EPA/600/R-94/143
August 1994
EVALUATION OF WATERSHED QUALITY IN
THE MINNESOTA RIVER BASIN
John W. Arthur , and James A Zischke"
Landscape Ecology Branch
Office of Environmental Processes and Effects Research
Environmental Research Laboratory - Duluth, MN
Department of 'Biology
St. Olaf College
Northfield, MN
ENVIRONMENTAL RESEARCH LABORATORY - DULUTH
OFFICE OF RESEARCH AND DEVELOPMENT
U.S. ENVIRONMENTAL PROTECTION AGENCY
DULUTH, MINNESOTA 55804
Printed on Recycled Paper
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DISCLAIMER
This document has been reviewed by the Environmental
Research Laboratory - Duluth (ERL-D), U.S. Environmental
Protection Agency and approved for publication. The mention of
trade names or commercial products does not constitute
endorsement or recommendations for use.
11
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PREFACE
Multiple stressors and responses continually define and
shape watersheds. The purpose of this research is to develop
procedures for defining watershed quality. This research focuses
on assessing their susceptibility from agricultural activity.
Section 101 in the Federal Clean Water Act requests that
procedures be developed to protect fish, wildlife and water
quality, and provide definitions for biological integrity. Past
studies have generally relied on either chemical-specific,
toxicological or biosurvey approaches to define healthy
watersheds. Simultaneous physical, chemical and biological
information is required if more holistic appraisals of watershed
quality are to be achieved. This research project addresses the
kinds of information necessary to establish baseline conditions
in a river basin and on individual watershed quality. An
important product of this research is to provide regulators with
procedures to classify and formulate goals on present status of
watershed resources .and later remediation activities.
111
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ABSTRACT
The Minnesota River has been noted for having water quality
problems, particularly for pollutants associated with sediment
transport. This research describes procedures and the results
obtained to evaluate the baseline (or existing) watershed quality
within the basin. Field work was conducted over three-years
(1989-1992). Three kinds of procedures were employed: physical
(or habitat related), chemical (surface and sediment pore water
quality) and biological (toxicological and macroinvertebrate
assessments). The basin was divided into four categories of
stream conditions: mainstem, principal tributary, reservoir, and
upper watershed locations. The study area extended from Lac Qui
Parle to Fort Snelling on the river's mainstem, and several
tributaries and upper watershed areas - most located near
Mankato, Minnesota. Aquatic insects were the major
macroinvertebrate component found at all sites. Habitat quality
estimates were highest in the principal tributary locations.
Significant associations were found between ammonia nitrogen and
sediment toxicity. Positive associations were found with ammonia
nitrogen and components of the macroinvertebrate community.
Correlations were also obtained with habitat and the
macroinvertebrate measurements. Lower quality watershed
locations generally exhibited lower macroinvertebrate diversity
and community integrity scores. Principal stressors affecting
the macroinvertebrate community appeared to be elevated
concentrations of ammonia and nitrite-nitrate nitrogen. More
watershed studies are needed to increase the confidence in
linking habitat and chemical stressors to biological quality.
IV
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CONTENTS
Preface - 111
ABSTRACT ... ............. iv
FIGURES vii
TABLES viii
ACKNOWLEDGEMENTS ..'...'. ix
LIST OF SELECTED ABBREVIATIONS AND SYMBOLS X
1. INTRODUCTION 1-1
1.1 BACKGROUND INFORMATION . . 1-1
1.2 SCOPE AND PURPOSE 1-2
2. METHODS 2-1
2.1 BASIN DESCRIPTION 2-1
2.2 STUDY DESIGN , 2-2
2.3 HABITAT 2-5
2.4 SEDIMENT PORE WATER 2-5
2.5 TOXICITY TESTING 2-6
2.6 MACROINVERTEBRATE PROCEDURES . 2-7
2.7 DATA MANAGEMENT AND STATISTICAL ANALYSIS ...... 2-8
3. EVALUATION OF WATERSHED QUALITY . 3-1
3.1 HABITAT ASSESSMENT 3-1
3.2 STREAM CHEMISTRY PROFILES ........ 3-6
3.3 TOXICITY FINDINGS 3-8
3.4 MACROINVERTEBRATE COMMUNITY CHARACTERISTICS . . . 3-11
3.5 INTERACTIVE WATERSHED COMPONENT ANALYSIS . . . . . 3-15
4. SUMMARY AND CONCLUSIONS 4-1
REFERENCES R-l
APPENDICES A-l
A. Minnesota River Basin Sampling Location . . A-2
B. Sediment Pore Water Nutrient Analytical Values ... A-3
C. Macroinvertebrate Community Characteristics -
Structural and Functional Groupings A-4
D. Macroinvertebrate Community Characteristics -
Average Indice Values A-6
E. Checklist of Macroinvertebrate Taxa A-7
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CONTENTS (continued)
F. Dominant Macro invertebrate Taxa Collected from
Hester Dendy Substrates
G. Dominant Macro invertebrate Taxa Collected from
Qualitative Samples
H. Ceriodaphnia and Selenastrum Toxicity Results .
A-9
A-10
A-ll
VI
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Figure 1-1
Figure 1-2
Figure 3-1
Figure 3-2
Figure 3-3
Figure 3-4
Figure 3-5
Figure 3-6
FIGURES
Location of Minnesota River mainstem and
tributary sampling sites . . .
2-3
Location of Minnesota River basin upper
watershed sampling sites 2-4
Minnesota River mainstem sampling sites
at Jordan and Morton 3-4
Minnesota River tributary sampling sites
at High Island Creek and Le Sueur River .
Macroinvertebrate structural community
characteristics
Macroinvertebrate functional community
characteristics
Calculated ICI biocriteria ,
Watershed component regression results
3-5
3-12
3-16
3-18
3-20
-Vll
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Table 3-1.
Table 3-2.
Table 3-3.
Table 3-4
Table 3-5
TABLES
Habitat characteristics 3-2
Surface and sediment pore water nutrient
characteristics 3-7
Toxicity results - Ceriodaphnia dubia exposed
to sediment pore water 3-9
Toxicity results - Selenastrum capricornatum and
sediment pore water 3-10
Analysis of biological community and environmental
factors ............... 3-22
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ACKNOWLEDGEMENTS
The authors gratefully acknowledge and thank the following
individuals who made important contributions towards this
project. Frank Puglisi and LeRoy Anderson, ERL-Duluth performed
the sediment pore water analyses. Charles Walbridge, ERL-Duluth,
assisted with the Ceriodaphnia bioassays, Jo Thompson, Integrated
Laboratory Systems - Duluth, performed the Selenastrum toxicity
tests. Surface water chemistry data were from the investigations
of Beth Proctor, Mankato State University, and Greg Payne, U.S.
Geological Service - St. Paul, MN. Habitat evaluations were done
by Bob Bellig, Biology Department, Gustavus Adolphus College.
Diane Waller, U.S. Fish Wildlife Service - La Crosse, supervised
and performed portions of the macroinvertebrate assessments.
Concurrent biological and habitat information was gathered in the
lower portions of the river (downstream from Henderson), and
furnished by D.- Kent Johnson, Metropolitan Waste Commission, St.
Paul, MN. We express special thanks to Mark Vlasak, with the
assistance of Charles Umbenhowar, Jr., Biology Department, St.
Olaf, for performing the descriptive statistics.
Tim Larson and Wayne Anderson, Minnesota Pollution Control
Agency, provided encouragement and logistical support throughout
this project.
Funding for portions of this project was provided by the
Legislative Commission for Minnesota Resources and the Minnesota
Pollution Control Agency.
IX
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LIST OP SELECTED ABBREVIATIONS AND SYMBOLS
ABBREVIATIONS
BOD
C
CCA
DMW
drn ar
EPT
ERL-D
ft
ICI
i.e.
in
mg
mg/l
mi
m
mm
NH3-N
NO2+NO3
NT
P < 0.01
QHEI
RPM
T-P
U.S. EPA
YCT
SYMBOLS
±
X G
biological oxygen demand
Celsius
canonical correspondence analysis
dilute mineral water solution
drainage area
Ephemeroptera/Plecoptera/Trichoptera
Environmental Research Laboratory - Duluth
foot
index community integrity
that is .
inch .
milligram
micrograms per liter
milligrams per liter
square miles
meters
millimeters
total ammonia nitrogen as N
nitrite plus nitrate nitrogen as N
not toxic
probability less than 1 % by chance alone
qualitative habitat evaluation index
revolutions per minute
total phosphorus as P
United States Environmental Protection Agency
yeast-cerophyl-trout chow
less than
greater than
less than or equal to
greater than or equal to
no information
percent
plus, minus
times gravity
x
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1. INTRODUCTION
1.1 BACKGROUND
The Minnesota River has long been known to have water
quality problems associated with sediment transport. An early
study by the Federal Water Pollution Control Administration
(1966), predecessor to the U.S. Environmental Protection Agency,
characterized the river as high in turbidity, bacteria coliform
and nutrient levels from Mankato (upper limit of study at river
mile 110) to the river's mouth at Fort Snelling near the Twin
Cities of Minneapolis and St. Paul, Minnesota. Upstream from
Chaska (river mile 30) benthic macroinvertebrate populations were
depicted as sparse and largely found on a bottom composed of sand
and gravel. Downstream from Chaska, the river bottom was
classified as mainly organic sludge/sand and dominated by
pollution-tolerant forms, especially sludgeworms. Subsequent
studies by the Minnesota Pollution Control Agency (MPCA, 1982)
and Mankato State University (King, 1985) characterized the river
as high in alkalinity, turbidity, and suspended solids. Total
phosphate and nitrate levels were also frequently found to be
elevated. Water quality standards most often exceeded were
coliform bacteria, turbidity, ammonia and dissolved oxygen (MPCA,
1982). The MPCA has recommended that the river's quality can be
upgraded through reductions in nonpoint source loadings of
sediments and nutrients.
