xvEPA
United States
Environmental Protection
Agency
Research and Development
Environmental Research
Laboratory
Duluth MN 55804
1 78
Environmental
Effects of Western
Coal Combustion
Part II
The Aquatic
Macroinvertebrates of
Rosebud Creek,
Montana
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RESEARCH REPORTING SERIES
Research reports of the Office of Research and Development, U.S. Environmental
Protection Agency, have been grouped into nine series. These nine broad cate-
gories were established to facilitate further development and application of en-
vironmental technology. Elimination of traditional grouping was consciously
planned to foster technology transfer and a maximum interface in related fields.
The nine series are:
1. Environmental Health Effects Research
2. Environmental Protection Technology
3. Ecological Research
4. Environmental Monitoring
5. Socioeconomic Environmental Studies
6. Scientific and Technical Assessment Reports (STAR)
7. Interagency Energy-Environment Research and Development
8. "Special" Reports
9. Miscellaneous Reports
This report has been assigned to the ECOLOGICAL RESEARCH series. This series
describes research on the effects of pollution on humans, plant and animal spe-
cies, and materials. Problems are assessed for their long- and short-term influ-
ences. Investigations include formation, transport, and pathway studies to deter-
mine the fate of pollutants and their effects. This work provides the technical basis
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aquatic, terrestrial, and atmospheric environments.
This document is available to the public through the National Technical Informa-
tion Service, Springfield, Virginia 22161.
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EPA-600/3-78-099
November 1978
ENVIRONMENTAL EFFECTS OF WESTERN COAL COMBUSTION
Part II - The Aquatic Macroinvertebrates of Rosebud Creek, Montana
by
Steven F. Baril
Department of Biology
Montana State University
Bozeman, Montana 59717
Robert J. Luedtke
Fisheries Bioassay Laboratory
Montana State University
Bozeman, Montana 59717
George R. Roemhild
Department of Biology
Montana State University
Bozeman, Montana 59717
Grant No. R803950
Project Officer
Donald I. Mount
Environmental Research Laboratory
Duluth, Minnesota 55804
ENVIRONMENTAL RESEARCH LABORATORY
OFFICE OF RESEARCH AND DEVELOPMENT
U.S. ENVIRONMENTAL PROTECTION AGENCY
DULUTH, MINNESOTA 55804
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DISCLAIMER
This report has been reviewed by the Environmental Research Laboratory,
U.S. Environmental Protection Agency, and approved for publication. Approval
does not signify that the contents necessarily reflect the views and policies
of the U.S. Environmental Protection Agency, nor does mention of trade names
or commercial products constitute endorsement or recommendation for use.
ii
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FOREWORD
The following report describes the impact of a mine mouth coal-fired
power plant on the macroinvertebrates of Rosebud Creek, Montana. The study
was limited to a short period of operation after start-up and before all units
were operating. Factors such as turbidity and temperature among others
appeared to cause more change than impact from the power plant. Other surveys
over time are needed to be sure of the true impacts.
Donald I. Mount, Ph.D.
Director
Environmental Research Laboratory-Duluth
-------
ABSTRACT
The aquatic macroinvertebrates of Rosebud Creek, Montana, were sampled
between February 1976 and March 1977 to provide data on their abundance,
distribution, and diversity. The sampling program was initiated during the
first year of operation of the coal-fired power plants located at Col strip,
Montana. The purpose of the study was to determine if any immediate impacts
of the power plant operation on the macroinvertebrate communities of Rosebud
Creek could be detected and to provide data for comparisons with future
studies.
Rosebud Creek supported a diverse bottom fauna with high population
numbers composed of species adapted to the turbid, silty conditions which are
common in the prairie streams of eastern Montana. Intact riparian vegetation
appeared to be important in maintaining stream bank stability and provided an
essential food source.
It was concluded that faunal variation among sampling stations during
the study period was attributable to physical factors including turbidity,
water temperature, current velocity, and substrate, and not to potential
impacts from coal mining and combustion.
IV
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CONTENTS
Foreword ill
Abstract iv
Figures vi
Tables vii
Acknowledgments ix
I Introduction 1
II Conclusions 3
III Recommendations 4
IV Description of Study Area 5
V Description of Sampling Stations 9
VI Materials and Methods 15
VII Results 17
Macroinvertebrate Numbers 17
Macroinvertebrate Wet Weights 28
Macroinvertebrate Distribution 31
Diversity and Redundancy 57
VIII Discussion 64
Water Chemistry: Metals 64
Physical Conditions 64
Macroinvertebrate Abundance and Composition 67
Sampling Considerations 68
References 70
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FIGURES
Number Page
1 Benthic invertebrate sampling stations, Rosebud Creek,
Montana 6
2 Monthly mean discharges for Rosebud Creek at the mouth
and near Col strip for USGS water years 1975 and 1976 7
3 Mean numbers and ranges of aquatic macroinvertebrates
per sample, March 1976 to March 1977 21
4 Mean wet weights and ranges of aquatic macroinvertebrates
per sample, March 1976 to March 1977 22
5 Mean numbers and ranges of aquatic macroinvertebrate
taxa per sample, March 1976 to March 1977 23
6 Significantly different means for total macroinvertebrates,
taxa, and wet weights per sample 24
7 Average numbers of aquatic macroinvertebrates per introduced
substrate sample, May 1976 to March 1977 26
8 Average macroinvertebrate wet weights per introduced
substrate sample, May 1976 to March 1977 33
9 Average numbers of selected taxa per introduced substrate
sample, May 1976 to March 1977 55
10 Seasonal variations in mean total numbers of Hydropsyahe sp.
B per introduced substrate sample at Stations 1, 5, and 7,
May 1976 to November 1976 58
11 Seasonal variations in mean total numbers of Dubivaphia minima
per introduced substrate sample at Stations 1, 5, and 7,
May 1976 to November 1976 59
12 Seasonal variations in mean total numbers of Choroterpes
albiannulata per introduced substrate sample at Stations
1, 5, and 6, May 1976 to November 1976 60
13 Total taxa per station and taxa collected by each of three
sampling methods, March 1976 to March 1977 61
VI
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TABLES
Number Page
1 Descriptions and locations of sampling stations,
Rosebud Creek, Montana 10
2 Physical characteristics of sampling locations in 1976 11
3 Physical characteristics of riffle sites in 1976 12
4 Water quality data, means and ranges, March 1976 to
March 1977 13
5 Total numbers of samples from each station by three
sampling methods, March 1976 to March 1977 18
6 Mean current velocities 7.5 cm from the substrate and
15 cm upstream of introduced substrate samplers, May 1976
to March 1977 19
7 Average total numbers, wet weights, and numbers of taxa
of benthic macroinvertebrates, March 1976 to March 1977 20
8 Macroinvertebrate mean total numbers per taxon and mean
percentages of the sample (introduced substrate), May
1976 to March 1977 25
9 Adult aquatic insects collected along Rosebud Creek
during 1976 27
10 Mean total numbers of aquatic macroinvertebrates per m2
and average percentages of the sample, March 1976 to
March 1977 29
11 Mean wet weights for macroinvertebrate taxa and average
percentages of the sample (introduced substrate), May
1976 to March 1977 32
12 Mean wet weights per m2 and average percentages of the
sample for aquatic macroinvertebrates, March 1976 to
March 1977 34
13 Checklist and distribution of aquatic macroinvertebrates,
March 1976 to March 1977 36
vn
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Number Page
14 Number of occurrences and average numbers per occurrence
for aquatic macroinvertebrates collected in introduced
substrate samplers, May 1976 to March 1977 40
15 Number of occurrences and average numbers per occurrence
for aquatic macroinvertebrates collected in Ekman dredge
samples, March 1976 to October 1976 . . . . 46
16 Number of occurrences and average numbers per occurrence
for aquatic macroinvertebrates collected in modified Hess
samples, March 1976 to March 1977 50
17 Mean macroinvertebrate diversities and redundancy per
sample, March 1976 to March 1977 62
vi ii
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ACKNOWLEDGMENTS
The writers wish to acknowledge C. J. D. Brown, Rodney K. Skogerboe,
James V. Ward, and Robert V. Thurston for reviewing the manuscript. We are
grateful to the following experts who checked specimen identifications:
Harley P. Brown (Elmidae), D. G. Denning (Trichoptera), C. Dennis Hynes
(Tipulidae), Dennis M. Lehmkuhl (Ephemeroptera), George Roemhild (Hemiptera
and Zygoptera), John Rumely (grasses), and the USDA Agricultural Research
Service, Beltsville, Maryland (Diptera and Coleoptera). Access to Rosebud
Creek sampling stations was kindly granted by area residents Don Polich,
Patti Kluver, Wallace McRae, and John Bailey.
This research was supported by funds provided to the Natural Resource
Ecology Laboratory, Colorado State University, and the Fisheries Bioassay
Laboratory, Montana State University, by the Environmental Research Labora-
tory-Duluth, Environmental Protection Agency, Research Grant No. R803950.
IX
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SECTION I
INTRODUCTION
Expansion of coal mines and construction of coal combustion facilities
for the generating of electricity is underway in eastern Montana. Two 350-
megawatt electricity generators adjacent to the strip mines at Col strip
became operational in 1975 and 1976; two 750-megawatt power plants are now
being planned for this same location. These facilities, and others being
considered for eastern Montana, have the potential to impact the limited
water resources of this region. Consequently, the need to document the water
quality of the lotic and lentic environments of eastern Montana is important.
Information obtained can be useful for site planning and construction design
or for modification of existing and proposed power generators bath in eastern
Montana and elsewhere in the northern Great Plains.
The benthic macroinvertebrates, an important component of the aquatic
biota, are primary and secondary consumers in the aquatic ecosystem and are a
food source for fishes and other aquatic animals. Knowledge of their species
composition, distribution, and relative abundance provides a tool for mea-
suring water quality. The present study was undertaken to examine the
benthic macroinvertebrate community in Rosebud Creek, an eastern Montana
prairie stream which flows within 13 km of Colstrip, and in so doing, flows
into and out of possible environmental impact areas near the Colstrip coal
mine and power plant. Groundwater from the eastern portion of the strip mine
fields at Colstrip flows eastward toward Rosebud Creek (Montana State Depart-
ment of Natural Resources, 1974). The prevailing wind direction is south-
easterly which may result in the deposition of smokestack emissions in the
Rosebud Creek drainage including the north and south forks of Cow Creek, a
small intermittent stream which flows into Rosebud Creek (Skogerboe et al..
1978). It is not known to what extent the water quality of Rosebud Creek may
be affected by inorganic salts and organic compounds and complexes resulting
from the coal mining and combustion operation at Colstrip.
There is little published information on the physical and biological
characteristics of north-central United States prairie streams. Tradition-
ally, streams of the midcontinent (Kansas, Nebraska, South Dakota) have been
considered typical of the prairie. Jewell (1927) described the aquatic
biology of the prairie and presented a description of a typical prairie
stream. McCoy and Hales (1974) surveyed the physical, chemical, and biologi-
cal characteristics of eight eastern South Dakota streams. Limnology of
major lakes and drainages was summarized for the midcontinent states by
Carlander et al. (1963) and for Minnesota and the Dakotas by Eddy (1963).
Limnology of these regions may be similar in many respects to that of eastern
Montana due to similar topographies and climates.
1
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In the more immediate vicinity of Rosebud Creek, Clancy (1978) has sur-
veyed the benthic fauna of Sarpy Creek, a small ephemeral stream which flows
northward into the Yellowstone River, northwest of Col strip. East of the
Rosebud drainage, Gore (1975) studied the composition and abundance of the
benthic invertebrates in the Tongue River, and Rehwinkel et al. (1976)
studied the invertebrates of the Powder River. Both of these rivers also
flow northward into the Yellowstone. Information has also been provided on
the composition and abundance of benthic macroinvertebrates of the Yellowstone
River by Newell (1976).
The primary objective of the present study was to obtain information on
the species composition, distribution, and abundance of the benthic macro-
invertebrates of Rosebud Creek during the early operational stages of the
Col strip power plants. A variety of macroinvertebrate sampling techniques
was used to determine which might be most efficient to sample Rosebud Creek.
The study was conducted between July 1976 and March 1977. Data obtained will
provide a basis for comparisons with results of future studies of Rosebud
Creek after the present and possible additional power plants at Colstrip have
been operational for some time, and will also add to the current limited
body of knowledge about benthic macroinvertebrate communities in eastern
Montana prairie streams and rivers.
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SECTION II
CONCLUSIONS
1. Present longitudinal variations in abundance, distribution, and compo-
sition of the benthic invertebrate fauna in Rosebud Creek are attributed
to the intrinsic physical-chemical characteristics of the stream:
i.e., temperature, turbidity, substrate, and current velocity. There
was no evidence that these variations were attributable to influences
from coal mining and combustion.
2. Rosebud Creek supports an abundant benthic invertebrate fauna which is
adapted to the conditions (i.e., high turbidity, slow current velocity,
warm summer water temperature, and silted substratum) of a transition
prairie stream; however, increased severity of these conditions cor-
responds with decreased numbers and diversity of less tolerant species
at downstream stations.
3. Intact riparian vegetation, particularly grasses, stabilizes the banks
of Rosebud Creek and prevents serious erosion, sedimentation, and the
consequential unproductive shifting substrate common in many prairie
streams.
4. Introduced substrate samplers were efficient in collecting taxa from
long, slow stretches common in Rosebud Creek and provided a reliable
method for comparing invertebrate populations among sampling stations.
A modified Hess sampler was inadequate for this type of stream due to
insufficient riffle habitat for sampling. The Ekman dredge, effective
only for sampling areas of fine substrate, provided less information
than did introduced artificial substrates.
