A supplemental assessment of use support in the Teton River based on periphyton composition and community structure

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MONTANA STATE LIBRARY

3 0864 1001 6091 3

A SUPPLEMENTAL ASSESSMENT OF USE SUPPORT

IN THE TETON RIVER

BASED ON PERIPHYTON COMPOSITION

AND COMMUNITY STRUCTURE

Prepared for:

State of Montana
Department of Environmental Quality-
Monitoring and Data Management Bureau
P.O. Box 200901
Helena, Montana 59620-0901

Project Officer: Carol Endicott
DEQ Contract No. 200012

Prepared by:

Loren L. Bahls, Ph.D.
Hannaea
1032 Twelfth Avenue
Helena, Montana 59601

DEC 0 2 fl99

DLQ I F'i'A

T/\TE DOCUMENTS COLLECTION

--^t Bureau

5 2002

MONTANA STATE LIBRARY

1515 E. 6th AVE.
HELENA, MONTANA 59620

December 1999

Printed on Recycled Paper

SUMMARY

Composite periphyton samples were collected from natural
substrates at 17 sites on the Teton River and tributaries in the
summer of 1998. All but 6 of these samples were evaluated in an
earlier report (Bahls 1999) . This report evaluates the support
of aquatic life uses at the remaining 6 sites: 3 on the North
and South Forks and 3 on the mainstem of the Teton River.

All 6 sites supported relatively small amounts of periphyton
growth. Insufficient numbers of diatoms were available in the
samples from the North and South Forks for conducting diatom
proportional counts, probably because of low nutrients.

The site at the Gaging Station had good water quality and
only minor impairment. Increasing diatom species richness and
diversity values and decreasing pollution index values indicated
increasing nutrient enrichment between the lower site on the
North Fork and the site at Breen's above Choteau .

Diatom metrics at the site near Collins indicated full
support of aquatic life uses when compared to criteria developed
for mountain streams, but only partial support and moderate
impairment when compared to criteria for prairie streams. The
probable causes of impairment here were siltation and nutrient
enrichment.

The sites at Kelly Ranch and Dent Bridge had very similar
diatom floras and metrics that indicated moderate impairment and
partial support of aquatic life uses. These sites had very low
diatom diversity for prairie streams and were dominated by a
single species of free-living diatom. The probable causes of
impairment here were siltation and habitat homogeneity (lack of
habitat diversity) .

INTRODUCTION

Composite periphyton samples were collected at 2 sites on
McDonald Creek and 15 sites on the Teton River in 1998. Analyses
of the McDonald Creek samples and of 9 of the Teton River samples
were reported earlier (Bahls 1999) . This report addresses the 6
Teton River samples that were not included in the earlier report.

This report evaluates the support of aquatic life uses, and
probable causes of impairment to those uses in the Teton River.
This evaluation is part of a larger assessment that was conducted
by staff of the Montana Department of Environmental Quality.

Evaluation of use support in this report is based on the
species composition and community structure of periphyton
(benthic algae) communities at 6 sites that were sampled in July
and August of 1998. The periphyton or phytobenthos community is
a basic biological component of all aquatic ecosystems.
Periphyton accounts for much of the primary production and
biological diversity of Montana streams (Bahls et al . 1992).

Plafkin et al . (1989) and Stevenson and Bahls (1999) list
several advantages of using periphyton in biological assessments
of streams:

• Algae are universally present in large numbers in all
streams and unimpaired periphyton assemblages typically
support a large number (>30) of species;

• Algae have rapid reproduction rates and short life cycles,
making them useful indicators of short-term impacts,-

• As primary producers, algae are most directly affected by
physical and chemical factors, such as temperature,
nutrients, and toxins;

• Sampling is quick, easy and inexpensive, and causes minimal
damage to resident biota and their habitat;

• Standard methods and criteria exist for evaluating the
composition, structure, and biomass of algal associations;

Identification to species is straightforward for the
diatoms, for which there is a large body of taxonomic and
ecological literature;

Excessive algae growth in streams is often correctly-
perceived as a problem by the public.

Periphyton and other biological communities reflect the
biological integrity^ of waterbodies ; restoring and
maintaining the biological integrity of waterbodies is a
goal of the federal Clean Water Act;

Periphyton and other biological communities integrate the
effects of different stressors and provide a measure of
their aggregate impact; and

Periphyton and other biological communities may be the only
practical means of evaluating impacts from non-point sources
of pollution where specific ambient criteria do not exist
(e.g., impacts that degrade habitat or increase nutrients).

