EPA-905/9-74-013
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CHEAT UKB MIUmVE OON1MCT PROGRAM
DECEMBER 1974
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Copies of this document are available
to the public through the
National Technical Information Service
Springfield, Virginia 22151
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WATER POLLUTION INVESTIGATION: DETROIT AND ST. CLAIR RIVERS
by
ENVIRONMENTAL CONTROL TECHNOLOGY CORPORATION
Ann Arbor, Michigan
In fulfillment of
EPA Contract No. 68-01-1570
for the
U.S. ENVIRONMENTAL PROTECTION AGENCY
Region V
Great Lakes Initiative Contract Program
Report Number: EPA-905/9-74-013
EPA Project Officer: Howard Zar
December 1974
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This report has been developed under auspices of the Great
Lakes Initiative Contract Program. The purpose of the
Program is to obtain additional data regarding the present
nature and trends in water quality, aquatic life, and waste
loadings in areas of the Great Lakes with the worst water
pollution problems. The data thus obtained is being used
to assist in the development of waste discharge permits
under provisions of the Federal Water Pollution Control
Act Amendments of 1972 and in meeting commitments under
the Great Lakes Water Quality Agreement between the U.S.
and Canada for accelerated effort to abate and control
water pollution in the Great Lakes.
This report has been reviewed by the Enforcement Division,
Region V, Environmental Protection Agency and approved
for publication. Approval does not signify that the
contents necessarily reflect the views of the Environmental
Protection Agency, nor does mention of trade names or
commercial products constitute endorsement or recommenda-
tion for use.
m
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ABSTRACT
This report presents the results of a historical review and water quality survey of the
St. Clair and Detroit Rivers. It includes a three-dimensional, steady-state model for the
Detroit River, which will allow for the projection of future water quality based on the
results of various management schemes for the Detroit Area.
The historical survey illustrates a gradual upgrading of water quality in the region over
the past decade, as a result of pollution abatement programs. The water quality surveys
performed have provided heretofore lacking or dated information with regards to the
biological communities and sediment chemistry.
This report was submitted in fulfillment of Contract Number 68-01-1570, by the
Environmental Control Technology Corporation, under the sponsorship of the
Environmental Protection Agency. Work was completed as of August, 1974.
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TABLE OF CONTENTS
Page
Section I Conclusions 1
Section II Recommendations 3
Section III Introduction 6
Section IV Historical Background 10
Section V Water Quality Survey 58
Section VI Mathematical Model for
Detroit River 184
Section VII Water Quality Projections 239
Section VIII References 244
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FIGURES
No. Page
1 Water Quality Survey Area °
2 Trends in Chloride Concentration, St. Clair River - SR 26.7 27
3 Trends in Chloride Concentration, St. Clair River - SR 17.5 28
4 Trends in Chloride Concentration, St. Clair River - SR 13.7 29
5 Trends in Chloride Concentration, St. Clair River - SR 10.0N & 10.0S 31
6 Trends in Chloride Concentration, Detroit River - DT 20.6 36
7 Trends in Chloride Concentration, Detroit River DT 14.6 37
8 Trends in Chloride Concentration, Detroit River-DT12.0W 38
9 Trends in Chloride Concentration, Detroit River - DT - 8.7W 39
10 Trends in Chloride Concentration, Detroit River - DT 3.9 40
11 Trends in Phenol Concentration, Detroit River DT 8.7W 41
12 Trends in Total Coliform Concentrations, Detroit River DT30.8W 42
13 Trends in Total Coliform Concentrations, Detroit River DT 20.6 43
14 Trends in Total Coliform Concentrations, Detroit River DT 14.6 44
15 Trends in Total Coliform Concentrations, Detroit River DT 12.0W 45
16 Trends in Total Coliform Concentrations, Detroit River DT 9.3E 46
17 Trends in Total Coliform Concentrations, Detroit River DT 8.7W 47
18 Trends in Total Coliform Concentrations, Detroit River DT 3.9 48
19 Sampling Station Locations 61-63
20 Mean Biochemical Oxygen Demand 71-73
21 Mean Chemical Oxygen Demand 74-76
22 Mean Cadmium Concentration 78-80
23 Mean Chromium Concentration 81-83
24 Mean Copper Concentration 84-86
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FIGURES
No. Page
25 Mean Lead Concentration 88-90
26 Mean Mercury Concentration 91-93
27 Mean Nickel Concentration 94-96
28 Mean Zinc Concentration 98-100
29 Mean Manganese Concentration 101-103
30 Mean Iron Concentration 104-106
31 Mean Kjeldahl Nitrogen Concentration 109-111
32 Mean Nitrate Nitrogen Concentration 113-115
33 Mean Total Phosphorus Concentration 116-118
34 Benthos Sampling Stations 1973-1974 132-134
35 Dominant Taxa - Detroit and St. Clair Rivers 140-142
36 Benthos St. Clair/Detroit Rivers 145-147
37 Shannon-Weaver Diversity - November 1973 Benthos 149
38 Shannon-Weaver Diversity - May 1974 150
39 Detroit River Mean Chlorophyll ^Concentration 156
40 Mean Chlorophyll jj Concentrations - November 1973 157
41 Mean Chlorophyll_a Concentrations - May 1974 158
42 Phytoplankton Species Richness (S-1/lnN) - August 1973 166
43 Phytoplankton Species Richness (S-1/lnN) - November 1973 157
44 Phytoplankton Species Richness (S-1/lnN) - May 1974 153
45 Phytoplankton Species Diversity (31 - August 1973 159
46 Phytoplankton Species Diversity (3) - November 1973 IJQ
47 Phytoplankton Species Diversity (cD - May 1974 ~L1~L
48 Percent Tolerant versus Intolerant Taxa Detroit River 178-179
49 Uniform Rectangular Volume ^gy
50 Model Segmentation - Upper Detroit River 189
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FIGURES
No. Page
51 Model Segmentation - Lower Detroit River 190
52 Average Chloride Concentration - Detroit River DT 17.4W - 1968 194
53 Model Verification-chloride, Detroit River DT 14.6 and 12.0-1968 ' 196
54 Model Verification-Chloride, Detroit River DT3.7W and 2.9-1968 197
55 Model Verification - Chloride, Detroit River DT 20.6 and 17.4W - 1969 198
56 Model Verification - Chloride, Detroit River DT 14.6W and 12.0W - 1969 199
57 Model Verification-Chloride, Detroit River DT3.7W and 3.9-1969 200
58 Model Verification - Chloride, Detroit River DT 20.6 and 19.0 - 1972 202
59 Model Verification - chloride, Detroit River DT 14.6W and 12.0W - 1972 203
60 Model Verification-Chloride, Detroit River DT8.7W and 3.9-1972 204
61 Model Verification - Phenol, Detroit River DT 17.4W and 14.6W - 1968 206
62 Model Verification - Phenol, Detroit River DT 12.0W and 8.7W - 1968 207
63 Model Verification - Phenol, Detroit River DT 3.9 - 1968 208
64 Model Verification - Phenol, Detroit River DT 17.4W and 14.6W - 1969 209
65 Model Verification - Phenol, Detroit River DT 12.0W and 8.7W - 1969 210
66 Model Verification - Phenol, Detroit River DT 19.0 and 14.6W - 1972 211
67 Model Verification - Phenol, Detroit River DT 12.0W and 8.7W - 1972 212
68 Model Verification - Total Iron, Detroit River DT 17.4W and 14.6W - 1968216
69 Model Verification - Total Iron, Detroit River DT 12.0W and 8.7W - 1968 217
70 Model Verification - Total Iron, Detroit River DT 3.9- 1968 218
71 Model Verification - Total Iron, Detroit River DT 17.4W and 14.6W - 1969219
72 Model Verification - Total Iron, Detroit River DT 12.0W and 8.7W - 1969 220
73 Model Verification - Total Iron, Detroit River DT 3.9 - 1969 221
74 Model Verification - Ammonia Nitrogen, Detroit River DT 19.0 and 14.6W222
1972
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FIGURES
No. Page
75 Model Verification - Ammonia Nitrogen, Detroit River DT 12.0W 223
and8.7W- 1972
76 Model Verification - Ammonia Nitrogen, Detroit River DT 3.9 - 1972 224
77 Model Verification - Ammonia Nitrogen, Detroit River DT 19.0 and
14.6W-1972 225
78 Model Verification - Ammonia Nitrogen, Detroit River DT 12.0W and 8.7W
and 8.7W-1972 226
79 Model Verification - Ammonia Nitrogen, Detroit River DT 3.9-1972 227
80 Model Verification - Total Phosphorus, Detroit River DT 19.0 and 229
14.6W- 1971
81 Model Verification - Total Phsophorus, Detroit River DT 12.0W and
8.7W-1971 230
82 Model Verification - Total Phosphorus, Detroit River DT 3.9 - 1971 231
83 Model Verification - Total Phosphorus, Detroit River DT 19.0 and
14.6W-1972 232
84 Model Verification - Total Phosphorus, Detroit River DT 19.0 and
14.6W-1973 233
85 Model Verification - Total Phosphorus, Detroit River DT 12.0W and
8.7W-1972 234
86 Model Verification - Total Phosphorus, Detroit River DT 12.0W and
8.7W-1973 235
87 Model Verification - Total Phosphorus, Detroit River DT 3.9 - 1972 236
88 Model Verification - Total Phosphorus, Detroit River DT 3.9 - 1973 237
Xll
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TABLES
No. Page
1 IJC Survey (1946-1948) - Stations 15
2 IJC Survey (1946-1948)- Analyses 15
3 Summary of Daily Average Waste Loads in Detroit River - United
States Side (1963-1964) 2 °
4 Current Monitoring Transects 22
5 Water Quality Standards for the St. Clair and Detroit Rivers 25
6 Allowable Heavy Metal Concentrations 25
7 Statistical Evaluation of Means - St. Clair River 1968 versus 1973 33
8 Average Phenol Concentration - Detroit River (1962-1973) 4-9
9 Average Ammonia Nitrogen Concentration - Detroit River (1962-1973)51
10 Average Nitrate Nitrogen Concentrations - Detroit River (1964-1973) 52
11 Average Total Phosphorus Concentrations- Detroit River (1968-1972) 53
12 Average Total Iron Concentrations - Detroit River (1967-1973) 55
13 Average Dissolved Solids Concentrations- Detroit River (1971-1973) 56
14 Statistical Evaluation of Means - Detroit River 1968 versus 1973 57
15 Station Locations 59-60
16 Sediment Correlation Matrix 128
17 Menhenick Formula Calculations - St. Clair River Benthos 143
18 Detroit River; Selected Stations Compared by Biomass and
Shannon-Weaver Diversity 152
19 November Similarity Matrix, Benthos, Detroit River 153
20 May Similarity Matrix, Benthos, Detroit River 153
21 Detroit River Phytopigments 155
22 Mean Chlorophyll^at Four Study Areas 155
23 Ratios of Chlorophylls£/a and b/a - St. Clair and Detroit Rivers 160
xi 11
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TABLES
No. Page
24 Values of Chlorophyll Ratios b/a and c/a 159
25 Mean Number of Phytoplankton 161
26 Dominant Groups of Phytoplankton 162-163
27 Phytoplankton Similarity - St. Clair River 174
28 Phytoplankton Similarity - Detroit River, August 1973 175
29 Phytoplankton Similarity - Detroit River, November 1973 175
30 Phytoplankton Similarity - Detroit River, May 1974 176
31 Negative Loads for Model - Phenol and Iron - Detroit River 214
Xiv
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ACKNOWLEDGEMENTS
The assistance of Mr. Joe Bodrie, owner and captain of the charter vessel "Clipper", in
the performance of the three surveys is acknowledged with sincere thanks.
The support and assistance of personnel from the U. S. Environmental Protection Agency,
the State of Michigan, and the Province of Ontario was appreciated.
This report was prepared by a team composed of J. E. Schenk, D. A. Scherger, J. J.
Goldasich, R. L. Weitzel, P. B. Simon, and D. E. Jerger, all of Environmental Control
Technology Corporation, with typing and final preparation for publication accomplished
by S. Conant. The assistance of Dr. Raymond P. Canale of the University of Michigan
in the mathematical modeling effort is also gratefully acknowledged.
xv
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SECTION I
CONCLUSIONS
The connecting waters of the Great Lakes in the Detroit area are significantly affected
by surrounding land uses and pollutional inputs. This fact has been observed since the
earliest investigations of these waters, although the most recent data indicates a degree
of recovery of water quality over the past decade.
Only minor changes in the chemical quality of the waters of the St. Clair River were
observed between milepoints SR 39.0 and SR 13.7. Localized problems exist with respect
to certain parameters below wastewater outfalls. A degree of enrichment in nutrients
and metals was observed in the downstream sediments of this river, although the degree
of enrichment was minor.
The biological communities in the St. Clair River are, in general, characteristic of unpolluted
waters. Dredging operations obviously affect the benthic community, otherwise this
population is characterized by clean water forms adapted to rapid current and hard
substrates, "^he phytoplankton population is dominated by the diatoms, and does not
vary significantly throughout the river.
The chemical characteristics of the Detroit River change substantially between the
headwaters at Lake St. Clair and the mouth at Lake Erie. Most parameters experience
increased concentrations, particularly below the influences exerted by the Rouge River
and the Detroit Wastewater Treatment Plant. Similarly, enrichment of the sediments exists
with respect to most parameters in this downriver area.
Established water quality standards and/or goals are presently being met, with the
occassional exception of phenol and mercury in the St. Clair River, and generally with
respect to total coliforms, phenol and mercury in the Detroit River. Water quality
projections using the developed mathematical model for the Detroit River and present
effluent limitations indicate that the goal of 2 pg/i average phenol concentration will
be met by 1977.
The biological communities are similarly altered in the downstream region. The upstream
area is characterized by the presence of clean-water or intermediate benthic forms, while
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the region between DT 18.0 and DT 12.0W is populated by pollution tolerant organisms.
A limited recovery of the benthic fauna exists from DT 9.3 downstream to Lake Erie.
The phytoplankton community shows considerable variation with time and distance,
although there is a slight increase in number of individuals in the downstream region.
The mathematical model developed for the Detroit River was verified using several different
water quality parameters. The model is verified only for the U. S. side of the river at
the present time as Canadian loading information was not available at the time of writing
this report. The model can be used to help evaluate the expected results of alternative
management plans for the river system.
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SECTION II
RECOMMENDATIONS
This program was designed to assess the present water quality of the connecting waters
of the Great Lakes in the Detroit area, and to obtain the information necessary to fill
existing data gaps and to allow for projections of future water quality. Due to necessary
limitations in the scope of this project, many of the factors initiated to accomplish the
program objectives should be continued to provide a more long-term data base and the
means to make more accurate projections of water quality. The tools developed during
the performance of this project should facilitate the accomplishment of these objectives.
The comprehensive monitoring programs presently being carried out by the state and
provincial agencies should suffice in documenting any changes in water quality. A primary
objective in this regard, however, should be to refine the data storage and retrieval systems
so that all data collected on the subject water can be evaluated. Continued monitoring
of the sediment phase should be undertaken to assess more fully the importance of this
phase as a source and/or sink for pollutants in the aqueous phase.
Additional work is required in the development of analytical techniques to allow for
broadening the scope of the monitoring program. Two notable areas of needed study
are the sediment exchange phenomenon and the determination of pesticides in the sediment
material. Techniques developed with regard to these two areas will allow for more accurate
determinations of future water quality by means of the developed model.
The biological monitoring initiated as a portion of this project should be continued on
a more routine basis, as well as being broadened in scope. A broader scope of benthic
macroinvertebrate samples should be undertaken in order to define the response of
individual communities to specific pollutional inputs. Samples should be analyzed
taxonomically and similarity and diversity calculations performed on the obtained data.
The microhabitat requirements for each group of organisms should also be recorded so
that a total ecological picture of the benthos communities in all areas samples can be
obtained.
Although the analysis of phytoplankton as performed in this study can serve to indicate
general trends of distribution, it fails to indicate the potential of these waters for the
ultimate development of nuisance algae. It is recommended that algal assay studies be
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undertaken to determine the relative level of significant nutrient enrichment at various
locations throughout the system. It is also recommended that more extensive evaluation
of photo-pigment concentrations be performed on a continuing basis, which would allow
for an evaluation of any shift in phytoplankton species dominants.
Two areas of recommended study which were not within the scope of this project are
biomagnification of pollutants and study of other segments of the microbiological
communities. Biomagnification potential should be determined by analyzing the body
tissues of various biological communities for the presence of heavy metals and pesticides.
Those communities deserving of study include the fish and benthos. Because bacteria
and fungi are the primary agents in the turnover of metabolizable materials and in the
concentration and precipitation of certain minerals, the examination of microbial
production and decomposition at various stations should be initiated.
The mathematical model developed for the Detroit River should be continually updated
to reflect any alterations which may occur in the river system. This can be accomplished
by reverifying the model using new loading information and water quality data as it
becomes available. The model should also be verified for the Canadian side of the river
once the necessary loading information is obtained. Additional sampling and evaluation
of the river between DT 19.0 and DT I4.6W should be undertaken to more fully understand
the drop in phenol and iron concentrations which occur. This may allow for the
development of a mathematical representation of this "sink" for incorporation into the
model.
Investigation and further verification of phosphorus concentrations, especially below the
Detroit Waste Treatment Plant, should be undertaken to aid in explaining the difference
between measured and projected concentrations. This is especially important if the model
is to be interfaced with the Hydroscience Model developed for Lake Erie.
Throughout the modeling program the most critical areas of the river appeared to be
between DT 19.0 and DT 14.6W, and along the U. S. and Canadian shoreline to DT
3.9. Additional studies in these areas should include information on heavy metals and
other water quality parameters which may be incorporated into the modeling program.
In this way, the full predictive capabilities of the model can be developed and made
available to those agencies responsible for water quality management in this region.
Finally, it would be desirable to continue the mathematical modeling initiated during this
project. An obvious extention of this work would be the development of a model for
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the St. Clair River similar to the one developed for the Detroit River. The second
recommended modeling effort is the development of a dynamic model for Lake St. Clair.
The third potential area for continued work in this regard would be the development
of non-steady state models for the two river systems, or portions thereof.. This total
effort, when coupled with an expanded, on-going monitoring program, will provide
essentially all of the necessary tools for effective water quality management planning in
the area.
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SECTION III
INTRODUCTION
GENERAL
The water quality of the Great Lakes system has evolved as one of the most critical
issues of the environmental movement, particularly during the past decade. Serving as
the primary water resource of the highly industrialized and urbanized area of the upper
midwestern United States and most populous region of Canada, it is logical that extensive
efforts towards the protection and enhancement of the quality of these waters be made.
As a result of several international agreements, most noticeably the U. S. Federal Water
Pollution Control Act (FWPCA) Amendments of 1972 and the U. S.-Canada Water Quality
Agreement of 1972, which have been promulgated, the Great Lakes area has been
experiencing, and will continue to experience, an infusion of pollution control measures,
as well as studies into the existing quality of these waters and additional measures which
can be taken to protect this vital natural resource for future generations.
The most critical of the Great Lakes from a water quality aspect is undoubtedly Lake
Erie. This critical nature evolves from the fact that this water body is most susceptible
to manifestations of water pollution of all the Great Lakes, due primarily to its physical
characteristics, as well as the fact that it serves as the primary water resource for the
densely populated Detroit-Toledo-Cleveland-Buffalo area of the United States, and the
developing area of southern Ontario.
The greatest affect on the overall water quality of Lake Erie has been determined to
be the Detroit area, served by the connecting waters of the St. Clair River, Lake St.
Clair, and the Detroit River. Approximately 93 percent of the total inflow to Lake Erie
emanates from the Detroit River, consequently the following reported investigation on
the existing and projected quality of these waters will serve to indicate to a considerable
degree the corresponding conditions which can be anticipated in Lake Erie.
LOCATION
The water bodies of concern in this investigation serve as the connecting waters from
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Lake Huron to Lake Erie. A map of this area is presented in Figure 1. Water from
Lake Huron enters the St. Clair River in the Port Huron-Sarnia area, and travels for
approximately 64 km (39 miles) before entering Lake St. Clair. With the exception of
the Port Huron-Sarnia area at the river's headwaters, the shoreline is much less developed
than the downstream Detroit River, and subsequently this body of water experiences less
pollutional inputs and consequently less serious water quality degradation than the waters
further downstream.
Lake St. Clair is a relatively small body of water in the Great Lakes chain, with a surface
area of 1,110 square km (430 square miles) and natural volume of 3.4 cubic km (4,500
million cubic yards). Several small tributaries enter into the lake, however 98 percent
of the total water input is derived from the St. Clair River. The area around the lake
is not highly developed, with the exception of the southern portions of the western shore
where the northeastern suburbs of Detroit are located. Water quality affects from these
suburbs are minimal however, since the wastewater from this area is transported to the
Detroit facility for treatment and discharge. Localized effects on the water quality do
occur, however, due to the inflow of the Clinton River and combined sewer overflows.
The outflow of Lake St. Clair (mean discharge of 5,400 m3/sec or 190,000 cfs) flows
into the Detroit River and thence to Lake Erie after traversing approximately 51 km
(32 miles). It is this portion of the connecting waters where the most significant pollution
and degradation of water quality occurs.
