy Anderson was the typist.
DISCLAIMER
Mention of trade names or commercial products does not constitute
endorsement or recommendation for use. This report has been reviewed
by the Montana Operations Office, U.S. Environmental Protection Agency,
and approved for publication -
- 1
»
t
ABSTRACT
Values for 31 biologically-related water quality parameters were
measured seasonally at 16 stations on 11 streams in northcentral Montana
from September 1977 to April 1978. Mean values for 15 key indicators
were used to develop a composite water quality rating based on bio-
logical conditions. Three stations had poor water quality from the
standpoint of stream biology: Big Sandy/ Muddy/ and Pondera Creeks.
All three suffered from heavy silt loads resulting from accelerated
stream bank erosion/ poor irrigation practices/ and natural causes.
Also/ nutrient levels were seasonally very high at these stations due
to agricultural runoff. Big Sandy and Pondera Creeks were affected
to a lesser extent by municipal discharges. Eleven other stations
were ranked as fair and were affected to varying degrees by non-point
source pollution. Two of these 11 stations — Milk River at Chinook and
Teton River near Dutton — also receive miinicipal discharges in need of
upgrading. Only two streams were rated as good: the Dearborn River
and the Missouri River at Cascade. On this basis / it was concluded
that non-point source pollution is the most serious / biologically de-
bilitating water quality problem at stations on the Northcentral Loop.
Survey results probably can be considered representative of overall
water quality in the lowland portions of northcentral Montana because
of similar water and land use practices.
•>
XI
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4
TABLE OF CONTENTS
§
*
ACKNOWLEDGEMENTS
DISCLAIMER
ABSTRACT
CONTENTS
PREFACE
INTRODUCTION
RATIONALE, METHODS, RESULTS, AND INTERPRETATIONS
Streamflow
Common Ions
Algal Nutrients
Algal Assay
Periphyton Production
Periphyton Community Structure
Macroinvertebrate Community Structure
SUMMARY AND CONCLUSIONS
LITERATURE CITED
RECENT REPORTS ON STREAM WATER QUALITY IN NORTHCENTRAL MONTANA . . .
APPENDIXES
A. Streams and Stations in the Montana Biological
Monitoring Network
B. Phosphate Concentrations
C. Total Phosphorus Concentrations
D. Nitrate Plus Nitrite Concentrations
E. Ammonia Concentrations
F. Kjeldahl Nitrogen Concentrations
G. Water Quality Requirements of Major Diatom Species . . . .
i
ii
iii
iv
1
4
6
9
14
19
27
38
46
51
54
55
57
58
59
60
61
62
- iii -
1
§
s
f
PREFACE
The importance of long term monitors is evident when
one considers the ecology of our biosphere, because it is
being increasingly manipulated and polluted by the civili-
zation of man. This is due to the increased population
which results in an increased demand for materials for life
and for habitation (Patrick, 1977) .
Tlie national goal of fishable and swimmable water by 1983 is sup-
ported by the fact that water quality that permits these uses is also
suitable for most other beneficial uses. This goal presxames that basic
biological communities and processes that permit these uses are main-
tained in a healthy balance. For example, it presumes that the small
aquatic animals that fish eat will be present in variety and abundance,
and it presumes that algae will not become a nuisance to boating,
swimming, and fishing. Until recently, basic biological processes
such as photosynthesis and aquatic life forms lower than fish had been
given little consideration in water quality planning and management,
yet these processes and life forms are basic to the integrity of the
entire aquatic ecosystem. Any effects here on the "ground floor" likely
' will have repercussions on up the food chain.
Chemical and physical properties of water affect living organisms
* in ways we are just beginning to understand. Aquatic organisms are
capable of integrating the many and diverse factors of their environ-
ment and of expressing their combined effect in terms of growth, repro-
ductive success, and diversity. Aquatic organisms vary in their sen-
sitivity to pollutants, hence some of the more sensitive and tolerant
taxa have become useful as water quality indicators. Lower life forms
are particularly useful as indicators because they are almost always
present in statistically significant munbers.
To maintain water quality for fish and aquatic life is public
policy of the State of Montana (Sec. 69-4801(1), R.C.M. 1947). Pollu-
tion is defined in part as "contamination, or other alteration of the
physical, chemical, or biological properties of any state waters ..."
(Sec. 69-4802(5), R.C.M. 1947). To measure our success at protecting
aquatic life and controlling pollution, we need a good yardstick. What
is a better yardstick than the biological organisms and processes them-
selves? Yet there has been no comprehensive, systematic, and continuing
biological monitoring to date in Montana.
The Montana Biological Monitoring Program is designed to help fill
this need. The program consists of a network of stations, a battery
of parameters, and a saitpling strategy.
XV
The network includes 79 stations on 60 streams statewide, selected
from completed water quality inventories and management plans (Water
Quality Bureau, 1976) on the basis of likely improvement or degradation
of water quality. Stations are grouped geographically into five loops,
each with about 16 stations. Streams and stations in the network are
listed in Appendix A. Sites monitored for biological parameters by the
U.S. Geological Survey were considered in station selection in order
to complement state and federal programs.
Data are gathered in seven biologically- related areas: streamflow,
common ions (including specific conductance and total alkalinity) , algal
nutrients, algal growth response to nutrient additions (algal assay) ,
periphyton production, periphyton community structure, and macroinver-
tebrate community structure.
Stations are monitored seasonally, once in summer, once in fall,
and once in spring. Ice has proven to be a serious impediment to sam-
pling. Consequently, winter sampling will not be pursued, even though
it is a season of stress for aquatic organisms.
Realistically, with available manpower, only one or two loops can
be monitored each year, hence each loop will be resampled every fourth
or fifth year. S\ibsequent reports will evaluate changes in water quality
over the intervening periods. Obviously, the program is not designed
for rapid detection of acute problems but rather for evaluation of chronic,
long-term trends.
Comments are welcome, especially now when the program is new. All
stations, parameters, and procedures are on trial and subject to con-
tinuing evaluation. If we have overlooked a stream of particular inter-
est to you, please let us know and give us your reasons why it should
be included in the network. We would also like your comments on the
overall usefulness of the program to you. It is hoped that these reports
will be more than just internal planning and management documents, and
that they will aid resource managers, municipalities, industries, and
laymen in assessing water quality conditions and trends in their area.
V
4
I
INTRODUCTION
This is the second in a continuing series of reports on biological
conditions in Montana rivers and streams .
Streams included in the Northcentral Loop of the Water Qualtiy
Bureau's Biological Monitoring Program are of many types. They range
from clear, nutrient poor, cold water trout streams to silt-laden,
nutrient rich, lowland streams. Most of the streams more closely ap-
proximate the latter category. In these streams, gradients and veloci
ties have been greatly reduced, sediment loads have accumulated, and
temperatures have increased over the miles traversed from their upland
origins. These are natural processes. However, agriculture, the econ-
omic base of northcentral Montana, has in many cases increased the
rate of these processes. Degradation of streams in northcentral Montana
results from sediment, dewatering, high temperature, nutrients, salinity,
coliforms, solid waste, and to a lesser extent, acid mine drainage and
oil spills (Water Quality Bureau, 1974, 1975).
The sixteen stream stations comprising this loop are listed in
Table 1, along with station locations and abbreviations used in sub-
sequent tables. Nine stations occur in the Missouri-Sun-Marias basin,
four are located in the Milk River basin, and the remaining three fall
within the Missouri-Smith basin.
Parameters covered in this report are listed in Table 2. An attempt
was made to collect all parameters seasonally, except common ions, which
v^ere restricted to the summer run (September 1977) . Late fall sampling
(December 1977) was greatly hindered by a winter storm, and heavy ice
formation on most of the streams resulted in much missing data. Also,
abnormally high flows during the spring (March 1978) , including some
n0ar record flows, caused additional problems and more missing data.
All future loops will be sampled earlier in the fall and spring to mini-
mize these problems, even though weather and stream discharge patterns
are never totally predictable.
The Northcentral Loop is scheduled to be sampled again in 1981-1982
or sooner, depending on available manpower and funds. At that time,
changes in values of the different parameters can be compared and evalu-
ation of long-term trends in water quality can begin. Also, missing
data points will be filled in and techniques refined to provide a more
complete and reliable information baseline. Meanwhile, the Water Quality
Bureau will strive to develop a comprehensive biological water quality
index to simplify the rating of streams and the evaluation of trends.
1
Table 1. Stream stations covered in this report
Code
Big Sandy Creek
Dearborn River
Lodge Creek
Marias River/Loma
Marias River/Shelby
Milk River/ Chinook
Milk River/Havre
Missouri River/Cascade
Missouri River/Ft. Benton
Muddy Creek
Pondera Creek
Smith River
Sun River /Ft. Shaw
Sun River/Vaughn
Teton River/Dutton
Teton River/Ft. Benton
Description
Big Sandy Creek near mouth
Dearborn River near mouth
Lodge Creek near Chinook
Marias River near Loma
Marias River south of Shelby
Milk River near Chinook
Milk River near Havre
Missouri River near Cascade
Missouri River at Fort Benton
Muddy Creek near Vaughn
Pondera Creek near mouth
Smith River near Ulm
Sun River near Fort Shaw
Sun River below Vaughn
Teton River north of Dutton
Teton River near Fort Benton
Location
T32N RISE 5DCC
T16N R03W 13 ACC
T33N R19E 26BCA
T25N R09E 2DDB
T31N R02W 20DBD
T33N R19E 34ACA
T32N R16E 6DAD
T17N ROIW 35ACC
T24N ROSE 26ACB
T21N ROIE 24DAC
T29N ROSE ISDAD
T19N R02E 14CCD
T20N R02W 2DDA
T21N R02E 30BCA
T2SN ROIW ISBBA
T24N ROSE 9DCC
2
Table 2 .
Parameters covered in this report
Instantaneous Streamflow (m /sec)
Common Ions
-Cation Ratio: Ca:Mg:Na
-An ion Ra tio : HCO ^ : SO : Cl
-Specific Conductance (micromhos @ 25 C)
-Total Alkalinity (mg/1 CaCO^)
Algal Nutrients
-NO +N0 -N; NH^-N; Kjeldahl-N; PO^-P;
Total P (all in mg/1)
-Total Soluble Inorganic Nitrogen (NO^+NO^-N plus NH^-N) :
PO -P Ratio
-TSIN and Total P as % of recommended maximum instream levels
(0.35 mg/1 TSIN and 0.05 mg/1 Total P)
Algal Assay
-Control
Mean Maximum Standing Crop (MMSC) (mg/1)
Statistical significance of MMSC
Limiting Nutrient
-Nutrient Spike
Mean Maximum Standing Crop (MMSC) (mg/1)
Statistical significance of MMSC
Limiting Nutrient
Periphyton Production 2
-Chlorophyll £ Accrual ^ (mg/m /day)
-Biomass Accrual (mg/m /day)
-Autotrophic Index
-Chlorophyll a/Pheophytin ^ Ratio (OD663 /OD663^)
-Carotene/Chlorophyll Ratio (OD430/OD663)
Periphyton Community Structure
-Rank of diatoms relative to other algae
-Percent Relative Abundance (PRA) of Major Diatom Species
-PRA Achnanthes species and Nitzschia species
-Number of Diatom Species _
-Diatom Species Diversity (d)
Macroinvertebrate Community Structure
-Mean PRA Major Macro invertebrate Orders
-Mean PRA Tolerant, Facultative and Intolerant Macro-
invertebrates
-Number of Macroinvertebrate Genera _
-Macroinvertebrate Genus Diversity (d)
-Number of Macro invertebrates collected per unit
effort sample time
3
RATIONALE, METHODS, RESULTS, AND INTERPRETATIONS
STREAMFLOW
Rationale
Accurate measurements of streamflow are essential for calculating
loads of dissolved constituents, particularly nutrients. Many aquatic
organisms have specific instream flow requirements for various activi-
ties. Exceptionally high and low flows — overbank flooding and complete
dewatering in the extremes — are rather traumatic events for a river and
its aquatic life. Periodic streamflow measurements also circumscribe
a stream's size, which in turn dictates the nature of the aquatic com-
munity it can support.
Methods
Flow rates were measured with a Pygmy current meter in small streams
and with a Price Type AA current meter in the larger streams. A straight
section of stream with a uniform cross-section and a smooth bottom was
chosen whenever available. A measuring tape was stretched across the
channel and depths and velocities were recorded at selected points such
that no more than 10 percent of the total discharge fell between two
consecutive points. Total instantaneous discharge was then estimated
by summing flows for each of the measured subsections. Streamflow mea-
surements were provided by the U.S. Geological Survey for the following
streams: Big Sandy Creek, Marias River/Shelby, Milk River/Havre, Missouri
River/Fort Benton, Pondera Creek, Sun River/Vaughn, and Teton River/Dutton.
Results
Instantaneous streamflows are presented in Table 3.
4
Table 3.
Instantaneous Streamflow (m /sec)
Station
Summer
Fall
Spring
Mean
Big Sandy Creek
0.00
FNM (ICE)
141.50
70.
75
Dearborn River
0.57
FNM (ICE)
6.99
3.
78
Lodge Creek
0.03(E)
FNM (ICE)
FNM
0.
03
Marias River/Loma
FNM
FNM (ICE)
FNM
FNM
Marias River/Shelby
4.22
5.09
52.07
20.
46
Milk River/ Chinook
0.68
FNM (ICE)
FNM
0.