Periphyton is a diverse as'sortment of simple photosynthetic
organisms called algae, and other microorganisms that live
attached to or in close proximity of the stream bottom. Most
algae, such as the diatoms, are microscopic. Diatoms are
distinguished by having a cell wall composed of opaline glass-- ■
hydrated amorphous silica. Diatoms often carpet a stream bottom
with a slippery brown film.

Some algae, such as the filamentous greens, are conspicuous
and their excessive growth may be aesthetically displeasing,
deplete dissolved oxygen, interfere with fishing and fish
spawning, clog irrigation intakes, create tastes and odors in
drinking water, and cause other problems.

The federal Clean Water Act directs states to develop water

^ Biological integrity is defined as "the ability of an
aquatic ecosystem to support and maintain a balanced, integrated,
adaptive community of organisms having a species composition,
diversity, and functional organization comparable to that of
natural habitats within a region" (Karr and Dudley 1981) .

pollution control plans (Total Maximum Daily Loads or TMDLs) that
set limits on pollution loading to water-quality limited waters.
Water-quality limited waters are lakes and stream segments that
do not meet water-quality standards, that is, that do not fully
support their beneficial uses. The Clean Water Act and EPA
regulations require each state to (1) identify waters that are
water-quality limited, (2) prioritize and target waters for
TMDLs, and (3) develop TMDL plans to attain and maintain water-
quality standards for all water-quality limited waters.

The purpose of this report is to provide information that
will help the State of Montana to determine whether certain
segments of the Teton River are water-quality limited and in need
of TMDLs .

PROJECT AREA AND SAMPLING SITES

The project area is in Teton and Chouteau Counties in
northcentral Montana. The Teton River is a tributary of the
Marias River in the Missouri River Drainage.

The North and South Forks of the Teton River head in the Bob
Marshall Wilderness and converge just east of the Rocky Mountain
Front about 20 miles west of Choteau, Montana. The Teton River
begins in the Northern Rockies Ecoregion, flows across the
Montana Valley and Foothill Prairies Ecoregion, and ends near
Fort Benton in the Northern Great Plains Ecoregion (Omernik and
Gallant 1987) .

The Teton River is classified B-1 above Deep Creek near
Choteau, B-2 between Deep Creek and Interstate 15, and B-3 from
1-15 to the mouth. The Teton River is stressed by dewatering for
agricultural irrigation, salinization (mostly discharges from
Freezeout Lake and Priest Butte Lakes) , channel instability,

habitat alteration, and sedimentation (MDEQ 1998; Carol Endicott,
MDEQ, personal communication) .

The headwaters of the Teton River begin in the Overthrust
Belt of the Northern Rocky Mountains . Here the surface geology-
consists of faulted blocks of Madison limestone alternating with
sandstones, shales, and mudstones of the Kootenai Formation. At
the base of the Rocky Mountain Front the Teton River flows across
a band of Bearpaw Shale that is about 20 miles wide. The lower
reaches of the river are underlain by Colorado Shale (Taylor and
Ashley, undated) .

Vegetation in the headwaters is mostly mixed conifer forest
dominated by douglas-fir and lodgepole pine, with mixed fescue
and wheatgrass grassland in the foothills, and shorter grasses
(e.g., needleandthread and related species) on the plains (USDA
1976) . The main land uses in the watershed are recreation,
waterfowl and wildlife production, livestock grazing, hay
production, and dryland farming. Choteau (pop. 1,729) is the
largest town in the watershed.

Periphyton samples were collected at 3 sites on the Forks of
the Teton River and 3 sites on the mainstem Teton River in July
and August 199 8 (maps; Table 1) . The 3 sites on the mainstem
extend from just below the forks to near the mouth. Elevations
at the sampling sites range from about 6,000 feet at the upper
sites on the North and South Forks to about 3,000 feet near the
mouth of the Teton River near Loma, Montana.