Benthic macroinvertebrate surveys and ambient toxicity
testing are useful in defining watershed quality.
Macroinvertebrate surveys furnish "ground truth" information as
to the living conditions of a waterbody. Factors making
macroinvertebrates useful are their relative permanence and
immobility in streams, occurrence in a wide variety of habitat
conditions, and their sensitivity to pollutant gradients. An
unimpacted stream usually has a diverse community of benthic
forms with relatively larger proportional numbers of pollution-
sensitive species. Impacted streams are usually characterized by
low diversity and greater numbers of pollutant-tolerant species.
Toxicity tests are useful in identifying problem watershed
reaches, and assist in elucidating cause/effects and
concentration gradients in waterways (Ankley et al., 1990). The
biological surveys reveal the extent of the degradation, the
toxicity test findings assist in verifying and quantifying the
problem watershed areas.
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2.1 SCOPE and PURPOSE
The purpose of this report is to present habitat, chemical,
and benthic survey and toxicity test results for characterizing
watershed quality in the Minnesota River basin. The field work
was conducted in 1989-1992. During the same time period,
determinations were made by others of land use practices and
chemical analyses were performed on the watershed quality.
Our objective is to further consolidate this information
into a format that describes problem reaches and supplies
information defining watershed integrity. These findings have
been described in a series of reports (Arthur et al., 1994;
Proctor, 1994; and Zischke et al., 1994) to the Legislative '
Commission on Minnesota Resources and recently published by the
Minnesota Pollution Control Agency. It was our hypothesis that
the relative influences from these physical, chemical, and
biological descriptors can be used to define watershed quality in
the Minnesota River basin.
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2. METHODS
2.1 BASIN DESCRIPTION
The Minnesota River is 335 miles long and begins at the
terminus of Big Stone Lake in eastern South Dakota. Three dams,
located at Big Stone, Marsh, and Lac Qui Parle Lakes, convert the
uppermost 85 miles into headwater lakes. Downstream from the
Granite Falls Dam the river flows unobstructed for 240 miles to
its confluence with the Mississippi River at Fort Snelling. The
drop in elevation between Big Stone Lake and Fort Snelling is 274
feet or an average gradient of 0.8 feet per mile. The Minnesota
River basin covers 17,000 square miles. Mean annual flow
measured at the mouth is 5,000 cubic feet per second (cfs). The
middle and lower sections of the river are slow moving in
velocity. The largest tributary entering of the Minnesota is the
Blue Earth River which enters at Mankato with a mean annual flow
of 1300 cfs. Other major tributaries entering from the southwest
are the Lac Qui Parle, Yellow Medicine, Redwood and Cottonwood
Rivers with combined mean annual flows of 600 cfs. Major
northern tributaries to the Minnesota are the Pomme de Terre and
Chippewa Rivers and Hawk Creek, combined mean annual flow of 450
cfs. The river greatly increases flow downstream, for example,
at Lac Qui Parle dam mean annual flow is 600 cfs, whil.e at river
mile 39 (Jordan) the mean flow is 3400 cfs. The lower 22 miles
of the river has been dredged to accommodate barge shipping
(Waters, 1977).
The Minnesota River basin lies within three U.S.. EPA
ecoregions (Gallant et al., 1989). The uppermost sections of the
river and headwater reservoirs lie in the Northern Glaciated
Plains, the middle undammed portion in the Western Corn Belt
Plains and downstream from Mankato the river is classified within
the North Central Hardwood Forest ecoregion. Using U.S.
Geological Survey mapping nomenclature, the river basin is in
Accounting Unit 070200, Upper Mississippi River Region 7.
Exceptionally high levels of nitrite-nitrate nitrogen levels are
present in the Northern Glaciated Plains and Western Corn Belt
ecoregions and have been associated with row crop fertilization
of corn and soybeans (Fandrei et al., 1988).
Land use throughout the Minnesota River .basin is principally
farming. Most of the land is under cultivation (over 90 percent)
and less than 3 percent is under forestation. Soil composition
ranges from clay to silt loam in composition. Erosion from
rainfall and wind is a common problem. The basin is flat to
gently rolling in topography. The area near Mankato has the
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greatest percentages of poorly drained wet soils and erosion
problems. Open ditch and tile drainage systems are commonly
found on much of the cultivated lands and contribute increased
nutrient loads to the river (MPCA, 1982).
Population densities are greatest in the eastern portions of
the basin. Human waste loadings (as 5-day BOD values)
progressively increase in the river's downstream reaches (MPCA,
1982). Major population centers in the basin are New Ulm,
Mankato Minneapolis, and St. Paul.
Koehler and Cooper (1994) have characterized 10 watersheds
near Mankato in the Blue Earth, Watonwan and Le Sueur river
subbasins. The vast majority of land use was found to be devoted
to agriculture, crops being two-year rotations of corn and
soybeans. This study estimated that approximately 200,000 tons
of soil per year is being lost from 64,000 acres of cropland, and
was primarily due to sheet and rill erosion. Approximately 19
percent of the erosion is delivered to the watershed outlets and
contributed to further downstream water quality problems.
2.2 STUDY DESIGN
For this study, we divided the Minnesota River Basin into
four categories of stream conditions - mainstem, principal
tributary, reservoir and upper (first to second order) watershed
locations. Fifty sampling locations were initially contained in
studies previously reported to the Legislative Commission on
Minnesota Resources. Fourteen of these sample sites are located
on the river's mainstem, 10 near the mouth of principal
tributaries, 4 are on reservoirs, and 22 are on upper watershed
sites. To maximize the likelihood of finding watershed
descriptors (or exposure and response indicators), 31 sites were
selected for further analysis. The sites selected in each of the
four watershed categories had relatively similar habitat
characteristics.
Descriptions of the location of these 30 sites is given in
Appendix A. Study emphasis during 1989-1990 was on a general
baseline assessment of the river's mainstem and principal
tributaries. Figure 1-1-shows location of the mainstem and
tributary stations. Sampling efforts in 1991-1992 were focused
on the low order streams, most of which were located south of
Mankato (Figure 1-2). Ten sites were located along the river's
mainstem, 8 sites near the mouths of principal tributaries, 3
sites near the terminus of reservoirs, and 9 were upper watershed
2-2
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MINNESOTA
IOWA
Miles 50
Main-stem Station
Tributary Station
Reservoir Station
Figure 1-1. Location of Minnesota River mainstem and tributary
sampling sites.
2-3
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Miles 50
UPPER WATERSHED SITES
= CATALOGING UNIT BOUNDARY
Figure 1-2. Location of Minnesota River Basin Upper Watershed
sampling sites.
2-4
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locations. Study reaches were positioned from 50 to 200 m
upstream or downstream from road bridge crossings. Areas sampled
at each station were generally two to four times the width of the
stream segments. Because the Minnesota Basin is dominated by
agricultural activities, it was anticipated that the low order
tributaries would be autotrophic, mud-bottomed, with open
canopies and affected by excessive inputs of sediment and
nutrients. The higher order tributaries and the river's mainstem
were found to be a mix of these characteristics. Using Ohio EPA
nomenclature (1987), the upper watershed sites can be classified
as headwater sites (drainage areas < 20 mi ) , about one-half of
the principal tributary sites as wading sites (drainage areas
between 20-500 mi^) , and the remaining principal tributaries
and all of the mainstem locations as boating sites (> 500 mi, ,
see Appendix A).
2.3 HABITAT
An appraisal of habitat quality was conducted.once at each
sampling location during the summer season. The habitat
assessment technique, as described by the Ohio Environmental
Protection Agency (1987, 1989), was used for this study. This
procedure includes a calculation of a Qualitative Habitat
Evaluation Index (QHEI), and provides an empirical evaluation of
lotic quality. The seven metrics used for computation of the
QHEI were: substrate type/quality, instream cover, channel
morphology, riparian zone/bank erosion, pool/riffle-run, map
gradient, and drainage area. The total QHEI score was determined
by adding together the individual metric scores, the best
attainable score being 100.
Substrate embeddedness (proportion of particles < 2.4 mm.
was determined at all mainstem and-tributary locations, and at
four of the upper watershed sites. Representative surficial
substrate samples (from a depth of 4 to .6 inches) were collected
with a scoop, and proportions of the finer particles separated by
passing the sample through a 2.4 mm sieve screen. Percentages of
the fine particles (< 2.4 mm) were determined by volume
displacement using a large graduated cylinder.
2.4 SEDIMENT PORE WATER
Stream bottom samples were collected with a petite Ponar
grab at three or more representative points at each monitoring
site for sediment pore water analysis. All samples were kept
cold (unfrozen, <4° C) in ice chests for transportation to the
laboratory. Sediment pore water was prepared in a refrigerated
2^5
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centrifuge (at 5° C) by spinning at 2500 X G for 20 minutes. The
supernatant (pore water) was refrigerated. Samples were analyzed
for anions and cations using ion chromatography and inductive
coupled plasma/atomic emission spectrometry procedures.
Nutrients (NH3-N, NO2+NO3-N, total phosphorus, and total nitrogen)
were determined with an automated ion analyzer and total organic
carbon with a Dohrmann instrument using U.S. EPA (1983)
procedures. All analyses were conducted using duplicates,
spikes, and known standards.
2.5 TOXICITY TESTING
Two standardized procedures were used for the toxicity
tests, with Ceriodaphnia dubia, a microcrustacean, and
Selenastrum capricornutum, a green alga. Both organisms have
been widely used by the U.S. EPA (Lewis et al.r (1992)) to
evaluate toxicity of ambient surface water/sediments and
effluents.