The lower Detroit River (below the confluence with the Rouge River) is the most critical
portion due to the discharge of municipal and industrial wastes from this point downstream.
OBJECTIVES
The primary objectives of the study reported herein is the delineation of the existing
water quality and the prediction of the degree of enhancement of water quality in this
region with the inauguration of "best practicable" and "best available" treatment of
wastewaters. In order to accomplish this prime objective, three basic program elements
were pursued.
The first task element was a thorough review of the literature with respect to previous
studies performed in the water bodies of concern. An additional apsect of this task was
to access the available data sources (state and provincial water quality monitoring agencies
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Figure 1
WATER QUALITY SURVEY AREA
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and the STORET system) in order to determine the scope of information available.
Based on the evaluation of the existing data base, a field survey program was developed
that would serve to remedy certain deficiences in presently available information, and
to provide some degree of verification of the previously obtained data. Task two was
then the performance of three separate water quality surveys to provide the desired
additional information.
The third task element was the development and verification of a steady-state,
three-dimensional mathematical model of the Detroit River. The model was developed
to treat conservative substances and non-conservative substances which follow first order
reaction kinetics. The use of such a model will allow for a better definition of waste
inputs as well as assisting in the determination of the impact on water quality of higher
degrees of wastewater treatment.
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SECTION IV
HISTORICAL BACKGROUND
PREVIOUS COMPREHENSIVE STUDIES
The earliest recorded systematic survey of water quality in this general area was performed
by the U. S. Geological Survey in 1906-19071. This study determined the general water
quality in Lake Erie and Lake Huron, but did not concern itself with the waters included
in the present study area. The basic findings indicated high quality of water both above
and below the Detroit area with respect to the chemical parameters monitored. No
bacteriological testing was included in this study, thus this important parameter cannot
be evaluated for this early period.
Prior to the U. S. Geological Survey study only isolated data from samples collected by
various water treatment plants are available. Since the great majority of the intakes for
these plants were purposely established in open- lake locations to avoid the influence of
localized pollution sources, the analyses from these sites are relatively useless in establishing
the general water quality existing during that period of time.
In 1913, a survey of coliform bacteria in the Detroit River, and certain other areas of
the Great Lakes, was performed under the auspices of the International Joint Commission
o
. Although bacteriological technology and manner of reporting results has changed
significantly since that time, this study is important in that it provides the first
comprehensive evidence of the deterioration of the bacteriological quality of the water
due to human activity and the change in land usage. The results of this study indicated
that, due primarily to the absence of sewage treatment and the presence of numerous
outfalls along the Rouge and Detroit Rivers, average coliform densities as measured by
the Phelps Index increased from 5 per 100 ml to 11,592 per 100 ml between the head
of the Detroit River and its mouth. These results can be crudely converted from this
index to MPN values by multiplying the index values by 2.4, resulting in median MPN
values of 12 and 27,800 at the head and mouth, respectively. In addition, the findings
of this study indicated the significant shoreline effects, particularly below the developing
industrial complex in the vincinity of the Rouge River.
Significant additional contributions to the data base for this region did not occur until
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the decade after World War II. Three major investigations were initiated during this period,
two involving water quality investigations as they applied to raw water supplies for local
units of government, and the third a general water quality investigation under the auspices
of the International Joint Commission.
Detroit Water Supply Report, 1948
In 1948, a report evaluating the effect of combined sewer overflows into the Detroit
River on the raw water supply for the City of Detroit was prepared by a board of consulting
o
engineers . This report provides little in the way of newly acquired data, however it
does summarize certain aspects of water quality as it was observed at the municipal water
intake at Water Works Park at the head of Belle Isle. Among the findings contained
in this report that pertain to water quality in the Detroit River are the following:
a. Pollution of Lake St. Clair and the Detroit River has increased over the years,
and this is reflected in the raw water quality.
b. The maximum MPN in any sample of the raw water at the intake during recent
years was 15,000 per 100 cc. and the maximum daily average was 7,030 per
100 cc.
c. For the most part the high MPN values follow rains and are accompanied by
recognizable increases in turbidity, but this is not always the case.
Wayne County Water Supply Report, 1955
A second investigation of river quality for water supply purposes during this period was
performed by Hazen and Sawyer for Wayne County . In addition to summarizing
previoulsy obtained data, this study included detailed investigations of water quality of
the lower Detroit River and the western end of Lake Erie. Since this study was concerned
with the determination of water quality with respect to its usefulness as a potable supply,
the main emphasis was on bacteriological quality and chloride levels as tracers of pollution
and an indication of current distribution. The results of this study illustrated once again
the significant shoreline effects of pollution, due to the relatively high rate of flow in
the river which retards transverse mixing. This is shown in the median coliform density
observed from Detroit Water Board sampling (1952-1955) and their study at Range C-1
(approximately milepoint 17.0W). The results for these four years, as well as previous
IJC data, showed median coliform densities at a point approximately 1,500 feet from
the west shore to range between 100 and 300 per 100 ml, while densities near the western
shore ranged between 40,000 and 100,000 per 100 ml.
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This same condition of relatively high quality bacteriologically in mid-river water and low
quality (median coliform densities greater than 10,000 per 100 ml) in the water near
shore was observed from the confluence of the Rouge River to the head of Grosse lie.
At this point the higher bacterial densities were observed to exist only in the Trenton
Channel on the west shore of Grosse lie, with the water in the Fighting Island Channel
to the east of Grosse Me exhibiting much lower median coliform densities. Based on the
coliform data obtained in this study the following observations were made.
a. A relatively small effect of upstream pollution and combined sewer overflows
from Detroit and Windsor was found to exist at Fort Wayne (milepoint 20.6)
during dry weather. At this point the shore pollution was found to be limited
to a narrow band, and low coliform densities prevail to within a few hundred
feet of both shores.
b. The most important sources of sewage pollution along the United States shore
in the lower part of the Detroit River were determined to be the Detroit Sewage
Treatment Plant effluent and the Rouge River.
c. The decrease in coliform density from the United States shore to the center
of the river is rapid throughout this section of the river (milepoint 20.6 to
Lake Erie).
d. Characterization of the lower Detroit River as the "sewer for Metropolitan
Detroit" is not warranted. The Trenton Channel does serve this purpose, but
the quality of the main flow of the river is affected to only a slight degree.
e. The water in the middle of the river does not escape all pollution, but the
rate of diffusion of shore pollution toward the center of the main flow is
low. The best water is generally found at or near the eastern side of the
ship channel.
Additional coliform analyses were performed during periods of intense storms to show
quantitatively the effects of wet weather and subsequent combined sewer overflows. A
total of eight sampling points were selected in order to evaluate water quality on both
sides of the shipping channel at the following ranges:
Fort Wayne (approximately milepoint 20.6)
Grassy Island (approximately milepoint 15.4)
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Fighting Island South Light (approximately milepoint 12.OE)
Stony Island (approximately milepoint 8.7E)
It was observed that the median coliform density near shore at Fort Wayne during wet
weather was 82 times the median coliform density during dry weather. However, 1000
feet from shore the median density during wet weather was only three times the density
during dry weather. Similarly, the western station at Grassy Island showed an increase
of nine times, while the eastern station showed only a two fold increase. Results at
Fighting Island South Light were similar to those at Grassy Island, while the Stony Island
stations showed nine fold increase at the western station and a corresponding six fold
increase at the eastern station. The conclusions drawn from this phase of the study were
as follows:
a. While the coliform density in the mid-river water is greater following rains
than in dry weather, the relative increase is small.
b. Shore pollution does not make its way across the river in concentrated slugs.
The pollution that reaches the main stream is mixed with a large volume of
water and diluted many times.
c. The effect of shore pollution on mid-river water quality increases moderately
with distance down the Detroit River as far as Fighting Island South Light;
below this point the effect is greater.
Analysis of the chloride data obtained in this study indicated the same general pattern
with respect to pollution along the western shore. Average chloride concentrations at
stations across the Detroit River above the Rouge River inflow were relatively constant,
varying between 6.7 and 7.8 mg/l. Starting at the Rouge River the chloride concentrations
along the United States shore were high, however relatively uncontaminated water, with
chloride levels between 8 and 10 mg/l, was observed within a few hundred feet offshore.
An important difference was observed between the coliform and chloride distributions,
however, in that a sharp increase in chloride levels was found between Fighting Island
and the Fighting Island Channel. These high levels were undoubtedly due to the leaching
from the waste beds located on the Island. The influences of these concentrations of
chloride were observed to occur in the Amhertsburg Channel to the east of Bois Blanc
Island, and to have relatively little impact on the Livingston Channel between Bois Blanc
Island and Grosse Me. This information provides further substantiation on the tendency
of the pollution to "streamline" along the shore.
13
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International Joint Commission Pollution Survey, 1951
The real foundation of systematic evaluation of water quality in this region was initiated
during the time interval between these two studies. On April 1, 1946, the governments
of Canada and the United States directed the International Joint Commission to inquire
into and report on the pollution of the St. Clair River, Lake St. Clair, and the Detroit
River. This investigation extended over the period July, 1946 to December, 1948, with
the final report of the findings being submitted to the two governments in October, 1950
The principal findings from this study were summarized as follows:
a. These waters are seriously polluted in many places on both sides of the
boundary. The most serious pollution exists in the St. Clair River below Port
Huron and Sarnia, in Lake St. Clair along the west shore, in the Detroit River
below Belle Isle, and in Lake Erie at the west end. There is progressive over-all
degradation of the water between Lake Huron and Lake Erie.
b. There is a transfer of pollution from each side of the boundary to the other.
This has been demonstrated by float studies, by analytical results, and by
accidental discharges of specific substances. (It should be noted that these
findings are not necessarily in contradiction of the previous studies which
emphasized the tendency of pollution to remain close to the shore, with the
central channel of the river remaining relatively clean. Since approximately
50 percent of the total flow passes through the central portion of the river,
the relatively high volume of water will tend to dilute any pollutants entering
this section to a greater extent than in the near shore areas with relatively
low flow rates.)
c. There has been, and remains a potential for, injury to the health and property
on both sides of the boundary.
d. Substantial progress has been made in control or elimination of pollution during
the period of the investigation.
The surveys performed as a part of this investigation encompassed sampling stations ranging
from the southern portion of Lake Huron (approximately four miles above the head of
the St. Clair River) to western Lake Erie. The extent of this survey effort can be seen
in the number of stations established, as shown in Table 1.
14
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Table 1
Body of Water
Lake Huron (southern
end)
Number of transects
Total number of stations
47
St. Clair River
12
59
Lake St. Clair and
tributaries
111
Detroit River
10
197
In addition, a total of six stations were established on four tributaries to the St. Clair
River and six stations on four tributaries to the Detroit River. The number of samples
collected and number of analyses performed during this study are presented in Table 2.
Table 2
Area of Source
Lake Huron
St. Clair River
Lake St. Clair
Detroit River
Lake Erie
Municipalities
Industries
Total
Bacteriological
Examinations
94
1688
1979
3806
534
1337
-
9438
Chemical
Samples
272
3082
2389
4295
746
494
788
12056
Examinations
Determinations
544
9431
14240
23894
3722
3327
7436
62594
15
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The importance of this study does not lie solely with the breadth of the survey, however,
but also in the establishment of a systematic grid of sampling locations and designations
of these sampling points, to allow for the correlation of the evaluation of trends in
water quality as a function of time. In addition to the above accomplishment, two highly
significant results of this study were the establishment of IJC objectives for water quality,
and the establishment of a technical committee to maintain continuing contact with
pollution control efforts and subsequent effects with respect to water quality in the area.
The basic parameters utilized in this study for evaluating the extent of pollution were
total coliform levels and phenol concentrations. The water at the southern end of Lake
Huron was observed to be of good sanitary quality and relatively free of any effects of
pollution. Median colifrom MPN values were generally in the range of 5 per 100 ml or
less, which is essentially the same as the levels observed in 1913. Similarly, high water
quality was shown by chemical analysis, with dissolved oxygen ranging between 9 and
11 ppm, average BOD values from 0.5 to 1.5 ppm, and a maximum phenol level of 4
ppb.
The high quality of the water entering the St. Clair River from lake Huron was observed
to continue in the middle third of the stream for a considerable distance downstream
from the headwaters at milepoint SR - 39.0. High coliform levels showed heavily polluted
zones near both shores in the upper section of the river, reflecting the discharge of untreated
sewage from Port Huron, Marysville, and Sarnia, and the highly polluted waters of the
Black River. Median coliform levels increased from five at the head of the St. Clair River
to 5,400 near the United States shore at SR - 35.4, showing the influence of the Black
River which enters the river approximately one mile upstream from this point. The
Canadian shore is seen to be similarly influenced with median coliform values of 930
below Sarnia (SR - 35.4) and 2,400 at Cornunna (SR - 30.1 E). This bacterial pollution
tended toward a more uniform distribution across the entire river at milepoint SR - 17.5,
with median levels of 1700, 180, 170, 240, 430 at distances from the United States
shore of 100, 1200, 1700, 2200, and 2600 feet, respectively. The water leaving the St.
Clair River was observed to have a bacterial load of coliform organisms 200 times greater
than the water entering the river from Lake Huron.
The intensity and distribution of pollution in Lake St. Clair were seen to be influenced
by the division of flows through the St. Clair flats, the direction of winds, the lake
-16-
-------
currents, the intermittent discharge of combined sewer overflows, the effects of natural
purification. Basically, the water within the lake was found to be of good bacterial quality
except in localized areas. The eastern portion of the lake was found to be relatively free
from pollution, with the exception of a one to two mile zone at the mouths of the
Chenal Ecarte and Thames River. Higher levels of coliform organisms were observed in
the northwestern portion of the lake, particularly at the outlets of the north and middle
channels of the St. Clair River and the Clinton River. These sources, along with combined
and storm sewer overflows from the lakeside communities, result in relatively higher levels
of pollution along the western shore of the lake. Patterns of relative phenol concentrations
follow the same general spatial relationship as the coliform values, which is to be expected
since both parameters are influenced by the same water movement. Average phenol values
were found to be generally below 10 ppb.
The analytical results for the Detroit River showed a littoral stratification similar to that
observed in the St. Clair River, with pollution effects remaining near the respective shores
in the upper reaches and spreading and diffusing across the entire width of the stream
below Fighting Island. Median coliform levels approached 100 per 100 ml along both
shores at the entrance to the Detroit River, with a value of about 10 at midstream. A
significant increase in coliform levels was observed on the United States side at the head
of Belle Isle as a result of combined sewer overflows emanating from Conners Creek.
Median coliform levels at this range (DT - 29.2W) were 200,000 and 93,000 per 100
ml at distances offshore of 50 and 100 feet, respectively. Moving downstream, the bacterial
pollution retained its shore hugging characteristics, although the zones of higher coliform
levels were observed to extend farther out from shore. Upstream from Zug Island - Rouge
River industrial complex (DT - 20.6), median coliform levels of 24,000 per 100 ml were
observed at the United States shore, decreasing to 2,400 per 100 at a distance of 300
feet from shore. Median values near the Canadian shore at this range were 8,200 and
2,400 at offshore distances of 100 and 400 feet, respectively. The mid-river median levels
at this range increased to 93 per 100 ml. Bacterial pollution from the Rouge River and
the Detroit Sewage Treatment Plant have an immediate effect on the United States
shoreline, resulting in a median coliform level of 93,000 at DT - 19.0 just 0.8 mile
downstream from the Rouge River. Surface currents from the Rouge River - Zug Island
area were observed to tend to cross the international boundary and to flow to the east
of Fighting Island. This results in a relatively uniform distribution of coliform across
this channel at levels between 1,500 and 3,500 per 100 ml. The channel to the west
of Fighting Island was characterized by high coliform levels near the United States shore
17
-------
and extending about one half the distance to the Island. Median coliform levels from
this point to the island shore were about 100 per 100 ml. As the flow continues
downstream to Grosse lie, the heavier pollution along the United States shore tends to
enter the Trenton Channel on the west side of the Island resulting in observed median
coliform levels of 10,000 per 100 ml and higher. The flow on the east side of the Island
shows the pollution fairly well distributed across the channel at milepoint 9.3E, with
median levels ranging from 1,100 to 9,300. At range DT - 3.9, across the mouth of
the river, the bacterial pollution on the Canadian side remained constant at about 5,000
MPN, while an increase was observed on the United States side due to the highly polluted
waters from the Trenton Channel, with median values reaching 43,000 per 100 ml.
Significant concentrations of phenol were observed primarily on the United States side
of the river downstream from the Rouge River. Average phenol values at this transect
(DT - 19.0) ranged from 11 to 39 ppb for a distance of 400 feet offshore, due to discharge
of phenols from the Rouge River (average concentration of 79 ppb) and the Detroit Sewage
Treatment Plant. Phenol concentrations upstream from this transect and on the Canadian
side are generally 8 ppb or lower. These elevated phenol concentrations were observed
to remain near the United States shore, with the primary pollution resulting from this
parameter occurring in the Trenion Channel on the west side of Grosse lie, where average
concentrations of 12 to 24 ppb were determined. Significant phenol pollution was observed
in Monguagan Creek, which enters the Trenton Channel immediately below the sampling
transect DT - 12.0W. This tributary exhibited an average phenol concentration of 3,490
ppb. At range DT - 3.9, the phenol concentration exhibited generally the same pattern
as the coliform, in that there is a diffusion across the river, with higher concentrations
on the United States side due to the quantities added from the Trenton Channel. BOD
and ammonia results showed low values above the mouth of the Rouge River, with
somewhat elevated levels below this point.
Comparing the average coliform results between the 1913 study and the 1946-1948 study,
it was observed that, while Lake Huron had remained essentially constant, the total bacterial
load at the mouth of the Detroit River had increased approximately three fold. The
overall increase from Lake Huron to the mouth of the Detroit River was approximately
800 times in 1913 and over 2,400 in 1946-1948.
U. S. P. H. S. Water Quality Survey, 1965
In March of 1962 a conference was held at the request of the State of Michigan to discuss
the present status of pollution in the southeast Michigan area. As an outgrowth of this
18
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conference, the Detroit River-Lake Erie Project was established by the United States Public
Health Service to determine the extent of pollution in the United States portion of the
Detroit River and the Michigan section of Lake Erie. In addition, this project was to
investigate the principal sources of pollution in this area, the contribution from these
sources, the effect of pollution on various water uses, and to prepare a plan for pollution
abatement in the area.
In order to provide this information, a comprehensive study was initiated in 1962, with
fi
the final report presented in April of 1965 . This report provides a detailed analysis
of the various water usages in the area, population and manufacturing trends, municipal
and industrial waste sources and their characteristics, and description of water quality.
The investigation of bacteriological quality showed that the total coliform concentration
near the United States shore, from Belle Isle to the mouth of the river, were significantly
affected by storm overflows, showing a five to ten fold increase during these periods.
Under dry conditions, the coliform level was not found high enough to interfere with
any water uses, except below the Rouge River and the Detroit Sewage Treatment Plant
outfall, in the United States section of the river. During or following periods of sufficient
rainfall to cause overflow of combined sewers, however, the entire river below Belle Isle
was found to be polluted to the extent that it is unsafe for recreational usage. In addition
to total coliform determinations, fecal coliform and fecal streptococcus analyses were
performed during the course of this study. Fecai coliforms were found to comprise from
30 to 90 percent of the total coliform population, with the higher values occurring below
the Rouge River during wet periods. At the mouth of the river the fecal coliform densities
ranged from 30 to 65 percent of the total of 1,000 to 10,000 per 100 ml. Fecal streptococci
levels were considerably lower than coliform levels, particularly during wet conditions.
One of the more critical chemical parameters investigated was the phenol concentrations
in the river. IJC objectives call for average phenol concentrations not to exceed 2 y g/l
and maximum values not to exceed 5 yg/l, in order to prevent taste and oodors in water
supplies^ . These criteria were exceeded at all ranges in the Detroit River during the
study period. Average phenol concentrations in the upper Detroit River ranged from
3 to 5 yg/l, while a near shore station just below the Rouge River exhibited an average
concentration of 28 yg/l. High phenol levels were particularly noticeable in the tributaries
of the Detroit River with maximum values of 10,980 yg/l and 290 yg/l in Monguagon
Creek and the Rouge River, respectively. Average phenol concentrations in these two
tributaries were 1500 and 12 yg/l, respectively. Average concentrations at the mouth
of the Detroit River ranged from 4 to 9 yg/l on the United States side of the International
Boundary, with from 33 to 70 percent of the samples taken within 5,500 feet of shore
showing concentrations in excess of 5 yg/l.
19
-------
The other chemical parameters investigated include: solids, chloride iron, biochemical
oxygen demand (BOD), dissolved oxygen (DO), nitrogen compounds, phosphates, pH, ABS,
alkalinity, chemical oxygen demand (COD), cyanide, hardness and certain toxic metals.
Although, in general, no serious problems were encountered with respect to the
concentrations of these materials, and little in the way of specific trends was delineated,
there was illustrated a general degradation of quality below the Rouge River. This was
particularly true with respect to chlorides, BOD, COD, and certain heavy metals.