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SECTION III
RECOMMENDATIONS
1. Because of the projected increase in coal mining and combustion opera-
tions in and near the Rosebud Creek drainage, and the resultant poten-
tial for disturbance of the aquatic fauna, monitoring of the aquatic
macroinvertebrate fauna in Rosebud Creek should continue. Future
studies should be conducted on a year-round basis and should include
comprehensive monitoring of water chemistry.
2. Future coal mining, agriculture, and other activities in the vicinity of
Rosebud Creek and tributary streams should ensure maintenance of a
buffer zone of riparian vegetation and grasses to minimize erosion.
3. It is recommended for future surveys that the uppermost (control)
sampling station of this study be located downstream where ecological
conditions are more comparable to the other stations, and that the
lowermost sampling station be moved farther upstream for the same
reason. Physical and biological characteristics of the lowest station
in the present study showed influence of the Yellowstone River.
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SECTION IV
DESCRIPTION OF STUDY AREA
Rosebud Creek originates on the east slope of the Wolf Mountains in
Bighorn County, Montana, in the Crow Indian Reservation. It then flows
northeast through the Northern Cheyenne Indian Reservation and privately
owned lands for approximately 370 stream kilometers before joining the
Yellowstone River near Rosebud, Montana (Figure 1). The total area drained
is approximately 3,372 km2 (U.S. Geological Survey, 1976). An alluvial plain
about 0.8 km wide supports a sparsely populated, agriculturally oriented
economy. Alfalfa, wild hay, and cereal grains are cultivated, and the stream
provides water for irrigation and livestock.
The headwaters of Rosebud Creek are erosional in nature; there is a
steep gradient (4.8 m/km) with a riffle-pool system that is similar to many
mountain streams. After leaving the mountains near the town of Busby and
flowing onto the plains, the gradient decreases (2.5 m/km) and the stream
becomes depositional in nature. Long, slow reaches with sand or gravel
bottoms predominate, and silted areas are,common. Suspended and dissolved
solids also increase progressively downstream.
The shallow valley of Rosebud Creek is cut in sedimentary layers of the
Tertiary period. Relief is composed mainly of strata from the Paleocene
epoch, specifically sandstones, shales, and coal of the Fort Union formation
which erode at moderate rates. Coal outcrops have burned in the middle and
upper Rosebud drainage and have metamorphosed adjacent layers producing beds
of highly fractured clinker, red to lavender in color, often incorrectly
called scoria (Renick, 1929). This material is highly resistant to weathering
and forms much of the substratum of Rosebud Creek.
Alluvial soils of the floodplain and adjacent low terraces generally
consist of Havre and 61 endive loams, Harlem silty clay loams, and aerie
fluvaquents. These form deep, calcareous soils of good water-holding capacity
subject to moderate erosion. Areas of moderately saline soil are present
along the floodplain (L. Daniels, U.S. Soil Conservation Service, Forsyth,
Montana, personal communication).
Mean monthly flows for Rosebud Creek from October 1974 to September 1976
are shown in Figure 2. Normal peak flows occur during the spring resulting
from snowmelt runoff. Rapid fluctuations in discharge can occur during
spring and summer because of rainfall. The historical mean annual flow is
35.8 cfs (1.01 m3 per sec); mean flow for March, the month of maximum flow,
is 84.3 cfs (2.39 m3 per sec); and the mean flow for September, the month of
minimum flow, is 6.4 cfs (0.18 m3 per sec). Records show approximately
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Ytllowtton* livtr
,/*%
ot«b
l-7»Somplt Slt««
10
20 30
Kilomtt«rs
Figure 1. Benthic invertebrate sampling stations,
Rosebud Creek, Montana.
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O 300
UJ
CO
UJ
Q.
UJ 200
Ul
u.
o
CD
O
UJ
o
100
1974
1976
NEAR MOUTH
NEAR COLSTRIP
ONDJ FMAMJJASONDJ FMAMJJ AS
MONTH
Figure 2. Monthly mean discharges for Rosebud Creek at the mouth and near
Colstrip for USGS water years 1975 and 1976 (U.S. Geological Survey, 1976,
1977)
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3000 cfs (84.9 m3 per sec) in March and periods of "no flow" in dry years
(U.S. Geological Survey, 1976, 1977).
Water temperature records in July and August range from 21°C to a maxi-
mum on record of 26.7°C; minimum temperatures are at freezing for many days
during winter months (Aagaard, 1969) and the stream is usually frozen over
from December to mid-February.
Riparian vegetation includes mixed grass, boxelder (Aaev rusgundo L.),
green ash (Fvaxinus pennsylvaniaa Marsh), chokecherry (Prunus sp.), rose
(Rosa spp.), willow (Salix spp.), and buffaloberry (Shepherdia sp.). Common
grasses are reed canarygrass (Phalaris arundinacea L.), prairie cordgrass
(Spc&tina peatinata Link.), smooth brome (Bvomus inevmis Leys.), and American
bulrush (Seivpus amsriaanus Pers.), all rhizomatous in character and especi-
ally important in streambank stability. Streamside vegetation is generally
intact which provides good wildlife habitat and aids in soil stabilization.
Rosebud Creek is characterized by heavily vegetated banks, extensive
organic deposits in the substrate and a moderately diverse benthic fauna with
high population numbers. These features are atypical of traditional prairie
streams, which have been described as being nearly devoid of benthic life and
having substrates practically free of organic deposits (Carlander et a!.,
1963). However, Rosebud Creek does have relatively high turbidity, areas of
shifting substrate, and rapid fluctuations in discharge; these character-
istics are descriptive of traditional prairie streams. Because its headwaters
originate in and flow through mountainous terrain and the lower reaches flow
through a prairie environment, Rosebud Creek can be termed a transition
prairie stream.
8
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SECTION V
DESCRIPTION OF SAMPLING STATIONS
Seven benthic invertebrate sampling stations were established in Febru-
ary 1976 and numbered consecutively upstream (Table 1, Figure 1). Selection
was made on the basis of concurrent chemical sampling locations (Skogerboe
et al., 1978), physical similarity, access, and potential for evaluating
impacts from coal development. An attempt was made to include three habitat
types (riffles, hard-bottom slow stretches, and pools) at each station.
Station 1 was downstream from the theoretical plume emission fallout
area from the Col strip stack. Stations 2 through 5 were within the primary
theoretical plume fallout area. In addition, Stations 3 and 4 bracketed Cow
Creek to evaluate potential effluents from that source. As a control, Sta-
tion 6 was established upstream from the theoretical plume fallout area.
Rosebud Creek at Station 7 was similar in nature to a mountain stream and
provided information concerning longitudinal changes in the invertebrate
community of the Rosebud Creek system.
In addition to other physical parameters a subjective evaluation of the
predominant substrate type at each station was made utilizing the classifi-
cation of Cummins (1962) (Table 2). Station 1 is unique in having a sub-
strate of washed rubble and boulder from Yellowstone alluvium and a riffle-
pool habitat caused by an increase in gradient as Rosebud Creek enters the
Yellowstone Valley. Typical substrate at Station 2 consists of flocculent
clay or silt with gravel common only in meanders at the valley edge. Stations
3, 4, and 5 have long meandering stretches with slow current velocity and a
substratum of gravel, sand, and silt. Station 6, in addition to long, slow
stretches, has sections of clean, rubble-bottom riffles alternating with
sand-bottom pools. The substrate at Station 7 consists mainly of gravel and
rubble in riffles and sand in pools.
Shallow riffles for bottom sampling were not common at Stations 2
through 5; however, riffle sampling sites were established at Stations 1, 3,
5, 6, and 7; physical parameters are given in Table 3. The riffle at Station
3, due to depth, was sampled only during periods of low flow.
As shown in Table 4, Rosebud Creek waters are alkaline with a very basic
pH and a high concentration of electrolytes. The water is a carbonate-
sulfate-magnesium type and unusual due to the higher concentration of mag-
nesium than calcium. Dissolved oxygen is near saturation throughout the
year.
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TABLE 1. DESCRIPTIONS AND LOCATIONS OF SAMPLING STATIONS,
ROSEBUD CREEK, MONTANA
Station
1
2
3
4
5
6
Elevation
(m)
756
814
869
869
896
960
Kilometers from
Yellowstone River
0.7
15.4
29.7
30.0
36.8
51.4
Legal description
NE1/4 Sec 21 R42E T6N
SW1/4 Sec 30 R43E T4N
NE1/4 Sec 5 R43E TIN
SE1/4 Sec 5 R43E TIN
NW1/4 Sec 34 R42E TIN
SW1/4 Sec 8 R41E T2S
Description
U.S.G.S gauging station near
1-90
Pollen ranch
Kluver ranch, 480 m down-
stream of Cow Creek
Kluver ranch, 680 m upstream
of Cow Creek
W. McRae ranch
Bailey ranch, border of
Northern Cheyenne Reservation
1195
85.8
NW1/4 Sec 29 R39E T6S
Near Kirby at Highway 314
culvert
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TABLE 2. PHYSICAL CHARACTERISTICS OF SAMPLING LOCATIONS IN 1976
Mean width (m)
Mean depth (m)
Valley gradient
(m/km to next site)
Stream gradient
(m/km to next site)
Mean turbidity
(nephelometric units)
Temperature (°C)
Mean August maximum
Mean August minimum
Mean October maximum
Mean October minimum
Substrate^
Vegetation-2/
1 2
7.5 5.0
0.4 0.7
2.46 2.38
1.32 1.09
11.4 9.5
23.4
19.3
4.1
2.1
40,60,0,0,0 0,40,10,10,40
0,1,99 73,5,22
Station
3456 7
4.2 3.6 5.5 6.1 2.5
0.6 0.7 0.8 0.6 0.4
2.39 2.39 2.74 4.80
0.99 0.99 1.01 1.60
4.9 4.7 4.5 4.9 5.5
22'; 0 19.5 20.0
20.4 17.4 15.9
3.7 5.2
2.8 3.5
10,60,10,20,0 0,70,0,20,10 10,50,20,20,0 30,30,30,10,0 10,40,30,20,0
18,5,77 6,4,90 18,20,62 13,41,46 28,33,39
-'Composition (%) in the following sequence: rubble, gravel, sand, silt, clay.
-Composition (%) in the following sequence: trees, shrubs, grass.
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TABLE 3. PHYSICAL CHARACTERISTICS OF RIFFLE SITES
IN 1976
Mean current
velocity (m/sec)
Mean depth (m)
Substrate
1
0.52
0.18
rubble,
boul der
Station
3 5
0.35 0.39
0.31 0.16
rubble gravel
6 7
0.51 0.46
0.17 0.09
rubble rubble
12
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TABLE 4. WATER QUALITY DATA,-'' MEANS AND RANGES (IN PARENTHESES), MARCH 1976 TO MARCH 1977
u>
pH
Specific conductivity
(umhos)
Alkalinity
(rng/1 CaC03)
Suspended solids
(mg/1)
Dissolved solids
(mg/l)
Dissolved oxygen
(mg/D
Da2* (mg/1)
NO; (mg/1)
P03-M (mg/1)
SO" (mg/1)
Cl~ (mg/1)
As Ug/1)
Cu (mg/1)
Dissolved Fe
(mg/D
~ ~ ' "*" " ~ ~ '"
1
8.45
(8.12-8.80)
1364.0
(558-1798)
409.6
(313-492)
534.0
(7.9-4308.0)
965.0
(431-1367)
9.8
(7.4-12.1)
84.3
(45-150)
0.18
(0.14-0.21)
0.53
(0.02-5.00)
404.0
(160-605)
a. 2
(2.1-28.0)
2.7
(1.1-9.5)
0.007
(0.005-0.010)
0.04
(0.01-0.11)
.