Source of Ceriodaphnia was from the (Environmental Research
Laboratory at Duluth, Minnesota (ERL-D) laboratory cultures. The
animals of known parentage were < 24 hours old when the tests
were begun. Acute toxicity tests (48 hours in duration) were
conducted only with the September 1989 surface water samples
following procedures given in Lewis et al. (1992). All remaining
toxicity tests were chronic life cycle tests. For the chronic
tests, one animal was placed into each of ten, 30 ml cups
containing 15 ml of test water. The same procedure was repeated
for a set of 10 replicate controls containing either Lake
Superior water or dilute mineral water solution (DMW). The
daphnids were fed a yeast-cerophy11-trout chow (YCT) and algae
daily, and test solutions were changed (renewed) on days 2 and 4
of the 7-day test period. Survival and young production during
the 7-days were analyzed for significant differences (P < 0.05)
from the controls using a pair-wise multiple range comparison
procedure. Additional test details are given in Lewis et al.
(1992) .
The source for Selenastrum cells was from ERL-Duluth
cultures. Dilution water consisted of stock culture medium
containing 100 /xg/1 EDTA. Water samples were filtered through a
0.45 fj. millipore filter and fortified with media mineral salts to
a concentration equal to the synthetic dilution water. A
dilution series was prepared with 30, 60 and 100 percent sediment
pore water and a dilution control. Each test received a starting
inoculum of 10,000 cells per ml; tests were cultured under
continuous illumination of 400 ± 50 foot candles, at 24 ± 2 °C.
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The test containers were continuously shaken at 100 RPM. Algal
growth was determined at 48 hours and at the end of the 96-hour
test with an electronic particle counter. Test results were
expressed as percent of the control growth (i.e. test/control X
100 = percent stimulation or inhibition).
2.6 MACROINVERTEBRATE PROCEDURES
Characteristics of the macroinvertebrate communities were
determined by using artificial substrate (Hester-Dendy samplers)
and instream dip net and hand-picking sampling procedures. The
multiplate Hester-Dendy samplers were selected (using
specifications according.to the Ohio Environmental Protection
Agency ,1987) to provide a consistent uniform substrate for
macroinvertebrate colonization.
Each Hester-Dendy artificial sampler consisted of eight 3x3
inch, one-eighth inch thick tempered masonite hardboard plates
fastened together with an eye-bolt. -The plates were separated by
one-inch square hardboard spacers. Three samplers were attached
by threaded rod to a concrete patio block, placed on the stream
bottom at a depth of 0.75 to 1.5 m, and left for 6-weeks of
colonization. During retrieval, to minimize loss of organisms, a
0.15 mm mesh drawstring net was placed over the submerged
samplers. Sampler plates were scraped and organisms retained on
a 40-mesh sieve screen (0.425 mm mesh) and preserved in.70
percent ethanol.
Macroinvertebrate kick samples were collected by disturbing
(agitating and kicking) the stream bottom while positioning an A-
frame dip net downstream to collect dislodged organisms. Samples
were also taken by hand-picking organisms from shoreline objects
such as boulders, logs, and bridge abutments. A standardized
time period of thirty minutes was used for handpicking collection
procedures at each location. The collected organisms were
preserved in 70 percent ethanol.
Organisms were sorted and tabulated in a glass tray over a
lighted glow box. Initial sample examination was done with a
magnifying lens and the final sorting was done with a
stereomicroscope. Samples were periodically further checked for
sorting completeness. Large numbers of a taxonomic group
(generally > 300) were subsampled in a glass tray divided into
equal quadrants. Macroinvertebrates were generally identified to
the genus taxonomic level. Midges were identified by mounting
the larval head capsule on glass slides for microscopic
examination. A reference collection of the organisms was
2-7
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assembled to maintain consistent and uniform identifications.
All count information was placed into a computerized format
to classify the community into structural and functional
groupings according to feeding habits, after Merritt and Cummins
(1987). The standard metrics used to classify structural
features were richness, diversity (Shannon-Weaver), equitability,
and percentages of Ephemeroptera^Plecoptera-Tricoptera (Weber,
1973). An Index of Community Integrity (ICI) was calculated
according to the Ohio EPA (1987). Qualitative field collections
were not made in 1991-1992, therefore ICI metric 10 could not be
determined and the final ICI score was derived using the first
nine metrics.
2.7 DATA MANAGEMENT AND STATISTICAL ANALYSIS
Individual survey data sheets were kept in bound notebooks.
Each analysis and sampling location had separate unique
identifications. All- surveys were sequentially numbered and data
compiled into computerized spreadsheets. Data was converted to
ASCII formats for the multivariate analyses.
Descriptive statistics were used to determine the habitat,
chemical, toxicity, and mac.ro invertebrate associations. Multiple
regression analyses were used to determine the toxicity
relationships with the sediment pore water measurements and the
habitat, nutrient, and macroinvertebrate findings. The levels of
high, medium, and low significance were set at P<0.01, P<0.05,
and P<0.1, respectively. Canonical correspondence analysis (CCA)
was used to associate all the taxa and the dominant
macroinvertebrate groups to eight environmental variables (ter
Braak, 1986). The eight variables were surface water and
sediment pore ammonia, nitrite-nitrate and total phosphorus, and
QHEI habitat score, and drainage area at the sampling site. All
macroinvertebrate counts were log transformed to reduce the
potential effect of extremely abundant taxa and downweighing the
influence of rarer taxa. Forward selection and Monte Carlo
permutation tests were used to determine the environmental
variables having the greatest influences.
2-8
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3. EVALUATION OF WATERSHED QUALITY
3.1 HABITAT ASSESSMENT
Habitat quality (based on the QHEI scores) was the highest
at the main tributary sampling sites. Overall, the QHEI scores
at the mainstem and upper watershed sites were 20 percent lower
(Table 3-1). Lowest scores (< 50) were found in the lower 25
miles of the mainstem and at 3 of 8 upper watershed sites.
Factors contributing to poor quality at these sites were a lack
of substrate heterogeneity (diversity), unstable substrates, and
excessive amounts of fines (particles < 2.4 mm). An open
dominant riparian cover was present at the poor quality upper
watershed sites. A wooded land cover was commonly found at most
tributary and mainstem locations.
Most samples were collected in relatively shallow water (< 3
ft). Samples collected downstream from Jordan were taken near
the edges of the barge channel in deeper water. River bottom
samples from the mainstem stations sediments downstream from
Delhi, in the reservoirs and at some of the upper watershed sites
were embedded with fine particles (> 50 percent by volume) and
with a mixture consisting of sand and gelatinous muck. Mainstem
stations upstream from Jordan were generally shallow and
exhibited moderate amounts of overhanging bank vegetation (Figure
3-1). The main tributary sediments were characterized by having
greater proportions of gravel and stones, and fine particles
amounted to < 50 percent by volume (Table 3-1). The tributary
streams had more variable water depths and greater .proportions of
overhanging vegetation (Figure 3-2). Higher average QHEI habitat
scores and lower amounts of substrate embeddedness were found at
the main tributary stations.
A greater degree of bank erosion was observed at the
mainstem locations. Slumping banks, and a lack of associated
vegetation and large rip rap for erosion protection were commonly
observed. The main tributary sites appeared to have the best
bank stability. A mixture of open grassland and wooded area were
found at most of the upper watershed sites. The upper watershed
sites typically had the least amounts of overhanging vegetation
and channel obstructions. A general absence of aquatic
macrophytes (both submerged and emergent) was noticed at all the
sampling locations.
Baker (1988) concluded that watershed size has a major
influence on pollutant loading and instream water quality.
Watershed size affects the seasonal export of particulate
, . 3-1
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Morton (river mile 203)
Jordan (river mile 42)
Figure 3-1. Minnesota River mainstem sampling sites at
Jordan and Morton.
3-4
-------
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associated pollutants and sediment. Exposure durations from
rainfall events tend to be more short-term in smaller watersheds,
but lower and longer-term in larger watersheds. Lenat (1984) in
a study of agricultural streams found that the amount of
substrate (< 2 mm) was related to farm management practices.
Although many of the stations listed in Table 3-1 showed a
general association between greater bank erosion and substrate
embeddedness, insufficient information was gathered in this study
to directly relate the occurrence of fine particles in the river
substrate to land use management practices.
3.2 STREAM CHEMISTRY PROFILES
Except for ammonia-nitrogen, similar nutrient concentrations
were generally found between the surface water and sediment pore
water samples (Table 3-2). Total ammonia-nitrogen (as N)
concentrations were highest in the mainstem and reservoir
sediment pore waters. Reservoir sediment pore water had about 10
times higher concentrations of ammonia nitrogen than at the other
sites. Concentrations of nitrite-nitrate nitrogen were 5-10
times higher in the main tributary than at the upper watershed
sites. Ammonia-nitrogen, nitrite-nitrate and iron concentrations
progressively increased at the downstream mainstem locations.
Arthur et al. (1994) report supplied a summary of surface water
anion and cation characteristics in the Minnesota River Basin.
Five cations, namely cadmium, chromium, copper, lead, and zinc,
were uniformly 'at or below the analytical limits of detectability
in the sediment pore waters. No differences were found by
location for the anion and cation concentrations or for surface
water total organic carbon and conductivity values.
The surface water nutrient concentrations reported in Table
3-2 are similar to those reported by Baker (1988) in corn/soybean
agricultural watersheds. He found higher nitrate concentrations
in the smaller watersheds. Although higher nitrate levels were
generally present in the upper watershed locations, no comparable
samples were collected in the low to higher order streams to
follow the nutrient changes after episodic rainfall events.
Amounts of land use devoted to agricultural activities have
been linked to decreased water quality in Minnesota (Fandrei et
al.r 1988). In the agricultural areas, these investigators
suggested that reference (or lowest) surface water values for
total ammonia, nitrite-nitrate nitrogen and total phosphorus
appear to be between 0.3-0.4, 0.5-4.2, and 0.2-0.3 mg/1,
respectively. Surface water ammonia concentrations at all of the
3-6
-------
Table 3-2,
SURFACE AND SEDIMENT PORE WATER
NUTRIENT CHARACTERISTICS (Av. Cone, -mg/1)
Surface Water
Sediment Pore Water
Mainstem Locations
Fort Snelling
35 W Bridge
Jordan
Henderson
St. Peter
Judson
Courtland
Fort Ridgely
Morton
Delhi
Upper Sioux
Reservoirs
Rapidan
Chippewa
Lac Qui Parle
Main Tributaries
High Island Cr.