Biological analysis was incorporated as a portion of this study, with investigations made
of microscopic plants and animals and bottom dwelling organisms. The free-floating
phytoplanktonic organisms were found to be relatively unchanged through the course of
the river, with the population basically dependent on those plankton which enter from
Lake St. Clair. The sewage fungus, Sphaerotillus , was found growing attached to submerged
objects, being particularly abundant below the Rouge River and Detroit Sewage Treatment
Plant outfall. Of the biological communities analyzed, the benthic organisms most clearly
illustrated the effects of pollution. Bottom samples collected at the headwaters above Belle
Isle contained a variety of clean-water associated species, such as caddisfly larvae.
Downstream from Belle Isle, along the Michigan shore, there no longer existed the
pollution-sensitive organisms, rather a preponderance of sludge worms and leeches were
collected. Forms with intermediate tolerances were found along the United States shore
from approximately range DT - 25.0 to the confluence of the Rouge River. At this
point a band of extremely pollution tolerant organisms existed, with essentially no
clean-water forms observed further downstream.
This study also included a comprehensive study of waste loadings from municipalities and
industries in the general area. A summary of the waste loadings determined from this
survey is presented in Table 3.
Table 3. SUMMARY OF DAILY AVERAGE WASTE LOADS IN DETROIT RIVER -
UNITED STATES SIDE (1963-1964)
Source
Industrial
Total waste
flow (MG)
1090
Phenols
(Ibs)
1410
Cyanides
(Ibs)
1030
Ammonia Oils
(Ibs) (aal)
8530 3350
Suspended
Solids (Ibs)
822000
Municipal
541
1270
34300
16000
626000
Total 1631 2680 1033 42830 19350 1448000
The analysis of water quality and waste loadings as determined in this study showed a
general improvement in water quality in the lower Detroit River when compared to the
20
-------
IJC survey of 1947-1948. This was particularly true with respect to coliforms and phenol.
The major reasons for this improvement appeared to be the progress made in pollution
abatement by the industrial segment during the preceeding fifteen years. Reduction of
70 to 80 percent in total loadings of phenol, cyanide, and oil was achieved by industry
during this period, along with a 22 percent reduction in ammonia loading and 51 percent
reduction of suspended solids loading. Municipal sources were not analyzed during the
previous survey, so no similar evaluation could be made for this sector.
Subsequent to this survey (1962-1963) routine monitoring of river water quality and point
source discharges has been performed by the Michigan and Ontario Water Resources
Commissions. The data from these surveys are forwarded to the IJC for their use as
well as the Commissions'. Summary reports based on this data are periodically prepared
by the IJC which evaluate the progress being made in pollution abatement. These results
will be considered in the discussion of water quality trends later in this report.
EXISTING MONITORING PROGRAMS
Since the conclusion of the comprehensive study of the Detroit River performed by the
U. S. Public Health Service, a continuing water quality survey program of the Detroit
area interconnecting waters has been maintained by various governmental agencies. At
the present time, The State of Michigan and the Province of Ontario have the prime
responsibility for the monitoring of these waters. In addition, the U. S. E. P. A. provides
continuing surveillance at selected stations. Although certain stations which were sampled
by the Public Health Service and in the early portion of the monitoring program have
been abandoned, and certain other stations have been established in recent years, the
current program has continued numerous stations which have been sampled several times
each year for the present decade. The information from these stations allows for the
examination of trends in water quality with respect to several parameters.
The river transects currently being monitored (1973) season, each of which generally has
a number of stations located across the river, are listed in Table 4.
In addition to the continuing monitoring program, additional studies are performed
periodically, such as industrial waste surveys, and the extensive study of Lake St. Clair
performed by the Michigan Water Resources Commission in the summer of 1973.
21
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Table 4, CURRENT MONITORING TRANSECTS
Transect
St. Clair River
SR 39.0
SR 35.0
SR 34.4
SR 33.9
SR 33.1
SR 30.7
SR 26.7
SR 17.5
SR 13.7
SR 10.0 S
SR 10.0 N
SR 7.6 N
SR 4.1 N
Detroit River
DT 30.8 W
DT 30.7 E
DT 25.7
DT 20.6
DT 20.2
DT 19.0
DT 17.0 E
DT 14.6 W
DT 13.12
DT 12.0 W
DT 9.3 E
DT 8.7 W
Stations per transect
United States Agencies Canadian Agencies
DT
DT
DT
6.7 E
6.2 E
3.9
2
6
7
6
6
6
3
3
3
3
7
3
5
2
2
3
6
6
6
6
6
7
4
6
3
7
3
8
3
11
2
5
4
9
3
2
1
12
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WATER QUALITY TRENDS
Methodology
The water quality data obtained by governmental agencies within the United States is
on file in the STORET system maintained by the U. S. Environmental Protection Agency.
A similar system, maintained by the Ontario Ministry of the Environment, contains the
data obtained by the Canadian agencies. Due to time restrictions, only the STORET
system was accessed in order to obtain the data which would allow for the delineation
of water quality trends for the two rivers of concern in this project. A total of six
transects in each of the rivers were used in the analysis, since these milepoints were the
ones containing sufficient long-term data to allow for meaningful interpretation.
In general, the data was analyzed by using the annual averages for various parameters
at the selected stations. In order to reduce the affect of any anomalies in the data,
three year moving averages were computed, thereby considering larger sample sizes (15-20
observations). Based on the preliminary analysis of such data transformation, it appeared
that a random grouping of yearly averages would best portray the average water quality
conditions for specific periods of time. Based on the data available and trends observed
from annual averages, the St. Clair River was grouped into the years 1946-1947, 1964-1969,
and 1970-1973, while the Detroit River was evaluated by comparing 1962-1963 data with
that from 1971-1973. Any statistical error which might have been induced by comparing
averages for various time durations was not investigated. It must also be stressed that
the concentration values observed do not take into account any variation in total river
discharge. Indications are that the discharge has increased approximately 10 percent over
the last decade (see Appendix D-3).
While the above approach provided a degree of qualitative indication of water quality
trends over the past decade, a more rigorous analysis was made by a statistical comparison
of the mean annual values at selected stations for the years 1968 and 1973.
Statistical evaluation of yearly means of selected chemical and biological parameters was
accomplished utilizing a t-test of the differences between two means. The null hypothesis
is that if the two samples come from the same population, they must have the same
parametric mean ( y * = v~ )• This test assumes equal variances in the two samples.
An alternative test considers two samples from different populations being heteroscedastic
(i.e. variances not equal).
Testing the homogeniety of variances of two sample sets was done utilizing the F test,
which calcualtes the ratio of the greater variance over the lesser one. When the homogeniety
of variance assumption was not tenable, the differences between the means were tested
using the t' test. The confidence limits for all tests were 95 percent.
23
-------
The formulae used in evaluating the data are summarized as follows:
A. Testing the homogeniety of variances.
H.,: a
05 ^ ^1' ^2 ^ accept null hypothesis
05 ^ V-|, V2) accept alternative hypothesis
B. t-test means of two samples
o r\
null hypothesis accepted (HQ: a -j = a 2 )
H0:
H :
^ < t.05 ^V^, \/2^ accept null hypothesis
^ > t.05 "• V-|, V2 accept alternative hypothesis
C. t' test means of two samples
alternative hypothesis accepted (H^: a ^ =/ a 2 '
H0 : u, = U2
H1 : P1 ^ P 2
*' s < tf 05 accept null hypothesis
*' s > tf 05 accept alternative hypothesis
24
-------
Finally, the data output from the STORET system was examined to check the compliance
of water quality with established standards and goals. The water quality standards
established by the State of Michigan for the St. Clair and Detroit Rivers are summarized
in Table 5 7.
Table 5. WATER QUALITY STANDARDS FOR THE ST. CLAIR AND DETROIT
RIVERS
Chlorides 50 mg/l monthly average
Dissolved Oxygen 6 mg/l
Filtrable Iron 0.3 mg/l
pH 6.7 to 8.5
Fecal Coliform 200 per 100 ml
Toxic Substances limited to concentrations established in Federal
Standards
For the purposes of evaluating the concentration of toxic heavy metals, the levels
0
recommended in the Water Quality Criteria-1972, published by EPA were used0. Pertinent
recommended criteria from this report are shown in Table 6.
Table 6. ALLOWABLE HEAVY METAL CONCENTRATIONS
Cadmium 30 micrograms per liter
Chromium 50 micrograms per liter
Copper 0.1 x 96 hour-LCgg *
Lead 30 micrograms per liter
Mercury 0.05 microgram per liter average
0.2 microgram per liter maximum
Nickel 0.02 x 96 hour-LC50
Zinc 0.005 x 96 hour-LC50 *
*LC values not established for this water
25
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St. Clair River
Prior to 1970, comprehensive data collection on the St. Clair River was limited to the
survey undertaken in 1946-1948 under the auspices of the International Joint Commission,
as reported in the historical review. In the mid-fifties, and again in the mid-sixties, a
limited amount of water quality data was obtained, particularly with respect to the phenol
concentrations. Insufficient data is available for these periods to perform a rigorous trend
analysis, however, certain general observations can be made for this period. Routine,
systematic monitoring of the St. Clair River at a number of new, as well as at several
previously established stations, has existed since 1970. The continued monitoring of these
stations will provide greater insight into overall water quality of the river, however the
four recently established stations do not provide sufficient data to allow for the
establishment of any trend. Consequently, only the six on-going stations will be considered
in this analysis. Furthermore, only chloride and phenol concentrations have received
enough emphasis at these stations to allow for a systematic analysis.
Results
Chlorides - The chloride concentrations at the head of the river (SR 39.0) have remained
relatively constant, with discrete samples ranging from 3 to 12 mg/l, and annual average
values ranging from 4.7 to 6.7 mg/l. A variation of the average chloride concentration
can be seen, however, at station SR 26.7 (Figure 2). The station located 100 feet from
the United States shore showed a slight improvement from 1946 to 1969 (8.1 mg/l to
7.6 mg/l), however, the most recent data shows the average values 1,900 feet from the
United States shore going from 8.2 mg/l (1946- 1947) to 13.3 mg/l during the late 1960's
and back down to 7.4 during 1970-1973. These changes are also reflected in mid-river
water quality, where the average chloride concentration has risen from 5 mg/l in 1946-1947
to 6.6 mg/l and 7.2 mg/l for 1964-1969 and 1970-1973, respectively.
The next station downstream for which continuing data is available is located at SR 17.5
(Figure 3). The average chloride levels for three different sampling periods can be seen
to remain relatively constant in the western portion of the river, except for the station
located 100 feet from shore, where the level has increased from approximately 8.5 mg/l
in both 1941-47 and 1964-65, to 10.6 during the period 1970-73. Results obtained near
the Canadian shore follow closely the conditions observed at SR 26.7, where a large increase
was observed in 1964-65, with a reduction in chloride levels found since 1970. The same
conditions observed at SR 17.5, were found at station 13.7 (Figure 4).
26
-------
LZ
Chloride Concentration (mg/1)
ho
O
O
O
cc
rr
O
rc
3
C
CO
vC
C
N3
§
f
ftt
CO
O
O
to
(—'
O
O
O
O
C
»-(
(t
N5
(t
O
l-l
I-1'
C.
ft
rr
i-i
te
rr
CO
n
ro
U>
-------
Figure 3. . Trends in chloride concentration St. Clair River SR 17.5
o
•H
» c
0)
o
CJ
o
u
16
o 12
1964-1965
X
1970-1973
/
/
/
.946-1947
0
I
I
I
I
2400
300
600
900
1200
1500
1800
2100
Distance from U.S. Shore (ft.)
270U
-------
Figure 4. Trends in chloride concentration St. Clair River SR 13.7
N>
o
•l-l
4-1
tti
1-1
4->
C
0)
O
C
O
o
0)
T3
•H
O
16
12
0
1964-1969
^1970-1973
946-1947
1
1
1
1
300
600 900 1200 1500
Distance from U. S. Shore (ft.)
Truir
-------
The final station for which sufficient monitoring has been performed to allow an analysis
of water quality trends is located at SR 10.0, which is located below the point where
the river splits into a north and south channel around Harsons Island. Results obtained
in the south channel follow closely the results obtained at SR 17.5 and SR 13.7, with
a relatively large increase in chlorides between 1946-47 and 1964-65, with a small decrease
observed since 1970. The north channel can be seen (Figure 5) to have experienced
a continual increase in chloride levels, although the magnitude of this increase has been
relatively small (6.8 mg/l to 8.9 mg/l).
Phenol - Phenol levels were found to be relatively high at most stations monitored during
the 1946-47 survey, with all stations having at least one sample which exceeded the IJC
objectives of a maximum 5 y g/l, and many stations exhibiting maximum concentrations
of 100 to 400 y g/l. Sampling programs during the 1950's showed phenols to remain
a problem, however, a marked decrease in phenol concentrations was observed. Only
one sample exhibited a concentration in excess of 50 yg/l, however, a total of 33 stations
had maximum concentrations in excess of the 5 y g/l objective. During the 1960's, the
number of stations where the maximum value was exceeded was reduced to 19, and the
maximum concentration observed was 30 y g/l.
By the 1970's, only two stations continued to exhibit a significant concentration of phenol:
SR 30.7 and SR 33.1. In both cases, the high maximum values were observed only at
one station located nearest to the Canadian shore, and to have little effect on the offshore
water quality. For example, the maximum concentrations observed during this period
occurred in 1973 at SR 33.1, 2,030 feet from the United States shore, with a range
of 1 to 21 yg/l for six samples, and an average of 5.67 y g/l. During this same period,
the station located 100 feet further out from shore ranged from 1 to 2 Mg/l, with an
average of 1.67. The effect of this concentration was manifest in the next downstream
station (SR 30.7 - 3,700 feet) where the phenol concentration ranged from 1 to 7 yg/l,
with an average of 3.33. Here the effect could be observed further from shore (SR 30.7
- 3,550 feet) where the values ranged from 1 to 4 with an average of 2.33. Downriver
from this point, no values above 4 yg/l were observed.
It is thus obvious that considerable progress has been made in preventing phenol pollution
in the river. With the possible exception of the industrial area south of Sarnia, the phenol
pollution sources have been reduced to the level where IJC objectives for the river are
being met.
30
-------
Chloride Concentration (mg/1)
OO
CTi
to
O
O
O
o
o
H-
CO
rt
03
3
O
n>
H)
§
VO
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h-1
o
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cr
o
ro
O -P- OO to
to
O
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o
o
VO
O
O
111!
"" oo
&3
f~^
o
oo
•••
—
\\
\
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1\
LV
\
\ \
\\
\\
\\
\ \
^ "ft
^ \l_.
I— • VO tTi
vO ^J -P-
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t — ' vO 0"*
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cm
a
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co
n
H-
a
n>
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o
n>
3
rt
H
03
rt
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rt
o
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0)
CO
M
O
O
03
3
C/3
!«
i—1
o
o
en
-------
Other parameters - Other parameters of interest in establishing water quality have received
systematic, continuing investigation only since the late 1960's or early 1970's. A small
amount of information on coliform and ammonia concentrations was obtained during the
1946-47 survey, however, the methods of analyses used for these parameters has changed
such that little insight is gained in comparing these earlier values with those obtained
during the more recent surveys.
Total coliform data was obtained in 1946-47 by the MPN method, whereas the membrane
filter method has been utilized in more recent surveys. Qualitative indications are that
a decrease in this parameter has occurred over the last two decades. Mean total coliform
levels are low at all stations (less than 1,000 per 100 ml) with maximum values within
the IJC goal of 1,000 per 100 ml. Fecal coliforms, although monitored only for the last
decade, show the same trend, generally accounting for approximately 10 to 50 percent
of the total coliform population.
Ammonia nitrogen was determined in 1946-47, and is included in current monitoring
programs. In general, ammonia was not detected during the earlier survey, however the
increased sensitivity of current analytical techniques with respect to ammonia precludes
attributing the presently detected levels to an actual increase in concentration. Nitrate
nitrogen and phosphorus were monitored periodically during the late 1960's, and have
been routinely monitored since 1970 with no appreciable trend being observed during
this period.
Little variation in suspended or dissolved solids has been observed, with the exception
that the most recent sampling season saw a significant increase in suspended solids at
the upstream stations. This is too short a time span to state affirmatively that a trend
is developing, however it does warrant paying particular attention to this parameter during
subsequent sampling seasons.
Statistical evaluation of the data from the St. Clair River was made for stations located
at milepoints SR 39.0 and SR 13.7. The results of comparing 1968 and 1973 mean
values is presented in Table 7. The three parameters for which significant differences
of annual means could be established were chlorides, nitrates, and total coliforms. As
is shown in Table 7, the chloride concentration at stations near the Canadian shore at
SR 13.7 have decreased significantly over the past five years. The nitrate concentration
has exhibited a significant decrease at milepoints SR 39.0 and SR 13.7 at most stations
monitored. The total coliform level, however, was observed to have increased significantly
at the head end of the river. Phenol and iron concentrations were also tested, however
no significant variation could be established between these two periods.
32
-------
Table 7. STATISTICAL EVALUATION OF MEANS - ST. GLAIR RIVER 1968 versus 1973
River Mile
39.0
Distance from shore (ft,)
100
4 foot depth
30 foot depth
1500
Chlorides
Nitrates
1968>1973
1968>1973
Total Coliforms
1968<1973
1968<1973
13.7
100
700
1000
1400
1900
1968>1973
1968>1973
1968>1973
1968>1973
1968>1973
U)
U)
-------
Generally speaking, the most recent surveillance data shows the water quality of the St.
Clair River to be in compliance with established standards and goals.
Detroit River
As discussed in the previous sections, the past two decades have seen increased activity
in the assessment and control of the water quality of the area. Prior to 1962, only
limited studies were undertaken to assess the water quality conditions, thus making a
detailed trend analysis for this time period extremely difficult. Some general conclusions
can be made, however, by considering the 1913, 1948, and 1962 studies performed under
the auspices of the International Joint Commision. The data from these studies has been
discussed in the previous sections and the following conclusions made. During the time
period of 1913 to 1948 the general water quality of the Detroit River continued to
deteriorate as measured by coliform bacteria and phenols. After the 1948 study, substantial
progress in pollution abatement was realized, and subsequently the general water quality
improved between 1948 and 1962.
In 1962 a comprehensive study the United States Public Health Service was initiated in
order to further assess the existing water quality. A number of stations established during
this study have been continually monitored up to the present time. Since 1966 most
of these stations have been maintained by the Michigan and Ontario Water Resources
Commissions. The data obtained during the course of the monitoring program provides
a data base for evaluating the trends in the water quality of the river over the past ten
years. The following discussion analyzes the changes in water quality over the past decade
as measured by several water quality parameters. These parameters include total coliform,
phenols, chlorides, ammonia nitrogen, nitrate nitrogen, total phosphorus, total iron,
cyanide, and total dissolved solids.
The STORET system maintained by EPA contains the water quality data from the United
States Public Health Service and Michigan Water Resources Commission surveys. This
retrieval system was used to access the data and to provide annual statistical summaries
for all of the stations which have been monitored. A similar system is maintained by
the Province of Ontario, however this system could not be accessed in time to include
the data from this source.
34
-------
A total of 23 stations located at six different milepoints along the Detroit River were
used in the analysis. These stations span the entire length of the river from the head
of the river at Lake St. Clair to the mouth of the river at Lake Erie. The stations were
chosen based on their location in the river and on the amount of data which was available.
Each of these stations was sampled five or six times during each year, this sampling
occurring approximately once a month from late April to early October.
Results -
Chlorides - The chloride concentrations have remained relatively constant at the head of
the river varying from 8-10 mg/l. There appears to have been a significant decrease,
however, in the concentrations in the lower portions of the river (milepoint 14.6 and
below). The largest decreases wery found at stations in the Trenton Channel at milepoint
8.7W. Graphical comparisons of the 1962-63 versus 1971-73 chloride levels are shown
in Figures 6-10. These decreases have resulted in the water quality now complying with
the chloride standard.
Phenol - Phenol concentrations have also generally decreased during the last ten years.
Again the most significant reduction has occurred in the Trenton Channel at milepoing
8.7W. Only two stations exhibited an increase in phenol concentration; both of these
being located at milepoint 14.6. Even though a general reduction has occurred, the
near-shore stations in the lower river, and all of the stations in the Trenton Channel,
continued to exceed IJC goals of 2 pg/l average and 5.0 ug/l maximum. Comparisons
of the data for various years is given in Table 8 and Figure 11.
Total coliform - It was difficult to assess a trend with regards to total coliform. Primary
sources of coliform loadings are the combined sewer overflows located along the river.
Due to the intermittent nature of these discharges, the sampling conditions as a function
of time since the last rainstorm, size of the storm, etc., are very critical when considering
the coliform concentrations. This is illustrated by the fact that for any given year large
variations occur between the maximum and minimum levels recorded. At several stations
these variations span several orders of magnitude (e.g. 100-10,000/100 ml). Because of
this large fluctuation, examining the data on a year to year basis provided little help
in defining a trend. At any given milepoint, several stations would show an increase,
while others showed decreased concentrations. Analyzing the data using three year moving
averages, however, tended to smooth out the yearly fluctuations and indicated that, on
the average, some changes have occurred. Figures 12 through 18 present graphical
comparisons of the averages for the years 1962-63, 1967-69, and 1970-72. In all cases,
35
-------
Figure 6. .Trends in chloride concentrations Detroit River - DT 20.6
10
6 8
o
•H
4-J
ctf
a)
a
8 5
QJ
? 4
1962-1963
JL
100
500 1000
Distance from U. S. shore (ft.)