METHODS

Periphyton samples were collected following standard
operating procedures of the MDEQ Planning, Prevention, and
Assistance Division. Using appropriate tools, microalgae were

scraped, brushed, or sucked from natural substrates in proportion

to the rank of those substrates at the study site. Macroalgae
were picked by hand in proportion to their abundance at the site.
All collections of microalgae and macroalgae were pooled into a
common container and preserved with Lugol's (IKI) solution.

Samples were examined to estimate the relative abundance and
rank by biovolume of diatoms and genera of soft (non-diatom)
algae according to the method described in Bahls (1993) . Soft
algae were identified using Prescott (1978) , Smith (1950) , and
Whitford and Schumacher (1984) . These books also served as the
main references on the ecology of the soft algae.

After the identification of soft algae, raw periphyton
samples were cleaned of organic matter using sulfuric acid, and
permanent diatom slides were prepared in a high refractive index
mounting medium following Standard Methods for the Examination of
Water and Wastewater (APHA 1998) . For each slide, between 400
and 441 diatom cells (800 to 882 valves) were counted at random
and identified to species. The following were used as the main
taxonomic and autecological references for the diatoms: Krammer
and Lange-Bertalot 1986, 1988, 1991a, 1991b; Patrick and Reimer
1966, 1975. Lowe (1974) was also used extensively as an
ecological reference for the diatoms.

The diatom proportional counts were used to generate an
array of diatom association metrics (Table 2) . A metric is a
characteristic of the biota that changes in some predictable way
with increased human influence (Barbour et al . 1999) .

Metric values from the Teton River were compared to numeric
biocriteria developed for Montana streams (Tables 3 and 4) .
These criteria are based on metric values measured in least-
impaired reference streams (Bahls et al . 1992) and on metric
values measured in streams that are known to be impaired by

various sources and causes of pollution (Bahls 1993) .

Because of inherent differences in periphyton composition
and community structure. between mountain streams and prairie
streams, two different sets of criteria are provided (Tables 3
and 4) . For the purpose of periphyton assessment, mountain
streams are those located in the Rocky Mountain and Montana
Valley and 'Foothill Prairies Ecoregions (Omernik and Gallant
1987) . These streams are generally 'classified B-1 and B-2 in the
Montana Surface Water Quality Standards. Prairie streams are
those located in the Great Plains Ecoregions and are generally
classified B-3 and C-3.

Of the 6 sites addressed in this report, periphyton metrics
from the forks of the Teton River and from the site just below
their confluence will be compared to criteria for mountain
streams in Table 3 . Metrics from the site near the mouth at
Kelly Ranch will be compared to criteria for prairie streams in
Table 4. Metrics from the remaining site near Collins will be
compared to criteria for both mountain and prairie streams.

The criteria in Tables 3 and 4 distinguish among four levels
of impairment and three levels of aquatic life use support: no
impairment or only minor impairment (full support) ; moderate
impairment (partial support) ; and severe impairment (nonsupport) .
These impairment levels correspond to excellent, good, fair, and
poor biological integrity, respectively.

Only periphyton samples collected in summer (June 21-
September 21) can be compared with confidence to reference stream
samples because metric values change seasonally and summer is the
season in which reference streams and impaired streams were
sampled for the purpose of biocriteria development.

Quality Assurance. Several steps were taken to assure that

7

•

the study results are accurate and reproducible. Upon receipt of
the samples, station and sample information were recorded in a
laboratory notebook and samples were assigned a unique number
compatible with the Montana Diatom Database, e.g., 1056-06. The
first part of this number (1056) designates the sampling site
(North Fork Teton River at Trailhead) ; the second part of the
number (06) designates the number of periphyton samples that have
been collected at this site to date for which data have been
entered into the Montana Diatom Database.

Sample observations and analyses of soft (non-diatom) algae
were recorded in a lab notebook along with station and sample
information provided by MDEQ . A portion of the raw sample was
used to make duplicate diatom slides.

On completion of the project, station information, sample
information, and diatom proportional count data will be entered
into the Montana Diatom Database. One set of diatom slides will
be deposited in the University of Montana Herbarium in Missoula.
The other set of slides will be retained by Hannaea in Helena.

RESULTS AND DISCUSSION

•Results are presented in Tables 5, 6, and 7, located near
the end of this report following the Literature Cited section.
Spreadsheets containing completed diatom proportional counts,
with species pollution tolerance classes (PTC) and calculated
percent abundances, are attached as Appendix A.