2
8.49
(8.17-8.81)
1282.0
(539-1531)
396.0
(298-498)
267.0
(10.1-1494.0)
878.0
(697-1335)
9.8
(6.9-12.3)
82.8
(37-140)
0.13
(0.12-0.13)
0.25
(0.02-1.70)
358.0
(160-515)
5.8
(2.7-10.0)
2.64
(1.0-8.4)
0.015
(0.003-0.074)
0.04
(0.01-0.13)
3
8.49
(8.09-8.70)
1281.0
(856-1496)
398.0
(294-480)
99.0
(9.8-459.0)
845.0
(610-980)
9.6
(6.7-11.6)
88.4"
(56-140)
0.09
(0.08-0.09)
0.14
(0.02-0.40)
336.0
(250-405)
5.2
(2.8-8.0)
1.77
(1.0-3.6)
0.012
(0.003-0.046)
0.06
(0.01-0.16)
Station
4
8.51
(8.08-8.76)
1274.0
(967-1437)
404.0
(341-488)
100.0
(10.8-463.0)
816.0
(591-1000)
9.8
(7.0-12.3)
90.4
(56-140)
0.08
(0.06-0.10)
0.12
(0.02-0.30)
325.0
(180-375)
5.1
(3.0-8.0)
1.64
(0.9-3.2)
0.010
(0.003-0.059)
0.06
(0.01-0.18)
5
8.52
(8.17-8.91)
1241.0
(954-1435)
402.0
(323-486)
154.0
(7.7-629.0)
814.0
(586-1080)
9.6
(7.1-12.4)
89.3
(56-140)
0.05
(0.05-0.05)
0.13
(0.02-0.30)
336.0
(204-540)
5.0
(3.0-8.5)
1.92
(0.4-4.4)
0.008
(0.003-0.027)
0.05
(0.01-0.13)
6
8.47
(8.12-8.85)
1164.0
(978-1325)
412.0
(348-490)
129.0
(5.4-573.0)
744.0
(598-960)
9.7
(7.3-12.9)
87.4
(55-130)
0.05
(0.05-0.05)
0.16
(0.02-0.75)
270.0
(155-400)
5.0
(3.0-11.0)
1.95
(0.6-5.2)
0.008
(0.003-0.043)
0.03
(0.01-0.10)
7
8.47
(8.15-8.81)
911.0
(846-979)
383.0
(325-425)
26.0
(6.3-68.0)
572.0
(500-780)
11.2
(9.2-12.2)
100.3
(75-110)
0.09
(0.04-0.15)
151.0
(110-260)
3.4
(1.5-7.0)
1.3
(0.9-2.4)
0.005
(0.003-0.006)
0.04
(0.02-0.05)
-------
TABLE 4 (continued). WATER QUALITY DATA,5/ MEANS AND RANGES (IN PARENTHESES), MARCH 1976 TO MARCH 1977
Undissolved Fe
(mg/1)
Hg (ug/D
K (mg/1)
Mg (mg/1)
Mr) (mg/1)
Na (mg/1)
Ni (mg/1)
Se (ug/1)
Zn (mg/1)
1
6.88
(0.25-44.0)
1.68
(0.07-10.3)
13.3
(7.4-23.0)
115.0
(30-190)
0.014
(0.001-0.05)
166.0
(60-740)
0.004
(0.003-0.005)
0.48
(0.3-0.8)
0.012
(0.001-0.032)
2
2.97
(0.24-17.0)
1.75
(0.12-9.4)
13.2
(8.5-23.0)
110.0
(30-190)
0.036
(0.001-0.32)
80.0
(45-100)
0.005
(0.003-0.011)
0.49
(0.3-0.7)
0.012
(0.001-0.050)
3
1.34
(0.16-4.3)
3.08
(0.05-16.0)
13.0
(7.8-22.0)
117.0
(69-170)
0.014
(0.001-0.05)
72.0
(45-90)
0.007
(0.005-0.030)
0.43
(0.3-0.6)
0.045
(0.001-0.380)
Station
4
1.26
(0.20-3.7)
2.40
(0.05^-18.3)
12.9
(7.7-22.0)
116.0
(79-170)
0.012
(0.001-0.05)
71.0
(43-87)
0.008
(0.003-0.040)
0.49
(0.3-0.6)
0.011
(0.001-0.048)
5
1.88
(0.18-7.6)
1.65
(0.10-15.0)
12.7
(7.6-21.0)
112.0
(86-180)
0.016
(0.001-0.05)
66.0
(58-85)
0.005
(0.002-0.010)
0.43
(0.03-0.7)
0.014
(0.001-0.090)
6
1.94
(0.20-7.6)
1.07
(0.05-9.0)
11.9
(7.3-19.0)
108.0
(78-160)
0.020
(0.001-0.056)
53.0
(44-66)
0.006
(0.002-0.020)
0.51
(0.4-0.7)
0.007
(0.001-0.017)
7
0.52
(0.23-1.1)
0.36
(0.05-0.29)
7.0
(5.0-9.2)
67.0
(61-74)
0.028
(0.003-0.05)
22.0
(17-25)
0.005
(0.005-0.005)
0.44
(0.3-0.5)
0.011
(0.001-0.034)
^/Collected and determined by the Fisheries Bloassay Laboratory, Montana State University, Bozeman, Montana, and the Natural
Resource Ecology Laboratory, Colorado State University, Fort Collins, Colorado.
-------
SECTION VI
MATERIALS AND METHODS
Sampling was initiated in March 1976 using a modified Hess sampler
(Waters and Knapp, 1961) to sample riffles. An Ekman dredge fastened to a
steel handle and with a manual closing release was used to sample pools.
Substrate in baskets was introduced in hard-bottom slow stretches, a common
habitat of Rosebud Creek, for colonization by macroinvertebrates.
Baskets, constructed from 1.27 cm hardware cloth, had dimensions of 15 x
15 x 30 cm and were filled with 40 pieces of hand-sorted clinker measuring 5
to 8 cm along the longest axis. At each station two samplers were anchored
on the bottom at similar depth and current velocity. The samplers were
allowed to be colonized for 6 weeks, and samples were then collected monthly.
The sampling procedure involved placing a nylon dip net (1 mm mesh) immedi-
ately downstream to catch organisms dislodged as the sampler was lifted.
Debris on the anchoring stake or basket handle was discarded, but debris
clinging to the sampler was collected. Substrate was removed and scrubbed
with a brush. For each sample, current .velocity was determined using a
Gurley (Model 625-F) current meter 15 cm in front of the basket; depth was
also measured. A subjective evaluation was made concerning the amount of
sediment and debris in the sampler. Baskets were sampled monthly from May to
November 1976, and in March 1977. Because of continuous ice cover the
samplers were removed from December 1976 to February 1977.
Two 0.023 m2 Ekman dredge samples were taken at each station during
March, June, August, and October 1976. Two 0.093 m2 Hess samples were taken
at Stations 1, 5, 6, and 7 in March, June, August, and November 1976, and in
February and March 1977. Samples were collected at Station 3 in August and
November 1976 and March 1977, using a modified Hess sampler. Qualitative
samples were collected at various locations at each station using a dip net.
All samples were preserved initially in 10% formalin.
Samples were later screened through a No. 30 U.S.A. Standard sieve (11.0
meshes/cm, 0.589 mm opening) and organisms were hand-sorted and stored in 7Q%
ethanol. Invertebrates were identified to genus or species where feasible
and possible, using keys by Brown (1972), Edmunds et al. (1976), Gaufin
et al. (1972), Jensen (1966), Johannsen (1934, 1935), Needham and Westfall
TT95T), Pennak (1953), Roemhild (1975, 1976), Ross (1944), and Usinger (1971).
Specimens were sent to recognized taxonomic experts for confirmation of
identifications. To aid in identifications, emerging adult insects were
collected and some naiads were reared to adults in an artificial stream at
Montana State University. Wet weight of the collections was determined with
a Mettler Type B5 analytical balance following the procedure of Slack et al.
(1973).
15
-------
Species diversity was calculated using the Simpson Index (Simpson,
1949), the Margalef Index (Margalef, 1957), and the Shannon Index (Patten,
1962) as modified by Hamilton (1975). Calculations were performed using the
Montana State University Sigma 7 computer.
In August 1976, stream width and thalweg depth at each station were
recorded at 10 locations 50 m apart. In addition, a subjective evaluation
was made concerning substrate and riparian vegetation compositon at each
location. At the riffle sites, water depth and current velocity 5 cm from
the substrate were measured at 30 cm intervals along transects spaced 2 m
apart.
Water samples were collected for turbidity analyses in October and
November 1976 and February 1977. Determinations were made using a nephelom-
eter (HF Instruments, Model DRT 200), following the procedure given by the
American Public Health Association (1976).
Continuous recording thermographs (Ryan Model D-15) were utilized at
Stations 1, 3, 5, and 7 during 10-25 August and 16-31 October 1976.
16
-------
SECTION VII
RESULTS
The total number of samples collected at each station by each sampling
method is given in Table 5. Mean current velocities immediately upstream
from the introduced substrate samplers are given in Table 6. Aquatic macro-
invertebrate abundance in terms of average total numbers of individuals, wet
weight, and number of taxa is shown in Table 7 and Figures 3, 4, and 5.
Analysis of variance of these parameters based on the method of unweighted
means (Snedecor and Cochran, 1967) showed that station means were signifi-
cantly different (a = 0.01) for total numbers of individuals, wet weight, and
number of taxa. Means were grouped according to the Newman-Keuls sequential
comparison test (Snedecor and Cochran, 1967) (Figure 6). Results from
modified Hess samples for Station 3 were not analyzed statistically due to
the small number of samples.
Pool habitats in Rosebud Creek supported a smaller standing crop than
riffles. Average wet weight per m2 was 10.8 g in riffles and 2.9 g in pools.
The mean number of individuals per m2 was 6007 in riffles and 4993 in pools;
these nearly corresponding numbers were due to the abundance of low-mass
individuals (e.g., Chironomidae and Oligochaeta) in pools.
MACROINVERTEBRATE NUMBERS
Invertebrate numbers were generally greater at Stations 5, 6, and 7
relative to Stations 2, 3, and 4. Station 1 normally had higher numbers than
Stations 2, 3, and 4.
Introduced Substrate Samplers
Analysis of introduced substrate samples gave results (Table 7) consis-
tent with the trends mentioned above. Average number of macroinvertebrates
per sample was greatest at Stations 5 and 6 and lowest at Station 2. Numeri-
cal abundance was similar at Stations 1 and 7. Likewise, Stations 3 and 4
were similar and supported low numbers of individuals.
Average total numbers per taxon and relative average percent of the
total sample is presented in Table 8 and Figure 7. Trichoptera, comprised
mainly of Hydropsychidae, were the most common invertebrates at most stations,
constituting from 22% of the total sample at Station 3 to 55% at Station 5.
Cheumatopsyehe spp. were abundant at all stations; Cheianatopsyche lasia
(Ross) may be a dominant species, as adults (Table 9) were commonly collected
at all stations. A Hydropsyche spp. complex of at least four species was
abundant at most stations. Lower numbers of Trichoptera were present at
17
-------
TABLE 5. TOTAL NUMBER OF SAMPLES FROM EACH STATION
BY THREE SAMPLING METHODS, MARCH 1976 TO MARCH 1977
Station
1
Introduced substrates 13 15 15 15 15 15 15
Ekman dredge 8888888
Modified Hess 12 0 6 0 12 12 12
18
-------
TABLE 6. MEAN CURRENT VELOCITIES 7.5 CM FROM THE
SUBSTRATE AND 15 CM UPSTREAM OF INTRODUCED SUBSTRATE
SAMPLERS, MAY 1976 TO MARCH 1977
Station
123 4567
Current velocity 0.36 0.42 0.46 0.38 0.50 0.38 0.41
(m/sec)
19
-------
TABLE 7. AVERAGE TOTAL NUMBERS, WET WEIGHTS, AND NUMBERS OF
TAXA OF BENTHIC MACROINVERTEBRATES, MARCH 1976
TO MARCH 1977
Average total
numbers
Average wet weight
(g)
Average total taxa
Station
1
2
3
4
5
6
7
1
2
3
4
5
6
7
1
2
3
4
5
6
7
Introduced
substrates^
1090
830
994
953
1633
1317
1029
1.92
3.25
1.72
1.84
2.75
2.29
3.17
20.9
16.3
19.0
18.9
22.5
24.0
22.9
Ekman
dredge-'
4402
2077
4774
4876
7664
3073
8076
2.20
1.98
0.95
3.23
2.07
1.03
8.74
6.5
7.1
5.6
8.8
10.5
5.8
5.4
Modified
Hess*/
6852
5278
2081
8690
7134
12.49
6.24
2.15
9.15
24.11
15.4
13.5
10.7
18.6
19.1
^Average total numbers and wet weights .per sample.
-'Average total numbers and wet weights per m2.
20
-------
2000
UJ
QL
Q 1000
<
LJ
_l
0.
cc
Ul
CL
CO
UJ
a:
m
UJ
H
o:
ut
400
200
CE
UJ
m
2OOO
1000
3783
3498
INTRODUCED SUBSTRATES
EKMAN DREDGE
MODIFIED HESS
345
SAMPLING STATIONS
Figure 3. Mean numbers (horizontal line) and ranges (vertical bar)
of aquatic macroinvertebrates per sample, March 1976
to March 1977.
21
-------
6.0
4.0
2.0
CO
5
tr
e>
z
(T
i o-
<
LJ
Q.
CO
cc
UJ
Q.
CO
CO
o
m
0.2
4.0
2.0
INTRODUCED SUBSTRATE
8.81
6.68
8.02
EKMAN DREDGE
-B-
6.47
MODIFIED HESS
S-
345
SAMPLING STATIONS
Figure 4. Mean wet weights (horizontal line) and ranges (vertical
bar) of aquatic macroinvertebrates per sample,
March 1976 to March 1977.
22
-------
30
20
10
UJ
o
CC
O
z
UJ
0.
2
<
OT
oc
UJ
a.
u.
o
cc
UJ
CD
5 20
10
2O
10
INTRODUCED SUBSTRATE
EKMAN DREDGE
... n
MODIFIED HESS
345
SAMPLING STATIONS
Figure 5. Mean numbers (horizontal line) and ranges (vertical
bar) of aquatic macroinvertebrate taxa per sample,
March 1976 to March 1977.
23
-------
INTRODUCED SUBSTRATE:
1 2
w
T
MW
TW
T
TW
MT
W
u
TW
T
MTW
TW
T
MTW
M
M
U
7
6
5
4
3
2
EKMA
7
6
5
4
3
2
N DREDGE:
1 234 56
MW
T
MW
MT
MW
T
T
MW
TW MW
MT
MODIFIED HESS:
1 5
7 TW
6 MT
5 MT
Figure 6. Significantly different means^-1^ for total
macroinvertebrates, taxa, and wet weights per sample.
-'M, T, and W indicate a significant difference (0.05) for
mean total macroinvertebrates, taxa, and wet weight,
respectively. Where symbols are absent, no real difference
existed.
Compare stations in the left vertical column with those in
the horizontal row.
24
-------
cn
TABLE 8. MACROINVERTEBRATE^ MEAN TOTAL NUMBERS PER TAXON AND MEAN PERCENTAGES^/ OF THE
SAMPLE (INTRODUCED SUBSTRATE), MAY 1976 TO MARCH 1977
Station Ephem.
1 85
(7.8)
2 65
(7.8)
3 192
(19.3)
4 162
(17.0)
5 203
(12.5)
6 185
(14.1)
7 83
(8.1)
Odon./
Zygop.