1500
-------
Figure 7. Trends in Chloride Concentration - Detroit River DT 14.6
bO
P
O
•H
4-)
CO
M
4-1
C
-------
OJ
oo
Figure 8. Trends in chloride Concentrations - Detroit River DT 12.0 W
60
bfl
O
•H
QJ
o
c
o
CJ
0)
-d
•r-t
o
50
40
30
20
10
0
1962-1963
1971-1973
J_
TCJO 500
Distance from U. S. shore (ft.)
1,000
-------
Chloride Concentration (mg/1)
CTv
O
o
o
CO
rt
03
3
o
ft)
i-h
i-S
O
3
CO
OT
O
tt>
Hi
rt
o
o
o
o
o
H-
OP
d
K
ro
MD
H
H
0)
co
5-
ro
o
o
3
O
(D
03
rt
H-
O
3
O
ro
rt
H
O
H-
rt
Ui
o
o
CO
-------
-------
Figure H- Trends in phenol concentration Detroit River - 8.7 W
50
40
30
20
0)
X
PM
10
0
1
1
1962-1963
1971-1973
1
100
500 1,000
Distance from U. S. shore (ft.)
1,500
-------
Figure 12. Trends in total coliform concentrations - Detroit River
30.8 W
10,000
1,000
o
o
1971-1973
w
^
cu
100
1962-1963
1C
50
OO
S
5W
Distance from U. S. shore (ft.)
42
-------
Figure 13. Trends in total coliform concentrations Detroit Riv
DT 20.6
100,000 —
10,000
E
o
o
w
>-l
0)
1,000
100 _
10
250 500 1,000 1,500
Distance from U. S. shore (ft.)
270^0
43
-------
Figure 14. Trends in total coliform concentrations - Detroit River
DT 14.6
100,000
10,000
l.OOC
100
1967-1969
1970-1972
—. —-—
1962-1963
_L
_L
250 500 1,500 2,000
Distance from U. S. shore (ft.)
44
-------
Figure 15. Trends in total coliform concentrations Detroit River
12.0 W
100,000 —
o
o
w
!~i
OJ
1
C
10,000
1,000
100
1970-1972
100
500
Distance from U. S. shore (ft.)
1,000
A5
-------
Figure 16
Trends in total coliform concentrations
DT 9.3 E
- Detroit River
100,000
10,000
o
o
w
5-4
1,000
1971-1972
100
I
I
1000 2000 5000
Distance from U. S. shore (ft.)
46
-------
Figure 17. Trends in total coliform concentrations Detroit River
DT 8.7 W
100,000
10,000
o
o
w
c 1,000
100
1967-1969
1970-1972
mr
ID £7700"
Distance from U. S. shore (ft.)
47
-------
Figure 18. Trends in total coliform concentrations Detroit River
DT 3.9
100,000
o
o
ca
-------
TABLE 8. AVERAGE PHENOL CONCENTRATION- DETROIT RIVER
(1962-1973)
Station Feet from
Milepoint U.S. shore 1962-63 1967-69 1971-73
30.0 100 3.5 2.0 1.0
300 3-5 2.0 1.0
20.6 50 3.7 2.7 1.2
400 3.5 2.0 1.2
1000 3.6 2.0 1.2
14.6 100 8.0 5.7 6.7
400 7.2 4.3 5.9
1000 4.1 2.0 2.6
12.OW 122 9.0 5-3 5.3
490 8.2 5-0 4.6
880 8.5 3.2 3.4
8.7W 80 41.0 21.2 7.4
480 12.0 6.2 4.8
980 10.0 4.2 4.6
1240 7.0 3-7 3.8
3-9 2500 9.5 5-9 5.9
5500 5.0 3.7 4.0
7500 3.7 2.3 2.7
9500 3.2 2.4 1.5
11500 3-0 2.3 1.0
15000 3-1 2.1 1.0
16500 2.7 2.0 1.0
18500 2.5 2.0 1.1
19000 2.4 2.0 1.0
Note: all concentrations as ug/1 phenol
49
-------
the average total coliform concentrations appear to be higher for the time periods of
1967-69 and 1970-72 than they were during the early sixties. The overall indication
is that the coliform levels increased from the early sixties through the rest of the decade.
The concentrations have decreased in the last few years but are still higher than during
the Public Health Service Study of 1962.
The International Joint Commission objective for total coliform is 1,000/100 ml. The
only stations which met these standards were at milepoint 30.8, and some stations at
milepoint 20.6. Thus, even though the trend appears to be a slight decrease in
concentrations since 1969, most of the stations are still above the recommended levels.
Nutrients - Ammonia and nitrate nitrogen have been routinely monitored at most stations
since 1966, while phosphorus has been monitored routinely since 1968. Prior to these
dates only a small amount of scattered information is available. Thus, except for a few
stations at milepoints 30.8 and 3.9, sufficient data was available to make an assessment
only for the last six or seven years. The data for ammonia, nitrate, and phosphorus is
presented in Tables 9, 10, and 11, respectively.
Ammonia nitrogen levels have remained relatively constant for most stations during the
last six years. The only stations exhibiting any significant change were those near shore
in the Trenton Channel. In this area, as measured at milepoint 8.7W, the concentrations
have decreased 20 to 30 percent.
The nitrate concentrations have increased at most stations since 1967. The stations at
milepoint 30.8 are only ones which have remained constant during recent years. Some
nitrate data for 1964-65 was available for stations at milepoints 30.8 and 3.9. At 30.8
the nitrate levels appear to be 50 percent lower for the 1967-69 period than 1964-65,
and since 1967 they have remained constant. At milepoint 3.9 the 1967-69 levels were
also lower than those measured in 1964-65. However, the levels have increased since
1967 and are presently as high as, or higher than, the 1964-65 levels.
Phosphorus - Total phosphorus concentrations have decreased at all stations since 1968.
Again, the most significant drop has occurred in the Trenton Channel at milepoint 8.7W.
Close to 50 percent reduction in phosphorus concentrations has been realized at the near
shore station in this area.
Iron - Total iron concentrations have decreased since 1967 at most stations along the
river. The near shore stations in the Trenton Channel showed the largest reduction,
50
-------
TABLE 9. AVERAGE AMMONIA-NITROGEN CONCENTRATIONS - DETROIT
RIVER (1963-1973)
Station Feet from
Mllep.olnt U.S. shore 1963-65 1967-69 1969-71 1971-73
30.8 100 .11 .04 0.7 .05
300 .14 .03 .04 .04
20.6 50 .03 .05 .05
400 .03 .05 .05
1000 .05 .08 .07
12.0 122 .46 .45
490 .16 .19
880 .08 .10
8.7W 80 .59 .43 .41
480 .28 .20 .24
980 .13 .12 .14
1240 .11 .11 .11
3.9 2500 .57 .60 .55
5500 .27 .32 .29
7500 .17 .22 .17
9500 .06 .07 .09
11500 .08 .08 .08
15000 .04 .03 .05
16500 .03 .04 .05
18000 .03 .05 .07
Note: All concentrations are mg/1 as Nitrogen
51
-------
TABLE 10.AVERAGE NITRATE NITROGEN CONCENTRATIONS - DETROIT
RIVER (1964-1973)
Station Feet
Milepoint U.S. Shore 1964-65 1967-69 1969-71 1971-73
30.8W 100 .23 .12 .12 .13
300 .22 .14 .11 .10
20.6 50 .09 .11 .17
400 .10 .12 .16
1000 .10 .12 .15
14.6 100 .25 .38 .51
400 .18 .25 .26
1000 .16 .20 .21
12.OW 122 .26 .31
490 .20 .26
880 .17 .24
8.7W 80 .29 .41 .43
480 .23 .35 .37
980 .17 .22 .26
1240 .20 .24 .24
3-9 2500 .34 .64 .63
5500 .25 .20 .32 .46
9500 .22 .15 .18 .25
11500 .21 .15 .20 .22
15000 .20 .15 .16 .20
16500 .20 .17 .16 .18
18500 .26 .20 .19 .23
Note: All concentrations are mg/1 Nitrogen
52
-------
TABLE 11. AVERAGE TOTAL PHOSPHOROUS CONCENTRATION - DETROIT
RIVER (1968-1972)
Station Feet from
Milepolnt U.S. Shore 1968-70 1970-72
30.8W 100 .16 .06
300 .08 .05
20.6 50 .13 .10
400 .07 .06
1000 .10 .08
1^.6 100 .18 .13
400 .16 .11
1000 .09 .07
12.OW 122 .24 .18
490 .15 .12
880 .11 .10
8.7 80 .41 .22
480 .23 .15
980 .17 .13
1240 .16 .12
3.9 2500 .36 .24
5500 .22 .17
7500 .15 .13
9500 .12 .08
11500 .08 .06
15000 .07 .05
16500 .07 .04
18500 .08 .04
Mote: All concentrations as mg/1 as Phosphorous
53
-------
presumably due to increased industrial pollution control. The total iron data is given
in Table 12. It can be seen in this table that the iron concentrations below DT 14.6,
exceed the present standards.
Dissolved Solids - Dissolved solids information is only available for 1971 through 1973
at most stations. During this short period, however, all stations have shown an increase
in total dissolved solids concentrations. In some cases these increases are greater than
20 percent. Even though this parameter has only been routinely monitored for the past
three years, the indication is that the levels are continually increasing, however they are
well within established standards. Data for dissolved solids is presented in Table 13.
Cyanide - Cyanide has been monitored for several years because of its potential toxic
effect on the river. Except for a few instances in the early sixties, cyanide concentrations
have remained constant in the river at a level of approximately 0.01 mg/l.
Statistical results - The results of statistically evaluating the mean annual values for 1968
and 1973 for the Detroit River are presented in Table 14. Chlorides were observed to
have decreased significantly at two stations, both relatively near the United States shore
at milepoints 12.0W and 3.9. Iron concentrations also decreased at three stations on
these two transects. The nitrate concentration was observed to have increased at three
stations in the downriver region. The most important results were observed with respect
to the phosphorus concentration which has decreased significantly at nearly all stations
below milepoint 12.0W. No statistically significant changes were observed with respect
to total coliform and ammonia nitrogen concentrations between these two years.
Summary - In general, the water quality of the river has improved over the past ten years.
The chloride, phenol, phosphate, and iron concentrations have all decreased. The past
four years have shown signs that the coliform levels may be dropping, although more
time will be required to determine if this trend will continue. The decrease in concentration
of these parameters appears to indicate that the industrial and combined sewer overflow
control programs are beginning to have a positive effect on the river water quality.
54
-------
TABLE 12. AVERAGE TOTAL IRON CONCENTRATIONS - DETROIT
RIVER (1967-1973)
Station Feet from
Milepoint U.S. Shore 1967-69 1969-71 1971-73
30.8 100 513 431 264
300 372 355 297
20.6 50 399 480 415
400 333 365 278
1000 311 373 263
14.6 100 854 692 641
400 614 650 571
1000 507 493 389
12.OW 122 789 719
490 698 610
880 484 490
8.7W 80 1240 1145 918
480 1079 858 642
980 733 633 548
1240 568 581 496
3.9 2500 980 826 706
5500 804 597 600
7500 668 526 502
9500 574 421 421
11500 538 408 358
15000 550 376 297
16500 564 475 354
18500 643 52Q 587
Note: All concentrations are ug/1 as Iron
55
-------
TABLE 13. AVERAGE DISSOLVED SOLIDS CONCENTRATIONS - DETROIT
RIVER (1971-1973)
Station Feet from
Mllepolnt U.S. shore 1971 1972 1973
30.8 100 133 134 168
300 127 143 165
20.6 50 129 132 162
400 123 116 158
1000 121 119 160
1^.6 100 139 151 187
400 141 150 163
1000 132 138 152
2000 131 139 153
12.0 122 166 175 192
490 148 148 162
880 136 149 165
8.7 W 80 167 182 193
480 143 140 168
980 142 139 167
1240 137 148 170
3-9 2500 173 192 188
5500 151 164 163
7500 140 162 162
9500 129 153 162
11500 125 150 157
14500 130 145 158
16500 155 197 180
18500 189 212 218
19000 230 245 210
-------
River mile
30.8 W
20.6
1A.6
12.0 W
8. 7 W
3.9
Table 14. STATISTICAL EVALUATION
Distance from
shore (ft.) Chlorides
100
300
50
400
1000
100
400
1000
122 1968>1973
490
880
80
480
980
1240
2500
5500 1968>1973
7500
9500
11500
15000
16500
18500
19300
OF MEANS - DETROIT RIVER 1968 versus 1973
Phenols Nitrates Phosphates
— — —
1968>1973
— _ __
_ _ _
_
_
— _ -.
_
1968>1973
1968<1973
- -
— — _
1968>1973
1968<1973
1968>1973
1968<1973 - 1968>1973
_ _
1968<1973 1968>1973
1968>1973 - 1968>1973
1968>1973
1968>1973
- _ _
1968>1973
1968>1973
Iron
—
-
_
_
-
_
_
-
1968>1973
1968>1973
-
_
_
-
-
_
_
_
1968>1973
-
_
_
_
-
-------
SECTION V
WATER QUALITY SURVEY
INTRODUCTION
Methodology
Field investigations were made during three seasonal periods, with surveys performed on
August 14-16, 1973 (summer period), November 6-8, 1973 (fall period) and May 13-15,
1974 (spring period). A 42 foot, steel-hulled vessel was equipped with the necessary cranes,
winches, and other sampling equipment for the survey operation. Due to the extended
range of the study area, each survey required three days for completion. In order to insure
the reliability of the analytical results, samples were returned to the laboratory at the
end of each day for analysis of those parameters which could not be determined in-situ
at each sampling location.
Station transects across the river were located by means of conspicuous landmarks.
Distances from shore were measured by a visual rangefinder in order to determine when
the survey vessel was on station.
Station Locations
The specific sampling stations to be surveyed were chosen on the basis of the historical
data base for the area, existence of on-going monitoring programs or surveys by other
groups, presence of significant wastewater inputs, and required information for the
modeling effort. As discussed earlier, the State of Michigan and the Province of Ontario
have programs of comprehensive water quality monitoring for both the St. Clair and Detroit
Rivers. The cross river transects to be used for this study were thus chosen to coincide
with those established and monitored by the agencies of these governments. Since budgetary
restrictions precluded sampling at all stations maintained by these agencies, the stations
surveyed at each selected transect were chosen to provide a representative overview of
each transect area. The stations selected and numbering system followed are presented
in Table 15 and Figure 19.
-58-
-------
TABLE 15. STATION LOCATIONS
River Transect Distance from Western
Station No. (mile point) Shore (ft. ) Station Description
1 SR 39
2 SR 39
3 SR 13
4 SR 13
5 DT 30
6 DT 30
7 DT 30
8 DT 20
.0
.0
. 7
.7
.8
.8
.7
.6
7
400
800
400
1,400
100
1,000
900
50
St. Glair R. at mou
of Lake Huron
St. Glair R. at mou
of Lake Huron
St. Glair R. near
Algonac
St. Glair R, near
Algonac
Detroit River west
of Peach Island
Detroit River west
of Peach Island
Detroit River east
of Peach Island
Detroit River app .
3,400 ft. south of
Ambassador Bridge
9 DT 20.6 1,000 Detroit River app.
3,400 ft. south of
Ambassador Bridge
10 DT 19.0 100 Detroit River at
mouth of Rouge River
11 DT 19.0 2,500 Detroit River at
mouth of Rouge River
12 DT 17.0 E 900 Detroit River at east
side of head of
Fighting Island
13 DT 16.0 W 100 Detroit River below
mouth of Ecorse River
14 DT 16.0 W 4,000 Detroit River below
mouth of Ecorse River
15 DT 14.6 W 100 Detroit River west
side of tip of
Grosse lie
16 DT 11'5 L200 Detroit River east of
Grosse lie at mouth
Rivier Aux Canards
17 DT U-5 4,000 Detroit River east of
Grosse lie at mouth
Rivier Aux Canards
59
-------
TABLE 15. STATION LOCATIONS (cont.)
River Transect Distance from Western
Station No. (mile point) Shore (ft.) Station Description
18 DT 8.7 80 Detroit River in
Trenton Channel at
Elizabeth Park
19 DT 3.9 2,500 Mouth of Detroit Rive
20 DT 3.9 5,500 Mouth of Detroit Rive
21 DT 3.9 13,000 Mouth of Detroit Rive
22 DT 3.9 16,500 Mouth of Detroit Rive
60
-------
Figure 19. Sampling station locations
LAKE HURON
LAKE
ST. CLAIfl
ONTARIO
61
-------
Figure 19.(cont.)- Sampling station locations
X
MICHIGAN
62
-------
Figure 19.(cent.)- Sampling station locations
ECORSE RIVER
MONGUASON CREEK
MICHIGAN
20* 21» 22'
LAKE ERIE
63
-------
CHEMISTRY
Introduction
The existing monitoring program of the various governmental agencies provide a great
deal of information with respect to the more common water quality parameters, such
as oxygen demanding carbonaceous material (BOD and COD), nutrients (nitrogen and
phosphorus species) and some specific toxic materials and heavy metals (iron, phenol and
cyanide). Parameters which have received little attention include the broader range of
heavy metals and pesticides in the aqueous phase, as well as the entire range of materials
present in the sediment phase.
The objective of surveys performed as a portion of this study was the closing of gaps
and deficiencies in the existing data base, as well as providing verification of existing data.
Consequently, the chemical portion of the survey encompassed three basic elements: an
analysis of the aqueous phase, including a broad spectrum of metal ions and pesticides
in addition to the more common water quality parameter;evaluation of the heavy metal,
nutrient, and organic content of the sediment; and a preliminary determination of the
potential for this same material to be released from the sediment into the aqueous phase.
Methodology
Field Sampling -
Insitu measurements of dissolved oxygen, temperature, and specific conductance were made
at measured depths using a remote sensing probe cluster. The oxygen sensing device was
of the polarographic type electrode utilizing a fluorocarbon semipermeable membrane. The
sensing unit was fitted with an agitation device which precluded an oxygen concentration
gradient around the probe. The variation in partial pressure of oxygen as a function
of temperature and depth was compensated for internally by the device. The thermistor
in this oxygen probe was used to sense water temperature and data readout was made
on the same meter by means of switch selection. Insitu measurement of specific
conductance was accomplished through the use of a remote sensing platinum conductivity
cell. Data output was by the direct-reading meter. For all insitu measurements, depth
was determined by calibration of the probe cluster supporting cable.
Water samples for laboratory analysis were taken with a two liter vertical Van Dorn bottle.
64
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Samples were obtained from the surface, approximately half the total river depth, and
approximately one meter from the river bottom, and composited in nonmetallic vessels
for subsequent distribution to proper transport and storage containers. The fraction of
sample for analysis of the Biochemical Oxygen Demand was transferred immediately to
an incubation bottle and refrigerated until it was transported to the laboratory at the
end of the day. Sample fractions for Chemical Oxygen Demand were transferred to glass
containers and were preserved with sulfuric acid (1 ml 1^804 per 100 ml sample) and
refrigerated. One liter fractions of the composite samples were transferred to linear
polyethylene containers and preserved with nitric acid (1 ml HNO3 per 100 ml sample)
for subsequent metal ion analysis. Four liter sample fractions were drawn for the analysis
of chlorinated organics. These samples were stored in reagent quality glass containers
with teflon liners and refrigerated at 4°C until analysis was initiated.
A gravity stratification corer was the primary means for procuring sediment samples,
although during the first survey a Ponar dredge was employed where satisfactory core
samples could not be obtained. Since samples obtained by the Ponar dredge are more
disturbed than those obtained by means of the coring device, efforts were made to reduce
the need for the Ponar. Consequently, for the second and third surveys, the coring device
was modified to provide positive sample recovery whenever the bottom material was
appreciably penetrable. The corer was finned and weighted and outfitted with a positive
retention coring head. The coring tube itself was lined with a removable polycarbonate
sleeve so that core samples could be removed essentially untouched. Upon removal of
the sample, the sleeve was fitted with water-tight end caps so that no loss of interstitial
liquid would occur prior to analysis.
Sediment samples taken by either device were refrigerated on board ship until they could
be transported to the laboratory at the end of each sampling day. Upon receipt in the
laboratory they were frozen and stored at minus 20°C until analysis was initiated.
Analytical Procedures
In general, all methods of chemical analysis were taken from widely approved compilations
of analytical procedures . Where methods were unavailable or insufficient to provide
the desired information, alternate analytical procedures were employed after their accuracy
and precision had been statistically verified. A brief synopsis of the analytical methodology
is contained in the paragraphs that follow.
Aqueous phase - Aqueous samples for the analysis of five-day Biochemical Oxygen Demand
65
-------
were allowed to warm from their refrigerated condition and to equilibrate with
respect to oxygen concentration at 20°C. Initial dissolved oxygen levels were determined,
the vessels were sealed, and the samples were incubated in the dark for five days at 20°
C. Final oxygen levels were measured after this incubation period and the BODg was
calculated. All dissolved oxygen determinations were made by means of a polarographic
electrode device.
The analysis of Chemical Oxygen Demand (COD) in the water samples was accomplished
through the standard potassium dichromate-sulfuric acid reflux method. The dichromate
oxidant was 0.025 JN_ in concentration.