Rush Riv.
Blue Earth Riv.
Le Sueur Riv.
Watonwan Riv. ,
Cottonwood Riv.
Redwood Riv.
Hawk Cr.
Yellow Med. Riv.
Upper Watersheds
Beau ford
Blue Earth
County Rd 13
Frost
Mountain Lk
St. James
Wells
Gay lord
NH,-N
—
< 0.1
< 0.1
< 0.1
< 0.1
< 0.1
< 0.1
< 0.1
< 0.1
-
• . -
0.1
0.1
0.3
< 0.1
< 0.1
< 0.1
< ,0.1
< 0.1
< 0.1
< 0.1
0.2
. , -
-
-
< 0.1
-
< 0.1
T-P NO,,+NO,
-
—
0.2
0.1
0.2
0.2
0.3
0.3
0.2
0.2
-
-
0.3
0.3
0.4
0.2
0.4
0.3
0.2
0.3
0.4'
0.2
0.3
-
-
—
0.4
-
0.9
-
—
5.2
4.2
2.3
1.5
1.3
1.0
0.5
0.6
-
-
0.1
6 '..4
12.0
13.2
15.3
14.6
8.8
3.5
3.9
2.6
17.7
16.8
18.6
17.3
19.4
12.9
18.9
NH3-N T-P NO,+NO, a
9.5
7.0
0.9
1.7 <
3.5
0.3 <
0.8
0.2 <
0.5
1.8
.0.2
4.8
4.0
13.2
0.2 <
< 0.5
0.4
0.2
0.3
0.5
- •
< 0.1
< 0.1
-
0.1
3.6
—
- -
-
< 0.1 •
1.5 -
0.7 1.6
0.7 3.0
0.1
0.1
0.2
0.1
0.1
0.1
0.1
0.2
0.2
0.9
1.8
5.2
0.1
0.2
0.6
0.1
0.2
0.3
-
0.5
0.2
-
0.1
0.2
—
- .
- .
< 0.1
< 0.1
1.6
3.4
3.4
2.1
1.5
0.3
0.1
0.4
-
1.1
< 0.1
< 0.1
3.5
13.9
11.1
12.4
7.9
4.1
-
< 0.1
1.6
-
9.5
< 0.1
—
—
-
13.7
3-,2
a NH3-N = Total ammonia nitrogen, T-P = Total phosphorus as (PO4)
NO2+NO3 = Nitrite+Nitrate nitrogen. - No information
Note: Surface water mainstem, reservoir, and tributary water data
from Payne (1994) , upper watershed data from Proctor (1994).
3-7
-------
stations in our study were generally comparable to their reference
levels. Most of the nitrite-nitrate concentrations exceeded .the
reference values, especially in the main tributary locations
associated with the Blue Earth drainage (south of Mankato) and at
all of the upper .watershed sites. Insufficient surface water
values were available for comparison with the reservoir stations
(Appendix B) . The Fandrei et al. (1988) report did not include
sediment pore water values.
Water quality values in the Fandrei et al. (1988) report
exceeding the 75th percentiles for total ammonia, nitrite-nitrate,
and total phosphorus were 0.6, 6.8, and 0.5 mg/1, respectively.
Only the nitrite-nitrate concentrations found in Table 3-2 exceeded
their 75th percentile value. Making this same comparison with the
average sediment pore water, the ammonia nitrogen values exceeded
their 75th percentile most often followed by nitrite-nitrate and
then total phosphorus. Using these guidelines, stations having the
best water and sediment pore water quality were found in the
river's mainstem and in the main tributaries entering upstream from
Mankato.
Relatively meager information was available ' on herbicide
concentrations. Thurman et al. (1991), have reported on surface
water total herbicide concentrations in the Minnesota River, and
found that the median concentrations were < 5 vg/I. -Atrazine was
found to be the most persistent herbicide monitored. Therefore, it
appears that herbicides may have played a minor role in our study
since it has been recently concluded that concentrations < 20 Mg/1
do not cause sustained observable ecosystem effects (Huber, 1993).
3.3 TOXICITY FINDINGS
None of the surface water samples collected during September
1989 were toxic to Ceriodaphnia. Only the sediment pore water
samples (Table 3-3) showed inhibitory test responses. Samples
toxic to Ceriodaphnia were found at 6 of the 26 sampled sites.
Mainstem locations upstream from the highway 35 W bridge and 8 of
9 tributary locations were not toxic. The most toxic samples were
gathered from the Lac Qui Parle Reservoir and two mainstem
locations at the, 35 W Bridge and Fort Snelling. Toxicity was found
on two of five occasions at the Rapidan Reservoir site and on one
sampling period at the Chippewa and High Island Creek, sites.
Ceriodaphnia reproduction was the most sensitive test response
(Appendix H). The significant test,response was final yield.where
young production was < 50 percent of the-controls. In only a few
tests did the sediment pore water samples cause complete mortality.
3-8
-------
TABLE 3-3.
TOXICITY RESULTS - CERIODAPHNIA DUBIA EXPOSED
TO SEDIMENT PORE WATER.
Sampling Period
1
Main Stem Locations
0/89
Fort Snelling 50-100% a
35 W Bridge <
Jordan
Henderson
St . Peter
Judson
Courtland
Morton
Delhi
Upper Sioux
Reservoirs
Rapidan
Chippewa
100%
NT
NT
NT
NT
NT
NT
NT
NT
NT
NT
Lac Qui Parle 50-100%
Main Tributaries
High Isl. Cr.
Rush Riv.
Blue Earth Riv.
Le Sueur Riv.
Watonwan Riv.
Cottonwood R.
Redwood Riv.
Hawk Cr.
Yellow Med. Riv.
Upper Watershed
Blue Earth
County Road 13
Wells
Camp Pope Cr.
Gaylord
a Range between no
b NT = No toxicity
NT
-
NT
NT
NT
NT
NT
NT
NT
-
-
'-
-
effect
found .
1/90
NT
h
NT b
-
NT
-
NT
NT
-
—
NT
—
25-50%
-
NT
NT
-
-
NT
-
-
—
-
-
-
- -
level
6/90
25-50%
25-50%
NT
c
NT
-
NT
NT
-
—
50-100%
50-100%
25-50%
-
NT
NT
NT
NT
NT
-
-
NT
-
-
-
-
9/90
50-100%
25-50%
NT
NT
NT
NT
NT
-
NT
—
50-100%
—
—
< 100%
—
NT
NT
NT
-
-
-
NT
-
-
—
-
(50%) and effect
5/92 7/92
NT
NT
NT .
NT
- -
NT
-. . • - •
- -
NT
_ «
NT - '
— —
•~ ~
NT
— —
NT
- -
. - -
- -
— • —
— —
NT
NT
NT
NT
NT NT
NT NT
level (100%) .
3-9
-------
TABLE 3-4. TOXICITY RESULTS - SELENASTRUM CAPRICORNATUM AND
SEDIMENT PORE WATER.
08/89
Sampling Period
10/89 06/90
Main Stein Locations
Fort Snelling
Jordan
Henderson
St. Peter
Courtland
Morton
Reservoirs
Rapidan
Lac Qui Parle
Main Tributaries
Blue Earth Riv.
Le Sueur Riv.
Watonwan Riv.
Cottonwood Riv.
Yellow Med. Riv.
29
93
NT
NT
15
7
22
30
12
55
45
24
19
30
NT
74
NT
32
5
NT
NT
NT
NT
NT
- = Toxicity test not conducted.
Effect level, as percentage yield in cell numbers against
control response.
NT = Not toxic, cell numbers > control response.
3-10
-------
Sediment pore water toxicity to Selenastrum was found at 8 of
the 15 sampled locations. Toxicity at the mainstem locations was
found beginning at Morton (river mile 203) and, with exception of
Jordan, at all downstream stations and both reservoir sites (Table
3-4) . Sediment pore water from the two reservoir sites yielded the
most inhibitory test responses. None of the main tributary samples
were toxic to Selenastrum. Overall, the most toxic locations (in
terms of inhibition) were at Fort Snelling, Henderson, and at both
of the tested reservoir locations. Samples from the Lac Qui Parle
Reservoir showed the greatest toxicity and the most uniform test
responses.
More sediment pore water samples were inhibitory (showed a
toxic response) with the Selenastrum than the Ceriodaphnia test.
Samples from approximately 50 percent (7/13) of the locations were
partially inhibitory with the Selenastrum test. By contrast, only
about 20 percent (6/31) of the locations were found to be
inhibitory with the Ceriodaphnia procedure.
3.4 MACROINVERTEBRATE COMMUNITY CHARACTERISTICS
A total of 135 macroinvertebrate taxa were collected; 81 were
found at the mainstem and tributary locations, and 92 taxa at the
upper watershed sites (Appendix E) . The five groups that accounted
for two-thirds of the overall community richness were: Diptera-
Chironomidae (midges) at 26 percent, Ephemeroptera (mayflies, 14
percent), Coleoptera (beetles, 10 percent), Trichoptera
(caddisflies, 9 percent) and other Dipterans (7 percent).
Flatworms, odonates, stoneflies, and hemipterans were more commonly
found at the mainstem and tributary locations. Leeches, snails,
and isopods were primarily limited to the upper watershed sites.
The most abundant macroinvertebrates (in terms of numbers
counted) were mayflies, caddisflies and midges (Appendix C) . These
three groups accounted for 98 percent of all the individuals
collected at all the mainstem sites, 87 percent at the tributary
locations, and 71 percent at the upper watershed sites.