3
(0.3)
-------
800
700
UJ
(T 60O
m
O 500
UJ
o
o
o
cr
UJ
a.
a:
UJ
m
400
3OO
200
100
Trichoptera
Dipt era
- Ephemeroptera
Coleoptera
902
34 5
SAMPLING STATIONS
Figure 7. Average numbers of aquatic macroinvertebrates per introduced
substrate sample, May 1976 to March 1977.
26
-------
TABLE 9. ADULT AQUATIC INSECTS COLLECTED ALONG ROSEBUD CREEK
DURING 1976
Ephemeroptera
Baetidae
Bast-is (near pvopinquus)
Leptophlebiidae
Chovoterpes afbiannulata McDunn.
Odonata
Gomphidae
GompTms externus Hagen
Libellulidae
Sympetrwn oocidentdle Wai ker
Zygoptera
Coenagrionidae
Argia fumipennis-violaaea (Hagen)
Isohnura perparva (Selys)
Calopterygidae
Hetaeri-na americana (Fabricius)
Hemi ptera
Gerridae
Gerris remiges Say
Veliidae
Rhagovelia distineta Champion
Trichoptera
Hydropsychidae
Bydpopsyohe "bvonta Ross
Hydrops-yahe separata Banks
Avatopsyehe sp.
Cheumatopsyche las-la Ross
Cheumatopsycke anal-Ls (Banks)
Cheumatopsydhe campy la ROSS
Psychomyiidae
Polyeentropus cineveus Hagen
Leptoceridae
Oeeet-is avara (Banks)
Leptcoella albida
Leptocella (near Candida]
Brachycentridae
Brachyeentrus oeeidentalis Banks
PIecoptera
Nemourldae
Braetyptera foskett-i Ricker
Perlodidae
Isopevla patvieia Prison
Diptera
Tabanidae
Chryaops proalivis Osten Sacken
Tipulidae
Tipula v-icina Dietz
27
-------
most stations. Lower numbers of Trichoptera were present at Stations 2, 3,
and 4. Diptera, particularly Chironomidae, were the next most abundant
taxon. Highest numbers were collected at Stations 3 and 6; fewer individuals
were present at Stations 1, 2, and 4. Ephemeroptera were most common at
Stations 3 and 4 where Choroterpes albiannulata was the major species.
Coleoptera appeared to increase in numbers from Station 2 through 6, then
declined at Station 7. Plecoptera were uncommon in basket samples and were
numerous only at Station 7, the most upstream location. Molluscs were most
abundant at Stations 2, 6, and 7, and Hemiptera were most common in the mid-
Rosebud (Stations 2 through 6). Oligochaeta appeared to increase in abundance
progressively upstream.
Ekman Dredge Samples
Mean numbers of aquatic macroinvertebrates collected with an Ekman
dredge from pools are given in Table 7. Macroinvertebrate populations per m2
were most dense at Stations 5 and 7 while Stations 2 and 6 supported the
lowest numbers. Stations 1, 3, and 4 supported similar total population
numbers.
Average total numbers per taxon is presented in Table 10. Diptera were
the most common macroinvertebrates collected, and ranged from 51 to 84% of
the total sample at each station; numbers were highest at Stations 5 and 7
and lowest at Station 2. Oligochaetes, the next most common group in Ekman
samples, were found in high numbers at Stations 1 and 7; Stations 2 and 3
supported the lowest populations. Molluscs were collected in significant
numbers only at Stations 2, 3, and 4. Coleoptera, particularly Dubivaphia
minima, comprised a large portion of the benthic population in pools and were
common at Stations 1 through 5. Trichoptera were found in highest numbers at
Station 5. Other taxa were uncommon and Plecoptera were absent from Ekman
dredge samples.
Modified Hess Samples
Macroinvertebrates were most abundant at Station 6 and least abundant at
Station 5 (Table 7). Stations 1 and 7 were similar in population densities.
Average total numbers per taxon and relative percent of the total sample are
presented in Table 10. Diptera were numerically the most abundant taxon
collected by this method and highest numbers were present at Station 6.
Trichoptera, the next most numerous taxon, were most common at Station 7 and
least at Stations 3 and 5. Taxa were often collected in low numbers at
Station 5.
MACROINVERTEBRATE WET WEIGHTS
Wet weight usually reflected numbers of individuals; however, certain
species of large body size contributed disproportionately to the sample
weight. For example, at Station 2 numerous Mollusca, Anbrysus mormon, and
Hydropsychidae resulted in high average wet weight per introduced substrate
sample even though total numbers of macroinvertebrates were low. Although
general trends for distribution of wet weight among stations were not evi-
dent, Station 7 consistently supported high biomass.
28
-------
PO
UD
TABLE 10. MEAN TOTAL NUMBERS OF AQUATIC MACROINVERTEBRATES^/ PER M2 AND AVERAGE
PERCENTAGES OF THE SAMPLED MARCH 1976 TO MARCH 1977
Station Ephem.
1 5
2 22
(1.0)
3 59
(1.2)
4 183
(3.7)
5 204
(2.7)
6 38
(1.2)
7 31
(0.4)
Odon./
Zygop.
11
(0.2)
16
(0.8)
5
(0.1)
32
(0.7)
11
(0.1)
32
(1.1)
6
(0.1)
Plecop.
0
0
0
0
0
0
0
Trich.
Skman
70
(1.6)
86
(4.1)
32
(0.7)
129
(2.6)
603
(7.9)
151
(4.9)
117
(1.4)
Coleop.
dredge
963
(21.9)
425
(20.5)
651
(13.6)
850
(17.4)
672
(8.8)
124
(4.0)
283
(3.5)
Dipt.
2179
(49.5)
1130
(54.4)
3190
(66.8)
2905
(59.6)
5902
(77.0)
2577
(83.9)
5896
(73.0)
Oligo.
1124
(25.6)
344
(16.6)
780
(16.3)
699
(14.3)
248
(3.2)
145
(4.7)
1722
(21.3)
Moll us.
11
(0.2)
54
(2.6)
48
(1.0)
48
(0.9)
0
0
12
(0.2)
Henri p.
38
(0.9)
0
5
(0.1)
5
(0.1)
0
0
0
Modified Hess
I 615
(9.0)
3 2505
(47.5)
2
2
2
(<0.1)
4
(0.1)
2909
(42.5)
362
(6.9)
760
(11.1)
77
(1.5)
2185
(31.9)
2249
(42.6)
349
(5.1)
40
(0.7)
5
(0.1)
18
(0.3)
2
(0.1)
-------
TABLE 10 (continued). MEAN TOTAL NUMBERS OF AQUATIC MACROINVERTEBRATES^ PER M2 AND AVERAGE
PERCENTAGES OF THE SAMPLED MARCH 1976 TO MARCH 1977
Station
5
6
7
Ephem.
294
(14.1)
1246
(14.3)
582
(8.2)
Odon./
Zygop.
0
98
(0.1)
109
(0.1)
Plecop.
0
14
(0.2)
32
(0.5)
Trich.
351
(16.9)
2309
(26.6)
4617
(64.7)
Coleop.
126
(6.0)
627
(7.2)
275
(3.9)
Dipt.
1163
(55.9)
4321
(49.7)
1313
(18.4)
Oligo.
128
(6.2)
118
(1.4)
278
(3.9)
Moll us.
0
1
19
(0.3)
Hemip.
(0.3)
9
(0.1)
0
= Ephemeroptera, Odon = Odonata, Zygop = Zygoptera, Plecop = Plecoptera, Trich = Trichoptera,
Coleop = Coleoptera, Dipt = Diptera, Oligo = Oligochaeta, Moll us = Mollusca, Hemip = Henri ptera.
In parentheses.
-------
Introduced Substrate Samples
Mean wet weight (Table 7) was greatest at Station 2 and lowest at
Station 3. Average wet weight per sample was also high at Stations 5 and 7.
Average wet weight and percent of the total sample for certain taxa are
presented in Table 11 and Figure 8. Trichoptera was the most common taxon in
most samples; however, in contrast to numbers, weight was low at Station 6
and high at Station 2, indicating differences in average larval size, state
of development, or species composition. Wet weight per sample for Odonata
and Zygoptera appeared to increase progressively upstream to Station 6.
Ephemeroptera biomass was low at Station 2 and high at Stations 3 through 6
due mainly to large numbers of Chovoterpes alb-lannulata and Ba&t-is spp. Wet
weights for Diptera were relatively high at all stations, especially 3 and 6.
Coleoptera biomass was higher at Stations 5 and 6 and Plecoptera comprised a
considerable portion of the wet weight only at Stations 6 and 7.
Ekman Dredge Samples
Macroinvertebrate wet weight per m2 was greatest at Station 7 where high
numbers of Chironomidae were collected (Table 7). All other stations were
not significantly different. Average wet weight and relative percent of the
total sample for certain taxa is given in Table 12. Diptera and Oligochaeta
constituted a large portion of the total wet weight; Diptera biomass was high
at Stations 5 and 7 and Oligochaeta at Stations 1 and 7.
Modified Hess Samples
Macroinvertebrate wet weight per m2 for modified Hess samples was
highest at Station 7 followed by Station 1 (Table 7); the lowest average wet
weight was found at Station 5. Average wet weight and percent of the total
sample for certain taxa is presented in Table 12. The largest portion of
most samples was comprised of Trichoptera with the exception of Stations 3
and 5 where total numbers were also low. Wet weights for many taxa were low
at Station 5.
MACROINVERTEBRATE DISTRIBUTION
A checklist of total taxa collected from Rosebud Creek and their respec-
tive distributions with regard to sampling stations is given in Table 13.
The number of occurrences and average number per occurrence for individual
taxa is listed for each sampling method in Tables 14, 15, and 16. Average
numerical abundance per introduced substrate sampler for common macroinver-
tebrates is shown in Figure 9. Average numbers and occurrences often tended
to be lowest at Station 2, then increased progressively upstream, often
declining at Station 7. Numbers were usually greater at Station 1 relative
to Station 2. Organisms with this pattern of distribution included
Leptophlebia gravastella, Tricorythodes minutus^ Baetis sp. B, Hydroptila
spp., Stenelmis oregonensi-s, Heliahus stviatus, and Heptagen-La elegantula..
Other macroinvertebrates (e.g., Choroterp&s albiannulataf Bvachyptera sp.,
Ambrysits mormon., S-Lmuliwn spp., and Sphaeriwn spp.} appeared to be most
abundant in the mid-Rosebud and did not increase in numbers progressively
31
-------
CO
INJ
TABLE 11. MEAN WET WEIGHTS5/ FOR MACROINVERTEBRATE TAXA^/ AND AVERAGE PERCENTAGES5/ OF
THE SAMPLE .{INTRODUCED SUBSTRATE), MAY 1976 TO MARCH 1977
Station
1
2
3
4
5
6
7
Ephem.
0.15
(7.6)
0.07
(2.1)
0.23
(13.6)
0.27
(14.6)
0.26
(9.5)
0.37
(16.0)
0.11
(3.6)
Odon./
Zygop.
0.04
(1.8)
0.05
(1.7)
0.06
(3.6)
0.11
(5.9)
0.22
(8.0)
0.35
(15.4)
0.23
(7.4)
Plecop.
0.00
<0.01
(0.1)
<0.01
<0.01
(0.1)
<0.01
(0.1)
0.01
(0.5)
0.08
(2.4)
THch.
1.26
(65.4)
1.95
(60.0)
0.50
(29.3)
0.65
(35.3)
1.51
(54.9)
0.58
(25.3)
2.26
(71.2)
Coleop.
0.05
(2.4)
0.03
(0.8)
0.03
(1.5)
0.04
(2.2)
0.14
(4.9)
0.14
(5.9)
0.04
(1.3)
Dipt.
0.40
(21.1)
0.54
(16.8)
0.74
(43.3)
0.46
(24.7)
0.43
(15.5)
0.67
(29.4)
0.37
(11.5)
Oligo.
<0.01
(0.2)
<0.01
<0.01
<0.01
(0.1)
<0.01
<0.01
(0.1)
0.01
(0.2)
Moll us.
0.03
(1.5)
0.28
(8.7)
0.03
(2.0)
0.25
(13.5)
0.01
(0.3)
0.03
(1.3)
0.05
(1.7)
Henri p.
<0.01
0.32
(9.7)
0.12
(6.7)
0.06
(3.3)
0.18
(6.5)
0.12
(5.4)
0.01
(0.4)
grams per sample.
= Ephemeroptera , Odon = Odonata, Zygop = Zygoptera, Plecop = Plecoptera, Trich =
Trichoptera, Coleop = Coleoptera, Dipt = Diptera, Oligo » OUgochaeta, Mollus = Mollusca,
Hemip = Henri ptera.
y In parentheses.
-------
UJ
5
(T
w>
03
r>
CO
UJ
o
2.00
1.80
§ '-60
cc
\-
- 1.40
1.20
a:
UJ
to
£
o
1.00
X 0.80
UJ
I-
UJ
UJ
o
<
0.60
0.40
0.20
0.00
Trichoptera
Dipt era
Ephemeroptera
Coleoplera
345
SAMPLING STATIONS
Figure 8. Average macroinvertebrate wet weights (grams) per introduced
substrate sample, May 1976 to March 1977.
33
-------
TABLE 12. MEAN WET WEIGHTS^ PER M2 AND AVERAGE PERCENTAGES OF THE SAMPLED FOR AQUATIC
MACROINVERTEBRATES,5/ MARCH 1976 TO MARCH 1977
Station Ephem.
1 0.0
2 0.02
(0.8)
3 0.03
(2.8)
4 0.28
(8.7)
5 0.05
(2.6)
6 0.05
(4.8)
7 0.01
(0.1)
Odon./
Zygop.