68
Milk River/Havre
0.74
0.42
155.65
52.
27
Missouri River/Cascade
85.19 (E)
169.00(E)
200.00(E)
151.
40
Missouri River/Ft. Benton
108.39
169.23
261.78
179.
,80
Muddy Creek
3.65
1.42(E)
2.21
2.
.43
Pondera Creek
0.00
0.01
50.94
16.
.98
Smith River
2.63
6.46(E)
FNM
4.
.54
Sun River/Ft. Shaw
1.36
2.26(E)
7.75
3.
.79
Sun River/Vaughn
5.52
4.24(E)
11.52
7.
.09
Teton River/Dutton
0.62
1.73
6.03
2
.79
Teton River/Ft. Benton
0.57
FNM (ICE)
FNM
0
.57
Mean
14.28
35.99
81.49
40
.85
FNM: Flow not measured
(E) : Estimate
5
Interpretation
Streamflow measurements are spotty for the fall sampling run in par-
ticular because of problems with ice. Most data for this period are based
on U.S. Geological Survey records. Some flows are recorded as estimates
because of poor gaging conditions or because U.S. Geological Survey mea-
surement sites varied somewhat from our stations. Missing data for the
spring run are the result of extremely high water or the lack of U.S.
Geological Survey gages near our stations.
On the average, spring flows were highest, followed by fall and then
summer flows. Many of the streams within the Northcentral Loop are sub-
ject to extremely large seasonal discharge fluctuations. This results
from heavy spring runoff into upland tributaries and/or flow regulation
by flood control and irrigation structures such as Fresno dam on the Milk
River. For example. Big Sandy Creek varied from a stagnant condition
in summer to 141.5 m^/sec in spring. At this time, Big Sandy Creek was
contributing roughly 90 percent of the Milk River's flow at Havre.
COMMON IONS
Rationale
Common ions are the basic ingredients of the chemical "soup" in
which aquatic organisms live. Their relative proportions often dictate
the nature of plant and animal communities inhabiting surface waters.
Specific conductance is a measure of osmotic stress on organisms — both
aquatic and terrestrial — that live in, drink of, or are irrigated by
the water in question. Total alkalinity measures the acid-neutralizing
capacity of water. It is, thus, an indicator of a water's resiliency to
acid and heavy metals pollution. It is also roughly proportional to a
water's basic fertility or productivity.
Methods
Unpreserved and unfiltered grab samples were collected in one liter
plastic bottles and transported xander ice back to the laboratory. Analy-
tical procedures followed the American Public Health Association (1971;
1975) or the U.S. Environmental Protection Agency (1974) . Specific con-
ductance was measured with a Wheatstone Bridge. Calcium and magnesium
were measured by EDTA titration. Sodixxn was measured by atomic absorp-
tion. Bicarbonate and total alkalinity were measured by the automated
methyl orange method or by titration with 0.02 N H^SO^ to a pH 4.5 end-
point. Sulfate was determined by the automated turbidimetric method.
Chloride was measured by the automated mercuric thiocyanate method or
by mercuric nitrate titration.
6
Results
Common ion ratios and conductance and alkalinity values for the
summer 1977 sampling run are presented in Table 4.
Interpretation
Streams of the Northcentral Loop, as determined from summer samples
at the sixteen stations, can be divided into five major chemical types:
calcium bicarbonate, magnesium sulfate, sodium sulfate, sodium bicarbon-
ate, and calcium sulfate, in descending order of frequency. Lodge Creek
had a mixed type of water containing sodium, calcium, and magnesium,
and bicarbonate and sulfate in roughly the same proportions.
Only two streams. Big Sandy and Pondera Creeks, had unusually high
specific conductance values. Both were in excess of 3,000 micromhos.
As such, these waters would be questionable for irrigation of crops
(E.P.A., 1973), but probably would not be responsible for a reduction
in the diversity of stream organisms. In both cases, the conductivities
were associated with disproportionately high sulfate ion concentrations.
It should be noted that both streams were sampled during stagnant periods
when water was restricted to small isolated pools. This is common on
both streams much of the year, resulting in high specific conductance
values through concentration of dissolved substances. However, such
values are not of much consequence since irrigation is unlikely along
these streams due to their low flows. The remaining streams had specific
conductance values suitable for irrigation and most other beneficial uses
(E.P.A., 1973). However, other factors such as sediment, substrate, tem-
perature, and flow are much more crucial for instream biological uses.
7
Table 4
Specific Conductance (umhos @ 25°C) , Total Alkalinity
(mg/1 CaCO^) , and common ion ratios (as meq/1)
Station
Specific
Conductance
Total
Alkalinity
Ca:Mg:Na
HC0,:S0, :C1
Big Sandy Creek
3431
496
1:1:4
1:3:1
Dearborn River
371
164
3:2:1
38:10:1
Lodge Creek
1145
328
1:1:1
19:18:1
Marias River/Loma
669
144
1:1:1
16:26:1
Marias River/Shelby
533
140
2:1:1
19:18:1
Milk River/Chinook
625
201
1:1:2
7:4:1
Milk River/Havre
474
150
2:1:2
9:6:1
Missouri River/Cascade
396
147
3:1:1
10:3:1
Missouri River/Ft. Benton 480
201
3:2:1
11:6:1
Muddy Creek
909
251
1:2:1
26:28:1
Pondera Creek
3130
233
1:1:1
5:41:1
Smith River
384
159
4:3:1
22:6:1
Sun River/Ft. Shaw
728
244
2:2:1
41:30:1
Sun River/Vaughn
918
244
1:2:1
25:31:1
Teton River/Dutton
767
193
1:2:1
20:25:1
Teton River/Ft. Benton
1119
205
1:1:1
8:28:1
Mean
1005
219
8
ALGAL NUTRIENTS
Rationale
Nitrogen and phosphorus are the two elements most commonly limiting
algal growth in lakes and streams. Phosphorus is usually limiting in
lakes because many common lake algae can use atmospheric nitrogen.
Nitrogen- fixers are not common in streams, therefore, this element is
more often a limiting nutrient in flowing water. Only the soluble in-
organic forms of these two nutrients — nitrate, nitrite and ammonia
nitrogen and ortho-phosphate — are readily available for plant uptake.
The sum of the soluble inorganic nitrogen fractions is called total
soluble inorganic nitrogen or TSIN.
Some indication of whether nitrogen or phosphorus is growth limiting
may be obtained by determining the weight ratio of the appropriate forms
of nitrogen and phosphorus found in a river, and comparing that with the
stoichiometric ratio required for growth (Zison ^ al. , 1977) . Specifi-
cally, let
^ (TSIN)
(PO4-P)
where (TSIN) equals the concentration of total soluble inorganic nitrogen
as N in mg/1 and (PO^-P) equals the concentration of phosphate as P in
mg/1. If R is greater than 10, phosphorus is more likely limiting than
nitrogen. If R is less than 5, nitrogen is more likely limiting than
phosphorus. If R is less than 10 but greater than 5, it's a tossup as
to which one is limiting. (See Table 5)
Nuisance growths of aquatic plants in streams usually can be avoided
if total phosphorus is kept below 0.05 mg/1 as P (Mackenthun, 1969) and
if TSIN remains less than 0.35 mg/1 as N (Muller, 1953). The phosphorus
criterion is particularly applicable if the stream enters a standing body
of water, which is eventually true of all streams in the Northcentral
Loop. If instream phosphorus and TSIN values are computed as a percentage
of these critical levels, as they are in Tables 6 and 7, the algae growth
potential of these waters can be assessed. Nuisance growths can be ex-
pected where both P and TSIN are significantly greater than 100 percent
of the critical levels, other factors being amenable to algae growth.
Methods
Unfiltered grab samples were collected in separate one liter plastic
bottles, each preserved with 4 ml of HgCl2 and transported under ice back
to the laboratory. Analytical procedures followed the American Public
Health Association (1971; 1975) or the U.S. Environmental Protection
Agency (1974) . Orthophosphate was measured by automated ascorbic acid
9
reduction. Total phosphorus was determined by persulfate digestion fol-
lowed by automated ascorbic acid reduction. Nitrate plus nitrite nitro-
gen was measured by the hydrazine reduction method. (Future analyses
will be done by the automated cadmium reduction method.) Ammonia was
measured by the automated phenolate method. Total Kjeldahl nitrogen was
determined by manual digestion followed by the automated phenolate pro-
cedure .
Results
Measured algal nutrient levels for the 1977-1978 sampling season
are listed in Appendixes B through F. TSIN-phosphate phosphorus ratios
are presented in Table 5. Tables 6 and 7 give instream TSIN and total
phosphorus values as percentages of maximum recommended instream concen-
trations.
Interpretation
From the nutrient ratios in Table 5, it appears that northcentral
Montana streams are generally nitrogen limited in summer. Nutrient
limitations in spring are variable or not determinable because of inter-
mediate ratios, i.e. , 10>R>5. The few data points for the fall run are
not sufficient to draw any general conclusions, although they suggest
phosphorus limitation at this time of year. Based on pooled data, seven
streaiiis are phosphorus limited: Marias River/Loma, Missouri River/Fort
Benton, Muddy Creek, both Sun River stations, and both Teton River sta-
tions. On the other hand. Big Sandy Creek, Lodge Creek, Pondera Creek,
the Smith River, and both Milk River stations appear to be nitrogen
limited. The remaining three streams have intermediate ratios and must
await confirmation from the algal assay tests. These interpretations
are based on averages which do not express the evident seasonal vari-
ability. All but four streams — the Dearborn River, Missouri River at
Cascade, the Sun River near Fort Shaw, and the Teton River near Dutton
had nitrogen and phosphorus levels significantly in excess of recommended
instream concentrations during the spring sample run (Tables 6 and 7) .
This enrichment results from agricultural runoff.
These twelve streams would be capable of producing nuisance algal
growths at this time of year assuming other growth factors were favorable.
However, high turbidities and scouring effectively inhibit such blooms in
spring. On the other hand, when growth conditions are more favorable,
such as in summer, none of the stream sites examined had both nitrogen
and phosphorus values exceeding recommended levels. Muddy Creek and the
Sun River below Muddy Creek border on the capacity to produce algal
blooms in summer given slightly greater concentrations of phosphorus.
But again, the tremendous sediment load and resultant turbidity contri-
buted by Muddy Creek to the Sun River would probably restrict algal
growth at both sites.
10
Table 5.
Ratio of total soluble inorganic nitrogen (NO^+NO^-N
plus NH^-N) to phosphate phosphorus (PO^ as mg/1 P)
Mean
Station
Summer
Fall
Spring
(Pooled)
Big Sandy Creek
1:1
ICE
2:1
2:1
Dearborn River
<1:1
20:1
8:1
9:1
Lodge Creek
<1:1
ICE
7:1
3:1
Marias River/Loma
<1:1
ICE
10:1
10:1
Marias River/Shelby
1:1
ICE
7:1
7:1
Milk River/Chinook
<1:1
ICE
2:1
2:1
Milk River /Havre
110:1
ICE
2:1
3:1
Missouri River/Cascade
<1:1
9:1
7:1
7:1
Missouri River/Ft. Benton <1:1
ICE
8:1
10:1
Muddy Creek
>500:1*
ICE
56:1
>64:1
Pondera Creek
40:1
ICE
4:1
4:1
Smith River
<1:1
ICE
2:1
2:1
Sun River/Ft. Shaw
520:1
1070:1
25:1
200:1
Sun River/Vaughn
172:1
ICE
20:1
39:1
Teton River/Dutton
<1:1
240:1
6:1
19:1
Teton River/Ft. Benton
<1:1
375:1
8:1
16:1
Mean*
>9:1
83:1
8:1
>9:1
(Pooled)
*Insuf f icient sample. Actual value not determined.
11
Table 6. Total soluble inorganic nitrogen (NO^+NO^-N plus NH^-N) as
a percentage of the recommended maximum xnstream level (0.35 mg/1)
Station
Summer
Fall
Spring
Mean
Big Sandy Creek
3
ICE
146
74
Dearborn River
<3
6
20
9
Lodge Creek
17
ICE
246
132
Marias River /Loma
<3
ICE
186
93
Marias River/Shelby
3
ICE
263
133
Milk River/Chinook
<3
ICE
163
82
Milk River/Havre
31
ICE
143
87
Missouri River/Cascade
<3
74
46
40
Missouri River/Ft. Benton <3
ICE
126
63
Muddy Creek
>286*
ICE
1651
>968
Pondera Creek
11
ICE
234
122
Smith River
<3
ICE
60
30
Sun River /Ft. Shaw
146
265
43
151
Sun River/Vaughn
246
ICE
220
233
Teton River/Dutton
<3
274
103
126
Teton River/Ft. Benton
<3
214
189
134
Mean*
>29
167
240
>139
♦Insufficient sample. Actual value not determined.
12 -
Table 7.
Total phosphorus as a percentage of the
recommended maximum instream level (0.05 mg/1)
Station
Summer
Fall
Spring
Mean
Big Sandy Creek
78
ICE
1180
629
Dearborn River
6
10
30
15
Lodge Creek
440
ICE
670
555
Marias River/Loma
24
ICE
1918
971
Marias River/Shelby
78
ICE
806
442
Milk River/Chinook
220
ICE
3340
1780
Milk River/Havre
28
ICE
1776
902
Missouri River/Cascade
36
80
86
67
Missouri River/Ft. Benton
118
ICE
466
292
Muddy Creek
74
ICE
1052
563
Pondera Creek
38
ICE
6760
3399
Smith River
48
ICE
872
460
Sun River/Ft. Shaw
36
16
44
32
Sun River/Vaughn
90
ICE
246
168
Teton River/Dutton
46
40
732
273
Teton River/Ft. Benton
26
40
1700
589
Mean
87
37
1355
628
13 -
ALGAL ASSAY
Rationale
The algal assay is based on Liebig's law of the minimum, which states
that "growth is limited by the substance that is present in minimal quan-
tity with respect to the needs of the organism" (U.S. E.P.A., 1971).