SAMPLE NOTES

All of the following samples were preserved with alcohol.
Because of the small numbers of diatoms in these samples, the
entire volume of each sample was processed for preparing diatom
slides .

North Fork Teton River at Trailhead (#2). No diatoms were
observed in this sample during a 10 minute scan. Diatom slides ■
were not prepared for this sample. The Calothrix in this sample
was colonial, lacked heterocysts, and had filaments that extended
beyond the sheaths, ending in fine points. This is a reference
site for the mountain ecoregions (Bahls et al . 1992) .

South Fork Teton River above Trailhead (#3) . Only three
diatom cells were observed during a 10 minute scan.

8

South Fork Teton River at Abbott's (#4) . Diatoms were very-
sparse in this sample.

Teton River at Gaging Station (#1) . Diatoms were sparse.

Teton River near Collins (#13) . This sample was silty and
diatoms were sparse .

Teton River at Kelly Ranch ("new site") . The Cladophora
in this sample was senescent. The sample was silty.

NON- DIATOM ALGAE

Algae were sparse in all of the samples (Table 5) . Diatoms
were rare to common and the only group present at all of the
sites. Besides diatoms, only two genera of green algae and two
genera of bluegreen algae were present .

Diatoms were rare in the samples from the North and South
Forks. The small standing crops of algae here probably reflect
low nutrient concentrations at these sites. The mainstem
supported larger standing crops. Phormidium, a eurytopic
cyanobacterium with many species, was the most abundant taxon at
these Teton River sites. Cladophora was present (but not
abundant) only at the farthest downstream site (Kelly Ranch) .

DIATOMS

The sample from the North Fork at the trailhead did not have
enough diatoms to warrant making diatom slides. Slides prepared
from samples collected at the 2 South Fork sites did not have
enough diatoms to allow for a proportional count of 800 valves.
For these reasons, diatom metrics could not be generated for
these 3 sites.

•

The site at the Gaging Station below the forks was dominated
by the pollution sensitive diatoms Achnanthes winutissiwa and
Gomphonema bohewicum (Table 6) . The number of species counted,
diatom species diversity, pollution and siltation index values
all indicated excellent water quality. Only minor impairment was
indicated by the disturbance index and percent dominant species.
This stress causing this impairment was probably natural in
origin .

The Gaging Station site had about half of its diatom flora
in common with the North Fork site upstream (Table 6) . This is
to be expected where two co-equal tributaries (i.e., the North
and South Forks) join and their floras are combined. A larger
change occurred between the Gaging Station and the next site
downstream at Breen's; these two sites shared less than a third
of their diatom floras. These 5 upper sites show progressively
increasing species richness and diversity (Table 6) , which is
probably caused by inorganic nutrient enrichment. The site at
Breen's shows minor impairment by nutrient enrichment.

When assessed using criteria developed for mountain streams,
the site near Collins shows minor impairment because of depressed
diversity and species richness, and a large percentage of the
dominant diatom Amphora pediculus (Table 6) . Most species of
Amphora are motile (Round et al . 1990) . Amphora pediculus is an
alkaliphilous species, prefers large concentrations of inorganic
nutrients, and is indifferent to small amounts of salt (Lowe
1974) . It is rarely abundant in stream samples (Patrick and
Reimer 1975) . Large numbers of this diatom near Collins are
probably a response to siltation and nutrient enrichment.

When compared to criteria developed for prairie streams, the
site near Collins exhibited moderate impairment and only partial
support of aquatic life uses (Table 7) . This is because prairie
streams are typically richer in species and have higher species

10

diversity values than mountain streams. The site near Collins
had very little in common, f loristically , with the closest sites
upstream (Highway 221) and downstream (Interstate 15).

The site at Kelly Ranch had a diatom flora that was very
similar to the one at Dent Bridge (Table 7) . The two sites
shared over 80% of their diatom floras. Both sites suffered from
moderate impairment and partial support of aquatic life uses as

indicated by low diversity and dominance by a single species.
Kelly Ranch also had a very small number of species for a prairie
stream. The causes of impairment at both sites were probably
siltation and the homogeneity of microhabitats (lack of habitat
diversity) .