Caddisflies comprised the largest proportion of the communities on
the mainstem and tributaries; midges were most common at the upper
watershed sites (Figure 3-3). Common mayfly genera were Baetis,
Caenis. Stenonema. Stenacron, Potomanthus. and Tricorvthodes.
Common midges were Glvptotendipes, Polvpedilum. and Tanvtarsus, and
the most abundant caddisflies taxa were Hydropsvche.
Cheumatopsyche, Potamvia,and Cyrnellus. By comparison, in a survey
of the Minnesota River's mainstem from Le Sueur (river mile 78)
to Ortonville (river mile 333) , Kirsch (1985) reported collecting
3-11
-------
Mainstem Stations
% Caddis
Mayflies
% Midges
Main Tributaries
% Caddis
% Mayflies
Midges
Figure 3.3. Macroinvertebrate structural community
characteristics.
3-12
-------
Upper Watershed
Caddis
% Mayflies
% Midges
Figure 3.3 (Cont). Macroinvertebrate structural community
characteristics.
3-13
-------
212 benthic taxa; insects comprised 90 percent of the
collected. The dominant insect groups in their study were
mayflies, caddisflies, and midges.
total
Similar numbers and kinds of major insect groups were
collected with both the artificial substrates and qualitative
sampling procedures (Appendix F and G) . Mayflies, caddisflies and
midges were the dominant groups collected with both procedures.
Flatworms, oligochaetes, annelids, snails and amphipod crustaceans
were commonly collected only with the qualitative procedures.
Insect genera found only in the qualitative samples were the water
boatman Cvmatia. and the damselfly Arqia. More midge taxa were
collected from the artificial substrates. Hester-Dendy samples
from the upper watershed sites had a more diverse assemblage of
taxa than samples from the mainstem and tributaries.
There were major differences between sampling locations in
richness and in indices of diversity and equitability (Appendix D) .
The greatest deviations in richness values were with the mainstem
stations while ranges in diversity and equitability were greater in
the upper watershed sites. Least variations in these indices were
found in mainstem locations upstream from St. Peter. Weber (1973)
has suggested that diversity values > 3.0 and equitability > 0.5
may be representative of relatively nonimpacted conditions or clean
water quality. Three main tributary sites (Le Sueur River,
Watonwan River and Hawk River) and two upper watershed sites (Camp
Pope Creek and Gaylord) met or exceeded these conditions.
Equitability values exceeding 0.8 were recorded at two other upper
watershed sites (Beauford and Wells).
Changes in abundance of macroinvertebrate groups in
agricultural drainages have been documented by others. Lenat
(1984) found that there were both shifts and declines in the
abundance of EPT taxa with a replacement by more tolerant
trichoptera and dipteran forms. Gammon (1981) noted that as stress
from nonpoint source pollutants increased, chironomids (midges)
became more abundant, trichoptera and ephemeroptera groups less
numerous and irregular in appearance. However, some studies have
not been able to document these changes (Marsh and Waters, 1980;
King, 1985). The King study was limited to benthic collections
along the Minnesota river's mainstem. Marsh and Waters (1980)
attributed the few benthic differences they found to local site-
specific factors.
Location differences were found in the functional
classification of the macroinvertebrate community (Appendix C) .
Collectors were especially common at the mainstem sites (between
3-14
-------
86-99 percent) indicating a good supply of fine particulate organic
matter. Scrapers progressively increased in higher proportions
upstream from Mankato. At the main tributary sites, collectors
remained dominant but were less abundant and replaced by predators
and scrapers. Shredders occurred mainly in the upper watershed
locations Figure 3-4). Some of these distributions may naturally
occur as a function of stream size and order. Camargo (1992) found
shredders were more abundant in headwaters, scrapers in the middle
reaches, collectors most commonly found in the lower reaches, and
predators were distributed throughout the stream. Also, these
functional distributions appear to follow the river continuum
theory (Cummins,- 1979). Menzel (1984) noted that in Iowa prairie
streams, collectors and scrapers were the dominant, and predaceous
insects less frequently collected. In agricultural streams, the
shredder species were replaced by noninsect groups such as Asellus,
Hyalella, and Orconectes and others tolerant of soft stream
substrates. In our study, a shift occurred in dominant taxa from
principally EPT forms to crustaceans and chironomids (Appendix F).
Indices of Community Integrity (ICI) values were generally
higher at the mainstem locations (Figure 3-5). Greatest variation
in ICI scores were obtained at the upper watershed sites. Only two
locations on the river's mainstem exceeded a recommended eastern
cornbelt biocriterion of 38 as derived by the Ohio EPA (1987) . The
two mainstem sites were at Morton and Delhi. None of the main
tributary locations met or exceeded this recommended biocriterion.
Overall, the locations with the highest ICI values were the
mainstem sites located upstream from Mankato, three main
tributaries (Le Sueur, Watonwan, Yellow Medicine Rivers) and the
County Road 13 and Camp Pope Creek sites in the upper watershed.
Factors contributing to the lower ICI scores were lower numbers of
EPT taxa and higher numbers of non-insects and dipteran insects
other than the midges.
3.5 INTERACTIVE WATERSHED COMPONENT ANALYSIS
Some strong associations (P < 0.01) were found among the
nutrient, habitat, and biotic variables (richness, EPT, and
ICI) Figure 3-6). ICI was strongly associated with surface water
ammonia nitrogen and slightly correlated with pore water ammonia.
Taxonomic richness was correlated with the other biotic metrics;
however, this would be expected because of the dominance of
mayflies, stoneflies and caddisflies in the benthic community
composition. Habitat (QHEI) scores showed less strong correlations
with the three biotic variables. No correlations were obtained
between the biotic variables and the riparian zone QHEI score. A
slight association was found between habitat scores and
3-15
-------
Mainstem Stations
% Collector* (92%)
% Scrapers (5%)
% Predator* (1%)
% Other (1%)
% Shredders (1%)
Tributary
% Collector* (76%)
% Scrapers (14%)
% Predators (8%)
% Other (1%)
% Shredder* (1%)
Figure 3-4. Macroinvertebrate functional characteristics,
3-16
-------
Upper Watershed
% Scrapers (28%)
% Collector* (44%)
% Predators (10%)
%Othar (10%)
Shredders (8%)
Figure 3-4 (Cont). Macroinvertebrate functional characteristics.
3-17
-------
48
43
as
33
28
23-
18-
13-
8
3
Mainstem Stations
CornbettBtocriterion
H
1
|
!
I
I
1
1
I
FSN JOB HEN STP JUD CTD MOR DEL UPS
48-]
43-
38
33-
28-
23-
18-
13-
8-
3
Main Tributaries
Combelt Biocriterion
I
I
I
HIS
RSH BER LSR WTW COT HWK YMR
Figure 3-5. Calculated Minnesota River ICI biocriteria,
3-18
-------
43-
38
33-
28
23
18
13
8
3
Upper Watershed
Combett Biocriterton
i
1
1
BFD BLE CR13 FRO MIT. STJ WEL CPC GAY
Figure 3-5 (Cont). Calculated Minnesota River TCI biocriteria.
3-19
-------
Richne**
"* P 0.01-0.05
*** P<0.01
EFT
***
EPT
S.05 - 0.1
.05
ilflcant
ICI
Ttrtft
***
ICI
Riparian
US
NS
NS
Riparian
QHEI
**
**
**
NS
QHEI
Drainage
Area
NS
NS
NS
NS
*
Surface Pore Surface Pore
Water Water Water Water
NH3-N NH3-N N02+NO3 N02+N03
ICI
* A *
*
NS
NS
P 0.05 -0.2
P 0.01 -0.05
*«* P<0.01
NS Not Significant
Figure 3-6. Watershed component regression results,
3-20
-------
size of the drainage area.
Analyses were also performed using the ICI values with the
ammonia and nitrite-nitrate nitrogen concentrations (Figure 3-6).
Slight to strong correlations were found with pore and surface
water ammonia nitrogen concentrations. No associations occurred
with the nitrite-nitrate values.
Regression analyses were conducted to estimate the
relationship between the mean pore water chemical values (in
Appendix B) and the observed ambient toxicity at the same
locations. Level of significance was set at: P < 0.05.
Significant positive associations were found for total ammonia
nitrogen at locations toxic to Ceriodaphnia and Selenastrum. Best
chemical toxicity associations were obtained with the Ceriodaphnia
test. Because the daphnid reproductive yield was the most
sensitive response, a comparison of yield was made against the
measured total pore water ammonia concentrations. From this
analysis (r2 = 0.63, n = 38), a 50 percent reduction in
reproductive responses was predicted for total ammonia nitrogen
concentrations of 8.8 mg/1 or higher (Arthur et al., 1994).
Ankley et al. (1990) in a Wisconsin watershed study found that
ammonia nitrogen was the chemical responsible for observed ambient
toxicity in sediment pore water. Total ammonia nitrogen
concentrations generally > 10 mg/1 were lethal to Ceriodaphnia;
total ammonia concentrations exceeding 2O mg/1 affected the growth
of Selenastrum. Although the agent(s) responsible for the observed
toxicity were not fully'characterized, ammonia nitrogen was the the
suspected toxicant in this study. Concentrations of heavy metals
in the sediment pore waters were uniformly near the limits of
detection. No measurements of nonpolar compounds were made on the
sediment pore water.
Correspondence analysis added additional information on the
interaction of nutrients and habitat quality for the three dominant
macroinvertebrate groups (Table 3-5) . In general, the Eigenvectors
were numerically similar in all four axes, indicating that no
particular axis explained the majority of the variations
encountered. Poorest correlations were encountered when all the
taxa and the midge group were analyzed. For the mayfly and
caddisfly groups, the ordinations explained approximately 70
percent of the variation encountered, and the first results found
in the first two axes accounted for approximately 50 percent of the
variation. Highest correlations were found between the surface
water nutrients and the mayfly and caddisfly groups. Best
3-21
-------
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associations were obtained with surface water ammonia and nitrite-
nitrate nitrogen. Smaller drainage areas were generally associated
with increasing nutrient concentrations. No particular
associations were evident between the sediment pore water values
and the macroinvertebrate community. For the mayfly group,
additional associations were found with surface water ammonia,
nitrite-nitrate, and QHEI. When biplots were
made (not shown), no strong associations were found between any
individual taxa, stations, or the eight environmental variables.