Algal assays are used: 1) to confirm or refute conclusions regarding
limiting nutrients based on N/P ratios; 2) to determine biologically
the availability of algal growth- limiting nutrients; 3) to quantify
biological response to change in concentrations of algal growth-
limiting nutrients; and 4) to determine whether various compounds or
water samples are toxic or inhibitory to algae. The basic reasons for
including algal assays in this monitoring program are to determine each
stream's algal growth potential and sensitivity to additions of algal
nutrients.
Methods
Algal assays were conducted following "bottle test" procedures pub-
lished by the U.S. Environmental Protection Agency (1971) . The unicellular
green alga Selenastrum capricornutum Printz was used as the test alga.
Combined nutrient spikes consisted of 0.10 mg/1 P plus 1.00 mg/1 N.
(Spikes with a chelating agent, i.e., EDTA, to test for algal growth
inhibition by heavy metals, were not applied in this instance, but will
be applied in all future assays.) Three replicates were run on each
treatment, i.e., control and combined nutrient spike. Maximum standing
crop was measured and reported in terms of mg/1 dry weight, averaged over
the three replicates. Theoretical maximum standing crop (TMSC) was deter-
mined by multiplying measured ortho-P and TSIN values by the appropriate
production coefficient (430 and 38, respectively) and by taking the lesser
of the two resulting values. Statistical reliability of mean maximum
standing crop (MMSC) results as compared to theoretical maximum standing
crop (TMSC) was determined from coefficient of variance criteria presented
by Miller ^ al . (1978) :
+ 50% for TMSC <1.00 mg/1
+ 30% for TMSC >1.00 but <3.00 mg/1
+ 20% for TMSC >3.00 but <10.00 mg/1
+ 10% for TMSC >10.00 mg/1
Low MMSC values that are significantly different could be due to:
1) micronutrients limiting; 2) something toxic or inhibitory in the water
sample; and/or 3) nutrients incorrectly overestimated in analysis. High
values that are significantly different could be the result of incorrectly
underestimating nutrients in analysis.
14
Results
Algal assay results for summer and fall 1977 and spring 1978 are
presented in Tables 8, 9, and 10, respectively.
Interpretation
The algal assay data substantiate or clarify the nutrient limitation
predictions based on nitrogen to phosphorus ratios. Of these two nutrients,
nitrogen was in short supply (limiting) in the assay water relative to the
needs of the test alga (Selenastrum capricornutum) for the following
streams: Marias, Missouri, and Smith rivers. Lodge and Big Sandy creeks,
and the Milk River at Chinook. Phosphorus was limiting in the Sun River
and Muddy Creek. In the remaining five streams, nitrogen and phosphorus
exchange the role of limiting nutrient from season to season or they are
co-limiting. More complete data for the fall period would help to clarify
seasonal nutrient availability trends.
15 -
Table 8. Algal assay results, Sunuiver 1977
CONTROL
NUTRIENT SPIKE
Station
Mean
Mciximum
Standing
Crop
(mg/1)
Signi-
ficantly
Different
from
TMSC?
Limiting
Nutrient
Mean
Maximum
Standing
Crop
(mg/1)
Signi-
ficantly
Different
from
TMSC?
Limiting
Nutrient
Big Sandy Creek
0.27
NO
N
39.36
NO
N
Dearborn River
1.35
YES-High
N or P
50.82
YES-High
N
Lodge Creek
0.83
YES-Low
N
45.60
YES-High
N
Marias River/Loma
0.44
NO
N
45.22
YES-High
N
Marias River/Shelby
0.37
NO
N
37.66
NO
N
Milk River/Chinook
3.49
YES-High
N
41.09
NO
N
Milk River/Havre
0.35
NO
P
41.54
NO
N
Missouri River/Cascade
0.56
NO
N
39.86
NO
N
Missouri River/Ft. Benton
0.43
NO
N
40.13
NO
N
Muddy Creek
4.34
YES-High
P
55.33
YES-High
P
Pondera Creek
0.26
NO
P
4.00
YES-Low
N
Smith River
0.38
NO
N
38.48
NO
N
Sun River/Ft. Shaw
0.48
NO
P
54.18
YES-High
P
Sun River/Vaughn
0.49
YES-Low
P
48.05
NO
P
Teton River/Dutton
0. 38
NO
N
36.67
NO
N
Teton River/Ft. Benton
0.30
NO
N
33.41
YES-Low
N
16 -
Table 9. Algal assay results. Fall 1977
Station
Big Sandy Creek
Dearborn River
Lodge Creek
Marias River/Loma
Marias River/Shelby
Milk River/Chinook
Milk River/Havre
Missouri River/Cascade
Missouri River/Ft. Benton
Muddy Creek
Pondera Creek
Smith River
Sun River/Ft. Shaw
Sun River/Vaughn
Teton River/Dutton
Teton River/Ft. Benton
CONTROL NUTRIENT SPIKE
Mean Signi- Mean Signi-
Maximum ficantly Maximum ficantly
Standing Different Standing Different
Crop from Limiting Crop from Limiting
(mg/1) TMSC? Nutrient (mg/1) TMSC? Nutrient
ICE ICE
0.38 NO P 42.67 NO N
ICE ICE
ICE ICE
ICE ICE
ICE ICE
ICE ICE
7.18 YES-LOW N 63.36 YES-High N
ICE ICE
ICE ICE
ICE ICE
ICE ICE
0.30 NO P 65.66 YES P
ICE ICE
0.36 YES-LOW P 62.1 YES-High P
0.32 YES-LOW P 67.32 YES-Low P
17 -
Table 10. Algal assay results. Spring 1978
CONTROL NUTRIENT SPIKE
Mean
Maximum
Standing
Crop
Signi-
ficantly
Different
from
Limiting
Mean
Maximum
Standing
Crop
Signi-
ficantly
Different
from
Limiting
Station
(mg/1)
TMSC?
Nutrient
(mg/1)
TMSC?
Nutrient
Big Sandy Creek
16.92
YES -Low
N
70.87
YES-High
N
Dearborn River
0.49
NO
N
79.92
YES-High
N
Lodge Creek
11.13
YES-Low
N
71.88
YES-High
N
Marias River/Loma
12.42
YES-LOW
N
73.56
YES-High
N
Marias River/Shelby
24.69
NO
N
87.61
YES-High
N
Milk River/Chinook
12.55
YES-Low
N
81.85
YES-High
N
Milk River/Havre
-SAMPLE LOST-
•SAMPLE LOST—
Missouri River/Cascade
4.52
YES-Low
N
60.03
YES-High
N
Missouri River/Ft. Benton
3.65
YES-Low
N
71.60
YES-High
N
Muddy Creek
65.56
YES-High
P
65.70
YES-Low
P
Pondera Creek
33.74
NO
N
103.60
YES-High
N
Smith River
22.46
YES-High
N
76.20
YES-High
N
Sun River/Ft. Shaw
0.66
YES-Low
P
83.66
YES-High
N
Sun River/Vaughn
2.55
YES-Low
P
8.06
YES-Low
P
Teton River/Dutton
-SAMPLE LOST-
-SAMPLE LOST-
Teton River/Ft. Benton
14.04
NO
N
81.59
NO
N
18 -
PERIPHYTON PRODUCTION
Rationale
Periphyton is the conununity of plants and animals, most of them
microscopic, living attached to or in close proximity of the stream
bottom. In terms of primary production — converting solar energy to
plant biomass — it is the most important community in the majority of
Montana streams.
Measuring the growth of periphyton organisms on artificial sub-
strates placed in a stream is one method of estimating the productive
potential of the stream. The two parameters most commonly measured
are chlorophyll a (the most significant photosynthetic pigment) and
ash-free weight or biomass. Measurements of these parameters have
been made on a great variety of surface waters worldwide and in
Montana. Chlorophyll accrual rates in Montana streams have been
summarized by Klarich (1976). An assessment of a streams' trophic
status can be made by comparing its rate of accrual to rates in other
waters known to be oligotrophic, mesotrophic or eutrophic.
The autotrophic index (AI) is the mass ratio of biomass to chlor-
ophyll a. Chlorophyll a usually contributes from 1 to 2 percent of
algal dry weight, resulting in AI values of 50 to 100 in pure algal
cultures. As a stream is enriched with organic compounds, the pro-
portion of consuming, non- chlorophyll bearing organisms increases and
the fraction of autotrophic, chlorophyll bearing organisms (algae)
decreases. Unpolluted stream AI values normally range from 50 to 200.
Larger AI values indicate poor water quality (A.P.H.A., 1975).
The amount of pheophytin ^ in a periphyton sample relative to the
amount of chlorophyll ^ is an indicator of the physiological condition
of the algae. Pheophytin a. is derived from chlorophyll £ upon break-
down and loss of magnesium ion. Acidification in the laboratory has
the same effect. Acidification of a solution of pure chlorophyll a
results in a 40 percent reduction in optical density, yielding a
before/after acidification ratio of about 1.7. Field samples with a
ratio of 1.7 are considered to contain little if any pheophytin ^ and
to be in excellent physiological condition. Solutions of pure pheophy-
tin show no reduction in optical density upon acidification and have
a before/after ratio of 1.0. Thus, mixtures of chlorophyll a_ and pheo-
phytin a have optical density ratios ranging between 1.0 and 1.7
(A.P.H.A. , 1975).
The ratio of yellow pigment (carotene) to green pigment (chloro-
phyll) in a sample of mixed algae can be used as an index of community
stability and productivity (Margalef, 1969) . In young, vigorously
growing algal communities, the green photosynthetic pigment chlorophyll
a predominates and the yellow to green optical density ratio is low,
19
usually about 2. As the community ages and becomes more diversified,
yellow pigments predominate and the yellow to green ratio increases
to 3 or greater (Odum, 1963) .
Methods
Artificial substrates (glass microscope slides) were used to
measure the accrual of periphyton pigments and biomass. The slides
were placed in a plastic carriage (Periphytometer II) produced by
Design Alliance, Inc. of Cincinnati, Ohio. The carriage and slides
ensemble was tied to a cement cinder block, which served as an anchor.
The sampling device was placed in water of moderate current velocity
(0.1 to 0.5 m/sec) and moderate depth (0.3 to 1.0 m) such that the
slides were oriented vertically with their surfaces perpendicular to
the direction of flow. The slides were exposed from 13 to 28 days
depending on season, water temperature, and inherent productivity.
Upon retrieval, the slides were removed from the carriage and
immediately placed into light-proof slide boxes. The boxes were
labeled and transferred to the laboratory on ice. On arrival at the
lc±>, the boxes were placed in a freezer for at least 24 hours to
enhance cell lysis.
Pigment extraction and measurement were then performed according
to the American Public Health Association (1975) with the following
procedural exceptions. Periphyton was scraped into 50 ml, foil-
wrapped centrifuge tubes. For each slide scraped, 10 ml of 90 per-
cent acetone-10 percent saturated MgCO, solution was added to the
tube. Usually, one sample consisted of scrapings from 4 slides, con-
sequently, the total acetone volxome equalled 40 ml. The tubes were
placed in a sonic bath for at least 20 minutes to aid pigment extrac-
tion and then allowed to steep for at least 24 hours in the dark
under refrigeration at 4°C. Pigment optical density readings were
made with a Perkin-Elmer Model 200 Spectrophotometer at a resolution
setting of 1.0 nanometer.
Biomass determinations were also made according to the A.P.H.A.
(1975) with the following variations. Biomass and chlorophyll were
measured on separate slides for the summer 1977 rion but the same
material was used for both measurements during the spring 1978 run.
Inconel alloy metal crucibles were used. Prior to placing the samples
in the drying oven, the acetone was evaporated under a bank of sun
lamps.
Results
Tables 11 through 15 contain chlorophyll a accrual rates, biomass
accrual rates, autotrophic index values, chlorophyll a/phoophytin a
ratios, and carotene/chlorophyll ratios, respectively. Analysis for
the last parameter was begun only in spring and results are incomplete.
- 20
Interpretation
Chlorophyll a accrual rates in streams of northcentral Montana
averaged from 0.11 to 2.59 mg/m^/day (Table 11) . Klarich (1976) re-
ported mean accrual values ranging from 0.7 at Laurel to 12.2 at
Huntley for a stretch of the Yellowstone River he describes as
"mesotrophic". Ingman (1978) found accrual rates averaging 3.1 for
a moderately enriched section of Prickly Pear Creek below the Helena
sewage treatment plant discharge. At the other extreme, Bahls (1978)
found two very oligotrophic streams in northwestern Montana to have
mean chlorophyll a accrual rates of 0.13 and 0.14 mg/m^/day. Streams
of the Northcentral Loop thus might be rated oligotrophic to meso-
trophic, with the Marias River near Shelby least productive in terms
of chlorophyll a accrual. However, realistic comparisons between
streams cannot be drawn because of the many missing data points.