0.06
(2.9)
0.55
(28.1)
0.02
(2.2)
0.52
(16.1)
0.19
(9.1)
0.51
(49.7)
0.01
(<0.1)
Plecop.
0.0
0.0
0.0
0.0
0.0
0.0
0.0
Trich.
Ekmm
0.18
(8.4)
0.17
(8.7)
0.0
0.69
(21.6)
0.43
(20.6)
0.16
(15.9)
0.74
(8.4)
Coleop.
dredge
0.28
(12.8)
0.12
(6.3)
0.13
(13.4)
0.22
(6.9)
0.18
(8.9)
0.05
(5.3)
0.05
(0.6)
Dipt.
0.53
(24.3)
0.45
(22.6)
0.33
(34.1)
0.23
(7.2)
1.12
(54.2)
0.18
(18.0)
5.94
(67.9)
Oligo.
1.10
(50.1)
0.28
(14.2)
0.35
(36.3)
0.35
(10.9)
0.09
(4.4)
0.06
(6.3)
1.56
(17.9)
Moll us.
0.01
£<0.1)
0.38
(19.1)
0.09
(9.5)
0.87
(27.0)
0.0
0.0
0.34
(3.9)
Hemip.
0.03
(1.2)
0.0
0.01
(l.D
0.01
(0.3)
0.0
0.0
0.0
Modified Eesa
1 0.88
(7.0)
3 1.64
(26.1)
0.24
(1.9)
0.07
(1.1)
0.03
(0.2)
0.06
(1-0)
9.03
(72.3)
0.65
(10,3)
0.33
(2.6)
0.03
(0.4)
1.13
(9.0)
2.03
(32.4)
0.33
(2.7)
0.01
(0.2)
0.22
(1.7)
1.64
(26.1)
0.07
(0.6)
0.13
(2.1)
-------
TABLE 12 (continued). MEAN WET WEIGHTS5/ PER M2 AND AVERAGE PERCENTAGES OF THE SAMPLE-/ FOR
AQUATIC MACROINVERTEBRATES,-/ MARCH 1976 TO MARCH 1977
co
en
Station
5
6
7
Ephem.
0.34
(16.1)
0.99
(10.8)
0.56
(2.3)
Odon./
Zygop.
0.0
0.92
(10.1)
1.40
(5.8)
Plecop.
0.0
0.07
(0.8)
0.07
(0.3)
Inch.
0.60
(27.9)
3.89
(42.7)
16.85
(69.8)
Coleop.
0.04
(1.8)
0.23
(2.5)
0.16
(0.7)
Dipt.
1.05
(49.2)
2.77
(30.4)
4.47
(18.5)
Oli go.
0.05
(2.4)
0.04
(0.4)
0.14
(0.6)
Moll us.
0.0
0.0
0.28
(1.2)
Hemip.
0.04
(1.7)
0.16
(0.7)
0.0
-In grams.
-'In parentheses.
^Ephem = Ephemeroptera, Odon = Odonata, Zygop = Zygoptera, Plecop = Plecoptera, Trich =
Trichoptera, Coleop = Coleoptera, Dipt = Diptera, Oligo = Oligochaeta, Mollus = Mollusca,
Hemip = Hemiptera.
-------
TABLE 13. CHECKLIST AND DISTRIBUTION OF AQUATIC
MACROINVERTEBRATES, MARCH 1976 TO MARCH 1977
Ephemeroptera
Ephemerldae
Ephovon album (Say) X X
Heptageniidae
Heptagenia elegantuta (Eaton) X X X X X X X
Heptagenia sp. A X
Stenonema termination (Walsh) X X
Rhithrogena sp. X X
Baetidae
Baetis sp.A XXXXXXX
Baetis sp. B XXXXXXX
Centvoptilum sp. X X X X X X
Pseudocloeon sp. XXXXXXX
Cdllibaetis sp. X
Isonyahia siaca (Walsh) X
Leptophlebiidae
Choroterpes albiannulata McDunn. XXXXXXX
Leptophlebia gravastella (Eaton) XXXXXXX
Traverella albertana (McDunnough) X
Ephemerallidae
Ephemerelta inermis Eaton X XX
Caenidae
Caenis sp. X X
Tricorythidae
Triaorythodee minutus Traver XXXXXXX
Odonata
Gomphidae
Gamphus sp. A XXXXXXX
Gomphus sp. B X
Ophiogomphus sp. (near sevevus) X X X X X X
Libellulidae
Sympetinm sp. X
Zygoptera
Calopterygidae
Retaerina amerioana (Fabricius) X X X X X
Coenagrionidae
Amphagvion abbreviation (Selys) X XX
Argia fumipennis-violaaea (Hagen) XX XXX
Enallagma sp. X X X X XX
36
-------
TABLE 13 (continued). CHECKLIST AND DISTRIBUTION OF AQUATIC
MACRO-INVERTEBRATES, MARCH 1976 TO MARCH 1977
4
Plecoptera
Nemouridae
Brachyptera sp. (prob. fosketti)
Nemoura sp.
Capn-ia sp.
Perlodidae
Isoperla patricia Prison
Hemi ptera
Corixidae
Palmaaorixa gilleti Abbott
Triahoeoviaca sp.
Naucoridae
Ambrysits mormon Montandon
Megaloptera
Sialidae
S-Lalis sp.
Trichoptera
Psychomyiidae
Polycentropus oinereus 1
Hydropsychidae
Hydropsyche bronta Ross
Hydropsyche sp. A
Hydropsyche sp. B
Hydropsyahe sp. C
Chetanatopsyohe spp.
Hydroptilidae
Hydroptila sp. A
Hydroptila sp. B
Mayatri-chia sp.
Ithytriahia sp.
Phryganeidae
Ptilostomis sp.
Limnephilidae
Limnephilus sp.
Onoaosmoecus sp.
Anabolia sp.
Leptoceridae
Oecetis avara (Banks)
Triaenodes sp. (near tarda)
Neotopsyche sp. (Leptooella)
Brachycentridae
Broobyoentrus sp.
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
37
-------
TABLE 13 (continued). CHECKLIST AND DISTRIBUTION OF AQUATIC
MACROINVERTEBRATES, MARCH 1976 TO MARCH 1977
Lepidoptera
Pyralidae
Cataolysta sp.
Coleoptera
Dytiscidae
Liodessus affinis (Say)
Hydrophilidae
Helophorus sp.
Dryopidae
Helichus striatue LeConte
Heliehus suttu>alis LeConte
Elmidae
Stenelmie oregonensis
Dubiraphia minima
Microcylloepus pusillus (LeConte)
Optioservus divergens (LeConte)
Diptera
Tipulidae
Tipula spp.
Holorusia sp.
Ormosia spp.
Dicvanota spp.
Lirmophila (Eloeophila) sp.
Hexatoma (Erioeera) sp.
Psychodidae
Periaoma sp. A
Perieoma sp. B
Psychoda sp.
Culicidae
Chaoboms sp.
Sltnullldae
Simtlium spp.
Chironomidae
Heleidae
Palpomyia spp.
Dasyhelea spp.
Stratiomyidae
Tabanidae
Chrysops spp.
Tdbamis sp.
Dolichopodldae
Hydrophorus sp.
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
38
-------
TABLE 13 (continued). CHECKLIST AND DISTRIBUTION OF AQUATIC
MACROINVERTEBRATES, MARCH 1976 TO MARCH 1977
Diptera (continued)
Empididae
sp. A
sp. B
Turbellaria
Nematomorpha
Oligochaeta
Hirudinea
Glossiphoniidae
Amphipoda
Talitridae
Hyalella azteea (Saussure)
Acari
Basommatophora
Physidae
Physa spp.
Lymnaeidae
Lymnaea sp.
Ancylidae
Ferrissia sp.
Planorbidae
Gyraulus sp.
Heterodonta
Sphaeriidae
Sphaeriwn sp.
Pisidium sp.
Eulamellibranchia
Unionidae
X X X X X X X
X X X X X X
X X X X
X X
X X X X X X X
X
X
X X X X X
X XXX
X X XXX X X
X XX
X
X X X X X X X
XXX X
Total taxa
60 42 50 50 60 59 60
39
-------
TABLE 14. NUMBER OF OCCURRENCES^ AND AVERAGE NUMBERS PER OCCURRENCE^/ FOR AQUATIC
MACROINVERTEBRATES COLLECTED IN INTRODUCED SUBSTRATE SAMPLES, MAY 1976 TO MARCH 1977
Sampling stations
Ephemeroptera
Heptageniidae
Heptagen'ia elegantula (Eaton)
Eeptageni-a sp. A
Stenonema terminatum (Walsh)
Rhithrogena sp.
Baetidae
Baetie sp. A
BaeHe sp. B
Centroptilum sp.
Pseudocloeon sp.
Cal'l'ibaet'is sp.
Isonyohia eiaaa (Walsh)
Leptophlebiidae
Choroterpee alb^annulata McDunn.
Leptophlebia gvavastella (Eaton)
Ephemerellidae
JSphemevella inermia Eaton
Caenldae
Caenie sp.
Tricorythidae
Tricorythodea mlnutua Traver
Odonata
Gomphldae
Gomphus sp. A
Gomphus sp. B
Ophiogomphua sp. (near aeverus)
Libellulidae
Sympetrim sp.
6 24
7(11)
1(4
1(1)
KD
KD
13(46)
3(12)
2(1)
12(17)
KD
1(1)
KD
7(2) 13(5) 13(7) 15(15) 12(13) 13(6)
5(19)
9(6)
3(2)
15(54)
KD
6(2)
3(1)
KD
8
10
3
3
32)
4)
1)
17)
15(138)
6(3)
KD
KD
3(1)
36)
7)
8(29)
11(18)
24)
5(23)
15(114)
5(4)
KD
7(1)
2(1)
7(2)
4(2)
1(3)
10
2
24
12)
15(118) 15(84)
3(13) 9(9)
1(2)
13(28) 12(27) 11(43) 12(45)
10
15(31)
1(5)
6(3)
7(9)
10(5)
15(38)
KD
9(1)
-------
TABLE 14 (continued). NUMBER OF OCCURRENCES^/ AND AVERAGE NUMBERS PER OCCURRENCE^/ FOR AQUATIC
MACROINVERTEBRATES COLLECTED IN INTRODUCED SUBSTRATE SAMPLES, MAY 1976 TO MARCH 1977
Sampling stations
Zygoptera
Calopterygidae
Hetaerina amerieana (Fabricius)
Coenagrionidae
Amphagrion abbreviatum (Selys)
1
5(3)
1(3)
Apgia fumipennis-violaeea (Hagen) 6(2)
Enallagma sp. 4(3)
Plecoptera
Nemouridae
Braehyp-teva sp. (prob. fosketti]
Perlodidae
Isoperla patricia Prison
Hemi ptera
Corixidae
Palmaoorixa gilleti Abbott
Tri.ahoaor-i.sxx, sp.
Naucoridae
Ambry sus mormon Montandon
__
2(1)
2
2(2)
KD
3(2)
__
10(12)
3
1(2)
1(1)
3(2)
2(1)
--
9(7)
4
KD
KD
2(2)
4(2)
KD
6(10)
5
2(1)
KD
KD
KD
2(4)
KD
9(9)
6
7(7)
4(1)
3(1)
4(5)
4(3)
4(2)
KD
7(9)
7
KD
5(2)
10(21)
--
7(1)
Megaloptera
Sialidae
SiaUa sp. -- - 1(1) 5(1)
-------
TABLE 14 (continued). NUMBER OF OCCURRENCES^/ AND AVERAGE NUMBERS PER OCCURRENCE^ FOR AQUATIC
MACROINVERTEBRATES COLLECTED IN INTRODUCED SUBSTRATE SAMPLES, MAY 1976 TO MARCH 1977
PO
Trichoptera
Psychomyiidae
Polyaentropue oinereua ?
Hydropsychidae
Hydropsyche bronta Ross
Hydropeyche sp. A
Hy dropsy ahe sp. B
Hydropsyahe sp. C
Ch&imatopsyche spp.
Hydroptilidae
Hydroptila sp. A
HydropHla sp. B
Maya.trioh'ia sp.
Ithytriokia sp.
Phryganeidae
Ptilostomis sp.
Limnephilidae
Limnephilus sp.
Onoooemoeaus sp.
Anaboli-a sp.
Leptocerldae
Oecet-is avara (Banks)
Triaenodee sp. (near tavda)
Neatopeyche sp. (LeptoGella)
Brachycentridae
Braehyaentrue sp.
1
--
13 136)
9 20)
11 155)
7 11)
13 234)
4(24)
4(5)
KD
7(13)
1(3)
M1!
1(1)
9(14)
1(2)
8(8)
11(28)
2
11(5)
10 9)
14(123)
--
15(196)
3(7)
KD
3(4)
Sampling
stations
345
9(10) 11 ^
10(3) 13 :
12(52) 13 '
..
.
n 15(14)
18) 13(26)
13) 15(125)
.
15(62) 15(177) 15(609)
7(3) 4(6) 5(5)
1(
3(2) 1(
6(3) 6(^
1 KD
L
1 5(4)
6
KD
7 7)
9 3)
15 37)
15(390)
10 17)
5 18)
2 1)
3 5)
2(1) 1(1)
2(2)
1(4) -
2(6)
1U) 315)
8(4)
1(1)
12(24)
.
10(5) 8(5) 9(6)
_.
.