Although weak taxa associations were found, individual taxa that
were identified from the ordination analyses were the midge genera:
Microtendipes and Tanypus, the mayfly Stenacron and the caddisfly
genus Polycentropus. Findings from the ordination analyses
generally paralleled the regression analyses.
This study used procedures similar to an investigation
conducted in an agricultural region located in central Michigan
(Richards et al. , 1993) . As in our study, they found that the most
important factors affecting the macroinvertebrate community were
physical habitat and elevated nutrient" concentrations, particularly
ammonia. Significant associations were also found between numbers
of EPT taxa and substrate quality. These investigators concluded
that by increasing substrate and channel heterogeneity and
controlling nutrient additions, the macroinvertebrate quality could
be enhanced in these streams. Our findings in the Minnesota River
Basin appear to corroborate these findings.
3-23
-------
-------
4. SUMMARY AND CONCLUSIONS
The Federal Water Act has encouraged the definition of
conditions necessary for maintaining physical, chemical, and
biological integrity in receiving waters. This study supplies
descriptive information on several physical, chemical, and
biological components in the Minnesota River Basin. The most
important stressor affecting the basin's biological integrity was
found to be excessive inputs of nutrients (particularly ammonia
and,nitrite-nitrate nitrogen) and reaffirms the conclusions by
others as to the continual dominance and role of these stressors
in degrading the Minnesota River Basin. The dominant habitat
characteristics adversely affecting the basin were a general lack
of substrate heterogeneity and high substrate embeddedness from
fine particles. Highest habitat scores and water quality and
least impacted biological communities were found upstream from
Mankato on the river's mainstem, the Yellow Medicine tributary,
and the upper watershed site at Camp Pope Creek near Redwood
Falls.
For most sites, the calculated Index of Community Integrity
(ICI) values fell below recommended biocriteria for eastern
cornbelt areas in the United States. In many of the more
impacted locations, the functional predator and shredder
components of the community were depressed.
A good correlation was found between ammonia nitrogen and
the macroinvertebrate community. The more impacted sites had
fewer numbers of Ephemeroptera/Plecoptera/Tricoptera (EPT) taxa,
less richness, and lower ICI scores. Ammonia nitrogen appeared
to be a strong predictor of biological quality. Where ambient
pore water toxicity occurred (total ammonia nitrogen
concentrations > 8 mg/1) a degraded macroinvertebrate biological
community was also present.
Additional stream studies are needed to obtain quantitative
basin-wide response and exposure indicators (descriptors) for
defining stream integrity. Concurrent results by others in the
midwestern cornbelt regions need to be interrelated with this
study's findings to further describe the kinds and magnitude of
stressors affecting agricultural watersheds. Once done,
watershed impairment can be linked with dominant habitat
characteristics, chemical stressors and macroinvertebrate
communities and can bring the nonpoint source pollution problems
from agricultural activities into a clearer focus.
4-1
-------
-------
REFERENCES
Ankley, G.T., A. Katko, and J.W. Arthur. 1990. Identification
of ammonia as an important sediment-associated toxicant in the
lower Fox River, Green Bay, Wisconsin. Environ. Toxicol. Chem.
9: 313-322.
Arthur, J.W., J.A. Thompson, C.T. Walbridge, and H.W. Read.
1994. Ambient toxicity assessments in the Minnesota River basin.
IN: Minnesota River Assessment Project Report, Volume III.
Biological and Toxicological Assessment, Report to the
Legislative Commission on Minnesota Resources, Minnesota
Pollution Control Agency, January, Rept. No. 4, 10 pp. +
appendices.
Baker, D.B. 1988. Sediment, nutrient and pesticide transport in
selected lower great lakes tributaries. Great Lakes National
Program Office, Chicago, Illinois 60604, February, EPA-905/4-88-
001.
Camargo, J.A. 1992. Structural and trophic alterations in
macrobenthic communities downstream from a fish farm outlet.
Hydrobiologia 242:41-49.
Fandrei, G., S. Heiskary, and S. McCollar. 1988. Descriptive
characteristics of the seven ecoregions in Minnesota. Minnesota
Pollution Control Agency, Division of Water Quality, March, 140
pp.
Federal Water Pollution Control Administration. 1966. A report
on pollution of the Upper Mississippi River and major
tributaries. Chapter V. Effects of pollution on water quality.
71 p. Twin Cities-Upper Mississippi River Project, July.
Gallant, A.L., T.R. Whittier, D.P. Larson, J.M. Omernik and R.M.
Hughes. 1989. Regionalization as a tool for managing
environmental resources, Environmental Research Laboratory,
Corvallis, OR 97333, July, EPA-600/3-89/060.
Gammon, J.R., M.D. Johnson, C.E. Mays, D.A. Schiappa, W.L.
Fisher, and B.L. Pearman. 1983. Effects of agriculture on
stream fauna in central Indiana. Environmental Research
Laboratory - Corvallis, Corvallis, Oregon 97333, EPA-600/3-83-
020,
Huber, W. 1993. Ecotoxicological relevance of atrazine in
aquatic systems. Environ. Toxicol, Chem. 12:1865-1881.
R-l
-------
King, K. 1985. Longitudinal zonation in the Minnesota River.
Water Resources Research Center, WRRC Report No. 6, March,
Mankato State University.
Kirsch, N.A., S.A. Hanson, P.A. Renard, and J.W. Enblom. 1985.
Biological survey of the Minnesota River. Special Publ. 139,
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March.
Koehler, T. and P. Cooper. 1994. Minnesota River assessment
project (MNRAP) level II land use analysis. IN: Minnesota River
Assessment Project Report, Volume IV. Land Use Assessment,
Report to the Legislative Commission on Minnesota Resources,
Minnesota Pollution Control Agency, January, Rept. No. 3, 84 pp.
+ appendices.
Lenat, D.R. 1984. Agriculture and stream water quality: A
biological evaluation of erosion control practices. Environ.
Mgmt. 8:333-344.
Lewis, P.A., D.J. Klemm, and J.M. Lazorchak. 1992. Short-term
methods for estimating the chronic toxicity of effluents and
receiving waters to freshwater organisms. Environmental
Monitoring Systems Laboratory-Cincinnati, Cincinnati, OH 45268,
EPA/600/4-91/022, February.
Menzel, B.W., J.B. Barnum and L.M. Antosch. 1984.
alterations of Iowa prairie-agricultural streams.
Jour. Res. 59:5-30.
Ecological
Iowa State
Minnesota Pollution Control Agency. 1982. Minnesota River
watershed water quality. An assessment of non-point source
pollution. Division of Water Quality, September.
Marsh, P.C. and T.F. Waters. 1980. Effects of agricultural
drainage development on benthic invertebrates in undisturbed
downstream reaches. Trans. Amer. Fish. Soc. 109:213-223.
Merritt, R.W. and K.W. Cummins, Eds. 1984. An Introduction to
the Aquatic Insects of North America. Second Edition.
Kendall/Hunt Publishing Co., Dubuque, Iowa.
Ohio Environmental Protection Agency. 1987. Biological criteria
for the protection of aquatic life: Volumes II and III. User's
manual for biological field assessment of Ohio surface waters. .
Addendum, updated January, 1988. Ecological Assessment Section,
Division of Water Quality, Columbus, OH 43266-0149.
R-2
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Payne, G.A. 1994. Sources and transport of sediment, nutrients,
and oxygen-demanding substances in the Minnesota River basin,
1989-1992. IN: Minnesota River Assessment Project Report, Volume
II. Land Use Assessment, Report to the Legislative Commission on
Minnesota Resources, Minnesota Pollution Control Agency, January,
Rept. No. 1, 71 pp.
Proctor, B. Characterization of sediments, settleable solids and
water quality of stormwater runoff in the Minnesota River
watershed. IN: Minnesota River Assessment Project Report, Volume
III. Biological and Toxicological Assessment, Report to the
Legislative Commission on Minnesota Resources, Minnesota
Pollution Control Agency, January, Rept. No. 3, 134 pp. +
appendices.
Richards, C., G.E. Host, and J. Arthur. 1993. Identification of
predominant environmental factors structuring stream
macroinvertebrate communities within a large agricultural
catchment, USA. Freshwater Biology 29:285-294
ter Braak, C.J.F. 1986. Canonical correspondence analysis: a
new eigenvector technique for multivariate direct gradient
analysis. Ecology 67: 1167-1179.
Vannote, R.L., G.W. Minshall, K.W. Cummins, J.R. Sedell and C.E.
Gushing. 1980. The river continuum concept. Can. J. Fish.
Aquat. Sci. 37: 13O-137.
Weber, C.I., Ed. 1973. Biological field and laboratory methods
for measuring the quality of surface waters and effluents.
Office of Research and Development, Cincinnati, OH 45268, EPA-
670/4-73-001, July.
Zischke, J.A., G. Erickson, D. Waller and R. Bellig. 1994.
Analysis of benthic macroinvertebrate communities in the
Minnesota River watershed. IN: Minnesota River Assessment
Project Report, Volume III. Biological and Toxicological
Assessment, Report to the Legislative Commission on Minnesota
Resourcesj Minnesota Pollution Control Agency, January, Rept. No.
6, 82 pp.
R-3
-------
-------
APPENDICES
A-l
-------
Appendix A
MINNESOTA RIVER BASIN SAMPLING LOCATIONS.
Location fAbbr.