Mean biomass accrual rates in streams of the Northcentral Loop
ranged from a low of 134 mg/m /day in the Marias River near Shelby
to a high of 431 mg/m^/day in Muddy Creek (Table 12) . Klarich (1976)
reported extreme values of 50 and 730 mg/m^/day in the Yellowstone
River above and below Billings, respectively. Ingman (1978) reported
a mean biomass accrual rate of 338 mg/m^/day for Prickly Pear Creek.
Bahls (1978) found mean biomass accrual rates of 115 and 102 mg/m^/day
for the two oligotrophic northwestern Montana streams. Normal bio-
mass production rates for streams range from 300 to 4,100 mg/m2/day
according to Whittaker (1970) . Consequently, biomass accrual in north-
central Montana streams falls toward the low end of the stream pro-
ductivity spectrum, substantiating the oligotrophic to mesotrophic
classifications applied on the basis of chlorophyll a accrual. Again,
caution should be used because of missing data and because existing
stream vegetation may compete with colonizing algae for available nu-
trients .
Mean autotrophic index values ranged from 400 (Sun River/Vaughn)
to 1,247 (Marias River/Shelby). Mean values for all 16 stations indi-
cate poor water quality. However, the summer figures are suspected
to be unnaturally high due to faulty procedures. With the few remain-
ing data points, very little can be said with confidence in the inter-
pretation of these results.
Mean chlorophyll a/pheophytin a ratios ranged from 1.58 (Missouri
River/Cascade) to 1.74 (Smith River) with an overall mean of 1.68
(Table 14). This indicates that the physiological condition of
algae colonizing artificial substrates in northcentral Montana streams
is good.
"Yellow/green" or carotene/chlorophyll ratios were between 6.85
and 10.41 (Table 15). All the values signify stable, mature floras.
However, figures are available only for the spring run of five streams.
Therefore, seasonal and station- to-station comparisons cannot be made.
21 -
Table 11. Chlorophyll a_ accrual (mg/m^/day)
Station
Summer
Fall
Spring
Mean
Big Sandy Creek
DNA
DNA
DNA
DNA
Dearborn River
.25
DNA
.08
.16.
Lodge Creek
.34
DNA
DNA
.34
Marias River/Loma
DNA
DNA
DNA
DNA
Marias River/Shelby
.11
DNA
DNA
.11
Milk River/Chinook
. 35
DNA
DNA
.35
Milk River/Havre
DNA
DNA
DNA
DNA
Missouri River/Cascade
DNA
DNA
2.59
2.59
Missouri River/Ft. Benton
DNA
DNA
DNA
DNA
Muddy Creek
.64
DNA
DNA
.64
Pondera Creek
DNA
DNA
DNA
DNA
Smith River
.52
DNA
DNA
.52
Sian River/Ft. Shaw
.44
DNA
.15
.30j
Sun River/Vaughn
.40
DNA
.99
.65
Teton River/Dutton
.94
DNA
.10
.52
Teton River/Ft. Benton
DNA
DNA
DNA
DNA
Mean
.44
DNA
.78
.56
DNA: Data not available
Table 12. Biomass accrual (mg/m^/day)
Station
Summer
Fall
Spring
Mean
Big Sandy Creek
DNA
DNA
DNA
DNA
De a rbo r n River
213
DNA
65
139
Lodge Creek
148
DNA
DNA
148
Marias River/Loma
DNA
DNA
DNA
DNA
Marias River/Shelby
134
DNA
DNA
134
Milk River/Chinook
414
DNA
DNA
414
Milk River/Havre
DNA
DNA
DNA
DNA
Missouri River/Cascade
DNA
DNA
198
198
Missouri River/Ft. Benton
DNA
DNA
DNA
DNA
Muddy Creek
431
DNA
DNA
431
Pondera Creek
DNA
DNA
DNA
DNA
Smith River
398
DNA
DNA
398
Sun River/Ft. Shaw
371
DNA
49
210
Sun River/Vaughn
231
DNA
212
195
Teton River/Dutton
611
DNA
30
320
Teton River/Ft. Benton
DNA
DNA
DNA
DNA
Mean
328
DNA
111
250
DNA: Data not available
23 -
Table 13. Autotrophic Index
Station
Summer*
Fall
Spring**
Mean
Big Sandy Creek
DNA
DNA
DNA
DNA
Dearborn River
847
DNA
782
814
Lodge Creek
430
DNA
DNA
430
Marias River/Loma
DNA
DNA
DNA
DNA
Marias River/Shelby
1247
DNA
DNA
1247
Milk River/Chinook
1245
DNA
DNA
1245
Milk River/Havre
DNA
DNA
DNA
DNA
Missouri River/Cascade
1048
DNA
77
562
Missouri River/Ft. Benton
DNA
DNA
DNA
DNA
Muddy Creek
679
DNA
DNA
679
Pondera Creek
DNA
DNA
DNA
DNA
Smith River
646
DNA
DNA
646
Sun River/Ft. Shaw
841
DNA
329
585
Sun River/Vaughn
577
DNA
224
400
Teton River/Dutton
652
DNA
308
480
Teton River/Ft. Benton
DNA
DNA
DNA
DNA
Mean
821
DNA
344
662
DNA: Data not available
*Biomass and chlorophyll measurements on separate slides
**Biomass and chlorophyll measurements on same slide (s)
24 -
Table 14. Chlorophyll a/Pheophytin ^ ratio (OD 663j^/OD 663^)
Station
Summer
Fall
Spring
Mean
Big Sandy Creek
DNA
DNA
DNA
DNA
Dearborn River
1.72
DNA
1.58
1.65
Lodge Creek
1.90
DNA
DNA
1.90
Marias River/Loma
DNA
DNA
DNA
DNA
Marias River/Shelby
1.73
DNA
DNA
1.73
Milk River/ Chinook
1.65
DNA
DNA
1.65
Milk River/Havre
DNA
DNA
DNA
DNA
Missouri River/Cascade
1.43
DNA
1.72
1.58
Missouri River/Ft. Benton
DNA
DNA
DNA
DNA
Muddy Creek
1.65
DNA
DNA
1.65
Pondera Creek
DNA
DNA
DNA
DNA
Smith River
1.74
DNA
DNA
1.74
Sun River/Ft. Shaw
1.64
DNA
1.58
1.61
Sun River/Vaughn
1.73
DNA
1.70
1.72
Teton River/Dutton
1.61
DNA
1.63
1.62
Teton River/Ft. Benton
DNA
DNA
DNA
DNA
Mean
1.68
DNA
1.64
1.67
DNA: Data not available
- 25
Table 15. Carotene/Chlorophyll ratio (OD 430/OD 663)
Station
Summer
Fall
Spring
Mean
Big Sandy Creek
DNA
DNA
DNA
DNA
Dearborn River
DNA
DNA
10.05
10.05
Lodge Creek
DNA
DNA
DNA
DNA
Marias River/Loma
DNA
DNA
DNA
DNA
Marias River/Shelby
DNA
DNA
DNA
DNA
Milk River/Chinook
DNA
DNA
DNA
DNA
Milk River/Havre
DNA
DNA
DNA
DNA
Missouri River/Cascade
DNA
DNA
10.41
10.41
Missouri River/Ft. Benton
DNA
DNA
DNA
DNA
Muddy Creek
DNA
DNA
DNA
DNA
Pondera Creek
DNA
DNA
DNA
DNA
Smith River
DNA
DNA
DNA
DNA
Sun River/Ft. Shaw
DNA
DNA
10.16
10.16
Sun River /Vaughn
DNA
DNA
10.24
10.24
Teton River/Dutton
DNA
DNA
6.84
6.84
Teton River/Ft. Benton
DNA
DNA
DNA
DNA
Mean
DNA
DNA
9.54
9.54
DNA; Data not available
26
PERIPHYTON COMMUNITY STRUCTURE
Rationale
Except in the lower reaches of our largest rivers— the Kootenai,
Clark Fork, Missouri and Yellowstone— the stream periphyton (bottom)
community is more important than the stream plankton (open «^ter)
community in terms of plant diversity and plant production. ^he pen
phyton community may have more than 300 different kinds of pla ts
(mostly single-celled algae) on one square inch of river bottom.
In unpolluted waters, the dominant algae are diatoms. Diatoms
are microscopic, golden-brown plants encased in silica. They are
often attached to the river bottom by a short gelatinous stalk.
Millions of these creatures underfoot can make a river bottom treac
erous, yet they are a sign of good river health. Moreover, they are
the preferred food of many aquatic invertebrates.
When a river is polluted and its chemical and biological equili-
bria are disturbed, diatoms are often displaced by coarser, less pal
atable green and blue-green algae (Patrick, 1978). In Montana stream
and elsewhere, this takeover is often accomplished by the long, fila
mentous green alga Cladophor_a, which often becomes a
this reason, we have ranked diatoms relative to other significant algae
as a rough index of stream well-being. Theoretically, the lower dia
toms are ranked, the more polluted and unbalanced is the river,
should be noted that some non-diatom algae may be seasonally very
abundant in nearly pristine streams, for example, the blue-green alga
Nostoc.
Each one of the many thousand different species of stream diatoms
is unique in the conditions it requires for growth. Many of the more
common species have been classified as to their general environmental
requirements and pollution tolerances (Ir^we, 1974). They ®
from tolerant to intolerant. Consequently, diatoms are va ua p
tion indicators and subtle shifts within the ‘^^^tom association o
river bottom can signal environmental disturbances long before
becomes totally "unglued" and nuisance growths appear.
Achnanthes and Nitzschia are two particularly useful 'ii^tom indi-
cator^ Achni^Tthes is almost always found in significant numbers, but
only in water h^g a high concentration of
ing saturation. Nitzschia, on the other hand, is usually
with waters high in nitrogen. The relative abundance of Nitzsch^ is
often directly proportional to the amount of nitrogen contained in
;ft". some ^ciL of Nitzschia, such as N. require organic
nitrogen for their growth (Cholnoky, 1968).
27
Clean waters usually have many different species with some fairly
common but with none really dominant. Polluted waters have fewer
species, often with one or two species very abundant. Clean water is
said to have high diversity and polluted water is said to have low
diversity. Diversity can be measured simply by counting the number
of species in a sample or by calculating a rather involved formula
called a diversity index. The most widely accepted diversity index
is the Shannon-Weaver Index or d. Bahls (In Press) found that benthic
diatom associations in unpolluted Montana streams average between 25
and 40 species with d values greater than 3. Species numbers signi-
ficantly below 25 and diversity values significantly below 3 are indi-
cations of pollution.
Methods
Periphytic algae were collected from natural substrates on the
stream bottom. Quantities of larger, macroscopic species were picked
in proportion to their abundance relative one to one another and to
the attached diatom (slime) community as a whole. Accordingly, an
appropriate amount of the diatom community was collected by scraping
rocks and other submerged substrates with a razor blade, pocket knife,
or scalpel. Different substrates in turn were scraped in proportion
to their areal coverage. An effort also was made to collect algae
from both pools and riffles, again in proportion to the extent these
stream features prevail at a given site. The ultimate objective is
to obtain a sample of algae that is a miniature replicate of the
stream's periphyton community. Samples were preserved with Lugol's
(IKI) solution and returned to the lab for analyses.
Conspicuous non-diatom algae were removed, examined microscopi-
cally, and identified to genus. The relative abundance and rank of
each significant non-diatom genus and the diatom community as a whole
were then recorded. A portion of the diatom community was used to
prepare a permanent, randomly strewn mount using sulfuric acid and
potassium dichromate as the oxidizing agents and Cargille's "Carmount-
165" as the mounting medium (A.P.H.A., 1975). A diatom species pro-
portional count was performed on each slide following the technique
outlined by Weber (1973) , except that in excess of 300 rather than
250 cells were tallied. The results were used to compute percent
relative abundance of indicator taxa and diatom species diversity
using the Shannon-Weaver formula recommended by Weber (1973) :
d = I (N log^Q N-5ji.log^Qn.)
viiere C = 3.321928; N = total number of individuals; and n^ = number
of individuals in the i^^ species.
28
Results
Parameters depicting periphyton community structure are presented
in Tables 16 through 21.
Interpretation
Diatoms dominated the periphyton of most streams in the Northcentral
Loop (Table 16) . However, diatoms were substantially outranked by other
algae in Lodge and Big Sandy Creeks, indicating serious perturbations
in these streams. Schizomeris, a green alga, dominated the algal flora
at the Sun River station below Vaughn in September (summer 1977) .
Prescott (1968) describes this alga as being favored by water enriched
with nitrogen wastes, and elsewhere (Prescott, 1964) he reports that
it is often found near the entrance of drains or sewage treatment plant
discharges. The Muddy Creek station at Vaughn was dominated at this
time by Cladophora, another green alga that is responsive to nutrient
enrichment (Whitton, 1970) . Cladophora was easily the most abundant
and most frequently occurring non-diatom alga at Northcentral Loop sta
tions .
Water quality requirements of major diatom species from the North-
central Loop are summarized in Appendix G. Most of these species (Table
17) indicate alkaline, somewhat salty water approaching eutrophic con-
ditions. Particularly eutrophic conditions were indicated by the domin-
ance of Navicula perparva in the spring collection from Muddy Creek,
Navicula minima in the summer collection from Lodge Creek, and Nitzschia
palea in the spring collection from the Teton River near Dutton.