Both the Kelly Ranch and Dent Bridge sites were dominated by
Cymhella sinuata {=Reimeria sinuata) . ■ This is a free-living
species (Round et al . 1990) with ecological requirements that are
very similar to those of Amphora pediculus (Lowe 1974) . Amphora
pediculus was the second most abundant diatom at Kelly Ranch.
Both species probably tolerate siltation because of their
motility and/or free-living lifestyles. They are not included in
the siltation index because they are seldom abundant in streams.
Also common at both sites was Navicula tripunctata, a motile
species that is included in the siltation index.

The diatom flora changed considerably between Kelly Ranch
and the site near the mouth of the Teton River. These sites had
less than a third of their floras in common (Table 7) . Habitat
conditions were evidently much improved near the mouth over
conditions at Dent Bridge and Kelly Ranch.

^

11

•

LITERATURE CITED

APHA. 1998. Standard Methods for the Examination of Water and
Wastewater. 20th Edition. American Public Health
Association, Washington, D.C.

Bahls, L.L. 1979. Benthic diatom diversity as a measure of
water quality. Proc . Mont. Acad. Sci . 38:1-6.

Bahls, L.L. 1993. Periphyton Bioassessment Methods for Montana"
Streams (Revised) . Montana Department of Health and
Environmental Sciences, Helena.

Bahls, L.L. 1999. Support of Aquatic Life Uses in McDonald

Creek and the Teton River Based on Periphyton Composition
and Community Structure. Montana Department of
Environmental Quality, Helena.

Bahls, L.L., and P. A. Bahls. 1976. An Algal Survey of Surface
Waters in Eastern Montana Suspected to be Influenced by
Saline Seep, with Special Emphasis on Salinity Indicators
and Potentially Toxic Species. Montana Department of Health
and Environmental Sciences, Helena.

Bahls, L.L., Bob Bukantis, and Steve Tralles. 1992. Benchmark

Biology of Montana Reference Streams. Montana Department of
Health and Environmental Sciences, Helena.

Barbour, M.T., J. Gerritsen, B.D. Snyder, and J.B. Stribling.

1999. Rapid Bioassessment Protocols for Use in Streams and
Wadeable Rivers : Periphyton, Benthic Macroinvertebrates and
Fish. Second Edition. EPA/841-B-99-002 . U.S. EPA, Office
of Water, Washington, D.C.

Karr, J.R., and D.R. Dudley. 1981. Ecological perspectives on
water quality goals. Environmental Management 5:55-69.

Krammer, K., and H. Lange-Bertalot . 1986. Bacillariophyceae,
Part 2, Volume 1: Naviculaceae . In Ettl, H., J. Gerloff,
H. Heynig, and D. Mollenhauer (eds.), Freshwater Flora of
Middle Europe. Gustav Fischer Publisher, New York.

Krammer, K., and H. Lange-Bertalot. 1988. Bacillariophyceae,
Part 2, Volume 2: Bacillariaceae, Epithemiaceae,
Surirellaceae . In Ettl, H., J. Gerloff, H. Heynig, and D.
Mollenhauer (eds.). Freshwater Flora of Middle Europe.
Gustav Fischer Publisher, New York.

12

Krammer, K., and H. Lange-Bertalot . 1991a. Bacillariophyceae,
Part 2, Volume 3: Centrales, Fragilariaceae, Eunotiaceae.
In Ettl, H., J. Gerloff, H. Heynig, and D. Mollenhauer
(eds.), Freshwater Flora of Middle Europe. Gustav Fischer
Publisher, Stuttgart.

Krammer, K., and H. Lange-Bertalot. 1991b. Bacillariophyceae,
Part 2, Volume 4: Achnanthaceae, Critical Supplement to
Navicula (Lineolatae) and Gomphonema, Complete List of
Literature for Volumes 1-4. In Ettl, H., G. Gartner, J.
Gerloff, H. Heynig, and D. Mollenhauer (eds.). Freshwater
Flora of Middle Europe. Gustav Fischer Publisher, Stuttgart.

Lange-Bertalot, Horst . 1979. Pollution tolerance of diatoms as
a criterion for water quality estimation. Nova Hedwigia
64:285-304.

Lowe, R.L. 1974. Environmental Requirements and Pollution
Tolerance of Freshwater Diatoms. EPA-670/4-74-005 .

McFarland, B.H., B.K. Hill, and W.T. Willingham. 1997. Abnormal
Fragilaria spp . (Bacillariophyceae) in streams impacted by
mine drainage. Jour, of Freshwater Ecology 12 (1) : 141-149 .