Rd. Crossing
2
County Drn Arfmi)
R. Mi.
Main Stem Locations
Fort Snelling(FSN) State Park
35 W Bridge(35W)
Jordan(JOR)
Henderson(HEN)
St. Peter(STP)
Judson(JUD)
Courtland(CTD)
Morton(MOR)
Delhi(DEL)
Upper Sioux(UPS)
Reservoirs
Rapidan
Chippewa
Lac Qui Parle
Main Tributaries
Interstate Hwy
SC
MN
MN
BE
BE
MN
RN
YM
BE
CH
LQP
Co.
19
22
Co.
Co.
19
Co.
Co.
Co.
Co.
Co.
9
42
45
21
21
9
15
20
Hennepin
Hennepin
Scott
Sibley
Le Sueur
Blue Earth
Blue Earth
Renville
Renville
Yellow Med.
16,100
16,000
15,530
15,020
11,200
10,840
8,920
7,970
7,090
Blue Earth
Chippewa
Lac Qui Parle
3
11
42
73
98
127
140
203
219
237
High Isl. Cr. (HIS)
Rush Riv. (RSH)
Blue Erth Ri. (BER)
Le Sueur Riv. (LSR)
Watonwan Riv. (WTW)
Cottonwood R. (COT)
Hawk Cr. (HWK)
Yell. Med. R. (YMR)
SI Co.
MN 93
Sibley
MN 66
US 169
Cottwd.
YM Co.
MN 67
6
Park
St.Br.
21
Sibley
Sibley
Blue Earth
Blue Earth
Blue Earth
Brown
Yellow Med.
Yellow Med.
240
400
3,450
1,110
880
1,208
470
650
Blue Tributary Upper Watersheds
Beauford (BFD)
Blue Earth (BLE)
Cty Rd 13 (CR13)
Frost (FRO)
Mountain Lk(MTL)
St. James (STJ)
Wells (WEL)
Camp Pope Cr. (CPC)
Gaylord (GAY)
MN 22
FA Co.
FA Co.
FA Co.
MN 60
WA Co.
MN 22
RD Co.
MR 22
8
13
13
104
9
Blue Earth
Faribault
Faribault
Faribault
Cottonwood
Watonwan
Faribault
Redwood
Sibley
9
8
10
12
10
18
10
3
6
Drn Ar = Drainage area in mi
.2
A-2
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Appendix D
MACROINVERTEBRATE COMMUNITY CHARACTERISTICS
Richness
Main Stem Locations
Fort Snelling (FSN)
35 W Bridge (35W)
Jordan (JOR)
Henderson (HEN)
St. Peter (STP)
Judson (JUD)
Court land (CTD)
Morton (MOR)
Delhi (DEL)
Upper Sioux (UPS)
Mainstem Av.
Main Tributaries
High Island Cr. (HIS)
Rush Riv. (RSH)
Blue Earth Ri. (BER)
Le Sueur Riv. (LSR)
Watonwan Riv. (WTW)
Cottonwood R. (COT)
Redwood Riv. (RWR)
Hawk Cr. (HWK)
Yell. Med. R. fYMR)
Tributary Av.
Upper Watersheds
Beauford (BFD)
Blue Earth (BLE)
County Rd 13 (CR13)
Frost (FRO)
Mountain Lk (MTL)
St. James (STJ)
Wells (WEL)
Camp Pope Cr. (CPC)
Gavlord (GAY)
8
—
±7
11
19
21
21
21
19
19
17
15
15
16
25
24
20
18
21
14
19
9
18
15
12
17
13
11
16
13
Average Index Values
Diversity Ecruitabilitv ICI
0.5
-
1.1
1.5
2.0
2.7
2.7
2.3
2.7
2.0
1.9
2.9
2.8
2.8
3.2
3.6
2.6
2.9
3.0
2.6
2.9
2.5
2.1
2.4
1.8
2.4
2.0
2.8
3.4
3.0
0.3
'-
0.2
0.3
0.3
0.4
0.4
0.4
0.5
0.3
0.3
0.7
0.7
0.6
0.5
0.8
0.5
0.6
0.5
0.6
0.6
0.9
0.3
0.5
0.4
0.4
0.5
0.9
0.9
0.9
8
-
24
15
30
36
36
39
38
25
28
19
18
24
36
26
26
25
25
29
25
28
27
35
10
14
29
15
36
24
Upper Watershed Av.
14
2.5
0.6
24
A-6
-------
Appendix E
CHECKLIST OP MACRO INVERTEBRATE TAXA COLLECTED.
PLATYHELMINTHES
Dugesia
OLIGOCHAETA
HIRUDINEA
Erpobdella
Glossiphonia
Helobdella
Placobdella
Theromyzon
GASTROPODA
Ferris ia
Fossaria
Gyraulus
.Helisoma
Lymnea
Physella
Stagnicola
PLECYPODA
Sphaeriidae
HYDRACARINA
AMPHIPODA
Gammaus
Hyalella
ISOPODA
Asellus
DECAPODA
INSECTA
COLLEMBOLA
Isotomurus
Podura
ODONATA
Anax
Argia
Calopteryx
Dromogomphus
Enallagma
Gomphurus
Hetaerina
Nehalennia
Stylurus
PLECOPTERA
Acroneuria
Isoperla
Paracapnia
Paragnetina
Perlesta
Mnstem/
Trib.
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
Upper
Mnstem/ Upper
Wtrshd .
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
PLECOPTERA (cont) .
Perlinella
Pteronarcys
HEMIPTERA
Belastoma
Rhagoylea
Salda
Trichocoria
COLEOPTERA
Agabus
Ancyronyx
Berosus
Curculonidae
Dineutus
Dubiraphia
Gyrinidae
Hal ipus
Helichus
Hydrochus
Liodessus
Macronuchus
Optioservus
Stenelmis
EPHEMEROPTERA
Ameletus
Baetis
Brachycercus
Caenis
Callibaetis
Centropt ilum
Ephoron
Heptagenia
Heterocloen
Hexagenia
Isonychia
Leptophlebia
Paraleptophlebia
Parameletus
Potomanthus
Pseudocleon
Stenacron
Stenonema
Tr icory thodes
TRICHOPTERA
Agraylea
Cheumatopsyche
Chimarra
Cyrnellus
Trib. Wtrshd.
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
A-7
-------
Appendix E (cont.)
CHECKLIST OF MACROINVERTEBRATE TAXA.
Mnstem/ Upper Mnstem/
Tr ib. Wtrshd. Trib.
Upper
Wtrshd.
TRICHOPTERA (cont).
Dolophilodes x
Hydropsyche x
Hydroptila x
Mayatrichia x
Nectopsyche
Nyctiophylax
Potamyia x
Polycentropus x
MEGALOPTERA
Corydalus x
Sialis
DIPTERA
Atherix x
Culiseta
Empididae x
Hemerodromia
Hexatoma x
Palpomyia
Prionocera
Sintulium x
Tabanus
Tipula x
. CHIRONOMIDAE
Ablabesmyia x
x Brillia
x Chironomus x
x Conchapelopia x
x Cricotopus x
x Cryptochironomus
Dicrotendipes x
Endochironomus
Goeldichironomus x
Glyptotendipes x
x Hydrobaenus
Kiefferulus x
x Microtendipes x
x Natarsia
Nilotanypus
x Orthocladius x
Parachironomus x
x Parametriocnemus
x Paralauterborniella x
x Paratanytarsus
x Paratendipes
x Pentaneura x
Polypedilum x
Procladius x
Psectrocladius x
Pseudochironomus x
Rheocricotopus
Rheotanytarsus x
Smittia x
Stenochironomus
Stictochironomus x
Tanypus x
Tanytarsus x
Thienemanniella
Thiennemannimyia
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
Total Taxa Encountered
= 135
Total Mainstem/Tributary Taxa =. 81
Total Upper Watershed Taxa = 92
A-8
-------
Appendix F
DOMINANT MACROINVERTEBRATES COLLECTED FROM HESTER DENDY SUBSTRATES.
Mainstern Tributary Upper Watershed
1989 1990 1989 1990 1991 1992
PLATYHELMINTHES - Dugesia
x ~
OLIGOGHAETA
HIRUDINEA
Erpodella
Placobdella
GASTROPODA - Physella
AMPHIPODA - Hyalella
ISOPODA - Asellus
PLECOPTERA - Perlesta
COLEOPTERA - Stenelmis
ODONATA
EPHEMEROPTERA
Baetis
Caenis
Heptagenia
Paraleptophlebia
Potomanthus
Stenacron
Stenonema
Tricorythodes
TRICHOPTERA
Cheumatop syche
Cyrnellus
Hydropsyche
Hydroptila
Potamyia
Polycentropus
DIPTERA
Chironomidae
Ablabesmyia
Chironomus
Cricotopus
Cryptochironomus
Dicrotendipes
Glyptotendipes
Hydrobaenus
Orthocladius
Parametriocnemus
Paratanytarsus
Polypedilum
Rheotanytarsus
Tanytarsus
Thienemannimyia
Other
Culiseta
Hemerodromia
Simulium
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
Total Dominant Taxa
10
12
14
15
22
Common Taxa (> 1% occurrence); Common Taxon (> 5% occurrence)
A-9
-------
Appendix G
DOMINANT MACROINVERTEBRATES COLLECTED FROM QUALITATIVE SAMPLES.
Mainstern Tributary
___ 1989 1990
1989
1990
PLATYHELMINTHES - Dugesia
OLIGOCHAETA
GASTROPODA - Physella
AMPHIPODA - Hyalella
HEMIPTERA - Cymatia
COLEOPTERA - Stenelmis
ODONATA - Argia
EPHEMEROPTERA
Baetis
Caenis
Isonychia
Potomanthus
Stenacron
Stenonema
Tricorythodes
TRICHOPTERA
Cheumatop syche
Chimarra
Hydropsyche
Potamyia
DIPTERA
Chironomidae
Chironomus
Glyptotendipes
Polypedilum
Tanytarsus
Other
Atherix
Simulium
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
Total Dominant Taxa
19
14
14
13
8 Common Taxa (> 1% occurrence); Common Taxon (> 5% occurrence)
Note: No qualitative surveys performed at the upper watershed
locations.