A large number of collections had low relative abundance values for
oxygen-indicating Achnanthes species (Table 18) . In all cases where two
stations were sampled on one river (Marias, Milk, Missouri, Sun, Teton),
the downstream station had the lower mean relative abundance. However,
this difference was not significant between Cascade and Fort Benton on
the Missouri. Other streams with low relative abundance values for
Achnanthes were Big Sandy and Lodge Creeks and the Smith River. ^ Conse-^
quently, these streams are the ones most likely to suffer from depressed
dissolved oxygen concentrations.
Most of the streams in the Northcentral Loop had substantial popu-
lations of Nitzschia species (Table 19). One notable exception was the
Sun River at Fort Shaw which had consistently low populations of this
nitrogen indicator diatom. Particularly high values were recorded for
Big Sandy Creek, the Marias River near Shelby, and the Teton River near
Dutton. These stations may be more affected than others by nitrogenous
wastes .
Diatom diversities and numbers of diatom species were significantly
lower in spring than in summer or fall. Three particularly stressed
stations at this time were Pondera Creek, the Marias River at Loma, and
the Teton River at Fort Benton. All three had fewer than 25 species
and diversity values less than 3. Although only 22 species were recorded
for Muddy Creek, diatom diversity was satisfactory in this stream.
- 29
Table 16.
Estimated rank of diatoms and other significant algae.
Station Summer
Big Sandy Creek
1 • Chara
2 . Spirogyra
3. Diatoms
4. Mougeotia
Ice
Dearborn River
1 . Diatoms 1 .
Eivularia
1,
2 . Chara 2 .
Diatoms
2.
3 . Zygnema
4 . Mougeo tia
3.
5 . Spirogyra
6. Ehisoalonium
Lodge Creek
1 . Spirogyra
2 . Oedogonium
3. Audouinella
4. Mougeotia
Ice
5. Diatoms
Marias River/Loma
1. Diatoms
2 . Chara
3 . Cladophora
Ice
1.
Marias River/Shelby
1 . Diatoms
Ice
1.
2 . Cladophora
3 . Cosmarium
2.
Milk River/Chinook
1 . Diatoms
Ice
1.
2 . Phormidium
2.
3 . Saenedesmus
3.
Milk River/Havre
1 . Diatoms
Ice
1.
2 . Spirogyra
2.
3 . Cladophora
3.
Missouri River/Cascade
1 . Cladophora 1 .
Cladophora
1.
2 . Diatoms 2 .
Diatoms
2.
3 . Enteromorpha
3.
4.
Missouri River/Fort Benton
1 . Diatoms
Ice
1.
2.
Muddy Creek
1 . Cladophora
2. Diatoms
Ice
1.
by volume
Spring
Flood
Diatoms
Ulothrix
Phormidium
Flood
Diatoms
Lyngbya
Diatoms
Phormidium
Diatoms
Osoillatoria
Diatoms
Phormidium
Rivularia
Diatoms
Cladophora
Eormidium
Ulothrix
Diatoms
Cladophora
Diatoms
30 _
Table 16. (Continued)
Station
Summer
Fall
Spring
Pondera Creek
1.
Diatoms
Ice
1.
Diatoms
2.
Ctadophora
3.
Oedogoni-wn
4.
Spirogyra
5.
Pediastvum
Smith River
1.
Diatoms
Ice
1.
Diatoms
Sun River/Fort Shaw
1.
Diatoms
1.
Diatoms
1.
Diatoms
2.
Cladophora
2.
Cladophora
2.
Ulo thrix
Sun River/Vaughn
1.
Sohizomerds
Ice
1.
Diatoms
2.
Diatoms
2.
U to thrix
Teton River/Dutton
1.
Diatoms
Ice
1.
Diatoms
2.
Spirogyra
3.
Cosmarium
4.
Saenedesmus
Teton River/Fort Benton
1.
Diatoms
1.
Diatoms
1.
Diatoms
31 -
Table 17
Percent relative abundance of major diatom species (Appendix G)
Station
Summer
Fall
Spring
Big Sandy Creek
NIFR: 17.6
DPPU: 11.9
ENOR: 10.4
Ice
Flood
Dearborn River
ACMI : 26.3
CMMC: 12.5
DITE: 36.8
ACMI : 20.4
CMMC: 14.2
ACMI: 25.1
GOOL: 13.2
NIDI: 12.1
Lodge Creek
NAMI; 21.9
Ice
Flood
Marias River/Loma
CMMC: 23.1
ACMI: 12.2
SYDE: 10.3
Ice
DITE: 69.6
FRVA: 14.5
Marias River/ Shelby
FRVA: 28.3
ACMI: 22.0
Ice
AMPE: 45.4
RHCU: 16.8
Milk River/Chinook
STSU: 28.8
AMPE: 13.9
CYME: 11.5
Ice
GOTE: 25.6
RHCU: 15.4
Milk River/Havre
ACMI : 54.0
CMMC: 10.8
Ice
ACMI : 30.3
CMMC: 21.6
FRVA: 14.3
Missouri River/Cascade
EPSO: 51.1
NIFR: 11.9
DIVU: 22.0
NIFR: 16.4
NATR: 27.7
GODL: 19.6
DIVU: 18.2
Missouri River/Fort Benton
NIFR: 11.3
NAMI: 10.7
Ice
AMPE: 18.6
NAMI: 18.3
NARA: 17.8
COPL: 11.4
Muddy Creek
ACMI: 31.7
CMAF: 15.6
Ice
NAPE: 19.6
ACMI: 19.0
NIFR: 15.8
AMPE: 14.9
Pondera Creek
SYPU: 12.6
NIFR: 11.5
ACMO: 11.0
Ice
STHA: 77.3
NIAC: 14.7
32
Table 17. (Continued)
Station
Summer
Fall
Spring
Smith River
AMPE: 15.9
Ice
COOL: 43.9
DIVU: 13.5
SYUL: 11.0
Sun River/Fort Shaw
ACMI: 19.8
FRVA: 18.9
DITE: 25.4
ACMI: 18.5
ACMO: 10.3
ACMI: 16.5
DITE: 15.3
SYRU: 14.8
FRVA: 10.8
COOL: 10.5
Sun River/Vaughn
DIVU: 12.3
ACMI: 11.4
Ice
SYRU: 19.3
DITE: 15.2
Teton River/Dutton
CMMN: 28.0
FRVA: 12.6
ACMI: 11.7
DITE: 11.1
Ice
NIPA: 19.9
DITE: 10.5
Teton River/Fort Benton
CMMC: 16.6
APPE: 13.4
ACMI: 10.9
NIMI: 10.9
CMMC: 22.1
CMAF: 20.4
ACMI: 11.2
DITE: 10.3
GOOD: 40.7
DITE: 35.6
- 33
Table 18.
Table 18. Percent relative
abundance
of Achnanthes
species
Station
Simimer
Fall
Spring
Mean
Big Sandy Creek
5.4
Ice
Flood
5.4
Dearborn River
27.1
20.1
27.8
25.0
Lodge Creek
3.8
Ice
Flood
3.8
Marias River/Loma
13.6
Ice
1.2
7.4
Marias River/Shelby
22.0
Ice
25.4
23.7
Milk River/Chinook
1.5
Ice
6.8
4.2
Milk River/Havre
52.9
Ice
30.3
41.6
Missouri River/Cascade
3.1
1.8
0.8
1.9
Missouri River/Fort Benton
2.6
Ice
1.0
1.8
Muddy Creek
31.7
Ice
65.0
46.4
Pondera Creek
21.0
Ice
0.0
10.5
Smith River
3.5
Ice
0.5
2.0
Sun River/Ft. Shaw
29.6
29.3
20.5
26.5
Sun River/Vaughn
11.7
Ice
13.4
12.6
Teton River/Dutton
12.0
Ice
3.8
7.9
Teton River/Fort Benton
2.6
11.2
1.0
4.9
Mean
15.3
15.6
14.1
14.8
- 34
Table 19.
Table 19. Percent relative
abundance
of Nitzschia
species
Station
Summer
Fall
Spring
Mean
Big Sandy Creek
34.2
Ice
Flood
34.2
Dearborn River
13.0
7.6
16.5
12.4
Lodge Creek
26. 3
Ice
Flood
26.3
Marias River/Loma
11.6
Ice
0.6
6.1
Marias River/Shelby
36.9
Ice
7.5
22.2
Milk River/Chinook
16.7
Ice
19.7
18.2
Milk River/Havre
14.2
Ice
9.0
11.6
Missouri River/Cascade
15.8
21.7
10.3
15.9
Missouri River/Fort Benton
26.5
Ice
14.6
20.6
Muddy Creek
10.9
Ice
16.7
13.8
Pondera Creek
23.7
Ice
18.1
20.9
Smith River
22.8
Ice
2.2
12.5
Sun River/Ft. Shaw
4.1
1.7
2.0
2.6
Sun River/Vaughn
24.0
Ice
17.7
20.8
Teton River/Dutton
10.6
Ice
33.5
22.0
Teton River/Fort Benton
24.7
9.4
10.7
14.9
Mean
19.8
10.1
12.8
15.8
35
Table 20.
Number of diatom species
Station
Summer
Fall
Spring
Mean
Big Sandy Creek
44
Ice
Flood
44
Dearborn River
56
32
38
42
Lodge Creek
50
Ice
Flood
50
Marias River/Loma
47
Ice
17
32
Marias River/Shelby
33
Ice
31
32
Milk River/ Chinook
44
Ice
28
36
Milk River/Havre
46
Ice
35
40
Missouri River/Cascade
32
39
31
34
Missouri River/Fort Benton
58
Ice
28
43
Muddy Creek
28
Ice
22
25
Pondera Creek
42
Ice
13
28
Smith River
61
Ice
32
46
Sun River/Fort Shaw
37
41
38
39
Sun River/Vaughn
56
Ice
45
50
Teton Rive r/Dut ton
36
Ice
49
42
Teton River/Fort Benton
44
35
23
34
Mean
45
37
31
38
- 36 -
Table 21
Diatom species diversity (d)
Station
Summer
Fall
Spring
Mean
Big Sandy Creek
4.42
Ice
Flood
4.42
Dearborn River
4.42
3.05
3.79
3.75
Lodge Creek
4.53
Ice
Flood
4.53
Marias River/Loma
4.33
Ice
1.64
2.99
Marias River/Shelby
3.55
Ice
3.02
3.28
Milk River/Chinook
3.97
Ice
3.86
3.92
Milk River/Havre
3.28
Ice
3.37
3.33
Missouri River/Cascade
3.01
4.01
3.24
3.42
Missouri River/Fort Benton
4.84
Ice
3.51
4.18
Muddy Creek
3.56
Ice
3.34
3.45
Pondera Creek
4.33
Ice
1.24
2.79
Smith River
5.00
Ice
3.04
4.02
Sun River/Fort Shaw
4.00
3.82
3.80
3.87
Sun River/Vaughn
4.84
Ice
4.27
4.56
Teton River/Dutton
3.67
Ice
4.49
4.08
Teton River/Fort Benton
4.24
3.69
2.56
3.50
Mean
4.12
3.64
3.23
3.70
37
MACROINVERTEBRATE COMMUNITY STRUCTURE
Rationale
Macroinvertebrates comprise the energy link between periphyton and
fish in Montana streams. Most organisms in this community of bottom
dwellers are immature insects. As with the periphyton, macroinverte-
brates are differentially tolerant to pollution, thereby allowing cer-
tain groups to be used as indicators. Another characteristic in common
with the periphyton is their ability to integrate the effects of a
variety of water quality constituents over time. Macroinvertebrate
life cycles are considerably longer than those of periphyton organisms:
up to three years as compared to just a day or two for diatoms. Conse-
quently, they reflect water conditions over a much longer period of
time than do the diatoms.
Of the common aquatic insects in Montana steams, three groups are
generally indicators of waters with little organic pollution and ample
dissolved oxygen. These are the stoneflies (Plecoptera) , mayflies
(Ephemeroptera) , and caddisflies (Trichoptera) . Another group, the
order of true flies (Diptera) , has species that are either tolerant or
intolerant of pollution. Two remaining orders, the bugs (Hemiptera)
and beetles (Coleoptera) , are generally considered tolerant of pollution.
On closer examination, a number of invertebrates are actually fac-
ultative or able to get along in both clean and polluted water (Weber,
1973). For a large number of Montana stream insects, water quality pre-
ferences simply are not known. Nevertheless, the relative abundance
of organisms in various sensitivity groups is still a valid approximator
of water quality conditions.
The number of macroinvertebrate genera and macroinvertebrate genus
diversity are more concise and perhaps more valid estimators of macro-
invertebrate community health. Wilhm (1970) reported clean waters to
have from 11 to 54 species and Shannon-Weaver diversity values from 2.6
to over 4. Polluted streams, on the other hand, had diversity values
less than 2 and frequently less than 1. From our experience, unpolluted
streams with favorable dissolved oxygen levels, temperatures, and sub-
strates generally produce a minimum of 10 genera. The number of macro-
invertebrates collected per unit effort of sampling time is an indicator
of productivity and habitat availability. It should be noted that genus
diversities computed from samples of less than 100 organisms should be
interpreted with caution (E.P.A., 1973).
Methods
The technique used for macroinvertebrate collection is a modification of
the "unit-effort- traveling-kick" method described by Kinney e^ a^. (In
Press) .
38 -
The objective is to sample each type of habitat at the designated site
in a random fashion, and to apply a similar amount of effort at each
station, except where bugs are scarce. Equipped with a long-handled
D-frame aquatic net (Ward's 10W0620)*, the sampler works all the major
habitat types — riffles, pools, submerged vegetation, etc. — by dislodg-
ing organisms with his feet and capturing them as they drift downstream.