Total concentrations of the metals cadmium, chromium, copper, iron, lead, manganese,
mercury, nickel, and zinc were determined in acidified water samples. High temperature
flameless atomic absorption spectrophotometry was employed for all metals except
mercury, nickel, and zinc. Mercury was analyzed using the cold vapor atomic absorption
technique of Hatch and Ott . Nickel and zinc were analyzed using conventional
air-acetylene flame atomic absorption spectrophotometry. The method of standard addition
was utilized throughout in order to compensate for matrix effects on instrument calibration.
The analysis of water samples for chlorinated organic species was performed in accordance
with the procedures outlined by the Environmental Protection Agency '. The samples
were triple extracted with 15 percent (v/v) ethyl ether in hexane and the extracts dried
with anhydrous sodium sulfate. (All solvents used in the characterization of organic species
were of "Distilled in Glass" quality purchased from Burdick and Jackson, Muskegon,
Michigan.) The extracts were then concentrated and transferred to the top of a column
of florisil (activated at 550 °C for 24 hours). The chlorinated species were eluted with
15 percent ethyl ether in hexane and again concentrated. The concentrations were then
subjected to analysis by vapor phase chromatography utilizing an electron capture detector.
The resultant peaks were integrated either together or discretely to provide either "total
chlorinated hydrocarbon" levels or the concentration of individual pesticide species.
Calibration of instrument response was accomplished using external standards.
Sediment phase - Sediment samples were thawed and extruded from the polycarbonate
sleeve in preparation for subsequent analyses. Physical descriptions were noted while the
sediment was wet. Where core samples were available, the top five centimeter section
was isolated, weighed and placed in an evaporating dish to air dry to constant weight.
In the case of Ponar grab samples, the entire sample was homogenized while wet and
66
-------
a 200 gram subsample was weighed, transferred to an evaporating dish, and air dried.
After the dry weights were recorded, all sediment samples were ground with a mortar
and pestle. Stones larger than five mm were manually excluded. No distinct sieving
of the sediment was undertaken.
The analysis of carbonaceous material in the sediments included the determination of COD
using the potassium dichromate-sulfuric acid digestion method '. Volatile solids were
determined by ashing the samples at 550° C for 24 hours. Kjeldahl nitrogen was measured
by the digestion-distillation-titration technique ^' . Nitrate-nitrogen was obtained by
refluxing the sediment in acid media followed by filtration and reaction with Brucine
sulfate under the controlled temperature conditions of the extended Brucine method '.
Total phosphorus was determined by vanadomolydophosphoric acid test following a
persulfate-sulfuric acid digestion.
Sediment samples for metal analysis (with the exception of mercury) were prepared by
dry ashing at 550 °C for 24 hours, acid leaching the residue with a nitric acid - hydrogen
peroxide solution, and removing the undissolved residue by filtration. The filtrate was
analyzed for cadmium, chromium, copper, iron, lead, manganese, nickel and zinc using
conventional air-acetylene flame atomic absorption spectrophotometry. Mercury analysis
1R
was accomplished using a wet digestion of the sediment . The finely divided samples
were allowed to react overnight with fuming nitric acid and potassium dichrbmate. Excess
hydroxylamine hydrochloride was then added and the sample vessel was degassed.
Reduction of the mercury with stannous chloride was followed by detection of the
elemental mercury using the cold vapor atomic absorption method .
Sediment samples for analysis of chlorinated organic species were taken after they had
air dried to constant weight at room temperature (approximately 25°C). An eight hour
soxhlet extraction was performed using chloroform as the solvent. The extract was
evaporated to dryness on a water bath to remove the chloroform. Caution was exercised
to prevent excessive drying which could result in degradation of the pesticides. The residue
was taken up in 15 percent (v/v) ethyl ether in hexane and the fractions were collected
and concentrated for final detection by electron capture vapor phase chromatography.
Calibration was accomplished by means of external standards. Extraction and clean-up
recoveries were verified using spiked samples.
Sediment exchange experiments - In order to gather preliminary information on the
potential for component exchange from the bottom sediments to the aqeuous phase, a
10 gram sample of dried sediment was agitated in an air-tight vessel containing 250 ml
67
-------
of exchange water. This exchange water for samples from the first survey consisted of
deoxygenated distilled water. However, the lack of hardness and alkalinity in this water
resulted in unrealistic exchange levels and subsequently, exchange experiments for the final
two surveys utilized a synthetic "river water". This synthetic exchange water contained
100 mg/l calcium hardness and sufficient alkalinity to buffer the system to pH 8.25. Such
concentrations approximate fairly closely the major constituents in the St. Clair and Detroit
River waters. Throughout all the exchange studies, the dissolved oxygen of the exchange
water was intentionally less than 0.5 mg/l in order to simulate the most favorable conditions
for exchange - that is, anaerobic conditions - as well as the conditions which are likely
to exist in the river sediments.
The sealed exchange vessels were agitated on a reciprocating shaker (10 cm strokes, 100
cycles per minute) for 10 days at room temperature. The samples were then allowed
to settle for 24 hours and the supernatant was decanted off. No centrifugation or filtration
was employed to remove suspended particulates. Aliquots of the supernatant were used
for subsequent chemical analysis.
The COD of the exchange water was determined by the potassium dichromate-sulfuric
acid digestion procedure. Total phosphorus was measured using acid digestion procedure.
Total phosphorus was measured using the persulfate-sulfuric acid digestion and
vanadomolybdophosphoric acid detection. Nitrate-nitrogen was measured after refluxing
in acid media through the extended Brucine method. Kjeldahl-nitrogen in the exchange
water was isolated by the standard digestion and distillation procedures. However, in
order to provide sufficient sensitivity, the detection of this nitrogen form was accomplished
1V 1R
with an ammonia gas sensing electrode ''I0 .
The metal concentrations in the exchange water were determined by atomic absorption
spectrophotometry. Cadmium, chromium, copper, iron, lead, manganese, nickel, and zinc
were all determined after digesting the exchange samples with nitric acid and hydrogen
perioxide. Mercury was not determined in the exchange waters due to the limited sample
volumes available.
Results
Aqueous phase -
The analytical results obtained on the water samples collected during the three surveys
are summarized in Figures 20 through 30, which present the mean values for each station.
68
-------
The discrete values obtained for each individual sample are presented in the Appendix,
Tables A-1 through A-7. Throughout this discussion, notation is based on station number,
rather than river mile and distance from shore. These station numbers are defined in
Figure 19 and Table 15.
Dissolved oxygen - The data resulting from the insitu measurement of dissolved oxygen
is presented in the Appendix, Tables A-1 through A-3. Analysis of this data reveals that
during the summer survey (August 1973) the overall dissolved oxygen level rose slightly
from the head of the St. Clair River to its mouth (8.3 to 8.7). Very little variation
in dissolved oxygen concentrations was observed as a function of depth, with the exception
of station 1, which had a somewhat higher concentration at the surface. No dissolved
oxygen levels below 6.0 mg/l were observed at any station or depth. More substantial
variation in dissolved oxygen concentration as a function of depth was observed in the
Detroit River during this survey. Although the dissolved oxygen concentration at the
surface was 6.7 mg/l or greater at all stations, half of the stations exhibited values below
6 mg/l at depths ranging from 3 to 10 meters (10 to 34 feet). The overall average dissolved
oxygen concentration was observed to drop from a value of 7.6 mg/l at the head end
of the river to 7.0 mg/l at the mouth.
During the November survey, dissolved oxygen levels were generally higher than during
the previous survey, undoubtedly due to the higher oxygen solubility at the lower
temperature. The two very low values reported at station 1 are probably due to equipment
malfunction. A greater variation of dissolved oxygen with respect to depth was observed
in the St. Clair River and the head of the Detroit River. The levels were more constant
with depth in all of the Detroit River other than the headwaters.
Dissolved oxygen levels of less than 6.0 mg/l were observed in the St. Clair River at stations
2 and 4 near the bottom. The Detroit River yielded only two values below 6.0 mg/l.
These were recorded in 24 feet of water at stations 5 and 6. During this November
survey, the net change in dissolved oxygen from the head to the mouth of the Detroit
River was an increase of about 3 mg/l.
The May survey indicated very little dissolved oxygen gradient as a function of depth
in either of the two rivers. Similarly, neither of the rivers exhibited dissolved oxygen
concentrations below 6.0 mg/l. There was no net change in the average dissolved oxygen
from the head to the mouth of the St. Clair River, while the average concentration in
the Detroit River decreased from 11.6 to 10.9 mg/l between the head and the mouth.
69
-------
Temperature - Virtually all stations appeared to be relatively homogeneous from surface
to maximum depth with regards to temperature during all three surveys. The temperature
differential between upstream and downstream stations followed different patterns in the
two river systems. In the St. Clair River, the average temperature decreased 1.4°C at
the time of the August survey, and increased 0.9°C at the time of the May survey, with
no change being evident during the November survey. The Detroit River was observed
to experience a temperature increase during all three surveys, amounting to 1.7°C in August,
0.5°C in November, and 3.I°C in May.
Specific Conductance - Specific conductance was measured insitu at each station during
each of the three surveys. (Tables A-1 through A-3.)
A survey of the specific conductance data reveals a reasonably well-defined trend of
increasing conductance (and hence increasing dissolved ion concentration) as the waters
progress from the head of the St. Clair River, through Lake St. Clair and subsequently
to the mouth of the Detroit River. The net overall effect observed in the August survey
is an increase in conductance of 50 percent. Such a trend is not evident in the data
from the November survey. Indeed, no net change was observed through the total system.
During the May survey, the trend of increasing conductance was again evident, though
the net increase through the total system amounted to only about 40 percent.
Biochemical Oxygen Demand - Analysis of the biochemical oxygen demand (BOD) data,
presented in Figures 20 and Tables A-4 through A-6, indicates that the BOD load entering
the St. Clair River is relatively small. Mean BOD levels at station 3 and 4 in the St.
Clair River is relatively small. Mean BOD levels at station 3 and 4 in the St. Clair River
are only slightly higher than the upstream stations 1 and 2. Very little change in the
mean BOD is observed in the Detroit River prior to stations 10 and 11. At this point
the loadings from the Rouge River and adjacent industrial and municipal outfalls are
reflected in the elevated BOD at station 10. Waters on the Canadian side of the river
at this milepoint are still relatively unaffected, with BOD levels essentially the same as
influent waters from Lake St. Clair (stations 5-7). The elevated BOD is evident at all
stations along the western shore of the river from station 10 to the point of entry into
Lake Erie. At the same time, the BOD in and to the east of the shipping channels appear
to remain essentially constant to the interface with Lake Erie.
Chemical Oxygen Demand - Chemical Oxygen Demand (COD) data for the aqueous phase
follow much the same pattern as BOD (Figure 21 and Tables A-4 through A-6). Little
difference is seen in the values from the headwater and mouth stations of the St. Clair
70
-------
Figure 20. Mean biochemical oxygen demand
water
(ing/ 1)
-
LAKE HURON
LAKE
ST. CL/Ufl
71
-------
Figure 2Q.Mean biochemical oxygen demand
(continued)
72
-------
Figure 20.Mean biochemical oxygen demand
(continued)
water
(mg/1)
-
19. 20* 2> 22
C.*KE CRIE I
MICHIGAN
73
-------
Figure 21.Mean chemical oxygen demand
74
-------
Figure 21.Mean chemical oxygen demand
(continued)
waeer (mg/l)
sediment (fflg/g)
LAKE HURON
SOUTH CHANNEL
CAKE
ST. CL.UH
75
-------
Figure 21.Mean chemical oxygen demand
(continued)
76
-------
River. No appreciable differences are observed in the Detroit River until stations 10 and
11. At station 10 the COD approximately doubles - following the same pattern as the
BOD at that station. By contrast, COD values for station 11 remain close to the level
observed at stations 5, 6, and 7. An evident increase in COD is seen at station 12 in
the Canadian waters, where only a very slight increase in mean BOD was observed. As
in the case with BOD, elevated COD values are noted at all stations along the United
States shore of the river. Canadian waters below station 12 are only slightly higher in
COD than the influent water from Lake St. Clair.
Trace metals - A major consideration in the chemical field monitoring program was to
provide information on the concentrations of trace metals in the water column. Since
little historical data was available, the information generated during this phase of the study
would serve as a preliminary step in diagnosing the condition of the rivers in terms of
trace metals. Nine metals were chosen for study, primarily on the availability of relevant
toxicity information. The metals included were: cadmium, chromium, copper, iron, lead,
manganese, mercury, nickel and zinc.
Mean cadmium concentrations in the water column (Figure 22) do not vary appreciably
from the head of the St. Clair River to the confluence of the Rouge River with the
Detroit River. At station 10 the mean cadmium concentration rises approximately 67
percent over levels observed upstream. This level is maintained downstream along the
United States shoreline and into the Trenton Channel. At station 18, below most of
the industrial outfalls on the United States shore, the mean cadmium concentration rises
to three times the levels observed at stations 5, 6, and 7. This level falls off only slightly
by the time the water reaches station 19. Cadmium levels in the remainder of the Detroit
River remain essentially the same as background levels until stations 21 and 22 where
mean concentrations are approximately 33 percent higher than influent water from Lake
St. Clair.
Chromium results are summarized in Figure 23. Unlike cadmium, a variation in aqueous
chromium levels does occur in the St. Clair River stations and the upriver stations of
the Detroit River (stations 5-9). Mean levels range from 2.7 to 6.1 y g/l, with station
1 being the lowest and station 3 the highest. The levels above station 10 in the Detroit
River vary from 4.3 to 12.1 yg/l. From station 10 downstream along the United States
shore to Lake Erie, chromium concentrations remain high (10.8 to 17.1 yg/l). The
remainder of the downriver stations reflect concentrations which do not vary appreciably
from background levels at stations 5, 6, and 7.
Mean copper concentrations observed in the water column are presented in Figure 24.
77
-------
Figure 22.Mean cadmium concentration
water (ug/1)
ladimenc (mg/kg)
MICHIGAN
LAKE HURON
SOUTH CHANNEL
ST
78
-------
Figure 22.Mean cadmium concentration
(continued)
79
-------
Figure 22 .Me_aj\_ f^dmjLjarn concentration
continued;
80
-------
Figure 23.Mean chromium concentration
wacer (ug/1)
sediment (mg/kg)
LAKC MUROM
ST.
81
-------
Figure 23. Mean .chromium concentration
(continued)
82
-------
Figure 23.Mean chromium concentration
(continued)
83
-------
Figure 24.Mean copper concentration
water (ug/1)
sediment (mg/kg)
LAKE HUnON
LAKE
ST. CLAII1
84
-------
Figure 24.Mean copper concentration
(continued)
85
-------
Figure 24.Mean copper concentration
(contimSedT
19. 20* 2> 22 •
LAKE CRIE
86
-------
Differences in the mean concentrations in the St. Clair River indicate slightly higher levels
of this metal at Stations 1 and 4. Waters entering the Detroit River from Lake St. Clair
contain between 4.6 and 7.1 yg/l of total copper. A substantial enrichment is seen
along the United States shoreline as early as station 8. The concentrations rise even higher
at stations 10 and 13 (12.3 and 15.0 yg/l respectively), and remain elevated along the
western shore until the waters enter Lake Erie at station 19. Unlike heavy metals already
reviewed, mean copper levels are elevated at the mid-river station 14. (This level is due
primarily to a very high level observed during the May survey.) Along the Canadian
shoreline, no appreciable change is seen in copper concentration from the influent levels
of Lake St. Clair until station 22 (Lake Erie interface).
Lead levels in the St. Clair River were observed to remain essentially constant from the
headwater to the mouth (Figure 25). Mean concentrations in the water column remain
around 2 yg/l. Influent water to the Detroit River are also of this concentration. Elevated
levels are observed on both sides of the river as early as stations 8 and 9, although
contamination along the United States shore is by far more evident. Waters at station
10 are approximately three times the background concentration, while the waters
downstream on the United States side reach five times the background level. The evidence
of the lead loadings is notable at stations 19 and 20. The Canadian waters do undergo
some enrichment in lead as they move downstream, however the mean concentrations
observed in this area never equal the corresponding values in waters along the western
shore.
Data on aqueous mercury levels were collected during the November and May surveys
only. This information is summarized in Figure 26 and presented in Tables A-5 and
A-6. Mean mercury concentrations in the St. Clair River range between 1.3 and 4.6 yg/l,
with the upstream stations averaging approximately twice the level of the downstream
stations. Influent waters to the Detroit River show a two-fold increase in this heavy
metal over stations 3 and 4 in the lower St. Clair River - apparently the result of activity
in the Lake St. Clair basin. No further enrichment is seen throughout the entire length
of the Detroit River, with the notable exception of station 12. At this point, total mercury
in the water column averages 6.4 y g/l. It should be noted that a rather substantial
difference was observed between aqueous mercury levels recorded during the November
survey and the May survey with substantially higher levels observed in November. In
Q
general, observed values were higher than EPA recommended levels .
Nickel concentrations in the aqueous phase was monitored during all three field surveys.
Mean concentrations are presented in Figure 27. A review of the mean values indicates
87
-------
Figure 25. Mean lead concentration
water (ug/1)
sediment (mg/kg)
LAKE HURON
ONTARIO
1.9
104
__»_ 3
W4
2.1
27
LAKE
ST. CLAIM
88
-------
Figure 25.Mean lead concentration
(continued)
89
-------
Figure 25.Mean lead Soncentration
(continued)
90
-------
Figure 26.Mean mercury concentration
water (ug/1)
sediment (mg/kg)
LAKE HURON
LAKf
ST. CLAIH
91
-------
Figure 26..Mean. merciiry concentration
6 CcontinuedT
92
-------
Figure 26.Mean mercury concentration (continued)
19. 20* 21* 22 •
LAKE CRIE
93
-------
Figure 27.Mean nickel concentration
water (ug/1)
sedtmenc (mg/kg)
LAKE HURON
18
37
-*- 3
ALGONAC
A=>^
14
44
ST.
94
-------
Figure 27.Mean nickel concentration
(continued)
95
-------
Figure 27.Mean nickel concentration
(continued)
96
-------
-------
Figure 28.yiean .zinc concentration
water (ug/L)
sediment (mg/kg)
LAKE HURON
MICHIGAN
ONTARIO
52
86
_^_ 3
ALGONAC
7* -*-
82
91
SOUTH CHANNEL
LAKE
ST. CLAin
98
-------
Figure 28.Mean zinc concentration
(continued)
water (ug/1)
sediment (mg/kg)
X
99
-------
Figure 28.Mean zinc concentration
(continued)
84
346
.
I
J_ 19. 2
7 ''
Y ft", ^A
\ '-'; ^9
65
270
21» 22 •
LAKE ERIE
100
-------
Figure 29.Mean manganese concentration
water (ug/1)
sediment (mg/kg)
LAKE MUnON
LAKE
ST. C LA 111
101
-------
Figure 29.Mean manganese concentration
(continued)
102
-------
Figure 29.Mean manganese concentration
(continued)
19. 20" 21- 22
/LAKE CR1E
103
-------
Figure 30. Mean iron concentration
water (ug/l)
sediment (mg/g)
I
—<&—
SOOTH CHANNEL
LAKE
ST. CLAIIl
104
-------
Figure 30.Mean iron concentration
(continued)
105
-------
Figure 30.Mean iron concentration
(continued)
106
-------
recorded for station 7 is more than ten times higher than that of stations 1 and 2. Iron
at stations 8, 9, and 11 remain somewhat over 500 yg/l, however the mean level recorded
at station 10 was 1780 yg/l. Station 12 is similarly enriched. Waters along the United
States shoreline remain heavily enriched in iron through station 19 where the total iron
concentration averages 2,300 yg/l. Canadian waters below station 11 are also enriched,
with mean values never falling below 830 yg/l.
Pesticides - In addition to the monitoring of heavy metals, an important area of investigation
in the chemical field survey program included toxic organic substances, particularly
chlorinated pesticides. In an attempt to obtain a preliminary indication of the level of
these substances in the water column, samples were collected during the August 1973
survey for analysis of the gross level of chlorinated hydrocarbons present. (In such an
analysis the species present in a routine analysis for chlorinated pesticides are not
differentiated, but rather the total area of a vapor phase chromatogram is integrated as
a unit and the results are present in terms of some arbitrary chlorinated hydrocarbon
standard.) Results of these analyses are contained in the appended Table A-4. The first
survey indicated fairly uniform levels in the St. Clair River with the exception of station
1 which was about 35 percent higher than the other three stations. Levels in the influent
waters to the Detroit River were somewhat lower than in the St. Clair River, but were
observed to have increased in concentration by the time they had reached stations 10
and 11. The only further increases were reported at station 18 below most of the industrial
outfalls along the Trenton Channel, and station 21 at the interface with Lake Erie.
Following requests by the federal project monitor and state environmental agency
personnel, the analysis for gross chlorinated hydrocarbon content was replaced by analysis
for specific chlorinated pesticides on samples taken during subsequent surveys. Included
in the list of pesticides determined were endrin, aldrin, dieldrin, lindane, heptachlor,
heptachlor epoxide, DDT, ODD, and DDE. Polychlorinated biphenyls were not included
in the discrete analyses, though such substances are included in the chlorinated hydrocarbon
analysis carried out on the August 1973 samples. The results of the discrete pesticide
analysis are presented in the Appendix, Table A-7. A review of this data reveals substantial
variation throughout the St. Clair and Detroit River systems. However, since rigorous
interpretation of discrete pesticide levels is beyond the scope of this project, the data
presented in this report serves primarily to add to the relatively limited bank of information
available on discrete pesticide concentrations in these two river systems.