A-10
-------
Appendix H
CERIODAPHNIA AND SELENASTRUM TOXICITY RESULTS.
A. Ceriodaphnia dubia Acute
Bioassay
Fort Snelling (FSN)
Jordan (JOR)
Henderson (HEN)
St. Peter (STP)
Judson (JUD)
Courtland (CTD)
Morton (MOR)
Delhi (DEL)
Upper Sioux (UPS)
Rapidan Reservoir
Chippewa Reservoir
Lac Qui Parle Reservoir
High Isl. Cr. (HIS)
Rush Riv. (RSH)
Le Sueur Riv. (LSR)
Watonwan Riv. (WTW)
Cottonwood Riv. (COT)
Hawk Cr. (HWK)
Yell. Med. R. (YMR)
Test Results - 48 hour duration
Surface Water Samples
Sample Sample Bioassay
Date
Cone. Survival
Yield
890815
890815
890815
890815
890816
890816
890817
890817
890817
890814
890817
890817
890815
890814
890814
890815
890816
890817
890817
100
100
100
100
100
100
100
100
100
100
100
100
100
100
100
100
100
100
100
100
100
100
100
100
100
100
100
100
100
100
100
100
100
100
100
100
100
100
B. Ceriodaphnia dubia Chronic Test Results - 7-day duration
Sediment Pore Water
Fort Snelling (FSN)
35 W Bridge (35W)
Jordan (JOR)
Henderson (HEN)
St. Peter (STP)
Judson (JUD)
Courtland (CTD)
Morton (MOR)
Delhi (DEL)
Upper Sioux (UPS)
Rapidan Reservoir
Chippewa Reservoir
Lac Qui Parle Reservoir
Lac Qui Parle Reservoir
Lac Qui Parle Reservoir
High Isl. Cr. (HIS)
Blue Earth Riv. (BER)
Le Sueur Riv. (LSR)
Watonwan Riv. (WTW)
Sample
Date
891023
891023
891023
891024
.891024
891025
891026
891025
891027
891027
891024
891025
891025
891025
891025
891023
891024
891024
891024 .
Sample
Cone.
100
100
100
100
100
100
100
100
100
100
100
100
100
50
25
100
100
100
100
Bioassay
Survival
80
100
100
100
100
100
100
100
100
100 ,
100
100
0
100
100
100
100
100
100
Bioassay
Yield a
4
12
23
22
22
24
25
23
19
22
•19
22
< 1
20
24
24
23
20
22
A-11
-------
Appendix H (cont.)
B. Ceriodaphnia dubia Chronic Test Results - 7-day duration.
Cottonwood Riv. (COT)
Hawk Cr. (HWK)
Yell. Med. R. (YMR)
Fort Snelling (FSN)
Jordan (JOR)
St. Peter (STP)
Courtland (CTD)
Morton (MOR)
Rapidan Reservoir
Rapidan Reservoir
Lac Qui Parle Reservoir
Lac Qui Parle Reservoir
Lac Qui Parle Reservoir
Blue Earth Riv. (BER)
Cottonwood Riv. (COT)
Fort Snelling (FSN)
Fort Snelling (FSN)
Fort Snelling (FSN)
35 W Bridge (35W)
35 W Bridge (35W)
35 W Bridge (35W)
Jordan (JOR)
St. Peter (STP)
St. Peter (STP)
Courtland (CTD)
Courtland (CTD)
Rapidan Reservoir
Rapidan Reservoir
Rapidan Reservoir
Chippewa Reservoir
Chippewa Reservoir
Chippewa Reservoir
Lac Qui Parle Reservoir
Lac Qui Parle Reservoir
Lac Qui Parle Reservoir
Rush Riv. (RSH)
Rush Riv. (RSH)
Blue Earth Riv. (BER)
Blue Earth Riv. (BER)
Le Sueur Riv. (LSR)
Le Sueur Riv. (LSR)
Watonwan Riv. (WTW)
Watonwan Riv. (WTW)
891026
891027
891027
Sample
Date
900122
900123
900123
900124
900124
900124
900124
900124
900124
900124
900123
900124
Sample
Date
900625
900625
900625
900625
900625
900625
900625
900625
900625
900627
900627
900626
900626
900626
900626
900626
900626
900626
900626
900626
900625
900625
900627
•900627
900627
900627
900627
900627
100
100
100
Sample
Cone.
100
100
100
100
100
100
50
100
50
25
100
100
Sample
Cone.
100
50
100
100
50
25
100
100
50
100
50
100
50
25
100
50
25
100
100
100
100
50
100
50
100
50
100
50
100
100
100
Bioassay
Survival
100
100
100
100
100
90
100
0
100
100
100
100
Bioassay
Survival
0
0
100
90
90
90
100
100
100
100
100
80
100
90
100
100
90
0
100
100
100
90
100
100
100
100
100
100
19
20
18
Bioassay
Yield
19
20
21
18
24
18
21
0
5
19
23
18
Bioassay
Yield
0
0
15
6
6
10
23
17
20
18
18
12
16
15
7
21
25
o •
12
17
22
25
22
25
21
28
26
26
A-12
-------
Appendix H (cont.)
B. Ceriodaphnia dubia Chronic Test Results - 7-day duration.
Cottonwood Riv. (COT)
Cottonwood Riv. (COT)
Yell. Med. R. (YMR)
Fort Snelling (FSN)
Fort Snelling (FSN)
Fort Snelling (FSN)
35 W Bridge (35W)
35 W Bridge (35W)
35 W Bridge (35W)
Jordan (JOR)
Jordan (JOR)
Henderson (HEN)
Henderson (HEN)
St. Peter (STP)
St. Peter (STP)
Judson (JUD)
Courtland (CTD)
Delhi (DEL)
Rapidan Reservoir
Rapidan Reservoir
High Isl. Cr. (HIS)
Blue Earth Riv. (BER)
Le Sueur Riv. (LSR)
Watonwan Riv. (WTW)
Yell. Med. R. (YMR)
Fort Snelling (FSN)
Fort Snelling (FSN)
35 W Bridge (35W)
35 W Bridge (35W)
Jordan (JOR)
Henderson (HEN)
Judson (JUD)
Delhi (DEL)
Rapidan Reservoir
Rapidan Reservoir
Rapidan Reservoir
High Isl. Cr. (HIS)
Yell..Med. R. (YMR)
Wells (WEL)
900627
900627
900627
Sample
Date
900924
900924
900924
900924
900924
900924
900924
900924
900921
900921
900921
900921
900925
900926
900927
900925
900925
900921
900925
900925
900920
900927
Sample
Date
920518
920518
920518
920518
920518
920518
920519
920519
920519
920519
920519
920518
920519
Sample
Date
920722
100
50
100
Sample
Cone .
100
50
25
100
50
25 .
100
50
100
50
100
50 .
100
100
100
100
50
100
100
100
100
100
Sample
Cone.
100
50
100
50
100
100
100
100
100
50
25
100
100
Sample
Cone .
100
90
100
100
Bioassay
Survival
100
100
100
100
100
100
100
100
100
50
100
100
80
100
100
80
100
90
100
90
100
100
Bioassay
Survival
100
100
100
100
100
100
100
100
90
100
100
100
100
Bioassay
Survival
100
22
22
20
Bioassay
Yield
17
29
28
12
17
26
24
24
25
24
13
22
17
16
14
3
9
17
30
22
26
17
Bioassay
Yield
30
31
29
32
31
29
24
28
19
28
30
28
26
Bioassay
Yield
27
A-13
-------
Appendix H (cont.)
B. Ceriodaphnia dubia Chronic Test Results
Wells (WEL)
Camp Pope Cr. (CPC)
Gaylord (GAY)
Gaylord (GAY)
920722
920722
920721
920721
50
100
100
50
- 7-day duration.
100 29
• 100 34
100 31
100 30
C. Selenastrum capricornutum Chronic Test Results - 4-day duration
Sediment Pore Water
Sample Sample Bioassay Bioassay
Henderson (HEN)
St. Peter (STP)
Courtland (CTD)
Morton (MOR)
Rapidan Reservoir
Lac Qui Parle Reservoir
Fort Snelling (FSN)
Henderson (HEN)
St. Peter (STP)
Courtland (CTD)
Morton (MOR)
Rapidan Reservoir
Lac Qui Parle Reservoir
Fort Snelling (FSN)
Jordan (JOR)
St. Peter (STP)
Courtland (CTD)
Rapidan Reservoir
Lac Qui Parle Reservoir
Blue Earth Riv. (BER)
Le Sueur Riv. (LSR)
Watonwan Riv. (WTW)
Cottonwood Riv. (COT)
Yell. Med. R. (YMR)
Date
Cone.
Survival
Yield
890814
890814
890814
890814
890814
890814
100
100
100
100
100
100
29
93
100
100
15
7
Sample
Date
891023
891023
891023
891023
891023
891023
891023
Sample
Cone.
100
100
100
100
100
100
100
Bioassay
Survival
—
-
-
- • •
-
-
-
Bioassay
Yield
22
30
12
,55
- 45
24,
19
Sample Sample Bioassay Bioassay
Date Cone. Survival Yield.
900625
900625
900625
900625
900625
900625
900625
900625
900625
900625
900625
100
100
100
100
100
100
100
100
100
100
100
30
100
74
100
32
5
100
100
100
100
100
Ceriodaphnia Yield - Average number of young produced in test
concentration.
gelenastrum Yield - Percentage cell number yield against control
response.
A-14
•jSrU.S. GOVERNMENT PRINTING OFFICE: l*»4 - 5SO-OOI/00193
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