2(2) 2(2) 7(1)
6(211) 6(237) 6(130)
3(3
2(2
2(2
13 7)
14)
9 12)
6(29)
7
3(1)
13(5)
1(1)
15(197)
15(193)
14(58)
2(1)
3 2)
6 6
2 1)
9(1)
2(2)
14(22)
-------
TABLE 14 (continued). NUMBER OF OCCURRENCES^ AND AVERAGE NUMBERS PER OCCURRENCE^ FOR AQUATIC
MACROINVERTEBRATES COLLECTED IN INTRODUCED SUBSTRATE SAMPLES, MAY 1976 TO MARCH 1977
CO
Sampling stations
Coleoptera
Dytiscidae
L-Lodessus affords (Say)
Hydrophilidae
Helophorus sp.
Dryopidae
Heli-chus stria.tus LeConte
Heliohus suturalis LeConte
Elmidae
Stenelmis oregonensis
Dubi'Vaphia minima
Mieroaylloepus pusillus
(LeConte)
Optioservus dtvergens (LeConte)
Diptera
Tipulidae
Tipula (Yamatotipula) spp.
Holorusia sp.
Ormos-La spp.
Diepanota spp.
L-imnophila. (Eloeophila) sp.
Hexatoma (Evioeera) sp .
Psychodidae
Perieoma sp. A
Periaoma sp. B
Simuliidae
Si-multum Spp.
Chironomidae
1
KD
2(2)
--
8(29)
11(11)
13(39)
--
__
KD
10(217)
13(165)
2
KD
5(4)
__
9(10)
8(3)
12(17)
--
_.
2(4)
--
KD
__
--
14(304)
15(63)
3
--
4(3)
--
11(10)
10(6)
13(27)
--
--
--
4(2)
--
--
--
15(390)
15(147)
4
--
4(3)
10(17)
12(22)
13(25)
--
--
--
3(5)
--
--
14(238)
15(104)
5
KD
7(15)
14(31)
13(11)
15(32)
KD
KD
--
8(11)
KD
15(246)
15(173)
6
7(14)
KD
13(50)
13(17)
11(21)
3(1)
3(2)
14(281)
15(228)
7
2(1)
7(6)
7(1)
11(8)
10(4)
10(5)
5(1)
2(1)
--
8(3)
KD
M1!
id)
9(9)
15(363)
-------
TABLE 14 (continued). NUMBER OF OCCURRENCES^/ AND AVERAGE NUMBERS PER OCCURRENCE^/ FOR AQUATIC
MACROINVERTEBRATES COLLECTED IN INTRODUCED SUBSTRATE SAMPLES, MAY 1976 TO MARCH 1977
Sampling stations
Diptera (continued)
Heleidae
Palpamyia spp.
Dasyhelea spp.
Strati omyidae
Tabanidae
Chryeops spp.
Dolichopodidae
Hydpaphorue sp.
Empididae
sp. A
sp. B
Turbellaria
Nematomorpha
Oligochaeta
Hirudinea
Glossiphoniidae
Malacostraca
Amphipoda
Talitridae
Hyalella azteca (Saussure)
Acari
1
1(2)
__
._
KD
--
KD
10(17)
5(2)
»_
2
2(3)
--
6(2)
1(6)
8(5)
KD
««
3
3(2)
KD
8(5)
2(1)
2(4)
11(6)
3(4)
KD
4
3(1)
.-
5(3)
KD
5(4)
KD
12(8)
2(3)
__
5
6(2)
/ s
1(1)
KD
-.
KD
7(7)
2(8)
6(19)
--
11(4)
--
3(1)
1(2)
6
11(5)
--
6(3)
3(2)
3(6)
14(20)
--
3(4)
2(1)
7
5(4)
1(44)
KD
8(4)
4(1)
13(31)
--
3(1)
2(1)
-------
TABLE 14 (continued). NUMBER OF OCCURRENCES^/ AND AVERAGE NUMBERS PER OCCURRENCE^/ FOR AQUATIC
MACROINVERTEBRATES COLLECTED IN INTRODUCED SUBSTRATE SAMPLES, MAY 1976 TO MARCH 1977
-------
TABLE 15. NUMBER OF OCCURRENCES^ AND AVERAGE NUMBERS PER OCCURRENCE^/ FOR AQUATIC
MACROINVERTEBRATES COLLECTED IN EKMAN DREDGE SAMPLES, MARCH 1976 TO OCTOBER 1976
Ephemeroptera
Heptageniidae
Heptagenia eleganbula (Eaton)
Baetidae
Baetie sp. B
Centroptilum sp.
Leptophlebiidae
Chovotevpes albiannulata McDunn.
Caenidae
Caenie sp.
Tricorythidae
Tricorythodes minutus Traver
Odonata
Gomphidae
Gomphue sp. A
Ophiogomphus sp. (near sevevua]
Zygoptera
Coenagrionidae
Argia fumipennie-violacea (Hagen)
Endtlagma. sp.
Hemiptera
Corixidae
Palmaaorixa gilleti Abbott
Triahoaorixa sp.
1
--
-
--
KD
KD
KD
--
KD
2(3)
Sampling stations
2345
1(1) - 1(2)
1(1) - KD
1(1)
2(6) 3(2) 2(2)
1(1) -- 3(8) 6(6)
2(1) 1(1) 3(1) 1(2)
KD
__ __
-_
KD KD
6 7
__
1(3) 1(1)
2(2)
2(2)
4(1)
KD
KD
.
-------
TABLE 15 (continued). NUMBER OF OCCURRENCES^/ AND AVERAGE NUMBERS PER OCCURRENCE^/ FOR
AQUATIC MACROINVERTEBRATES COLLECTED IN EKMAN DREDGE SAMPLES, MARCH 1976 TO OCTOBER 1976
Sampling stations
Megaloptera
Sialidae
Sialis sp.
Trichoptera
Psychomyiidae
Polyoentropus ei-nereus 1 1(1)
Hydropsychldae
Hydropsyche bronta ROSS 1(1)
Hydropsyahe sp. A
Hydropsyahe sp. B 2(1) 3(1)
Cheumatopsyohe spp. 2(3) 5(2)
Hydroptilldae
Hydroptila sp. A 1(2)
Limnephilidae
Limnephilus sp.
Leptoceridae
Oeeetia avara (Banks) 1(1) 1(1)
Neetopsyohe sp. (Leptooella)
Brachycentridae
BYaahycentrue sp.
Coleoptera
Elmidae
Stenelmis ovegonensi-s 1(1) 2(2)
Dubiraphia minima 8(21) 6(12)
Mierooylleopus pus-Lllus (LeConte) 4(2) 3(1)
11
3(2)
4(2)
2(3) 3(3)
KD
8(15)
2(2)
3(3)
7(21)
3(1)
KD
2(1)
52
7(10)
1(4)
2(1)
3(4)
4(2)
5(3)
8(13)
3(2)
KD
2(12)
KD
KD
3(1)
7(2)
1(3)
KD
2(5)
2(2)
2(1)
KD K3)
7(7)
-------
TABLE 15 (continued). NUMBER OF OCCURRENCES^/ AND AVERAGE NUMBERS PER OCCURRENCE^/ FOR
AQUATIC MACROINVERTEBRATES COLLECTED IN EKMAN DREDGE SAMPLES, MARCH 1976 TO OCTOBER 1976
Sampling stations
Diptera
Tipulidae
Ormoeia spp.
Dievanota spp.
Psychodidae
Peyahoda sp.
Simuliidae
SirmHum spp.
Chironomidae
Heleidae
Palpomyia spp.
Tabanidae
Chvyaope spp.
Empididae
sp. B
Turbellaria
Oligochaeta
Hirudinea
Glossiphoniidae
1
__
2(4)
8(48)
5(3)
--
8(26)
2
__
3(3)
3(2)
8(24)
4(2)
--
7(9)
--
3
__
1(1)
1(7)
8(61)
5(19)
KD
~
8(18)
--
4
1(D
1(3)
1(3)
8(42)
4(40)
KD
8(16)
KD
5
--
4(3)
--
4(2)
8(132)
6(4)
KD
2(2)
8(6)
--
6
__
1(2)
KD
8(48)
3(31)
--
KD
7(4)
7
__
1(11)
7(134)
2(4)
--
7(40)
Malacostraca
Amphipoda
Talitridae
Hyalella azteea (Saussure)
2(2)
-------
TABLE 15 (continued). NUMBER OF OCCURRENCES^/ AND AVERAGE NUMBERS PER OCCURRENCE-/ FOR
AQUATIC MACROINVERTEBRATES COLLECTED IN EKMAN DREDGE SAMPLES, MARCH 1976 TO OCTOBER 1976
Sampling stations
Basommatophora
Physidae
Physa spp. 1(1) ~ -- 2(2)
Heterodonta
Sphaeriidae
Sphaevi-wn sp.
P-isidium sp.
Eulamellibranchia
Unionidae
__
KD
2(2)
3(2)
--
1(2)
3(2)
--
2(1)
2(2)
__ --
1(1)
KD
indicates absence from samples.
i
In parentheses.
-------
tn
o
TABLE 16. NUMBER OF OCCURRENCES^ AND AVERAGE NUMBERS PER OCCURRENCE^ FOR
AQUATIC MACROINVERTEBRATES COLLECTED IN MODIFIED HESS SAMPLES, MARCH 1976 TO MARCH 1977
Sampling stations
Ephemeroptera
Ephemeridae
Ephoron album (Say)
Heptageniidae
Eeptagenia elegantula (Eaton)
Baetidae
Baetis sp. A
Baetis sp. B
Peeudoaloeon sp.
Leptophlebiidae
ChoroterpeB dLb-icmnulata McDunn .
Leptophlebia gvavaetella (Eaton)
Traverella albertana (McDunnough)
Caenidae
Caenis sp.
Tricorythldae
Trieorythodes minutus Traver
1
1(4)
2(42)
9(8)
3(8)
11(42)
1(2)
KD
7(6)
3
2(2)
KD
2(5)
2(1)
2(2)
5(270)
KD
3(9)
5
KD
--
2 3)
5 7)
3 1)
11(25)
__
4(3)
6
__
3(1)
2(11)
12(39)
4(13)
12(45)
2(4)
__
11(28)
7
_ _
3(3)
Ml
12(35)
KD
1(3)
\ ^ *
10(21)
Odonata
Gomphidae
Ophiogomphus sp.
(near severus)
2(1)
KD
Zygoptera
Calopterygidae
Hetaevi.no. americana (Fabricius)
Coenagrionidae
Enallagma sp.
7(1)
KD
5(2)
1(2)
-------
TABLE 16 (continued). NUMBER OF OCCURRENCES^/ AND AVERAGE NUMBERS PER OCCURRENCE^/ FOR
AQUATIC MACROINVERTEBRATES COLLECTED IN MODIFIED HESS SAMPLES, MARCH 1976 TO MARCH 1977
Sampling stations
Plecoptera
Nemouridae
Nemoura sp.
Braohyptera sp. (prob. fosketti)
Capnia sp.
Perlodidae
Isoperla patx>iaia Prison
Hemi ptera
Corixidae
Palmaoorixa gilleti Abbott
Naucoridae
Ambryeus mormon Montandon
Megaloptera
Sialidae
S-ialis sp.
Trichoptera
Hydropsychidae
Hydropsyche bronta Ross
Hydropsyche sp. A
Hydropsyohe sp. B
Hydropsyohe sp. C
Cheimatopsyehe spp.
Hydroptilidae
Hydroptila sp. A
Hydroptila sp. B
Mayatriahia sp.
1(2)
2(1)
12(71)
3(10)
11(105)
2(6)
12(84)
6(4)
2(8)
2(1)
2(1)
2(2)
43
2(2)
3(8)
6(25)
3(2)
2(4)
4(4)
2(1)
7(4)
10(34)
1(1
1(1
KD
3(3)
5(1)
KD
3(3)
6(5)
3(2)
12(36)
12(149)
9(24)
3(1)
1(15)
KD
1(1)
8(4)
1(3)
10(3)
12(162)
12(231)
11(32)
1(11)
-------
TABLE 16 (continued). NUMBER OF OCCURRENCES^ AND AVERAGE NUMBERS PER OCCURRENCE^/ FOR
AQUATIC MACROINVERTEBRATES COLLECTED IN MODIFIED HESS SAMPLES, MARCH 1976 TO MARCH 1977
Sampling stations
en
tva
Trichoptera (continued)
Limnephilidae
Limneplvilus sp.
Onooosmoeoua sp.
Leptocerldae
Oeoetie avora (Banks)
Neetopeyche sp. (Leptoeella)
Brachycentridae
sp.
Lepidoptera
Pyralidae
Cataelysta sp.
Coleoptera
Dryopidae
Helichue striatus LeConte
Elmldae
Stenelmis ovegonensis
Dubtraphia minima
Miaroaylloepus pusillus (LeConte)
Optioeervus divevgens (LeConte)
Diptera
Tipulidae
Tipula (Yamatotipula) spp.
Holorueia sp.
Ormos-ia spp.
Di-Qvanota spp.
Limnophila (Eloeophila) sp.
5(2)
4(30)
5(4)
1(2)
8(15)
8(3)
11(64)
1(1)
5(4)
2(1
1(1
5(5)
2(3)
3(5)
4(4)
2(4)
4(7)
9)
4\
13)
1(2)
7(7)
Kl)
4(6
1(1
3(8)
12(33)
10(4)
8(31)
4(3)
KD
7(6)
1(2)
1(2)
7(4)
KD
8(2)
10(4)
12(8)
12(14)
4(4)
3(3
11(4
2(2
-------
TABLE 16 (continued). NUMBER OF OCCURRENCES5/ AND AVERAGE NUMBERS PER OCCURRENCE^/ FOR
AQUATIC MACROINVERTEBRATES COLLECTED IN MODIFIED HESS SAMPLES, MARCH 1976 TO MARCH 1977
Sampling stations
Diptera (continued)
Culicidae
Chaoborus sp.