Research has shown this method to have better statistical reproducibil-
ity than artificial substrate and Surber samplers in semi-arid regions
where the fauna tends to be patchy and sparse (Kinney, e^ , In Press) .
When an adequate number of insects has been collected, the sampler
randomly selects 100 or more specimens from the net and places them in
a small jar one- third full of water. Care is taken not to be biased
by size of the organism. The jar is then filled with 95 percent ethanol,
labeled, and returned to the lab for analysis. (A few drops of glycer-
ine are added if extended storage is required.) Organisms were iden-
tified to genus wherever possible. Enumeration results were used to
compute the percent relative abundance of major insect orders and pollu-
tion sensitivity groups (Weber, 1973) . Shannon-Weaver diversity was
calculated in the same fashion as it was for the diatoms (See "Peri-
phyton Community Structure - Methods").
Results
Macroinvertebrate sampling of Northcentral Loop streams was difficult,
owing to ice cover in the fall and high water in the spring. Some
drainages experienced early spring floods and severe scouring. At
such times, it was impossible to reach the main stream channel because
the water was over the banks. A thorough sample never was collected
from the Missouri River at Fort Benton because of naturally deep water.
The only sample obtained from Lodge Creek was lost in transit. Macro-
invertebrate community parameters are presented in Tables 22 through
26.
Interpretation
Streams in the Northwest Loop yielded diverse types of macroinver-
tebrate associations. For most, the aquatic fauna was dominated by
four orders: Plecoptera (stoneflies) , Ephemeroptera (mayflies) , Tri-
choptera (caddisflies) , and Diptera (true flies) . However, in the
Dearborn, Smith, and Marias rivers, beetles (Order Coleoptera) , dragon-
flies (Order Odonata) , and true bugs (Order Hemiptera) were also im-
portant. Macroinvertebrates found in Pondera Creek were limited to
beetles (Families Hydrophilidae and Elmidae) , araphipod crustaceans
(Genus Gammarus) , and dragonflies (Genus Ishnura) . Big Sandy Creek
contained primarily amphipod crustaceans (Genus Hyalella) .
*Approximately 21.5 meshes per inch with 1 mm openings
39
with few exceptions, pollution tolerant taxa were never plentiful
in streams of the Northwest Loop (Table 23) . Facultative or uncate-
gorized forms averaged 34 percent and pollution intolerant taxa domin-
ated, averaging 60 percent of all organisms. However, mostly toler-
ant and facultative organisms were collected at four stations. These
were Big Sandy and Pondera creeks, plus the Sun River below Vaughn
and the Milk River at Havre.
Numbers of macroinvertebrate genera varied greatly from stream to
stream and from season to season, the latter due in part to sampling
conditions. Seven streams failed to produce at least 10 genera on
any one visit. Five of these seven streams (Big Sandy, Milk River/
Chinook, Milk River/Havre, Pondera, Sun River/Vaughn) had poor sub-
strates and suffered from heavy silt loads. Two of these five streams.
Big Sandy and Pondera creeks, commonly go dry in summer. The Teton
River near Fort Benton had a favorable substrate but failed to produce
a variety of taxa for unknown reasons. (The final stream, the Missouri
River at Fort Benton, produced only a few taxa, possibly because of
the difficulty in sampling.)
Macroinvertebrate genus diversity values (Table 25) ranged from
a low of 0.54 in Big Sandy Creek to a high of 3.52 in the Dearborn
River. Five stations had mean diversities greater than 2.6, indica-
ting relatively clean water and an unstressed invertebrate association.
These are, in descending order: Dearborn River, Sun River/Fort Shaw,
Marias River/Loma, Muddy Creek, and Marias River /Shelby . Diversities
between 2.0 and 2.6 were tallied for Missouri Rive r/Cas cade , Milk River/
Havre, Smith River, Teton River/Dutton, and Milk River /Chinook. On
the basis of this parameter, invertebrates in these streams are under
some stress, perhaps resulting from silt, lack of a suitably diverse
habitat, pollution, or a combination of these factors. The remaining
five streams — Pondera Creek, Sun River/Vaughn, Teton River/Fort Benton,
Missouri River/Fort Benton, and Big Sandy Creek — had values less than
2.0, indicating more severe stress. However, caution should be used
because values for some of the streams were derived from only one
sample. Also, some mean values were depressed owing to the scarcity
of macroinvertebrates in spring. Table 26 best expresses the seasonal
availability of macroinvertebrates in these streams.
40
Table 22.
Mean percent relative abundance of major macroinvertebrate orders
Station
Plecop-
tera
(Stone-
flies)
Ephemer-
optera
(may-
flies)
Trichop-
tera
(caddis-
flies)
Diptera
(true
flies)
Coleop-
tera
(beetles)
Hemip-
tera
(true
bugs)
Miscel-
laneous
Big Sandy
0
0
0
12.5
0
0
87.5
Dearborn River
31.1
13.9
29.2
13.1
11.8
.7
.2
Lodge Creek
DNA
DNA
DNA
DNA
DNA
DNA
DNA
Marias River/Loma
31.2
14.8
17.5
11.6
0
5.0
19.9
Marias River/Shelby
14.1
13.8
66.4
3.9
1.1
0
.7
Milk River/Chinook
0
31.7
63.5
0
1.9
0
2.9
Milk River/Havre
0
89.4
0
0
0
5.3
5.3
Missouri River/Cascade
2.3
34.5
26.0
34.4
2.8
0
0
Missouri River/Ft. Benton
4.4
84.4
4.4
6.8
0
0
0
Muddy Creek
23.6
17.9
26.8
19.4
0
1.2
11.7
Pondera Creek
0
0
0
0
60.0
0
40.0
Smith River
27.2
47.6
4.9
2.2
0
17.0
1.1
Sun River/Ft. Shaw
28.5
10.4
28.0
29.0
1.6
2.5
0
Sun River /Vaughn
5.0
58. 2
18.4
0
0
0
18.4
Teton River/Dutton
2.3
14.7
73.9
8.0
0
0
1.1
Teton River/Ft. Benton
0
5.5
57.0
33.3
1.4
0
2.8
Mean
11.3
29.1
27.7
11.6
5.4
2.1
12.8
#
41
Table 23.
Mean percent relative abundance of tolerant, facultative
and intolerant macroinvertebrates
Station
Tolerant
Facultative or
Unknown
Intolerant
Big Sandy Creek
0
100.0
0
Dearborn River
12.5
27.7
59.8
Lodge Creek
DNA
DNA
DNA
Marias River/Loma
0
41.1
58.9
Marias River/Shelby
1.2
13.9
84.9
Milk River/Chinook
1.9
4.8
93.3
Milk River /Havre
5.3
52.6
42.1
Missouri River/Cascade
2.8
40.7
56.5
Missouri River/Ft. Benton
0
6.7
93.3
Muddy Creek
• 6
29.9
69.5
Pondera Creek
60.0
40.0
0
Smith River
.5
36.1
63.4
Sun River/Ft. Shaw
1.6
33.9
64.5
Slin River/Vaughn
2.6
63.4
34.0
Teton River/Dutton
0
4.6
95.4
Teton River/Ft. Benton
1.4
19.4
79.2
Mean
6.0
34.3
59.7
42
Table 24.
Number of macroinvertebrate genera
Station
Summer
Fall
Spring
Mean
Big Sandy Creek
2
—
—
2
Dearborn River
15
20
12
16
Lodge Creek
—
—
—
—
Marias River/Loma
11
—
7
9
Marias River/Shelby
18
—
12
15
Milk River/Chinook
9
—
—
9
Milk River/Havre
8
—
—
8
Missouri River/Cascade
13
—
10
12
Missouri River/Ft. Benton
7
—
—
7
Muddy Creek
12
—
8
10
Pondera Creek
4
—
—
4
Smith River
14
—
7
12
Sun River/Ft. Shaw
12
11
13
12
Sun River/Vaughn
7
—
3
5
Teton River/Dutton
11
—
—
11
Teton River/Ft. Benton
6
—
3
4
Mean
10
16
8
10
43
Table 25.
Macroinvertebrate genus diversity (d)
Station
Summer
Fall
Spring
Mean
Big Sandy Creek
0.54
—
—
0.54
Dearborn River
3.08
3.52
3.00
3.20
Lodge Creek
—
—
—
—
Marias River/Loma
2.96
—
2.72
2.84
Marias River/Shelby
2.63
—
2.60
2.62
Milk River/Chinook
2.02
—
—
2.02
Milk River/Havre
2.46
—
—
2.46
Missouri River/Cascade
2.63
—
2.40
2.52
Missouri River/Ft. Benton
1.22
—
—
1.22
Muddy Creek
3.02
—
2.49
2.75
Pondera Creek
1.92
—
—
1.92
Smith River
2.19
—
2.50
2.34
Sun River/Ft. Shaw
2.83
2.65
3.03
2.84
Sun River/ Vaughn
2.36
—
.92
1.64
Teton River/Dutton
2.18
—
—
2.18
Teton River/Ft. Benton
1.54
—
1.58
1.56
Mean
2.24
3.08
2.36
2.34
44
Table 26.
Number of macroinvertebrates collected per unit
effort sample time
Station
Summer
Fall
Spring
Mean
Big Sandy Creek
8
-
-
8
Dearborn River
134
140
72
115
Lodge Creek
Sample lost
-
-
-
Marias River/Loma
64
-
10
37
Marias River/Shelby
137
-
62
100
Milk River/Chinook
104
-
-
104
Milk River/Havre
19
-
-
19
Missouri River/Cascade
152
-
99
126
Missouri River/Ft. Benton
45
-
45
Muddy Creek
84
-
52
68
Pondera Creek
5
-
-
5
Smith River
93
-
15
54
Sun River/Ft. Shaw
133
39
67
80
Sun River/Vaughn
19
-
10
14
Teton River/Dutton
88
-
-
88
Teton River/Ft. Benton
36
-
3
20
Mean
75
90
43
65
- 45
SUMMARY AND CONCLUSIONS
This report presents data for 31 biologically-related water quality
parameters at 16 stations over three seasons. There is clearly a need
for consolidating this information so that stations in the Northcentral
Loop can be compared at a glance and prioritized from the standpoint
of management urgency. Two such consolidation schemes are presented.
Both schemes incorporate mean values for 15 key indicators. The many
missing data points for some stations necessitated selective utiliza-
tion of only relatively complete sets of results. Use of the incomplete
data (all fall data and spring data for certain parameters) would have
inaccurately shifted overall averages for most stations and resulted
in misleading comparisons. The 15 indicator parameters used in the
two schemes are listed below, together with the seasons for which their
means were determined.
Parameter
Seasons
1. Specific conductance (micromhos 0 25C)
2. Total soluble inorganic nitrogen (mg/1)
3. Total phosphorus (mg/1)
4. Algal assay control maximum standing crop (mg/1)
2
5. Chlorophyll a^ accrual (mg/m /day)
2
6. Biomass accrual (mg/m /day)
7. Autotrophic Index (Biomass accrual/Chlorophyll a^ accrual)
8. Percent relative abiindance Achnanthes species
9. Percent relative abundance Nitzschia species
10. Number of diatom species
11. Diatom species diversity (d)
12. Percent relative abundance intolerant macroinvertebrates
13. Number of macro invertebrate genera
14. Macroinvertebrate genus diversity (d)
15. Number of macroinvertebrates collected per unit effort
sample time
Summer
Summer, Spring
Summer, Spring
Summer, Spring
Summer
Summer
Summer
Stimmer, Spring
Summer, Spring
Summer, Spring
Summer, Spring
Summer
Summer
Summer
Summer
46
In Scheme A, the assumption is made that the least amount of nutri
ents and production, whatever the cause, is the most desirable case. All
mean values are listed in order from lowest to highest for each indicator.
Indicators where the highest value is presumed to reflect the best water
quality are numbers 8 and 10-15 in the preceding list. Indicators where
the lowest value is presumed to reflect the best water quality are num-
bers 1-7 and 9. The station with the extreme (highest or lowest) value
indicating the poorest water quality is given a ranking of one for that
indicator. The station with the second highest or lowest value indica-
ting the second poorest water quality is then given a rank of two, and
so on until all 16 stations are ranked for that indicator. When all 16
stations have been ranked for each of the 15 indicators, ranks for each
station are totalled and divided by the number of indicators measured
at that station. The resulting composite rank may be used to assess
relative biological health among the 16 stations of the Northcentral
Loop.
Scheme B presumes that moderate amoiants of nutrient enrichment are
desirable and that too much (eutrophication) or too little (natural steri-
lity or man-caused toxicity) production is not good. Scheme B differs
from Scheme A in that production-related indicators (numbers 2-6) are
ranked according to their divergence from the median value, which is
considered representative of a moderately enriched stream in northcentral
Montana. In other words, the station with the median value is given a
ranking of 16 and the value most distant from the median is given a rank-
ing of 1. The remaining indicators, which are principally indicators
of water quality (#1, 7, 8, 9, and 12) and community stability and diver-
sity (#10, 11, 13, 14, and 15) are ranked as they were under System A.
Composite rankings under the two schemes, arranged in order from
highest (best quality) to lowest (worst quality) , are presented in
Table 26.
47
Table 26.