Sediment Phase -
The sampling program for the sediment phase was conceived primarily to provide
information on this relatively neglected portion of the St. Clair and Detroit River systems.
107
-------
This program was not designed as a comprehensive evaluation of sediment history in tho
river bottoms, but rather it was intended to provide a preliminary characterization of
the sediment condition of these rivers. As a result, analyses were limited to determining
total sediment content of a given constituent, rather than differentiating the various forms
of the constituent as a function of particle size distribution. Eh, pH, and/or depth.
The parameters to be studied during the sediment surveys were chosen to include
carbonaceous loadings, the biological nutrients nitrogen and phosphorus, the most common
heavy metals, and chlorinated organic species. A brief description of sediment morphology
was recorded for each sample collected. A compilation of all the sediment data generated
during the three surveys is contained in the appended Tables A-8 through A-11.
Summarized data for many of the parameters are presented in figure form within the
body of this report. The values indicated in such figures represent the arithmetic average
of all data for a given parameter gathered at a particular station during the three surveys.
In some cases the average is calculated from less than three values, and in a few instances
no mean value is reported at all. Sediment samples were not always obtainable by the
methods employed, therefore, certain sampling stations have no recorded sediment data
for one or more of the sampling dates.
Mean values for Chemical Oxygen Demand (COD) are presented in Figure 21. Review
of this data indicates an apparent increase in the sediment COD burden as the St. Clair
River travels from Lake Huron to Lake St. Clair. This increase amounts to approximately
a doubling of the COD concentration. Sediments at the head of the Detroit River (stations
5, 6, and 7) are approximately half that observed at the mouth of the St. Clair River
(stations 3 and 4). Progressing down the Detroit River, a substantial increase in the
background COD is seen at station 8, while the value recorded in the Canadian waters
at that milepoint (station 9) is relatively low. Mean values for stations in Canadian waters
below this milepoint are relatively constant at 40-50 mg/kg to the Lake Erie interface.
Stations along the United States shore, however, are varied and generally exhibit much
higher concentrations than the Canadian counterparts. Sediment concentrations at stations
10, 13 and 19 are about an order of magnitude higher than those at the head of the
river. Physical descriptions of the samples taken at these three stations further indicate
that these are areas where organic deposition is appreciable.
The Kjeldahl-nitrogen values, recorded in Figure 31, characterize the reduced nitrogen forms
present in the river sediments. From this data it is evident that some increase in the
mean level of reduced nitrogen forms in the sediment does occur as the waters of the
St. Clair River descend from Lake Huron. In comparison to station 1 this increase is
108
-------
Figure 31.Mean kjeldahl nitrogen concentration
sediment
(mg/kg)
LAKE MUROM
LAKE
ST. CLAin
109
-------
Figure 31. Mean Jcjel
(continue
nitrogen concentration
sediment
(rag/kg)
110
-------
Figure 31.Mean kj'eldahl nitrogen concentration
(continued)
sediment
(mg/kg)
19. 20* 21* 22»
LAKE CRIC
MICHIGAN
111
-------
relatively small, but when compared to the very low level recorded at station 2, this increase
becomes appreciable. Mean concentrations recorded at the head of the Detroit River are
about 300 mg/kg lower than stations 3 and 4 in the St. Clair, ranging between 310 and
430 mg/kg. As in the case of COD, Kjeldahl-nitrogen enrichment occurs at station 8
along the United States shore, while sediments underlying Canadian waters at the same
river mile (station 9) show little change from values recorded at the head of the river.
The sediments along the United States shore, beginning with station 10, show every
appreciable enrichment in reduced nitrogen forms all the way downstream to the Lake
Erie interface. Mean values at stations 10, 13, 19 and 20 range between 1140 and 2220
mg/kg. Canadian sediments, beginning at station 12, show significant enrichment also.
Mean values recorded at stations 16 and 17 are over 1000 mg/kg, and the mean at station
21 is 690 - almost twice the level recorded at the head of the river.
One of the oxidized forms of nitrogen-nitrate - was measured in the sediment samples
and the mean concentrations are recorded in Figure 32. Levels for the St. Clair River
do not indicate any appreciable difference in this nitrogen from between the head and
mouth of the river. Stations 1 and 4, however, are notably higher (about 100 percent)
than stations 2 and 3. Mean values at the head of the Detroit River range from 66
to 93 mg/kg (as nitrogen). Descending down the river, some increase is seen at stations
9 and 10, however the only appreciable differences observed in the Detroit River sediments
occur at stations 13, 19, and 20. The mean concentrations recorded at these stations
range from 228 to 359 mg/kg.
The level of total phosphorus in the sediment samples was determined to provide
information on any accumulation of this biostimulant in the sediment phase. Overall mean
concentrations for this parameter are presented in Figure 33. Values for the St. Clair
River stations indicate some accumulation of phosphorus in the surface sediments as the
river descends from Lake Huron. As was observed for Kj eldahl and nitrate nitrogen,
phosphorus levels at station 2 appear to be appreciably lower than other areas surveyed
in the St. Clair River (370 mg/kg versus 620 to 960 mg/kg). Mean phosphorus
concentrations at the head of the Detroit River range between 570 and 850 mg/kg.
Sediment levels further downstream in the Detroit River show appreciable enrichment over
these background levels at stations 10, 13, 15, 17, 19, and 20. Enrichment in the mean
concentrations of stations 15 and 17 amounts to about 30 percent. At station 10 the
increase is approximately 100 percent. Sediment from station 13 averages more than
3600 mg/kg. Station 20 at the Lake Erie interface records a mean concentration of 1070
mg/kg. Station 19, however, is by far the most phosphorus rich sediment observed during
the study. With an exceptionally high average of 5160 mg/kg, the sediment at this
112
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Figure 32.Mean nitrate nitrogen concentration
sediment
(mg/kg)
LAKE HURON
LAKE
ST CLA1I1
113
-------
Figure 32.Mean nitrate nitrogen concentration
(continued)
sediment
(mg/kg)
114
-------
Figure 32.Mean nitrate nitrogen concentration
(continued)
-------
Figure 33.Mean total phosphorous concentration
ledimene
(»g/VCB)
LAKE HURON
LAKE
ST. ClAln
116
-------
Figure 33. Mean total phosphorous concentration
(continued)
sediaent
(mg/kg)
LAKE ST. CLAIR
L17
-------
Figure 33.Mean total phosohorous concentration
(continued)
(•dimenc
(ng/kg)
19. 20* 2> 22«
LAKE C!JI£
MICHIGAN
118
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station is enriched by more than 4000 mg/kg over sediment at the head of the Detroit
River.
Sediment samples were analyzed for the same heavy metals as in the aqueous samples.
These analyses included cadmium, chromium, copper, iron, lead, manganese, mercury,
nickel, and zinc. As previosuly noted, discrete analytical results are contained in appended
Tables A-8 through A-10, while analytical averages are presented in figure form throughout
the text of this report.
Average cadmium concentrations for the St. Clair and Detroit River systems are presented
in Figure 22. Values for the stations in the St. Clair range from 0.5 to 2.9 mg/kg, with
station 2 reporting the very low level of 0.5 mg/kg.Essentially no difference is seen in
the level of sedimentary cadmium between the upstream and downstream stations of this
river. Levels of 0 to 4 mg cadmium per kg dry sediment are common for glacially derived
sediment. Thus the levels observed in the St. Clair River indicate little anthropogenesis
of this very toxic heavy metal. Cadmium concentrations at stations 5, 6 and 7 in the
Detroit River are similarly low. As the river descends toward Lake Erie, however,
enrichment in cadmium is observed at stations 10, 13, 19 and 20. At station 10 a mean
concentration of 6.2 mg/kg is reported. The mean value at station 13 is 8.5 mg/kg -
more than four times the background levels at the head of the river. The sediments
at stations 19 and 20 contain 7.6 and 6.5 mg/kg respectively. This amounts to a net
enrichment of approximately 200 percent over background levels. Elsewhere in the Detroit
River, enrichment in sedimentary cadmium is neglibible.
The summarized results of sediment chromium analyses are presented in Figure 23. Mean
concentrations upstream in the St. Clair River range between 20 to 30 mg/kg. The
downstream stations 3 and 4 report mean levels of 39 and 80 mg/kg respectively. The
increase at station 4 appears to be relatively significant. Similarly, the mean concentration
recorded at station 5 in the Detroit River is considerably higher than those recorded at
stations 6 and 7. Background levels of 30 to 40 mg/kg are present in most of the less
polluted areas of the Detroit (e.g. stations 6, 7, 14, 16 and 17). Chromium enrichment
occurs principally at stations 10, 13, 19 and 20. From the mean values reported in Figure
23, some enrichment may also be occurring at stations 8 and 21. An exceptionally high
chromium concentration (2680 mg/kg) was recorded at station 13 during the August 1973
survey, which accounts in large part for the very high mean value reported for this station.
A notable phenomenon concerning chromium in the sediments lies in the fact that, in
general, the concentrations determined were lower on each succeeding survey. Whether
119
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this resulted from scouring, release of this material due to solubility relationships, or some
other phenomenon could not be determined.
Sediment copper concentrations are presented in Figure 24. The mean concentrations
recorded in the St. Clair River range from 11 to 16 mg/kg, with the highest value recorded
at station 1 and the lowest at station 2. The limited range of the values observed in
the St. Clair River indicates little anthropogenic influx of this trace metal. Copper levels
in the sediment at the head of the Detroit River are comparable to those of several in
the St. Clair River. Substantial enrichment along the United States shore occurs as early
as station 8. The mean concentration at station 10 is 87 mg/kg. At station 13 the
average is 116 mg/kg - nearly an order of magnitude higher than background levels at
the head of the river. Stations 19 and 20 also show the presence of anthropogenic copper.
Sediments in Canadian waters undergo little, if any, enrichment.
Average lead concentrations are presented in Figure 25. Values from the St. Clair River
show appreciable variation. While a relatively low level (6 mg/kg) is recorded at station
2, stations 1 and 4 exhibited values of approximately 30 mg/kg. A relatively high level
of 104 mg/kg was recorded at station 3, although this value is largely the result of an
exceptionally high concentration recorded on the sample taken in August 1973 (see
appended Tables A-8 through A-10). Sediments at the head of the Detroit River range
from 15 to 30 mg/kg, values which are common in deep-water sediments of glacial origin.
With the exception of certain stations along the United States shore, mean sediment lead
levels throughout the river fall into this range. At stations 8, 10, 13, 19 and 20, the
effect of anthropogenic lead is obvious from the very high mean concentrations observed.
A slight increase over background levels is observed at stations 13 and 21 also.
Mercury concentrations in the river sediments were determined on samples taken during
the November and May surveys. The summarized results of these analyses are presented
in Figure 26. Mean values for the St. Clair River sediments are relatively low, ranging
from 0.06 to 0.53 mg/kg. Station 4 records the highest concentration in the St. Clair
River, 0.53 mg/kg, though interpretation of this fact is hindered by the very limited number
of samples analyzed for mercury. Sediments at the head of the Detroit River have mercury
content similar to those of the St. Clair River, averaging 0.19 to 0.50 mg/kg. All
downstream stations in the Detroit, with the exception of 10, 12, 13, 19 and 20, fall
into this general range. Mean levels for stations 13 and 20 are only slightly higher than
the background concentrations. The mean values for stations 19 and 10, however, are
three and four times the maximum background, respectively. The average concentration
for station 12 is approximately an order of magnitude higher than background levels.
120
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This high value is due to the relatively high mercury content of the November sediment
sample from station 12 (see appended Table A-9). In order to evaluate the credibility
of this value, the analytical accuracy of this particular determination was checked and
found to be correct. In addition, it is interesting to note that the high sediment content
recorded at this point during November correlates well with a relatively high aqueous
mercury concentration observed at station 12 during the same sampling period (see
appended Table A-5).
Sediment nickel content was determined on all river bottom samples taken during the
August, November, and May surveys. The summarized results of these analyses are
presented in Figure 27. Mean values for the St. Clair River sediments range from 10
to 44 mg/kg, with the lowest level again at station 2 and the highest at station 4. From
the values in this figure, there is an apparent increase in nickel as the river descends from
Lake Huron. This observation should be tempered with the fact that the nickel
concentrations observed in sediments taken throughout the St. Clair River are within the
range found naturally in unpolluted sediment of this type. This is equally true for the
mean values observed at the head of the Detroit River (ranging from 24 to 32 mg/kg).
Elsewhere in the Detroit River, stations along the United States shoreline show no
appreciable enrichment over background except for stations 13 and 19, which average
142 and 66 mg/kg respectively. A lesser increase is apparent at stations 10, 12, 15 and
18, though the levels observed at these points are comparable to those of stations 3 and
4 in the St. Clair River.
Average sedimentary zinc concentrations are presented in Figure 28. In the case of zinc,
a substantial enrichment is seen in downstream sediments of the St. Clair River over
background levels of the upstream sediment. Mean values at stations 1 and 2 are 59
and 33 mg/kg, respectively, whereas those at stations 3 and 4 are 86 and 91 mg/kg,
respectively. Mean concentrations at the head of the Detroit River vary between 44 and
81 mg/kg. Although this is a substantial gradient for samples from the same milepoint,
values from 20 to 100 mg/kg are normally encountered in unpolluted deep-water glacial
clays of the type found at this milepoint. Thus the possibility exists that the gradient
may result from such natural causes as variation in particle type and size, rather than
anthropogenic influxes of zinc. Mean concentrations along the Canadian shore, with the
exception of stations 12 and 21, lie within the range observed at the head of the river.
Station 12 shows significant enrichment in sedimentary zinc, as does station 1. Along
the United States shoreline, a vast amount of zinc has found its way into the sediment
at station 10. The mean concentration recorded here was 385 mg/kg. The situation
is similar at station 13 where the average was 335 mg/kg. The zinc content drops somewhat
at station 15, to an average of 97 mg/kg. However, the Lake Erie interface stations
of 19 and 20, which receive the waters from along the United States shoreline, record
121
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average concentrations of 346 and 270 mg/kg, respectively. Such levels indicate very
significant inputs of anthropogenic zinc.
Manganese in the sediment phase is of paritcular interest for its sorption ability when
present as a hydrous metal oxide. Like iron, it plays an important role in retaining metals
and nutrient species in the bottom sediments. Mean values for sedimentary manganese
are presented in Figure 29. Sediments from the head of the St. Clair River average 190
to 380 mg/kg, while those at the downstream stations are somewhat higher at 430 and
580 mg/kg. Thus, as with aqueous manganese concentrations, there appears to be an
increase in sedimentary manganese as the river descends from Lake Huron. Mean values
at the head of the Detroit River range from 370 to 420 mg/kg - somewhat less than
the lower stations in the St. Clair River. Canadian waters downstream in the Detroit
River show little enrichment in sedimentary manganese to the Lake Erie interface. United
States stations are generally higher than corresponding Canadian stations, though, with
the exception of station 10, they do not show major changes in the sediment manganese
loadings.
Because of its sorption characteristics, iron is one of the most important constituents
in the sedimentary environment. Its role in regulating sediment exchange processes is
19 20 21
well documented ' ' . Primarily for this reason, iron was determined in all sediment
samples taken during the August, November, and May surveys. Mean values for these
analyses are presented in Figure 30. A review of this data indicates a net increase in
sedimentary iron as the St. Clair River descends from Lake Huron. Mean concentrations
recorded at stations 1 and 2 are 12,300 and 4,300 mg/kg respectively, while those at
the downstream stations 3 and 4 are 16,900 and 19,100 mg/kg, respectively. Iron content
of the sediment at the head of the Detroit River averages between 12,500 and 13,100
mg/kg - very close to that observed at station 1 in the St. Clair River. Elsewhere in the
Detroit River sediments show appreciable variation, from a low of 7,800 mg/kg at station
14 to a high of 27,100 mg/kg at station 10. The highest mean concentrations found in
the Detroit River occur along the United States shoreline, where other heavy metal
enrichment was observed (stations 10, 13 and 19).
In addition to nutrient and heavy metal analysis an attempt was made to determine the
chlorinated organic species present in the sediment samples collected during the three
surveys. Due to the large background of other organic materials present in the majority
of the river sediments, it was not possible to obtain satisfactory results with currently
available analytical techniques.
122
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Sediment Exchange -
The sediment exchange studies were designed to investigate procedures for estimating the
potential input of chemical constituents from the bottom sediments into the aqueous phase.
The influence of such an input on the water quality of the river can be important in
the formulation of a mathematical model of the river basin, and in projecting future water
quality. Estimation of sediment exchange inputs, however, is difficult and at present
can only be accomplished through empirical methods. Such ethods as reported Such
methods as reported in the literature are widely divergent in terms of technique and are
usually tailored to specialized simulations. Consequently, the procedures used during this
study were varied and modified in an attempt to find a satisfactory compromise in
simulating conditions which exist in the two river basins of concern.
The experimental systems used on sediments from the three field surveys have been
described earlier. The only major change after the onset of the experiments was the
substitution of "synthetic river water" for reagent water as the exchange medium for
sediments obtained during the November and May surveys. This synthesized river water
contained calcium hardness and carbonate alkalinity in concentrations closely
approximating those found in the actual river water. This substitution had profound effects
in the exchange levels of certain constituents.
The results of the exchange experiments are presented in the appended Tables A-12 through
A-14. The parameters represented in this table include Chemical Oxygen Demand (COD),
Kjeldahl nitrogen, nitrate-nitrogen, total phosphorus, cadmium, chromium, copper, iron,
manganese, nickel, lead, and zinc.
Reviewing the data in Appendix Tables A-12 through A-14, the exchangable quantity of
COD in the November and May sediments ranged from less than 0.1 percent to 2.49
percent. The use of adjusted-hardness water had apparently little effect on the exchangable
COD. Kjeldahl-nitrogen, on the other hand, seemed to be substantially affected by the
use of "synthetic river water". Values for the November and May sediments ranged from
1.0 to 6.1 percent, while those of the first experiment (August sediments) were much
higher. The effect on nitrate-nitrogen was not so evident. While exchange values for
the experiments using "synthetic river water" ranged from 0.21 to 27.2 percent, the values
from the August samples were observed to fall both above and below this range. Total
phosphorus exchange did not appear to be affected by the medium change. Values for
the November and May sediments ranged from 0.21 to 4.58 percent, while those from
August were generally in this same range. The affect of carbonate hardness was quite
apparent on the exchange coefficients of five of the metals studied. Copper exchange
123
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in the "synthetic river water" ranged from 0.02 to 0.5 percent (November and May
surveys), while values as high as 55.2 percent were observed with reagent water medium.
Iron was exchanged at between 0.07 and 3.50 percent in experiments with the November
and May sediments, while the August sediments exchanged to a much greater extent with
the reagent water medium. The effect was very similar with manganese, which exchanged
from 0.18 to 4.27 percent in the "synthetic river water". Nickel exchange values in
the adjusted - hardness water ranged from 1.2 to 4.8 percent. Though insufficient analytical
sensitivity was established for nickel during the first exchange experiment, the one value
that is reported is much higher than the corresponding values from subsequent experiments
in which the "synthetic river water" was used. Zinc, was most affected in the use of
water with carbonate alkalinity. Whereas exchange waters during the first experiment
reagent water leached from 10.4 to 97.4 percent of the total sedimentary zinc, the use
of "synthetic river water" dropped the exchange efficiency into the 0.3 to 5.9 percent
range. Cadmium, chromium, and lead exhibited only slight variations between exchange
in the two media.
Discussion
Aqueous phase - In discussing the condition of the aqueous phases of the St. Glair and
Detroit River systems, it is advantageous to deal with each of the rivers individually. The
St. Clair River, being a narrow, deep, and rapid flowing body is distinctly different from
the generally wider and lower velocity Detroit River.
The hydrology of the St. Clair River and the relative abundance and placement of industries
along the river reflect themselves directly in the water quality of the river system. Data
gathered during the present study indicate that dissolved oxygen, temperature and specific
conductance are only slightly influenced by inputs to the river system. The velocity and
turbulence in the river virtually preclude concentration gradients of any appreciable
magnitude.
Some influence by pollutional inputs is seen in the area of oxygen demanding material
(BOD and COD), though this influence is relatively small. Heavy metals in the aqueous
phase of the St. Clair River are enriched at certain points, particularly stations 1 and
4, though the magnitude of the enrichment limits the physical significance of the inputs.
The same holds true for chlorinated organic species.
The Detroit River system is rather a different case. The physical geography of this system
is such that a large percentage of the shoreline is covered by residential and industrial
124
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development, thus the pollutional inputs to this river system are much greater in magnitude.
This is compounded by the somewhat slower velocity and the presence of backwater areas.
The result is that pollutional inputs have a significant effect on the water quality in the
Detroit River.