MDEQ. 1998. Waterbodies in Need of TMDL Development. Montana
Department of Environmental Quality, Helena.

Om.ernik, J.M., and A.L. Gallant. 1987. Ecoregions of the West

Central United States (map) . U. S. Environmental Protection
Agency, Corvallis, Oregon.

Patrick, Ruth, and C.W. Reimer. 1966. The Diatoms of The United
States Exclusive of Alaska and Hawaii. Volume 1:
Fragilariaceae, Eunotiaceae, Achnanthaceae, Naviculaceae .
Monograph Number 13, The Academy of Natural Sciences,
Philadelphia .

Patrick, Ruth, and C.W. Reimer. 1975. The Diatoms of The United
States Exclusive of Alaska and Hawaii. Volume 2, Part 1:
Entomoneidaceae, Cymbellaceae, Gomphonemaceae,
Epithemiaceae . Nonograph Number 13, The Academy of Natural
Sciences, Philadelphia.

Plafkin, J.L., M.T. Barbour, K.D. Porter, S.K. Gross, and R.M.
Hughes. 1989. Rapid Bioassessment Protocols for Use in
Rivers and Streams: Benthic Macroinvertebrates and Fish.
EPA 440-4-89-001.

Prescott, G.W. 1978. How to Know the Freshwater Algae. Third
Edition. Wm. C. Brown Company Publishers, Dubuque, Iowa.

13

Round, F.E., R.M. Crawford, and D.G. Mann. The Diatoms: Biology
Sc Morphology of the Genera. Cambridge University Press,
Cambridge, U.K.

Smith, G.M. 1950. the Fresh-Water Algae of The United States.
McGraw-Hill Book Company, New York.

Stevenson, R.J., and L.L. Bahls. 1999. Periphyton Protocols.
Chapter 6 in Barbour, M.T., J. Gerritsen, B.D. Snyder, and
J.B. Stribling. Rapid Bioassessment Protocols for Use in
Streams and Wadeable Rivers: Periphyton, Benthic
Macroinvertebrates and Fish. Second Edition. EPA/841-B-99-
002. U.S. EPA, Office of Water, Washington, D.C.

Taylor, R.L, and J.M. Ashley. Undated. Geological Map of

Montana and Yellowstone National Park. Department of Earth
Sciences, Montana State University, Bozeman.

USDA. 1976. Climax Vegetation of Montana (map) . U. S.

Department of Agriculture, Soil Conservation Service,
Cartographic Unit, Portland.

Whitford, L.A., and G.J. Schuma-cher. 1984. A Manual of Fresh-
Water Algae (Revised) . Sparks Press, Raleigh, North
Carolina .

Whittaker, R.H. 1952. A study of summer foliage insect

communities in the Great Smokey Mountains. Ecological
Monographs 22:6.

14

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DIATOM PROPORTIONAL COUNTS

Teton River at Gaging Station (Site *1)

12/1/99

Sample I Genus/Species/Varietv

PTC

Count

Percent

095302 Achnanthes blasolettiana

3

56

6.60

095302;Achnanthes laevis

3

7

0.83

095302iAchnanthes minutissima

3

252

29.72

095302lAnnphora inariensis

3

2

0.24

095 302!Annphora pediculus

3

2

0.24

095302

Caloneis bacillum

2

5

0.59

095302

Cocconeis placentula

3

15

1.77

095302!Cyclotella meneqhiniana

2

2

0.24

095302

Cvmbella affinis

3

52

6.13

095302

Cvmbella cesatii

3

2

0.24

095302

Cymbella cymbiformis

3

6

0.71

095302

Cymbella delicatula

3

10

1.18

095302

Cymbella hebridica

3

8

0.94

095302

Cymbella microcephala

2

8

0.94

095302 Cymbella minuta

2

7

0.83

095302

Cymbella sileslaca

2

8

0.94

095302

Cymbella sinuata

3

32

3.77

095302

Denticula subtilis

2

9

1.06

095302

Diatoma hiemale

3

13

1.53

095302

Diatoma vulqare

3

3

0.35

095302

Diploneis oblonqella

3

2

0.24

095302

Eunotia sp.