Composite ranking of stations in the Northcentral Loop
Best possible rank = 15; Worst possible rank = 1
SCHEME A
SCHEME B
Water Quality
Station
Rank
Station
Rank
Good
Dearborn River
11.2
Marias River/Loma
8.7
Missouri River/Cascade
10.8
Smith River
8.5
Missouri River/Ft. Benton
9.2
Sian River/Vaughn
8.5
Smith River
9.1
Dearborn River
8.4
Sun River/Ft. Shaw
8.8
Lodge Creek
8.4
Teton River/Dutton
7.7
Missouri River/Cascade
8.2
Marias River/Shelby
7.5
Missouri River/Ft. Benton
7.9
Fair
Marias River/Loma
7.4
Teton River/Ft. Benton
7.8
Sun River/Vaughn
7.4
Marias River/Shelby
7.7
Milk River/Chinook
7.1
Milk River/Chinook
7.7
Lodge Creek
6.9
Milk River/Havre
7.6
Milk River/Havre
6.8
Sun River/Vaughn
7.0
Teton River/Ft. Benton
6.4
Teton River/Dutton
6.9
Muddy Creek
5.3
Muddy Creek
6.0
Poor
Big Sandy Creek
3.6
Big Sandy Creek
5.5
Pondera Creek
2.7
Pondera Creek
3.4
48
Under Scheme A, only two streams had good water quality relative to
other northcentral Montana streams on the basis of biological conditions.
These were the Dearborn River and the Missouri River at Cascade. Streams
rated as poor were Muddy, Big Sandy, and Pondera creeks. The other ele-
ven streams were arbitrarily categorized as fair, with many of these
having nearly equal scores.
The three poorest streams all suffer from excessive silt loads due
to accelerated stream bank erosion and poor irrigation practices (Water
Quality Bureau, 1974, 1975). Nutrient enrichment is also very great,
primarily as a result of agricultural runoff. It is suspected that
municipal discharges may contribute some nutrients to Pondera and Big
Sandy creeks. Nearly all of the "fair" streams suffer from some degree
of non-point source pollution and many receive municipal discharges as
well .
Scheme B resulted in some major shifts from the arrangement in
Scheme A. Only the three poorest streams remained in the same relative
position. The remaining thirteen stations had a very narrow range of
scores and, as a result, it was impossible to clearly distinguish "good"
streams from "fair" ones. Thus, under Scheme B, most of the northcentral
Montana streams sampled can be considered to be at least moderately en-
riched and productive.
On the basis of these composite rating systems, it may be concluded
that nearly all of the Northcentral Loop streams are affected by some
degree of biologically debilitating water quality degradation. Many
streams of the loop receive municipal discharges at one point or another.
Only three discharges are in need of upgrading. These affect the upper
Marias River (Valier) , the Milk River (Chinook) , and Big Sandy Creek
(Big Sandy) , but probably have no more than minimal impact for a short
distance (R. Braico, personal communication) . Therefore, the authors
conclude chat most of the serious water quality problems in streams of
the Northcentral Loop result from non-point pollution. Some of this is
due to the natural hyrdologic characteristics of lowland streams: large
silt and nutrient accumulations caused by natural erosion, sedimentation,
and runoff. Howver, it is known that natural pollution has been aggra-
vated by man's activities in this area. Practices contributing to water
quality degradation in northcentral Montana streams include overgrazing,
dewatering, irrigation returns, channel disturbances, and less commonly,
oil spills, solid waste disposal and acid mine drainage. Consequently,
achievement of a reasonable level of biological improvement will require
better land use practices.
Conditions at these 16 stations probably can be considered fairly
representative of overall water quality in the lowland portions of north-
central Montana. This assumption is based on the fact that land and
water uses in this region are overwhelmingly agricultural and very uni-
form. It is thus expected that water quality elsewhere in the region
would fall within the range of that encountered during this study.
- 49
The quality of upland tributaries in northcentral Montana, parti-
cularly those originating in the Rocky Mountains, was not documented
in this study. However, it is probably safe to assume that generally
they have healthier biological conditions than those at the monitoring
stations of the Northcentral Loop.
LITERATURE CITED
American Public Health Association, e^ a]^. 1971
Standard Methods for the Examination of Water and Wastewater.
Thirteenth Edition. A.P.H.A., Washington, D.C. 874 pp.
American Public Health Association, et al. 1975.
Standard Methods for the Examination of Water and Wastewater.
Fourteenth Edition. A.P.H.A. , Washington, D.C. 1193 pp.
Bahls, L. L. 1978. Aquatic Studies. ^ U.S.D.A. — Montana Department
of State Lands, Draft EIS, ASARCO Troy Project, Lincoln County,
Montana, pp 126-149.
Bloom, D. and M. K. Botz. 1974. Water Quality Inventory and Management
Plan — Milk River Basin, Montana. Water Quality Bureau, Helena.
119 pp.
Braico, R. D. and M. K. Botz. 1974. Water Quality Inventory and Manage-
ment Plan — Missouri-Sun- Smith Basin, Montana. Water Quality
Bureau, Helena. 162 pp.
Cholnoky, B. J. National Institute for Water Research, Pretoria, South
Africa. Letter to Loren L. Bahls dated February 21, 1971.
Garvin, W. H. and M. K. Botz. 1975. Water Quality Inventory and Manage-
ment Plan — Marias River Basin, Montana. Water Quality Bureau,
Helena. 118 pp.
Ingman, G. L. 1978. A Study of the Biological Impact of the Helena
Sewage Treatment Plant Effluent on Prickly Pear Creek. Water
Quality Bureau, Helena.
Kinney, W. L. J. E. Pollard and C. E. Hornig. In Press. Comparison of
Macroinvertebrate Samplers as they Apply to Streams of Semi-Arid
Regions. Proceedings of the Fourth Joint Conference on Sensing
of Environmental Pollutants, November 1977, New Orleans, Louisiana.
Klarich, D. A. 1976. Estimates of Primary Production and Periphyton Com-
munity Structure in the Yellowstone River (Laurel to Huntley, Montana).
Water Quality Bureau, Montana Department of Health and Environmental
Sciences, Billings. 58 pp.
Lowe, R. L. 1974. Environmental Requirements and Pollution Tolerance of
Freshwater Diatoms. EPA-67/4-74-005 . 334 pp.
Mace, H. H. 1953. Disposal of Wastes from Water Treatment Plants. Public
Works 84(7) :73, pp. 88-100. In Water Quality Criteria, Committee on
Water Quality Criteria, Washington, pp. 142.
51
Literature Cited (Continued)
Mackenthun, K. M. 1969. The Practice of Water Pollution Biology. Fed-
eral Water Pollution Control Administration, U.S. Department of
the Interior, Washington, D.C. 281 pp.
Margalef, R. 1969. Ecological Correlations and the Relationship Between
Primary Productivity and Community Structure. ^ Goldmen, C. R. ,
ed. Primary Productivity in Aquatic Environments, University of
California Press, Berkeley, pp. 357-364.
Miller, W. E., J. C. Greene, and T. Shiroyama. 1978. The Selenastrum
capricornutvim Printz Algal Assay Bottle Test: Experimental Design,
Application, and Data Interpretation Protocol. Corvallis Environ-
mental Research Laboratory, U.S. Environmental Protection Agency,
Corvallis, Oregon. 126 pp.
Muller, W. 1953. Nitrogen Content and Pollution of Streams. Water
Pollution Abstracts, Volume 28, No. 2. Abstract No. 454.
Odum, E. P. 1963. Ecology. Holt, Rinehart and Winston, New York.
152 pp.
Patrick, R. 1977. The Importance of Monitoring Change. ^ Cairns, J.,
K. L. Dickson, and C. F. Westlake, eds. Biological Monitoring of
Water and Effluent Quality. American Society for Testing and
Materials, Philadelphia, pp. 157-189.
Patrick, R. and C. W. Reimer. 1966. The Diatoms of the United States.
Volume 1. Monograph No. 13, The Academy of Natural Sciences of
Philadelphia. 688 pp.
Patrick, R. and C. W. Reimer. 1975. The Diatoms of the United States.
Volume 2, Part 1. Monograph No. 13, The Academy of Natural
Sciences of Philadelphia. 213 pp.
Prescott, G. W. 1964. How to Know the Freshwater Algae. Wm. C. Brown,
Co., Dubuque, Iowa. 272 pp.
Prescott, G. W. 1968. The Algae: A Review. Haughton Mifflin Company,
Boston. 436 pp.
Rounsefell, G. B. and W. H. Everhart. 1953. Fishery Science - Its
Methods and Applications. John Wiley and Sons, Inc., New York.
444 pp. In Water Quality Criteria, Committee on Water Quality
Criteria, Washington, pp. 142.
52
Literature Cited (Continued)
Schoeman, F. R. 1973. A Systematical and Ecological Study of the Diatom
Flora of Lesotho with Special Reference to the Water Quality.
National Institute for Water Research, Pretoria, South Africa.
355 pp.
U.S. Environmental Protection Agency. 1971. Algal Assay Procedure:
Bottle Test. Pacific Northwest Water Laboratory, Corvallis,
Oregon. 82 pp.
U.S. Environmental Protection Agency. 1973. Water Quality Criteria.
Committee on Water Quality Criteria, EPA-R3-73-033 , Washington.
594 pp.
U.S. Environmental Protection Agency. 1974. Methods for Chemical
Analysis of Water and Wastes. EPA-625/6-74-003 . 298 pp.
Water Quality Bureau. 1976. Water Quality in Montana. Montana Depart-
ment of Health and Environmental Sciences, Helena. 36 pp.
Water Quality Bureau. 1978. Proposed Water Quality Standards. ARM 16-
2. 14 (10) -S14481 . Montana Department of Health and Environmental
Sciences, pp. 16.
Weber, C. I. (ed.). 1973. Biological Field and Laboratory Methods for
Measuring the Quality of Surface Waters and Effluents. National
Environmental Research Center, U.S. E.P.A., Cincinnati, Ohio.
Whittaker, R. H. 1970. Communities and Ecosystems. The Macmillan
Company, Collier-Macmillan Limited, London. 158 pp.
Whitton, B. A. 1970. Biology of Cladophora in Freshwaters. Wa ter
Research, Volume 4, pp. 457-476.
Wilhm, J. L. 1970. Range of Diversity Index in Benthic Macroinverte-
brate Populations. Journal of the Water Pollution Control Federa-
tion, Volume 42, No. 2., Part 2. Pp. R221-R224.
Zison, S. W., K. F. Haven, and W. B. Mills. 1977. Water Quality Assess-
ment, A Screening Method for Nondesignated 208 Areas. EPA-600/9-
77-023. 549 pp.
Personal Communications
R. Braico, Water Quality Bureau, Montana Department of Health and Environ-
mental Sciences, Helena.
53
RECENT REPORTS ON STREAM WATER QUALITY
IN NORTHCENTRAL MONTANA
Anonymous. 1972. Missouri River Basin above Ervin Ridge, Interim Water
Quality Management Plan (Draft) . Montana Department of Health and
Environmental Sciences .
Bloom, D. and M. K. Botz. 1974. Water Quality Inventory and Management
Plan — Milk River Basin, Montana. Water Quality Bureau, Helena.
119 pp.
Braico, R. D. and M. K. Botz. 1974. Water Quality Inventory and Manage-
ment Plan — Missouri-Sun-Smith Basin, Montana. Water Quality Bureau,
Helena. 162 pp.
Garvin, W. H. and M. K. Botz. 1975. Water Quality Inventory and Manage-
ment Plan — Marias River Basin, Montana. Water Quality Bureau,
Helena. 118 pp.
Hehn, Erhardt R. 1978. Agricultural Nonpoint Source Assessment. Montana
Association of Conservation Districts, Helena. 384 pp.
Hill, W. J. 1976. Water Quantity and Quality of the Sun River from
Gibson Dam to Vaughn, 1973-1974. Montana Department of Fish and
Game .
Johnson, E. 1972. "Muddy Creek: A Pollution Study". Montana Academy of
of Sciences, Proceedings. 32:58-65.
Rasmussen, R. and D. Culwell. 1978. Evaluation of Water Quality Problems
and Management Needs Associated with Non-USFS Silvicultural Practices
in the Montana Statewide 208 Area. Statewide 208, Water Quality
Bureau. Montana Department of Health and Environmental Sciences,
Helena. 249 pp.
USDA Committee on Rural Development. 1977. Proposed Model Implementation
Program-Dearborn Drainage Basin, Montana.