Dissolved oxygen in the Detroit River shows much greater variation than in the St. Clair
River, especially during the summer months when water temperature rises. At certain points
in the river, particularly along the United States shore and downstream from the Rouge
River, the dissolved oxygen concentrations dip to undesirable levels. At station 19, where
the river velocity is drastically reduced, oxygen demanding materials further deplete the
available DO.
The distribution of oxygen demanding materials in the Detorit River follows closely the
distribution of heavy metals and other contaminants. Generally, the most polluted areas
lie downstream from the Rouge River. From station 10 south to Lake Erie, the waters
adjoining the United States shoreline are highly enriched in a wide variety of contaminants.
Waters adjoining the Canadian shoreline at station 12 seem also to be carrying an
appreciable pollutant burden - particularly mercury.
One very significant increase in the aqueous phase of both the St. Clair and the Detroit
Rivers which was noted during the field surveys was total iron. The net increase through
the combined St. Clair-Detroit River systems amounts to more than an order of magnitude.
Where mean concentrations of less than 100 mg/l are present in the headwaters of the
St. Clair River, waters entering Lake Erie from the Detroit River contain 830 to 2,300
mg/l, on the average. Such an enrichment is particularly significant because of the sorption
potential of hydrous iron oxides for heavy metals and biostimulants such as phosphorus
. In addition, there is some evidence that such a shift in aqueous iron concentrations
can result in a shift in the dominant type of algae from greens to more undesirable
0|T
blue-greens .
Sediment Phase - As stated earlier, the intent of the sediment analysis program was to
provide information on an important area of the river systems where only minor amounts
of such information has been obtained to date. To this end, the surveys were quite
successful. Nonetheless, results gathered during these surveys should be considered only
the initial effort for an on-going study of the sediment phase in the Detroit River and
the St. Clair River. The information gathered on sampling techniques, analytical techniques
and treatment of sediment data has been appreciable and should serve as the basis for
125
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further study.
Sediment sampling, for example, was found to be difficult in sections of the two rivers
where high velocity and greater depth were encountered. The use of a gravity-coring
device for sampling had been chosen for its ability to recover relatively undisturbed
sediment profiles. By comparison, a dredge sampler, such as the Ponar device, takes a
sample with a high surface area to depth ratio and disturbs the sediment so that no
sectioning of the sample by depth can be accurately accomplished. The samples taken
with the corer from the Detroit and St. Clair River bottoms were recovered with the
oxidized surface layer relatively intact. Sectioning of the cores to obtain the upper five
centimeter layer of sediment for analysis was thus a fairly accurate process.
Some difficulty in obtaining core samples during the August 1973 survey was encountered
with the original coring device. Despite the weight of the device (24.5 kg) the current
in the St. Clair River and at the head of the Detroit River caused the coring tube to
strike the bottom at an angle substantially different from the ideal 90° . The Ponar
dredge sampler was used as a backup and thus many of the sediment samples gathered
during this survey are dredge samples rather than cores. The coring device was subsequently
modified by adding weights and a finned guidance section resulting in a total weight of
30 kg. The sediment retaining head was also changed to provide better capture in
unconsolidated bottom materials. The resulting corer proved to be much more efficient
during the two remaining surveys. Nonetheless, there were times when no representative
bottom sample could be obtained either with the corer or the dredge sampler. If the
river bottom was covered with relatively large stones or unconsolidated sand, neither device
produced a satisfactory sample. Such limitations have been mentioned by other researchers
26
In evaluating the trends of constitutents in the river bottoms, the lack of one or two
of the three possible samples at a given station is a significant limitation. Mean values
for the St. Clair River, for example, are often based on less than three determinations.
Despite this limitation, some important conclusions can be drawn from the data gathered
during this study. The St. Clair River does show enrichment in certain sedimentary
constitutents (e.g. COD, Kj eldahl-nitrogen, total phosphorus, chromium, zinc, manganese
and iron) as it descends from Lake Huron. In most instances, however, this increase
is relatively small. The Detroit River sediments, on the other hand, show substantial
enrichment in many parameters, though this occurs primarily along the United States
shoreline. Stations 10, 13, 19, and 20 were found to be major zones of deposition for
most of the constituents surveyed. Station 12, along the Canadian shoreline, showed
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somewhat the same characteristics, especially with respect to the toxic heavy metal,
mercury.
Some corollary information on the mechanisms for retention of certain constituents in
the sediment phase can be developed from the data generated in this phase of the study.
Table 16 is a compilation of correlation analysis results between two hypothesized
mechanisms for such retention and several constituents determined in the St. Clair and
Detroit River bottom samples.
The higher the correlation coefficient, the stronger is the relationship between mechanism
and constituent. For examples, the adsorption capacity of iron, present as the hydrous
metal oxide, is very important in the scavenging and retention of cadmium and manganese.
It appears to be somewhat less important for the remaining constitutents, though the
relationship is significant for every constituent except mercury. Similarly, the chelation
and sorption by organic species, represented in this correlation by COD, is very important
with regard to cadmium, copper and zinc, and somewhat less so for all others, again with
the exception of mercury. Three other major sediment components are thought to be
of importance in retention and scavenging calcium carbonate, clay fraction and sulfide
19,20,21 since these materials were not determined in this study, they cannot be evaluated
with the data presently available.
Sediment Exchange -
In the sediment exchange experiments carried out in this study, the most favorable
conditions for release of sedimentary constitutents to the aqueous phase were utilized.
This provided simulation of the "worst possible" condition for pollutional inputs from
the sediments. In reality, such conditions do not exist, except when the aerobic-anaerobic
interface in the sediments rises to, or above, the sediment-water interface. Under conditions
usually found in the Great Lakes, dissolved oxygen is present in the waters immediately
above the sediments at levels greater than 1 mg/l. This results in a superficial layer of
oxidized sediment which serves as a barrier to the transport of sedimentary constituents
into the aqueous phase. The migration of metals and nutrient species dissolved in the
sedimentary interstitial liquid is halted at this barrier. At the same time, this layer serves
as a scavenger of phosphates, metals and other species directly from the aqueous phase.
As a consequence of this "semi-permeability", appreciable build-up of environmental
pollutants in the surface layer is often observed, which in turn makes the stability of
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Table 16. SEDIMENT CORRELATION MATRIX
Total Iron
Chemical Oxygen Demand
Specie
Cd
Cr
Cu
Fe
Hg
Mn
Ni
Pb
Zn
Total Phos-
phorus
n
26
41
n
41
41
41
41
26
41
41
41
41
41
(r)
.810
.592
,755
-
.015
.851
,672
.556
.723
.616
Minimum Significant Correlation
r (95%) r (9970)
.470 .565
.373 .454
(r)
.849
.635
.840
.753
.125
.526
,690
,622
.812
..748
128
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this trapping layer exceedingly important.
In relatively unpolluted waters, oxidized surface layer ranges in thickness from a few
millimeters to 2 to 3 centimeters. The exact thickness varies, especially in areas where
density-stratification occurs, according to the organic deposition to the sediments and the
availability of oxygen in the waters immediately above the sediments. If there is depletion
of oxygen in the hypolimnion, for example, or if the organic loadings to the sediments
are substantial, the thickness of this oxidized layer will decrease until the aerobic-anaerobic
interface rises to the sediment-water interface. At this point, relatively abrupt releases
of reduced manganese and nitrogen forms (as well as phosphate, silicate, carbonate
alkalinity and ferrous iron) result in significant changes in the quality of the overlying
9O
waters u . In some cases, an order of magnitude increase in the rate of phosphorus
release to the water column has been observed^7 . These sediment derived solutes are
then mixed throughout the overlying waters in a manner determined primarily by flow
pattern and turbulence.
During recent summers, sediments in the central basin of Lake Erie have undergone the
process described above as a result of dying plankton forming a strongly reducing layer
97
on the bottom, two centimeters thickz/ . Even when excess dissolved oxygen is
reintroduced, (for example, during overturn) recovery of the oxidized layer is slow and
the barrier it provides remains unstable for sometime.
There are four major factors which regulate the depth of the aerobic-anaerobic interface
and hence the exchange of sediment constituents into the aqeuous phase. They include:
(a) turbulence; (b) oxygen demand; (c) texture of the sediment surface; and (d) dissolved
oxygen in the overlying water. In the present study, an approximation was made for
each of these factors which produced the most favorable conditions for sediment exchange.
To accurately extrapolate the data generated in this study, further work is needed to
determine exchange coefficients under conditions of higher oxygen content, lower
turbulence, and with sediment water interfaces which more closely approximating those
of the actual river bottoms.
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BIOLOGY
Introduction
The assessment of the existing ecological status of an area can best be based upon the
evaluation of data obtained by monitoring various biological communities. As the study
of water quality becomes ecologically oriented, the question of the relationship between
animal and plant communities and the chemical characteristics of the water must be
explored. The classical response of organisms (if such a response exists) to their
environment has been detailed frequently, beginning as far back as 1850, although one
of the first practical applications was contained in the saprobian system of Kolkwitz and
Marsson™, which was based on a check list of organisms and their response to organic
wastes.
The biological phase of the current study was directed at using to the greatest extent
possible, the available historical records and data amassed on the biological characteristics
of the interconnecting waterways in the study region as well as adjacent areas. Communities
selected as important "on site" monitors of water quality within the area were the benthic
macroinvertebrates and the phytoplankton.
The benthos are directly subjected to adverse conditions of existence as a result of their
habitat requirements and their general inability to move great distances by self locomotion "
. The varied responses of different taxa of benthos give accurate and valuable information
on existing as well as indications of past conditions in a particular river section. As
organisms that comprise the benthic communities respond differently than other taxa to
environmental stress, the use of historical records of these responses is invaluable. Some
species, due to niche specificity, cannot tolerate any appreciable water quality changes,
whereas others can tolerate a wide range of conditions. In general terms, a natural,
unpolluted system will support many different taxanomic groups and few individuals of
each specie. In a polluted or otherwise altered area the converse is true, with many
organisms of each of a few species being present. The benthic community was used both
to complement historical records of the area and because of their intraspecific response
to changes in environmental quality.
The phytoplankton community was considered to be important for all the aforementioned
reasons, as well as the part they play in Lake Erie. The phytoplankton are, by nature,
free floating and are therefore transported by currents both vertically and horizontally.
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It is the horizontal disturbance, and more specifically the upstream-downstream
relationships, that were of interest. By studying the changes in the phytoplankton
community from the upstream areas through to Lake Erie it was hoped that the point
at which bloom causing organisms began to become significant could be identified. Once
this area was determined, the vector of pollution could be isolated and appropriate steps
taken toward correction of the problem. In addition to this specific aim, the phytoplankton
were studied to indicate present environmental quality. When the algal community is
Of)
studied in its entirety, that group may give reliable information as to water quality .
Methodology
Field Sampling -
Station locations for benthic macroinvertebrate collections in the St. Clair and Detroit
Rivers were chosen to be concomitant, where possible, with those locations sampled during
the United States Public Health Service study of 19646 (Figure 34). Each of the 22
collection sites were sampled during the first survey (August 1973) to qualitatively
determine if they were worthy of further quantitative evaluation. As this was the case
with all sites selected, the quantitative benthic study was undertaken during the two
subsequent surveys (November 1973, May 1974). Two samples were secured from each
of the station sites to allow for gross similarity comparisons and increased statistical
reliability.
A Ponar grab. Wildlife Supply Company (No. 1725), was chosen as the best method of
securing benthic macroinvertebrate samples. Both the St. Clair and Detroit Rivers have,
for the most part, comparatively hard substrates and high flows, making them amenable
to application of the Ponar Grab sampler. The Ponar has an effective sampling area of
23 x 23 centimeters (0.0529 m^) and weighs approximately 37 kg, as used in this study.
Upon retrieval, all benthic samples were washed on board, using a Ponar wash frame (Wildco
No. 188). This provides an efficient method for field washing - out of fines and silts,
leaving all organisms and particles larger than 520 m. The prewashed samples were
then transferred into one liter bottles containing freshwater, labeled and put aside for
later fixing. Each sample was fixed at the end of the day with 70 percent ethyl alcohol
or in the case of samples containing high percentages of annelid worms 45 percent formalin
solution"^'**" . Macroinvertebrate animals were hand picked from all samples prior to
identification, counting and cataloging.
Samples for phytoplankton analysis were taken from four areas of the Lake Huron - Lake
131
-------
Figure 34 . Benthos sampling stations 1973-1974
LAKE HURON
SOUTH CHANNEL
LAKE
ST. CLAIR
132
-------
Figure 34 (cont.) Benthos sampling stations 1973-197^
LAKE ST CLAIR
X
MICHIGAN
133
-------
Figure 34 (cont.) Benthos sampling stations 1973-197*1
MONGUAGON CHEEK
MICHIGAN
20» 21. 22.
LAKE ERIE
134
-------
Erie connecting waters. These areas included: Stations 1 and 2 - St. Clair River at Lake
Huron; stations 3 and 4 - St. Clair River in the vicinity of Algonac, Michigan; stations
5, 6, and 7 at Peach Island, mile mark 30.8, upper Detroit River; and stations 19, 20,
21, and 22, mile mark 3.9, lower Detroit River (Figure 34). A composite water sample
composed of three (3) volumes of a horizontal type Van Dorn water sample bottle (2.1
liter volume), was obtained at each station. Samples were collected from subsurface (0.5
m), one-third depth, and near bottom (approximately 0.5 m above the bottom).
Replicate liter (1000 ml) subsamples were taken for pigment extraction and chlorophyll
analysis. The subsamples for chlorophyll measurements were kept on ice and transferred
to the laboratory for analysis. Replicate 250 ml subsamples were taken from each
composite collection and preserved in Lugol's iodine solution until analysis was performed.
Analytical Procedures -
General - After the biological communities were sorted, counted, identified, and catalogued,
various biomathematical indicies were applied to aid in the characterization of species
associations and population similarities throughout the study region. Those indices directed
at specific communities are discussed within the respective community subsections. The
biomathematical expressions used to describe the taxanomic complexes of all communities
studied are presented in the following paragraphs.
The expressions used to describe species richness at specific sites sampled during the three
07
survey periods have been shown to correlate well with changes in water quality . One
formula is expressed as:
Richness = S-1/lnN
where: S= number of species
N= total individuals Margalef^
ln= natural log
The second formula used was: Richness d = S/ v/Nf Menhinick^y
Richness (diversity) is lowest when the community is composed of many individuals of
one species (diversity = 0)^ . Diversity increases when limiting or inhibiting factors
135
-------
are removed; the species complex becomes more diverse and the community is referred
to as being more stable. Such stability is the combined effect of several species undergoing
minor but differing shifts in population numbers as a result of reproduction, mortality,
and response to environmental factors ' .
The numerical assessment of population and community similarity was accomplished by
applying Pirolot's or Sorenson's Similarity Coefficient42,43 . ^'^ formula is:
2 c/a+b
where: a = number of species in population "A"
b = number of species in population "B"
c = number of species common in both "A" and "B"
The calculated values indicate a percent similarity when multiplied by 100; the level of
significance being chosen arbitrarily or statistically. Brown ^ indicates that researchers
of benthic communities often use 0.60 (60 percent) as a level of significant similarity.
Perhaps the most accepted measurements of diversity are based on indices which are
borrowed from information theory . These measures of "informational diversity" are
expressions of the degree of uncertainty involved in predicting the species identity of
a randomly selected individual. The more diverse an assemblage, the more uncertain the
prediction and, conversely, the less diverse, the more certain the prediction. The
informational diversity of a collection is given by:
d = (n-j/N) Iog2 (n-j/N) Shannon's formula ^
where: N = number of individuals of all species in the collection
n.| = the number of individuals of each species
Although each biomathematical expression of community diversity, richness or similarity
is extremely efficient and permits summarization of large amounts of information regarding
numbers and kinds of organisms, it is essential to relate the derived numbers to each
other, and to biomass determinations. In addition to this interrelationship, the
136
-------
macrohabitat requirement of species or groups of taxa were considered when discussing
the biological communities present in the interconnecting waterways and possible
environmental factors contributing to the specific biological development found to exist.
Benthos -
The previously picked benthic samples were transferred to a glass petri dish or Syracuse
watch glass and hand sorted by gross taxonomic characteristics. Groups of taxa were then
placed under a Bausch and Lomb variable zoom (10X - 70X) microscope for identification
and enumeration. Taxanomic keys used were Pennak^ , Usinger , Needham and Needham °
, Leonard and Leonard47 , Burks48 , Edmondson49 , Hamilton et al50, Hiltunen3^ ,
m RQ
Johannsen01 , Klemm0^ . The taxanomic data was then applied to various indices of
species richness and expressions of faunal similarity and diversity described earlier.
Various analytical procedures specific to the benthic population were biomass (wet weight),
subsampling, and clearing of the annelid worms for identification. The macroinvertebrate
biomass determinations were made on a Mettler Type H-6 analtyical balance. The biomass
determinations were made on the entire sample following removal of all external
preservative by blotting on filter paper for one minute. The cases of caddis flies
(Trichoptera) were excluded but shells of mollusks and crustaceans were included in
o
biomass wet weights. The calculation used for wet weight of benthic invertebrates (g/mz)
was:
wet weight of organisms in all samples (g)
Q
area of sampler (m ) x number of samples
Some benthic samples, notably those from stations 13 and 14, contained such large numbers
of small organisms (annelid worms) that it was impractical to pick or count them all.
In these samples the larger organisms and bits of detritus were removed by hand picking.
The remaining sample was made up to definite volume and aerated and agitated to a
homogenous mix. While the sample was thoroughly mixed a subsample of twenty five
percent of the original volume was removed by a dipper. This aliquot was then treated
as described above for identification. The total number of organisms per sample was
then obtained by multiplying the number in the subsample by the aliquot percentage.
Representative oligochaeta were cleared prior to mounting to enable visual observation
00
of the identifying characters employed in Hiltunen's00 taxonomic key. Suspension of
the organisms for several days (three to five) in Amman's lactophenol was found to be
the best method of clearing. Amman's lactophenol is comprised of 100 g phenol, 100
137
-------
ml lactic acid, 200 ml glycerine and 100 ml distilled water.
Phytoplankton - The subsamples for chlorophyll measurements were first filtered through
Whatman, Type GF/C, glass fiber paper. Analytical techniques were similar to those
spectrophotometric methods described by Slack, et al^ . Filtered samples were tissue
ground in 90 percent aqueous acetone and MgCOg, centrifuged, and absorbance of the
centrifugate read at wavelengths of 750 nm, 663 nm, 645 nm and 630 nm on a Varian
Techtron, Model 635 spectrophotometer. Chlorophyll a was quantified from the following
formulas:
chlorophyll^ (y g/ml) = 11.64e663 - 2.16e645 + 0.10e630
chlorophyll ^_ (p g/ml) = derived value ( ug/ml) x extract volume (ml)
volume collected (1)
Before completing these calculations a turbidity correction was made by subtracting the
750 nm reading from each absorbance. Data is presented as mean chlorophyll a ( g/l)
at each station, compared with other stations, and correlated with mean total numbers
of phytoplankton (no./I).
Replicate 250 ml subsamples were taken from each composite collection, preserved in
Lugol's iodine solution, and taken to the laboratory for species identification and
enumeration. After shaking, a ten milliter aliquot was removed from each subsample,
placed in a counting chamber, permitted to settle for a period of not less than ten hours,
and examined on a Wild, Model M-40, (400X magnification) inverted lens microscope.
From these replicate samples a composite species list of phytoplankton was constructed
expressing the occurrence of individuals as mean numbers/ml. These data were compared
through the use of species richness indices, Shannon-Weaver diversity, and population
similarity as discussed earlier.
138
-------
Results
Benthos •
St. Clair River - The benthic macro!nvertebrate assemblage of the St. Clair River is strikingly
homogenous, see Figure 35, Appendix B-1, and B-2. Only one genus was collected during
the May and November sampling runs at the upstream stations (1 and 2); the North
American prosobranch Goniobasis sp. Stations 3 and 4 were also dominated by Goniobasis,
although the appearance of the lighter Trichoptera such as Hvdrophvschae.
Cheumatopsychae, Macrgnemum, Brachycentrus and Athripsodes was documened, see
Appendix B-1 and B-2. Biomass calculations (grams/meter^ ) for the four stations on
the St. Clair River, averaged 20.92 and 31.60 for the November and May surveys
respectively; this represents a two percent decrease from November to May. Following
is the mean biomass of macroinvertebrates at the four stations in the St. Clair River:
Station X Biomass
November May
1 11.50 4.30
2 62.00 58.10
3 19.28 12.00
4 - 52.00
"X" 30.92 31.60
The May survey yielded an average of 45 percent fewer organisms (total numbers) than
the same stations sampled in November 1973.
The diversity and richness calculations applied to the benthic community sampled in the
St. Clair River generated real numbers only through the Menhinick formula (S/\/~N),
Table 17. The population density was low at both the upstream and downstream transect;
although much lower upstream (165 versus 302 individuals per meter^ ) during the May
1974 survey.
From these data the St. Clair River demonstrated an undiversified macroinvertebrate
community consisting of organisms indigenous to, and adapted for, rapidly flowing water
with hard underlying substrates ''
Detroit River - The Detroit River demonstrated a narrow range of benthic taxa and average
numbers of genera during both the May and November survey dates. The average number
139
-------
Figure 35. Dominant taxa Detroit and St. Glair Rivers
UAKE HURON
Dominant taxa/I dominance
November 1973
May 1974
Goniobasis sp./lOOZ
Gohiobas is so./100%
Goniobasis sp . /1007.