3

2

0.24

095302

Fraqilaria brevistriata

3

4

0.47

095302

Fraqilaria capucina

2

2

0.24

095302lFraqilaria construens

3

12

1.42

095302'Fraqilaria leptostauron

3

13

1.53

095302 Fraqilaria pinnata

3

28

3.30

095302iFraqilaria vaucheriae

2

27

3.18

095302IGomphonema anqustatum

2

4

0.47

095302lGomphonema bohemicum

3

107

12.62

095302iGomphonema minutum

3

43

5.07

095302lGomphonema olivaceoides

3

14

1.65

095302lGomphonema parvulum

1

9

1.06

095302lGomphonema subtile

3

12

1.42

095302!Hannaea arcus

3

20

2.36

095302

Meridion circulare

3

2

0.24

095302

Navicula cryptotenella

2

5

0.59

095302

Navicula exilis

2

1

0.12

095302

Navicula qregaria

2

2

0.24

095302|Navicula subtilissima

3

2

0.24

095302:Navicula tripunctata

3

1

0.12

095302lNit2schia amphibia

2

7

0.83

095302

Nitzschia dissipata

3

3

0.35

095302

Nitzschia fonticola

3

2

0.24

095302

Nitzschia linearis

2

2

0.24

095302

Nitzschia palea

1

6

0.71

095302

Synedra rumpens

2

10

1.18

095302

Synedra ulna

2

7

0.83

Page 1

Teton River near Collins above 1-15 (Site #1 3)

12/1/99

Sample Genus/Species/Variety

PTC Count 1 Percent

182501 Achnanthes biasolettiana

3 25l 2.89

182501

Achnanthes nninutissinna

3 40

4.63

182501

Amphora inariensis

3 84

9.72

182501

Amphora libyca

3

1

0.12

182501

Amphora pediculus

3

413

47.80

182501

Caloneis bacillum

2 1

0.12

182501

Cocconeis placentula

3 3

0.35

182501

Cymatopleura solea

2 1

0.12

182501

Cymbella affinis

3

2

0.23

1 82501 iCymbella amphicephala

3

2

0.23

1 82501 ICymbella muelleri

2

6

0.69

1 82501 iCymbella sinuata

3

144

16.67

1 82501 !Denticula kuetzinqii

3

39

4.51

182501

Gomphonema olivaceum

3

5

0.58

182501

Gomphonema parvulum

1

4

■ 0.46

1 82501 iNavicula caterva

2

7

0.81

182501 !Navicula cryptotenella

2

2

0.23

182501

Navicula reichardtiana

2

2

0.23

182501

Navlcula tripunctata

3

49! 5.67|

182501

Nitzschia amphibia

- 2

15

1.74

182501

Nitzschia dissipata

3

2

0.23

182501

Nitzschia frustulum

2

2

0.23

182501

Rhopalodia gibba

2

4

0.46

1 82501 'Synedra ulna

2

1

0.12

Page 1

Teton River at Kelley Ranch (New Site)

12/1/99

Sample Genus/Species/Variety

PTC

Count

Percent

182601 Achnanthes minutissima

3

13

1.47

1 82601 lAmphora foqediana

3

2

0.23

182601 Amphora inariensis

3

9

1.02

182601 Amphora pediculus

3

106

12.02

182601

Caloneis amphisbaena

2

3

0.34

182601

Caloneis bacillum

2

9

1.02

182601

Caloneis silicula

2

17

1.93

182601

Cymbella muelleri

2

8

0.91

182601

Cymbella silesiaca

2

2

0.23

182601

Cymbella sinuata

3

568

64.40

182601

Denticula kuetzinqii

3

7

0.79

182601

Epithemia sorex

3

13

1.47

182601

Fraqilaria construens

3

4

0.45

182601

Gomphonema parvulum

1

5

0.57

182601

Hantzschia amphioxys

2

3

0.34

182601

Navicula capitatoradiata

2

8

0.91

182601

Navicula tripunctata

3

77

8.73

182601

Nitzschia amphibia

2

6

0.68

182601

Nitzschia dissipata

3

3

0.34

182601

Nitzschia frustulum

2

12

1.36

182601

Nitzschia hunqarica

2

2

0.23

182601

Pinnularia microstauron

2

2

0.23

182601

Rhopalodia operculata

1

3

0.34

•

Page 1