Simuliidae
Sixmlivm spp.
Chironomidae
Heleidae
Palpomyia spp.
Tabanidae
Chryaops spp.
Tdbonus sp.
Empididae
sp. A
sp. B
Turbellaria
Nematomorpha
Ollgochaeta
Amphipoda
Talitridae
Hyalella azteea (Saussure)
Acari
1
--
12(51)
12(150)
4(2)
3(1)
KD
11(35)
KD
3
KD
4(225)
5(66)
KD
KD
3(2)
--
2(4)
4(6)
5
11(63)
12(44)
7(2)
--
2(4)
1(4)
3(4)
__
9(16)
--
6
12(132)
12(253)
8(13)
--
5(9)
2(2)
6(6)
10(13)
KD
2(2)
7
8(6)
12(108)
6(4)
5(1)
i \
KD
7(2)
3(2)
12(26)
2(1)
2(1)
Basommatophora
Physidae
Physa spp.
2(1)
-------
TABLE 16 (continued). NUMBER OF OCCURRENCES5/ AND AVERAGE NUMBERS PER OCCURRENCE^/ FOR
AQUATIC MACROINVERTEBRATES COLLECTED IN MODIFIED HESS SAMPLES, MARCH 1976 TO MARCH 1977
Sampling stations
en
Basommatophora (continued)
Ancylidae
Ferriesia sp.
Heterodonta
Sphaeriidae
Sphaerium sp.
Pieidium sp.
3(2)
1(10)
KD
1(2)
4(3)
1(5)
a/
Dash indicates absence from samples.
t
In parentheses.
-------
UJ
a.
5
to
a:
UJ
a.
to
UJ
a:
m
ui
h-
cc
ui
o
a:
o
(T
UJ
m
UJ
C5
<
UJ
40
30
20
IO
40
30
20
10
200
100
Sttn»/mis oregonensis
Dubiraphia minima
BatI'is sp. B
-- Boetis sp. A
Hydropsychg sp. B
Choroterpes sp.
Microcylloepus pusillus
Htlichus striatus
Tricorythodes mint/fas
Heptagenia eltgantolo
Brachycentrus sp.
Hydropsyche bronta
567123
SAMPLING STATIONS
Figure 9. Average numbers of selected taxa per introduced substrate
sample, May 1976 to March 1977.
55
-------
22
20
ui
J
0-
<
V)
CC
UJ
Q.
to
UJ
or
m
UJ
UJ
>
z
o
o:
o
u.
o
cr
UJ
CD
UJ
(E
Ul
10
10
400
200
-Isoperlo patricia
- - Otcatis avara
V-**'
-Pstudocloeon sp.
Leptophlebia gravas tafia
-Cheumatopsyche spp
Hydropsyche sp. A
-Hydroptilo sp. A
54
i
i
i
Ambrysus mormon
Nectopsycha spp.
Simulium spp.
567 123
SAMPLING STATIONS
Figure 9 (continued). Average numbers of selected taxa per introduced
substrate sample, May 1976 to March 1977.
56
-------
upstream. Hydropsyehe sp. A, Cheumatopsyahe spp., and Pseudooloeon sp. were
most abundant in introduced substrate samples at Station 5.
Restricted distribution patterns were evident for certain taxa (Table
13). Optioservus divergens was common only at Station 7 and absent from
Stations 1 through 4. Ephoron album was collected rarely and only at Stations
3 and 5. Caen-is spp. was common at Station 7, rare at Station 1, and absent
from intervening stations. Traverella albertana was collected only once at
Station 1 although it was found to be abundant in the Yellowstone River in
this vicinity (Newell, 1976). Sialis sp., collected in silted substrata at
Stations 6 and 7, was absent from Stations 1 through 5. Certain Tipulidae
(e.g., Tipula spp., Holorusia sp., and Limnophila sp.) were collected only at
Stations 5, 6, and 7. Perieoma spp. were collected only at Station 7.
Plecoptera were rare; however, nymphs of a winter stonefly, Brachyptera spp.,
were present at Stations 1 through 6 and possibly correspond to adult
Braohyptera fosketti collected in March 1976. Isoperla patricia was present
in greatest numbers at Station 7 and was absent from Stations 1, 2, and 4.
Certain taxa (e.g., Isonyahia siaaa, Hydropsyahe sp. C, Cataelysta sp., and
Sympetrum sp.) were collected only from the unique habitat present at Station
1.
A temporal pattern of emergence appeared to be present for certain taxa.
Population cycles for Hydropsyehe sp. B and Dttbiraphia minima reached numeri-
cal peaks during different months depending on the station (altitude) (Figures
10 and 11). In contrast, numbers of Choroterpes albiannulata appeared to peak
bimodally and simultaneously at all stations (Figure 12).
Results from modified Hess samples (Table 16) showed that individual
taxa were often numerically least abundant at Station 5, a distinct contrast
with data from introduced substrate samples. Total numbers for individual
taxa were generally highest at Stations 1,6, and 7. The mid-Rosebud
(Stations 2, 3, 4, and 5) could not be sampled adequately enough to give
species distribution for these stations.
DIVERSITY AND REDUNDANCY
A total of 92 taxa were collected in Rosebud Creek. Stations 1, 5, 6,
and 7 had similar numbers of species although the composition varied. Fewer
taxa were found at Stations 2, 3, and 4 (Figure 13). Average species
diversity and redundancy per sample is presented in Table 17.
Introduced Substrate Samples
The average number of taxa per sample (Table 7) is highest at Stations
5, 6, and 7 corresponding with trends for average numbers and biomass.
Ekman Dredge Samples
The average number of taxa in pools was highest at Stations 4 and 5 and
lowest at Stations 6 and 7, a condition contrasting with results from intro-
duced substrate and modified Hess samples. Station 3 was also low for
average number of taxa per sample.
57
-------
500
400
OC
LU
Q.
<
to
IE
U
Q.
tr
ID
CO
s
UJ
O
<
£
300
200
100
STATION I
STATION 5
- STATION 7
\
\
*
\
i
*
\
\
M
Figure 10. Seasonal variations in mean total numbers of
Hydropsyche sp. B per introduced substrate sample at
Stations 1, 5, and 7, May 1976 to November 1976.
58
-------
STATION I
STATIONS
STATION 7
Figure 11. Seasonal variations in mean total numbers of
Dubiraphia minima per introduced substrate sample at
Stations 1, 5, and 7, May 1976 to November 1976.
59
-------
300
200
o:
UJ
CO
UJ
o.
IT
UJ
00
UJ
UJ 100
M
A
STATION I
STATION 5
STATION 6
\
\
,/A \
' I *
A
MONTH
I X
( \
Figure 12. Seasonal variations in mean total numbers of
Choroterpes albicmnulata per introduced substrate-sample at
Stations 1, 5, and 6, May 1976 to November 1976.
60
-------
< 60
X
UJ
30
00
^ cc
o
15
TOTAL
INTRODUCED
SUBSTRATE
MODIFIED
HESS
345
SAMPLING STATIONS
EKMAN DREDGE
Figure 13. Total taxa per station and taxa collected by each of three
sampling methods, March 1976 to March 1977.
61
-------
TABLE 17. MEAN MACROINVERTEBRATE DIVERSITIES AND REDUNDANCY
PER SAMPLE, MARCH 1976 TO MARCH 1977
Shannon's Margalef Simpson
Station Index Index Index Redundancy
Introduced substrates
1 2.89 2.95 0.21 0.36
2 2.20 2.37 0.36 0.48
3 2.30 2.70 0.32 0.47
4 2.42 2.72 0.31 0.46
5 2.40 2.95 0.33 0.49
6 2.61 3.40 0.30 0.46
7 2.55 3.22 0.25 0.46
Efonan dredge
I 1.66 1.28 0.42 0.47
2 1.81 1.64 0.38 0.55
3 1.73 1.11 0.37 0.36
4 2.11 1.85 0.31 0.42
5 1.92 2.05 0.41 0.49
6 1.30 1.25 0.53 0.66
7 1.11 0.87 0.58 0.58
Modified Hess
1 2.48 2.36 0.28 0.41
3 1.90 2.26 0.38 0.57
5 1.99 1.91 0.39 0.48
6 2.82 2.79 0.21 0.35
7 2.43 2.84 0.26 0.44
62
-------
Modified Hess Samples
Average number of taxa per sample was highest at Stations 1, 6, and 7
(Table 7). Lowest numbers of taxa were found at Station 5; Station 3 was
also low in comparison to Stations 6 and 7.
63
-------
SECTION VIII
DISCUSSION
Basic information concerning the composition of the macroinvertebrate
community of Rosebud Creek in terms of distribution, diversity, and abundance
was gathered during this study. Variation of these parameters among sampling
stations was considered with respect to potential chemical effluents from
coal mining and combustion and with respect to the physical-chemical nature
of the Rosebud Creek system.
WATER CHEMISTRY: METALS
Concentrations of selected metals in Rosebud Creek (Table 4) are gener-
ally below criterion levels recommended by the U.S. Environmental Protection
Agency (1976). Average copper and zinc concentrations are highest at Sta-
tions 3 and 4 but probably do not present a threat to the benthic fauna.
Present levels are far less than the TL50 values (14 day) presented by Nehring
(1976) for Pteronarcys caHfomioa or Ephemerella gvandis or the 48-hr TLm
determined for copper on Ephemerella eubvaria (Warnick and Bell, 1969).
Average total mercury exceeded the criterion concentrations of 0.05 yg/1
total mercury recommended for freshwater aquatic life and wildlife by the
Environmental Protection Agency (1976). Aquatic insects vary widely in their
sensitivities to mercury but present concentrations in Rosebud Creek (Table
4) are less than the 2.0 mg/1 and 33.5 mg/1 toxic concentrations (96-hr
TLm) of mercury (HgCl2) for Ephemerella subvaria and Aovaneuria lyaoyiae
given by Vlarnick and Bell (1969). In this study it was not possible to
attribute low average numbers, standing crop, and taxa (introduced substrates)
at Stations 2, 3, and 4 to the reported mercury concentrations. Follow up
chemical and biological studies are warranted.
PHYSICAL CONDITIONS
Physical conditions of Rosebud Creek are typical of eastern Montana
transition prairie streams. Notable conditions include extreme turbidity,
high suspended load, and warm water temperatures all of which increase pro-
gressively downstream. These factors, and indirect effects from low stream
gradient, influence the abundance and distribution of the benthic
macroinvertebrate fauna.
Turbidity
Rosebud Creek is extremely turbid even during low flows, particularly at
Stations 1 and 2 (Tables 2 and 4). This condition results in a decrease
64
-------
in euphotic zone depth due to light extinction and a consequential reduction
in primary production (Bartsch, 1959). Most temperate streams are hetero-
trophic, that is, production from photosynthesis is exceeded by community
respiration and allochthonous material is an important source of energy
(Boling et al., 1975). The turbid state of Rosebud Creek results in alloch-
thonous detritus becoming more significant as an energy source and the
benthic community is composed of many organisms utilizing primarily detrital
food sources. For example, Hydropsychidae and Simuliidae, both common in
Rosebud Creek, are omnivorous collectors filtering fine particles from the
water column (Ross, 1944). Leptophlebiidae, the dominant mayfly family
encountered, are also omnivores and detritivores (Berner, 1959) and the
larvae and adults of Elmidae ingest decaying wood and encrusting algae
(Brown, 1972).
Temperature
Extreme summer water temperatures occur in Rosebud Creek and influence
the distribution of aquatic macroinvertebrates. Dodds and Hisaw (1925) con-
cluded temperature to be the main climatic cause for altitudinal zonation of
aquatic organisms. Altitudinal distribution of Plecoptera is due to the
maximum water temperature the nymphs can tolerate (Knight and Gaufin, 1966).
Of four taxa of Plecoptera collected from Rosebud Creek, two were collected
only at the uppermost location (Station 7) and Isoperla patriaia was common
only at Stations 6 and 7. This distribution is probably due to cooler summer
water temperatures near the headwaters. Braohyptera sp., a stonefly col-
lected at Stations 1 through 6, undergoes rapid development during fall and
winter and emerges during late winter or early spring. Naiads of Brachyptera
undergo summer diapause to escape warm water temperatures at that time
(Harper and Hynes, 1970). In addition, water temperature is a factor in
timing the emergence of aquatic insects (Nebeker, 1971). The apparent
temporal patterns of emergence in Hydropsyche sp. B and Dubiraphia minima
(Figures 10 and 11) may be due to cooler water temperatures at upstream
stations.
Substrate, Current Velocity, and Gradient
A complex interaction among stream gradient, discharge, suspended load,
and current velocity exists which influences the quality of the benthic
habitat. The longitudinal profile or gradient of most streams is typically
concave, decreasing downstream (Mackin, 1948) and is usually accompanied by a
downstream reduction in substrate size (Leopold and Maddock, 1953). Head-
waters typically have boulder or gravel substrates and steep slopes; down-
stream the size of bed material is smaller and sand may be common. Near the
mouth silt or clay may predominate. This generalized description of stream
substrate applies to conditions found in Rosebud Creek. Near the headwaters
gravel and cobble substrates are common; sand and gravel bed material are
more abundant downstream as the slope decreases. At Station 2, long, deep
reaches with flocculent clay or silt bottoms are prevalent. At Station 1 the
slope increases as Rosebud Creek approaches the Yellowstone River and there
is a corresponding increase in pool-riffle periodicity with rubble and boulder
substratum in the riffles. Riffles are uncommon at Stations 2, 3, and 4 due
to the low stream gradient.