54 -
APPENDICES
Appendix A. Streams and stations in the Montana biological monitor
ing network
<«
SOUTHWEST LOOP
Completion Year: 1978
Beaverhead River at Twin Bridges
Big Hole River near Twin Bridges
Boulder River below Boulder
Clark Fork River at Deer Lodge
East Gallatin River at Thompson Creek
Grasshopper Creek near mouth
Jefferson River near Three Forks
Madison River near Three Forks
Muddy Creek at mouth near Dell
Prickly Pear Creek above Lake Helena
Prickly Pear Creek at East Helena
Red Rock River above Lima Reservoir
Ruby River near Twin Bridges
Sheep Creek above Muddy Creek
Silver Bow Creek below Warm Springs Ponds
West Fork Madison River near mouth
West Gallatin River at Central Park
NORTHCENTRAL LOOP Completion Year: 1978
Big Sandy Creek near mouth
Dearborn River near mouth
Lodge Creek near Chinook
Marias River at Loma
Marias River at Shelby WTP intake
Milk River above Chinook
Milk River at Havre WTP intake
Missouri River at Fort Benton WTP intake
Missouri River at Cascade
Muddy Creek near mouth at Vaughn
Pondera Creek near mouth
Smith River near Ulm
Sun River below Vaughn
Sun River near Fort Shaw
Teton River at Loma
Teton River north of Dutton
NORTHWEST LOOP Completion Year: 1979
Bitterroot River at Maclay Bridge
Clark Fork River at Huson RR Bridge
Clark Fork River below Bonner Dam
Clearwater River at mouth
Fisher River at mouth
Flathead River at mouth
- 55
Appendix A. (Continued)
NORTHWEST LOOP (Continued)
Flathead River above Flathead Lake
Lake Creek at mouth
Little Blackfoot River at Avon
Middle Fork Flathead River near mouth
North Fork Flathead River at mouth
Swift Current Creek near Babb
Stillwater River near Kalispell
Swan River near mouth
Whitefish River near Kalispell
Yaak River at mouth
NORTHEAST LOOP Completion Year:
Beaver Creek near Saco
Box Elder Creek near Winnett
Big Muddy Creek near Culbertson
Big Spring Creek below Lewistown
Judith River near Danvers
Judith River near Utica
Milk River at Nashua
Missouri River at Culbertson
Musselshell River at Mosby
Poplar River at mouth
Redwater River near mouth
Redwater River at Circle
Wolf Creek at Denton
SOUTHEAST LOOP Completion Year:
Armell's Creek near Colstrip
Beaver Creek at Wibaux
Bighorn River at Bighorn
Clark's Fork River at Laurel
Little Missouri River at Capitol
Musselshell River at Delphia
Musselshell River at Bundy
Powder River near mouth
Powder River at Broadus
Rosebud Creek near Colstrip
Shields River near mouth
Tongue River at Miles City
Tongue River at Ashland
Yellowstone River at Glendive
Yellowstone River at Huntley Dam
Yellowstone River at U.S.G.S. Station in Billings
Yellowstone River at Livingston
1980
1981
- 56
Appendix B. Phosphate (PO^ as P in mg/1)
Station
Summer
Fall
Spring
Mean*
Big Sandy Creek
0.008
ICE
0.263
0.136
Dearborn River
4 0.001
0.001
0.009
0.003
Lodge Creek
0.170
ICE
0.130
0.150
Marias River/Loma
0.001
ICE
0.062
0.032
Marias River/Shelby
0.007
ICE
0.127
0.067
Milk River/Chinook
0.073
ICE
0.252
0.162
Milk River/Havre
0.001
ICE
0.238
0.120
Missouri River/Cascade
0.006
0.029
0.022
0.019
Missouri River/Fort Benton
0.009
ICE
0.054
0.032
Muddy Creek
0.002
ICE
0.104
0.053
Pondera Creek
0.001
ICE
0.203
0.102
Smith River
0.002
ICE
0.113
0.058
Sun River/Ft. Shaw
0.001
0.001
0.006
0.004
Sian River/Vaughn
0.005
ICE
0.037
0.021
Teton River/Dutton
0.003
0.004
0.063
0.023
Teton River/Fort Benton
0.001
0.002
0.085
0.029
Mean
0.018
0.007
0.110
0.057
*Assumes concentrations less than 0.001 equal zero
57
Appendix C. Total phosphorus (P in mg/1)
Station
Summer
Fall
Spring
Mean
Big Sandy Creek
0.039
ICE
0.590
0.
314
Dearborn River
0.003
0.005
0.015
0.
008
Lodge Creek
0.220
ICE
0.335
0.
278
Marias River/Loma
0.012
ICE
0.959
0.
486
Marias River/Shelby
0.039
ICE
0.403
0.
221
Milk River/Chinook
0.110
ICE
1.670
0.
890
Milk River/Havre
0.014
ICE
0.888
0.
451
Missouri River/Cascade
0.018
0.040
0.043
0.
034
Missouri River/Fort Benton
0.059
ICE
0.233
0.
146
Muddy Creek
0.037
ICE
0.526
0.
282
Pondera Creek
0.019
ICE
3.380
1.
700
Smith River
0.024
ICE
0.436
0.
,230
Sun River/Fort Shaw
0.018
0.008
0.022
0.
016
Sun River/Vaughn
0.045
ICE
0.123
0.
,084
Teton River/Dutton
0.023
0.020
0.366
0.
.136
Teton River/Fort Benton
0.013
0.020
0.850
0.
.294
Mean
0.043
0.019
0.677
0.
.314
58
Appendix D. Nitrate plus nitrite (NO^ + NO2 as N in mg/1)
Station
Summer
Fall
Spring
Mean*
Big Sandy Creek
<0.01
ICE
0.30
0.15
Dearborn River
<0.01
40.01
0.06
0.02
Lodge Creek
< 0.01
ICE
0.70
0.35
Marias River/Loma
^lO.Ol
ICE
0.60
0.30
Marias River/Shelby
^0.01
ICE
0.80
0.40
Milk River/Chinook
0
0
ICE
0.30
0.15
Milk River/Havre
0.10
ICE
0.30
0.20
Missouri River/Cascade
.4 0.01
0.24
0.15
0.13
Missouri River/Fort Benton
4 0.01
ICE
0.40
0.20
Muddy Creek
>1.00**
ICE
5.70
>3.35
Pondera Creek
<0.01
ICE
0.70
0.35
Smith River
0
0
ICE
0.16
0.08
Sun River/Fort Shaw
0.51
0.91
0.14
0.52
Sun River/Vaughn
0.84
ICE
0.73
0.78
Teton River/Dutton
< 0.01
0.90
0.30
0.40
Teton River/Fort Benton
4; 0.01
0.70
0.60
0.43
Mean*
>0.15
0.55
0.75
> .46
*Assumes concentrations less than 0.01 equal zero.
**Insuf f icient sample. Actual value not determined.
59
Appendix E. Ammonia (NH3 as N in mg/1)
Station
Summer
Fall
Spring
Mean*
Big Sandy Creek
0.01
ICE
0.21
0.11
Dearborn River
^0.01
0.02
o.di
0.01
Lodge Creek
0.06
ICE
0.16
0.11
Marias River/Loma
0.01
ICE
0.05
0.02
Marias River/Shelby
0.01
ICE
0.12
0.06
Milk River/Chinook
4.0.01
ICE
0.27
0.14
Milk River/Havre
0.01
ICE
0.20
0.11
Missouri River/Cascade
4 0.01
0.02
0.01
0.02
Missouri River/Fort Benton
4 0.01
ICE
0.04
0.02
Muddy Creek
4 0.01
ICE
0.08
0.04
Pondera Creek
0.04
ICE
0.12
0.08
Smith River
<0.01
ICE
0.05
0.02
Sun River/Fort Shaw
0.01
0.16
0.01
0.06
Sun River/Vaughn
0.02
ICE
0.04
0.03
Teton River/Dutton
4 0.01
0.06
0.06
0.04
Teton River/Fort Benton
4 0.01
0.05
0.06
0.04
Mean*
0.01
0.06
0.09
0.05
*Assumes concentrations less than 0.01 equal zero
60
Appendix F. Kjeldahl nitrogen (N in mg/1)
Station
Summer
Fall
Spring
Mean
Big Sandy Creek
0.76
ICE
2.80
1.
78
Dearborn River
0.17
0.08
0.20
0.
15
Lodge Creek
0.64
ICE
1.50
1.
07
Marias River/Loma
0.26
ICE
3.45
1.
86
Marias River/Shelby
0.38
ICE
1.68
1.
03
Milk River/Chinook
0.50
ICE
4.00
2.
25
Milk River/Havre
0.35
ICE
1.06
0.
70
Missouri River/Cascade
0.30
0.23
0.25
0.
26
Missouri River/Fort Benton
0.63
ICE
0.51
0.
57
Muddy Creek
0.33
ICE
2.5
1.
42
Pondera Creek
0.67
ICE
5.95
3.
31
Smith River
0.31
ICE
1.73
1.
02
Sun River/Fort Shaw
0.30
0.17
0.21
0.
26
Sun River/Vaughn
0.54
ICE
1.15
0.
84
Teton River/ Dutton
0.33
0.32
1.45
0.
70
Teton River/Fort Benton
0. 30
0.30
2.90
1.
17
Mean
0.42
0.22
1.96
1.
06
m
- 61
Appendix G. Water quality requirements of major diatom species
CODE
SPECIES
WATER QUALITY REQUIREMENTS
REFERENCE (S)
ACMI
Achnanthes minutissima Kutz.
Optimum pH
7. 5-7. 8; "high oxygen concentrations"
Lowe, 1974
ACMO
Achnanthes microcephala (Kutz.) Grun.
Optimum pH
6. 4-6. 6; tolerates some salt
Lowe, 1974
AMPE
Amphora perpusilla (Grun.) Grun.
Alkaliphil
(pH>7); epilithic (fixed, solid surfaces)
Patrick and
Reimer, 1975
APPE
Amphipleura pellucida Kutz.
Optimum pH
water
7.3; eutrophic; hard to slightly brackish
Lowe, 1974,
Patrick and
Reimer, 1966
CMAF
Cymbella af finis Kutz.
Optimum pH
7. 8-8. 5; summer form; tolerates some salt
Lowe, 1974
CMMC
Cymbella microcephala Grun.
Optimum pH
some salt
7.2; well aerated habitats; tolerates
Lowe, 1974,
Patrick and
Reimer, 1975
CMMN
Cymbella minuta Hilse ex Rabh.
Optimum pH
7. 7-7. 8; widespread; tolerates some salt
Lowe, 1974,
Patrick and
Reimer, 1975
COPL
Cocconeis placentula Ehr.
Optimum pH
8; epiphytic; tolerates some salt
Lowe, 1974
CYME
Cyclotella meneghiniana Kutz.
Optimum pH
8. 0-8. 5; halophilous; fall maximum
Lowe, 1974
DITE
Diatoma tenue Ag.
Optimum pH
water
7. 4-7. 8; halophilous; slightly salty
Lowe, 1974
Patrick and
Reimer, 1966
DIVU
Diatoma vulgare Bory
Optimum pH 8.2; eutrophic; winter dominant; cool,
flowing water
Lowe, 1974,
Patrick and
Reimer, 1966
DPPU
Diploneis puella (Schum.) Cl.
Hard to slightly salty water
Patrick and
Reimer, 1966
>
Appendix G. (Continued)
CODE
SPECIES
ENOR
Entomoneis ornata (J.W. Bail.) Reim.
EPSO
Epithemia sorex Kutz.
FRVA
Fragilaria vaucheriae (Kutz.) Peters
COOL
Gomphonema olivaceum (Lyngb . ) Kutz.
COTE
Gomphonema tenellum Kutz.
NAMI
1
Navicula minima Grun.
2 NAPE
Navicula perparva Hust.
NARA
Navicula radiosa Kutz.
NATR
Navicula tripunctata (O.F. Mull.) Bory
NIAC
Nitzschia acicularis W. Sm.
NIDI
Nitzschia dissipata (Kutz.) Grun.
NIFR
Nitzschia frustulum Kutz.
NIMI
Nitzschia microcephala Grun.
NIPA
Nitzschia palea (Kutz.) W. Sm.
RHCU
Rhoicosphenia curvata (Kutz.) Grun. ex Rabh
•i
WATER QUALITY REQUIREMENTS
Freshwater (<500 mg/1 Cl ); mud bottoms
Optimum pH 8. 3-8. 5; eutrophic; tolerates some salt
Optimum pH 6. 5-6. 9; eutrophic; o-15°C
pH range 6. 4-9.0; eutrophic; winter or spring form
Unknown
Optimum pH 7. 5-8.0; eutrophic; tolerates some salt
Optimum pH 8. 2-8. 4; obligate nitrogen heterotroph
Optimum pH 6. 5-7.0; water of low mineral content
Optimum pH 8.3; eutrophic; tolerates some salt
Optimum pH 8. 3-8. 5; eutrophic; tolerates some salt
Optimum pH 8.0; eutrophic; tolerates some salt
pH range 6. 2-8. 6; eutrophic; tolerates broad range
of salt
Optimum pH 8. 3-8. 5; stimulated by small amounts of
salt
Optimum pH 8.4; eutrophic; 0-30°C
Optimum pH>8.0; eutrophic; epiphytic; flowing water
REFERENCE (f
Patrick anc
Reimer, IS
Lowe, 1974
Lowe, 1974
Lowe, 1974
Lowe, 1974
Schoeman, 1
Lowe, 1974.
Patrick ai
Reimer, IS
Lowe, 1974
Lowe , 1974
Lowe, 1974
Lowe, 1974
Lowe, 1974
Lowe, 1974
Lowe, 1974
endix G. (Continued)
)E
SPECIES
WATER QUALITY REQUIREMENTS
lA Stephanodiscus hantzschii Grun.
■U Stephanodiscus subtilis Van Goor
)E Synedra demerarae Grun.
’U Synedra pulchella Ralfs ex Kutz.
Optimum pH 8.2; eutrophic; euplanktonic ; spring form
Unknown
Unknown
Water of high conductivity and mineral content
lU Synedra rumpens Kutz.
pH range 6. 0-9.0; tolerates some salt; widely dis-
tributed
IL Synedra ulna (Nitz.) Ehr.
pH range 5. 7-9.0; eutrophic; tolerates some salt
REFERENCE (S)
Lowe, 1974
Patrick and
Reimer, 1966
Lowe, 1974,
Patrick and
Reimer, 1966
Lowe, 1974
i
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