65
-------
Substrate conditions (I.e., size and degree of sedimentation) have been
termed the most important single factor influencing macroinvertebrate habitat
quality (Pennak, 1971). Large substrates such as rubble and cobble support
larger invertebrate populations than sand and gravel (Pennak and Van Gerpen,
1947). Riffles composed of stable substrates are the most productive type of
bottom in streams (Patrick, 1949). Consequently, a longitudinal decrease in
substrate size and frequency of riffles as occurs in Rosebud Creek will
result in lower macroinvertebrate production and standing crop downstream.
Two consequences of reduced gradient include diminished overall current
velocity (Reid, 1961), and lowered sediment carrying capacity which results
in deposition of part of the suspended load (Morisawa, 1968). The ultimate
factor influencing sediment transport relates to the supplied load; i.e.,
input from erosion. If supplied load exceeds carrying capacity then deposi-
tion and/or change in stream morphology will occur. In Rosebud Creek the
combined effect of the increasing sediment load and decreasing gradient in a
downstream direction results in deposition of sediments on the substratum
(Stations 2 through 5).
Deposition of inorganic sediment can turn otherwise suitable substrate
into poor macroinvertebrate habitat (Cordone and Kelley, 1961). Stable
substrates are covered and, more importantly, interstitial spaces in the
substrate, where much of the secondary production occurs, are filled. Many
aquatic organisms seek refuge from swift current and the abrasive effect of
bed load by inhabiting spaces between or under rocks. Further, much of the
secondary production in streams occurs deep within the substratum. Coleman
and Hynes (1970) found that 83% of the benthic community lived below 5 cm in
the substrate. Poole and Stewart (1976) reported that 33.6% of the total
number of organisms were deeper than 10 cm in the bed of a Texas river. It
is evident that occlusion of interstitial spaces with inorganic sediment will
eliminate habitat and decrease diversity and secondary production.
Conversely, deposition of organic sediments at slow current velocities
may increase benthic production (Ruttner, 1952). At slow current speeds
gravel and sand substrates become more stable; this, in combination with
enrichment from organic sediments, creates an environment suitable for many
invertebrates. In Rosebud Creek, the common long reaches with slow current
velocities of 0.6 m/sec and less, support productive bottom faunas, e.g.,
Oligochaeta and Chironomidae, dependent on allochthonous detritus.
Sedimentation and a decrease in overall substrate size probably con-
tributed to the lower benthic diversity and population numbers at Stations 2,
3, and 4 due to occlusion of interstitial spaces and decrease in habitat
variety. Lower diversities, in comparison to other sampling sites, were
found at Stations 2, 3, and 4 with introduced substrate samplers, at Stations
3 and 5 with modified Water's round samplers, and at Station 3 using an Ekman
dredge. Also, introduced substrates showed low numbers at Stations 2, 3, and
4 which may be due to low populations of benthic macroinvertebrates for
sampler colonization in these sections of Rosebud Creek.
Substrate conditions at the point of sampling influenced results from
modified Hess and Ekman dredge samplers. The infrequence of riffles in
66
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Rosebud Creek at many stations limited the choice of sampling location. For
example, the existing riffle at Station 5 consisted of unstable gravel which
resulted in low standing crop, numbers, and diversity from modified Hess
samples taken at this station. Conversely, introduced substrates showed
Station 5 to have a high population and diversity relative to other sampling
sites.
Low numbers, standing crop, and diversity encountered in Ekman dredge
samples at Station 6 can likewise be attributed to the sand substratum common
in pools. Sand supports notoriously small populations of benthic inverte-
brates due to its unstable, grinding nature and lack of available food.
Current Velocity
Many stream-dwelling aquatic organisms are morphologically or behavior-
ally adapted to select habitats on the basis of current velocity. In streams,
rapid flowing portions generally support higher numbers of benthic inverte-
brates than lentic stretches with the same substrate. Long, slow stretches
that are common in Rosebud Creek had reduced numbers and fewer species.
Hydropychidae, which depend on rapid current for proper functioning of their
nets (Ross, 1944), were encountered in lower numbers at Stations 2, 3, and 4
where current velocity is generally slow. Elmidae, known to inhabit rapidly
flowing portions of streams (Brown, 1972), were found in lower numbers at
Stations 2, 3, and 4.. Choroterpes alb-umnulata and Ambrysus mormon, both
abundant at Stations 2, 3, and 4, are tolerant of slow flowing situations
(Edmunds et a!., 1976; Roemhild, 1976). Current velocity may have directly
influenced the distribution of these and other taxa (Figure 9) but probably
had a more profound effect by influencing substrate composition.
The tendency for various taxa to be low in abundance at Stations 2, 3,
and 4 (introduced substrates) was influenced by any one or a combination of
the physical conditions imposed by extreme turbidity, sediment deposition,
small substrate size, slow current velocity, and high temperature in Rosebud
Creek. Certain of these conditions were most extreme at Station 2 (low
gradient, silted substratum, and slow current velocity) and imposed unfavor-
able conditions for many macroinvertebrates. Conversely, upstream sections,
because of increased gradient, and decreased turbidity and temperature
supported more productive macroinvertebrate populations.
MACROINVERTEBRATE ABUNDANCE AND COMPOSITION
The benthic fauna of Rosebud Creek is similar in composition to that
found in Sarpy Creek, approximately 40 km west (Clancy, 1977). The lower
Yellowstone River and the Powder River support faunas similar to Rosebud
Creek and also decrease in diversity downstream (Newell, 1976; Rehwinkel
et al.. 1976).
Despite an extreme environment, Rosebud Creek supports a surprisingly
abundant and diverse fauna that is adapted to the prevailing conditions. In
terms of numbers of benthic invertebrates, it could be described as a rich
stream. Very little quantitative data exist on comparable streams in
eastern Montana; however, population estimates of 4993 and 6007 invertebrates
67
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per m2 from pools and riffles, respectively, in Rosebud Creek were greater
than the average 2809 invertebrates per m2 for the middle Yellowstone River
(Thurston et al.. 1975). Data from the West Fork of the Gallatin River, a
typical mountain stream similar in size to Rosebud Creek, averaged 1877
invertebrates per m2 during 1970-1971 (unpublished data).
Among important conditions conducive to high population numbers of ben-
thic macroinvertebrates in Rosebud Creek was the intact riparian vegetation
which kept the stream within its banks; this prevented extreme erosion,
scouring, and siltation. This vegetation was also an important energy source
for Rosebud Creek where primary production was limited by turbidity.
Many of the commonly encountered macroinvertebrates of Rosebud Creek
were adapted to live in turbid, silt-laden, or slow-flowing habitats.
Cheumatopsyche spp. have been reported to be tolerant of a wide range of
ecological conditions; Chewnatopsyche las-la was commonly found in heavily
silted streams. Triaorythodes minutus, Caenis sp., Chovotevpes albi&nnulata,
Leptophlebia gravastella, and Isonyahia siaea occur in silted or slow-flowing
streams (Edmunds et al., 1976). Microaylloepus pusillus is tolerant of
siltation and turbidity (Brown, 1972). Isoperla patricia inhabits prairie
streams that originate in the mountains (Ricker, 1946). Dubiraphia minima,
collected abundantly from pools and riffles, can be classified as tolerant of
siltation and slow current velocity. Many taxa that are numerically abundant
in the mid-Rosebud, e.g., Simulium spp., Choroterpes albiannulata, Sphaerium
spp., and Ambrysus mormon* have wide tolerances to ecological conditions. As
a generalization, aquatic invertebrates present in large numbers in the
prairie portion of Rosebud Creek could be classed as tolerant of turbid,
silty conditions.
SAMPLING CONSIDERATIONS
To describe accurately the aquatic fauna, it is necessary to sample as
many habitat types and take as many samples as possible. Benthic organisms
select habitat on the basis of various physical and chemical conditions,
i.e., substrate, current velocity, depth, dissolved oxygen, temperature, etc.
Three habitat types including riffles, pools, and long, gravel-bottom runs
were sampled semi-quantitatively during this study. Analysis of results
indicated that species composition varied with habitat and sampling device.
Modified Hess and Ekman dredge samplers collected 62 and 46% of the total
taxa found, respectively. Introduced substrates were most efficient in
collection of numbers and taxa; 89% of the total taxa collected including 22
not collected by other methods were found in introduced substrate samples.
Certain organisms, e.g., Ephoron album and Cataelyeta sp., were collected in
modified Hess samples but were absent from other methods. Chironomidae and
Oligochaeta composed the majority of the pool fauna; Trichoptera, Diptera,
and Ephemeroptera predominated in riffles and in introduced substrate
samples.
The long, hard-bottom slow reaches that are the most common habitat in
Rosebud Creek could not be effectively sampled using an Ekman dredge or Hess
sampler. However, introduced substrate in baskets was an efficient method
for sampling these habitats. Their use permitted standardization of substrate
68
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kind and size and enabled selection of sampling sites which had comparable
water depth and current velocity. This made quantitative comparisons between
stations more valid than with conventional grab type samplers. In addition,
introduced substrates were proficient in collecting macroinvertebrate taxa.
The samplers offered clean unsedimented substrates exposed to the current
which were attractive to many organisms including Hydropsychidae, Simuliidae,
and Baetidae, and because they rested flat on the substrate, a degree of
sedimentation occurred near the basket bottom and invertebrates that dwell 1n
fine substrates (e.g., Oligochaeta, Odonata, Sphaeriidae, and Chironomidae)
also colonized the samplers. The number of species found in introduced
substrate samples and the distribution of these species among sampling sta-
tions was a relatively accurate population parameter. However, introduced
substrates are selectively colonized by various insects including mayflies,
caddisflies, and beetles (Grossman and Cairns, 1974). Consequently, results
did not represent the existing standing crop, population numbers, or dis-
tribution of individuals among the species. Accurate measurement of these
parameters would necessitate collection and analysis of cores of the existing
substrate at each station.
Year-round sampling is necessary to describe macroinvertebrate distri-
bution and abundance. Benthic organisms vary in population numbers from week
to week depending on details of life histories (Pennak and Van Gerpen, 1947).
In Rosebud Creek Bvaohypteva spp. are present in winter and spring but not in
summer samples. Various taxa, i.e., SimuHum spp. and Chorotevpee
albiannulata, exhibit tremendous peaks in population numbers and form a sub-
stantial portion of the standing crop at that time. Their numbers may be an
insignificant portion of the total aquatic population at other phases of the
life cycle (egg and adult). Life histories also influence accuracy of macro-
invertebrate identification. Early instars are often difficult to identify
and collection of later stages is needed for accurate identification in many
cases.
Longitudinal variations in the benthic macroinvertebrate fauna were due
to influences from the unique physical-chemical nature of Rosebud Creek and
to influences from domestic and agricultural practices. Variations in the
benthic community during the study could not be attributed to effluents from
coal mining or combustion.
69
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TECHNICAL REPORT DATA
(Please read Instructions on the reverse before completing)
1. REPORT NO.
EPA-600/3-78-099
2.
3. RECIPIENT'S ACCESSION NO.
4. TITLE AND SUBTITLE
Environmental Effects of Western Coal Combustion
Part II - The Aquatic Macroinvertebrates of Rosebud
Creek, Montana
5. REPORT DATE
November 1978 issuing date
6. PERFORMING ORGANIZATION CODE
7. AUTHOR(S)
8. PERFORMING ORGANIZATION REPORT NO.
Steven F. Baril, Robert J. Luedtke, and George R.
Roemhild
9. PERFORMING ORGANIZATION NAME AND ADDRESS
Montana State University
Bozeman, Montana 59717
10. PROGRAM ELEMENT NO.
11. CONTRACT/GRANT NO.
R803950
12. SPONSORING AGENCY NAME AND ADDRESS
Environmental Research LaboratoryDuluth, MN
Office of Research and Development
U.S. Environmental Protection Aqencv
Duluth, Minnesota 55804
13. TYPE OF REPORT AND PERIOD COVERED
Final
14. SPONSORING AGENCY CODE
EPA/600/03
15. SUPPLEMENTARY NOTES
16. ABSTRACT
The aquatic macroinvertebrates of Rosebud Creek, Montana, were sampled between
February 1976 and March 1977 to provide data on their abundance, distribution, and
diversity. The sampling program was initiated during,the first year of operation of
the coal-fired power plants located at Col strip, Montana. The purpose of the study was
to determine if any immediate impacts of the power plant operation on the macroinverte-
brate communities of Rosebud Creek could be detected and to provide data for comparisons
with future studies.
Rosebud Creek supported a diverse bottom fauna with high population numbers com-
posed of species adapted to the turbid, silty conditions which are common in the
prairie streams of eastern Montana. Intact riparian vegetation appeared to be
important in maintaining stream bank stability and provided an essential food source.
It was concluded that faunal variation among sampling stations during the study
period was attributable to physical factors including turbidity, water temperature,
current velocity, and substrate, and not to potential impacts from coal mining and
combustion.
17.
KEY WORDS AND DOCUMENT ANALYSIS
DESCRIPTORS
b.lDENTIFIERS/OPEN ENDED TERMS C. COS AT I Field/Group
Biological surveys
Energy development
Macro i nvertebra tes
Effects pollution
Mining effects
Pollution survey
Benthic survey
57H
68D
18. DISTRIBUTION STATEMENT
RELEASE TO PUBLIC
19. SECURITY CLASS (ThisReport)
UNCLASSIFIED
21. NO. OF PAGES
85
20. SECURITY CLASS (Thispage)
UNCLASSIFIED
22. PRICE
EPA Form 2220-1 (Rev. 4-77) PREVIOUS EDITION is OBSOLETE
75
4 U.S. GOVEMIMEKTIWrniK: OFFICE: 1978 657-060/1526
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