Goniobasis sp./1007.
PORT HURON
MICHIGAN
Gonxobasis sp. 36
LAKE
ST. CLAIfl
140
-------
Figure 35 (cont.)- Dominant taxa Detroit and St. Glair Rivers
Dominant taxa/7. dominance
November 1973
M^ L974Cheumatopsychae sp. 37%
LAKE ST. CLAIR
Cheumatopsychae sp . 61'
Hydropsy chae sp
Hdropsychae sp. 907.
Macronemum sp. 60%
Hydropsychae sp.78%
Macronemma sp. 33%
Hydropsychae sp~. 75%
Goniobasis sp. 267.
Hexagenia sp . 3-37.7
Pontoporeia affinis 337.
Limnodrilus cervica 46%
Sphaerium sp. 297.
Limnodrilus cervica 63%
Dina microstoma o//.
Tanypus sp. 92%
Limnodrilus cervica 867
141
-------
Figure 35 (cont.). Dominant taxa Detroit and St. Glair Rivers
Dominant taxa/% dominance
November 1973
May 1974
Limnodrllus cervica 97%
LicnodriLus cervica 92%
ECORSE RIVER
Limnodrilus cervica 99%
Limnodnlus cervica 111.
Lunnodrilus cervica 331
Dina micros coma 637.
MOMGUACON CREEX
Pnysa sp. 40
saamoryctides calirom
Liamocrilus
Pnysa sp. 1007.
ghysa sp. 537.
Lymnaea sp. 40T1
Chirotiomidae 49Z
Pisidiun sp . Z9"i
19. 20» 2> 22 •
Spnaerium 50"/
indium 507. ~
142
-------
Table 17. MENHENICK FORMULA CALCULATIONS - ST. CLAIR RIVER
BENTHOS
November Station 123
_ 2
X Biomass/m
(wet weight) 11.5 62.00 19,28
X Individuals/m2 66 359 217
Shannon Weaver Diversity
(X) 0.00 0.00 1.39
Richness (X) (S-l/lnN) 0.00 0.00 1.65
Richness (X) (S/ N) 0.50 0,22 1.49
May_ Station 1234
_ 2
X Biomass/m
(wet weight) 4.30 58.10 12.00 52.00
X Individuals/m2 28 302 113 491
Shannon Weaver Diversity
(X) 0.00 0.00 0,71 0.44
Richness (X) (S-l/lnN) 0.00 0.00 0.84 0.47
Richness (X) (S/ N) 0.85 0.27 1.03 0.50
143
-------
of genera collected at various transects, grouped with references to location on the river,
were: six for the "upstream" area, four in the "middle" region, and three in the "mouth"
area. The upstream area was represented by stations 5, 6 and 7 in the vicinity of Peach
Island: the middle area was delineated by stations 8-15 and encompassed the area from
the Detroit Harbor Terminals, Incorporated to the northwestern tip of Grosse He
(approximately 8.6 river miles) near the Trenton Channel, while the mouth area was
considered as stations 16-22; Figure 34. The Canadian side of the river had one more
genus than the American side, considering the average for all samples of both quantitative
surveys; five genera versus four genera respectively. Important also are the kinds of taxa
found to be indigenous to the analogous Canadian and United States stations. Stations
5 and 8 located in United States waters produced primarily Amphipoda, Gastropoda and
Ephemeroptera, while corresponding Canadian sample sites (7 and 9) were dominated by
Trichoptera and Gastropoda. The downstream points sampled in the vicinity of Mud Island
on the United States side (stations 10, 13, 14) yielded Gastropoda, Sphaeriidae, and
an overwhelming population of Annelid worms. Samples from Canadian waters (stations
12, 16, 17, 21, and 22) along the same reach produced Amphipoda, Ephemeroptera,
Chironominae, and some Tubidificidae (annelid worms). The "mouth" area stations
(15, 18, 19, and 20) located on the United States side consisted of Gastropoda, Hirundinea,
Tubificidae and Chironomidae. Most generally, the United States waters were observed
to have a benthic population most often associated with areas of low water quality54,55,41,8
The population density figures (Figure 36) for the Detroit River vary greatly with the
region in question. The upstream transect adjacent to Peach Island demonstrates close
replication between the two shoreline stations (numbers 5 and 7), while the sample located
in the shipping channel (station 6) had a lower population density than the near shore
stations on the November quantitative benthos survey. The higher numbers of benthic
animals during the November survey at stations 5 and 7 decreased drastically in the sampling
during May 1974; from 1947 to 198 individuals per square meter for station 5, and 2665
to 170 individuals per square meter for station 7, a 90 percent and 94 percent reduction,
respectively. Station number 6 had an increase of benthic animals during the six months
intervening, from 217 to 388 animals per square meter, representing a 44 percent increase.
The taxa collected were very similar during both the November 1973 and May 1974 sample
runs, consisting primarily of Trichopterans of the family Hydropsychidae at all stations.
Population density followed much the same trend of decreasing numbers of organisms
at stations 8, 9 and 11, although the total number of animals recovered was less than
the initial river influent stations. The area sampled just below the Detroit River - Rouge
River confluence showed the converse community seasonal variation, that is, the two
samples had an increase of approximately 42 percent from November to May (993 to
1701 individuals/m^ ). Station 12, located between Fighting Island and the Canadian
144
-------
Figure 36. Benthos St. Glair/Detroit Rivers
November 1973 individuals/nT
May 1974 individuals/m2
LAKE HURON
MICHIGAN
ALSCNAC
NORTH CHANNEL
SOUTH CHANNEL
LAKE
ST. CLAIIl
-------
Figure 36" (cont.)- Benthos St. Glair/Detroit Rivers
2
November 1973 individuals/m
May 1974 individuals/m2
LAKE ST. CUAIS
146
-------
Figure 36 (cont.)- Benthos St. Glair/Detroit Rivers
November 1973 individuals/m
May 1974 individuals/m2
ECORSE RIVER
-A-
MICHIGAN
147
-------
shore near LaSalle, Ontario, produced similar population densities on both surveys (1753
fy
and 1720 animals/m^ ). The November survey generated primarily Chironomidae of the
genus Tenypus (Meigen), while the May samples were dominated by the annelid worm
Limnodrilus cervix. The substrates collected at stations 13 and 14 were populated by
extremely large numbers of Tubificidae, 411, 701 and 229,017 individuals per square meter
at station 13 for the November and May surveys, respectively. Station 14 had lower,
although still inordinately high populations of Tubificidae, numbering 14,735 and 2,873
animals per square meter for the November and May surveys, respectively. Ljmnod_rjlus
cervix and _L. angustipenis were the dominant forms (Figure 35). The next four river miles
(12.0 - 8.0) were characterized by relatively constant population densities and benthic
community development. The transect consisting of sample stations 19-22 (river mile
3.9) was predominated by Gastropoda such as Lymnaea, Physa, and Valvata sp. in
November while Hexagenia sp. dominated in the May collections. Population densities
ranged from 38 individuals per square meter for station 22 in May to 907 per square
meter for station 20 in November. See Figure 35 for a composite of dominant taxa collected
at the various stations.
The species richness (S/v/TvT and S-1/lnN) of the northern most transect in the Detroit
River shows a high degree of similarity for both near-shore communities, and each indicate
a diverse benthic population. With respect to station 6 richness, November samples had
a lower diversity in the channel than comparable near-shore samples, however in May
the biomathematically derived figures showed that all transect stations to be close in
community richness. Station 8 had a higher species richness than station 9 on both
sampling dates, although both stations 8 and 9 showed an increased richness of taxa as
compared to the upstream stations in all but one sample; the May sample at station 9.
This was due to the recovery of only one taxa of the Hydropsychidae, see Appendix
B-1 and B2. Subsequent November samples indicate species richness values ranging from
1.37 at station 15 to 0.02 at station 13 where an average of the replicate samples produced
21,779 individuals per square meter represented by only three taxa. The May data
produced values ranging from 1.50 at station 21 to 0.06 again at station 13 (12,115
individuals per square meter represented by six taxa).
The Shannon-Weaver (3) diversity (informational theory) was calculated on all samples
although only selected transects point up interesting biological responses in the Detroit
River benthic faunal assemblage, Figures 37 and 38. These transects are delineated by
stations 5, 6, and 7 at Peach Island (river mile 30.8); 10 and 11 just below the confluence
of the Rouge and Detroit Rivers (river mile 19.0); 13 and 14 between Mud Island and
Grassy Island (river mile 14.6), station 15 in Trenton Channel (river mile 12.0W), and
148
-------
Figure 37. Shannon-Weaver diversity - November 1973 Benthos
1.5
1.3
1.1
0.9
0.7
0.4
0.3
FLOW
-------
Figure 38. Shannon-Weaver diversity - May 1973
Ln
O
1.5 ^
1.3
FLOW
U.S.
SHORE
-------
stations 16 and 17 just east of Grosse lie in the Fighting Island Channel (river mile 9.3).
The diversity of a particular community is best understood when it is related to biomass
figures derived from that community^" , Table 18. At the initial transect, November
diveristy calculations show station 6 to have both the lowest diversity, 0.50, and lowest
f\
mass of animals recovered (1.04 grams/m^) while the near shore, and thus more protected,
station 5 yielded biomass numbers of 6.62 grams per square meter and 20.04 grams per
square meter, respectively. The diversity of each community was 1.47. From this one
would expect the animals at station 7 to be more robust than those at station 5, assuming
either the same taxa were taken at each location or that heavier forms were represented
in the sample if different taxa were recovered, or both. In this case, both assumptions
were observed to hold true. Station 7 was represented by several Pleurocerid Gastropods,
a relatively heavy organism, while station 5 had only one individual of this taxa. The
May collection of this transect pointed up the seasonal fluctuation of macrofaunal benthos
in the Detroit Rver. The channel location (station 6) reported a higher diversity (0.77)
and biomass (11.15 g/m^ ) than either near shore station. The presence of the cold
water stenotherm, Pontoporeia affinis (Lindstrom), was also first noticed at station 6 during
this survey.
The two locations sampled below the mouth of the Rouge River indicated very high
diversities in November (1.64 for station 10 and 0.92 for station 11) while they were
lowered to 0.97 and 0.00, respectively, in the May collection. Benthic biomas was also
greatly reduced between November and May. Station 10 had the highest on each sampling
date with values of 31.10 in November and 9.44 individuals per square meter in May,
while station II had values of 1.66 and 0.86 in November and May, respectively. Stations
13 and 14 had an extremely low diversity of benthic forms while the biomass was high.
The indications of an organically enriched substrate in the vicinity of Mud Island are
unquestionable with biomass numbers of 133.70 and 66.85 grams per square meter. The
stations near Grosse lie (15, 16, and 17) show a general increase in the diversity from
the upstream stations of 12, 13, and 14, while the biomass decreases. Station 15 shows
the lowest diversity and highest biomass of these three stations however and is therefore
considered to be somewhat lower in overall quality to 16 and 17. See Tables 19 and
20 for computed similarity values for all Detroit River stations.
To summarize then, the upstream stations in the Detroit River are characterized by high
population densities, richness, and diversity and are dominated by animals in the order
Trichoptera. Samples taken in the section of the river below the Rouge River to Grosse
Me are extremely high in total numbers of individuals, with a subsequent low diversity
and richness, high biomass and consisted almost exclusively of Tubificidae and Sphaeridae.
151
-------
Table 18 . DETROIT RIVER, SELECTED STATIONS COMPARED BY BIOMASS
AND SHANNON-WEAVER DIVERSITY
Station
_ November 1973
X Biomass Shannon-Weaver
May 1974
X Biomass Shannon-Weaver
5
6
7
10
11
12
13
14
15
16
17
6.62
1.04
20.04
31.10
1.66
2.54
133.70
13.33
22.10
*
6.10
1.47
0.50
1.47
1.64
0.92
0.30
0.04
0.16
0.43
*
1.23
3.65
11.15
10.51
9.44
0,36
11.98
66.85
9.58
5.43
2.91
0.94
0.34
0.77
0.49
0.97
0.00
0.55
0.63
0.32
0.47
0.81
0.84
*no sample
152
-------
Ul
OJ
Station
5
6
7
8
9
10
11
12
13
14
15
18
5
6
7
8
9
10
11
12
13
14
15
18
Table 19, NOVEMBER SIMILARITY MATRIX, BENTHOS DETROIT RIVER
6 7 8 9 10
0.40 0.85 0.42 0.40 0.24
0.32 0.33 0.31 0.00
0.74 0.60 0.19
0.47 0.29
0.13
Table 20. MAY SIMILARITY MATRIX,
6 7 8 9 10
0.33 0.40 0.57 0.40 0.00
0.80 0.86 0.80 0.00
0.67 1.00 0.00
0.67 0.67
0.00
11
0.38
0.22
0.30
0.15
0.14
0.55
BENTHOS
11
0.00
0.00
0.00
0.00
0.00
0.57
12
0.40
0,00
0,32
0.17
0.31
0.40
0.44
DETROIT
12
0.00
0,22
0.00
0.00
0.00
0.18
0.25
13
0.14
0.00
0.11
0.18
0.00
0.67
0.50
0.57
RIVER
13
0.18
0.00
0.00
0.00
0.00
0.46
0.40
0,29
14
0.35
0.00
0.29
0.43
0.13
0.83
0.36
0.40
0.67
14
0.25
0.00
0.00
0,00
0.00
0.40
0.57
0,18
0.77
15
0.53
0.17
0.43
0.38
0.12
0.57
0.62
0.67
0.36
0.57
15
0.33
0.00
0.40
0.00
0.40
0.50
0.80
0.22
0,55
0,75
18
0.00
0.00
0.00
0.00
0.00
0.00
0.00
0.00
0.00
0.00
0.00
1.00
18
0.00
0.00
0.00
0.00
0.00
0.50
0.57
0.22
0.55
0.75
1.00
1.00
-------
Stations in the vicinity of Grosse lie show medium numbers of individuals, diversity, and
richness with low biomass and richness with low biomass figures. The stations in this
area were dominated by Phvsa and Tubificids although some Ephemeroptera such as
Hexaqenia began to appear. The lake area stations are characterized by low to medium
numbers, diversity, and richness with a low biomass and were dominated by mollusks.
Phytoplankton -
Phytoplankton populations in the St. Clair and Detroit Rivers were compared in terms
of chlorophyll a, b, and £ (pg/l), number of individuals/ml, percent dominance by major
taxanomic groups, comparison of abundant species, species richness (S-1/lnN) and (S//N),
species diversity (Shannon-Weaver expression), and population similarity (2c/a + b).
Contrary to other aspects of this survey, e.g., chemistry and benthic sampling,
Phytoplankton measurements were collected from four areas of the two rivers. This
included transects in the upper and lower (upstream and downstream) portions of the
St. Clair River and upper and lower (upstream and downstream) portions of the Detroit
River.
Chlorophyll - The results of the chlorophyll measurements are presented in Tables 21,
22 and 23 and Appendix C-1; trends are shown by Figures 39, 40, and 41. Values are
given for collections taken during November 1973 and May 1974. Measurements from
the August 1973 collection were extremely variable, with large experimental error, and
thus were not tabulated. The techniques were refined and greater sensitivity with less
variability was achieved in later measurements. In most cases replicate samples had fairly
similar values (Appendix C-1). During November the two stations in the upper St. Clair
River (stations 1 and 2) showed nearly identical mean levels of the respective chlorophyll
measurements although this did not hold true during May 1974 (Table 21). In the lower
St. Clair River (stations 3 and 4) the November and May chlorophyll levels were similar.
Table 21 further indicates that greater variability occurred in the Detroit River transects
(stations 5-7 and 19-22) than in the St. Clair River transects.
Mean chlorophyll a levels were similar in the upper and lower St. Clair River during both
the November and May collections (Table 22). However, the mean chlorophyll a^ levels
between the upper and lower Detroit River differed between November and May (Table
22 and Figure 39). During November the mean level of chlorophyll a_\n the upper Detroit
River was less than that measured in the lower Detroit River, however the opposite was
true during May (Table 22). At either time the Detroit River produced more chlorophyll
JL ( p g/0 than did the St. Clair River. This trend can be seen in Figures 40 and 41.
154
-------
Station
Table 21 DETROIT RIVER PHYTOPIGMENTS
Mean Chlorophyll a, b, £ (yg/1)
November 1973
Chi. a Chi. b Chi. c
May 1974
Chi. a Chi. b Chi. c
1
2
3
4
5
6
7
19
20
21
22
1
1
0
1
1
0
2
1
1
1
3
.2
.2
.8
.4
.4
.6
.4
.2
.2
.8
.0
0
0
0
0
0
0
0
0
0
0
0
.5
.6
.2
.2
.2
.4
.4
.2
.8
.2
.4
1
1
1
1
1
0
1
1
2
1
1
.2
.7
.0
.0
.1
.4
.4
.0
.6
.2
.2
2.
0.
1.
1.
3.
2.
-
2.
3.
1.
2.
0
8
0
2
8
0
2
8
8
5
0.5
0
0.1
0.4
0.7
0.6
-
0.6
0.7
0.2
0.4
2
0
0
1
2
2
2
2
1
1
.0
.6
.6
.6
.2
.0
-
.6
.5
.4
.3
Table 22.
MEAN CHLOROPHYLL a (ug/1) AT FOUR STUDY AREAS
Precision approximated according to Slack et
River Areas
November 1973
Chlorophyll a Precision (yg/1)
May 1974
Upper
Lower
Upper
Lower
St. Glair R.
St. Glair R.
Detroit R.
Detroit R.
n
4
4
6
8
1.
1.
1.
1.
2
1
5
8
± o
± o
± °
+ 0
.13
.13
.11
.09
n
4
4
4
8
1
1
2
2
.4 +
.2 +
.9 +
.6 +
0
0
0
0
.13
.13
.13
.09
155
-------
Figure 39.Detroit River mean chlorophyll a concentration (ug/D
November 1973
May 1974
LAKE ST. CLAIH
Detroit Slver phytopigments were aeastirad at trwo
locations, aila mark 3.9 (lower Detroit River) and
mile mark 30.3 (upper Detroit Siver)
MICHIGAN
ONTAfllO
156
-------
Figure 40. Mean Chlorophyll a Concentrations (yg/1)
November 1973
4.0
.0
2.0
1.0
0.9
^ 0.8
2 0.7
^s
«' n 6
Chlorophyll
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0.3
0.2
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157
-------
4.0
3.0
2.0
w>
to!
1.0
0.9
0.8
0.7
0.6
0.5
>•> 0.4
ex
o
^ °'3
o
0.2
Figure 41. Mean Chlorophyll £ Concentration (yg/1)
"May 1974
0.1
Upper St. Clair Lower St. Upper Detroit
River Clair River River
19 20 21 22
Lower Detroit River
158
-------
The levels of chlorophyll & ( ug/D presented in Table 21 indicate that there was similar
production in both the St. Clair and Detroit Rivers during November, while there was
greater production in the Detroit River during May. Little emphasis should be placed
on chlorophyll c. as an independent measure, as the literature suggests this measurement
is often variable and has a poor level of precision^ . Chlorophyll jc_ does indicate the
abundance of certain algal groups and will be used in a ratio of chlorophyll_c/a to show
trends throughout this river system. A similar ratio, chlorophyll b/a, will be used in
this manner.
Ratios as calculated for replicate samples are presented in Table 23. The ratio of
chlorophyll Jj/a. was most often greater during November than during May (Table 23),
this is verified by the list of mean values by river and transect in Table 24. A similar
trend was observed in the chlorophyll ratio_c/_a. Mean levels were always greater during
November than during May (Table 24).
Table 24. VALUES OF CHLOROPHYLL RATIOS b/a. AND c/a_
November 1973 May 1974
b/a .c/a b/a c/a
Upper St. Clair River 0.49 1.33 0.15 0.82
Lower St. Clair River 0.19 1.07 0.19 0.91
St. Clair River 0.34 1.20 0.21 0.87
Upper Detroit River 0.29 0.89 0.24 0.82
Lower Detroit River 0.29 1.05 0.21 0.78
Detroit River 0.29 0.99 0.18 0.79
Phytoplankton Abundance and Dominance - Total number of phytoplankton individuals
were determined from microscopic examination of replicate samples and expressed as mean
number of individuals/ml river water. The general trend observed was an increase in the
number of species and total number of individuals from the St. Clair River through the
Detroit River (Appendix C-2). Samples from the Detroit River carried the greater number
of total species. Numbers of total individuals/ml seemed quite variable throughout the
survey although during Novmeber 1973 there was little variation between all sample points.
Mean total numbers of individuals/ml ranged from 227 - 9695 during August; 526 - 1147
during November; and 1113 - 3208 during May (Appendix C-2). The upper Detroit River
(stations 5-7) carried the greater number of individuals/ml during August while having
fewer species than other river areas. During the other surveys the downstream Detroit
159
-------
TABLE 23. RATIOS OF CHLOROPHYLLS c/a AND b/a - ST. GLAIR AND
DETROIT RIVERS
November 1973 May 1974
Station/Sample Chlorophyll ratios Chlorophyll ratios
number c/a b/a c/a b/a
1A
IB
2A
2B
3A
3B
4A
4B
5A
5B
6A
6B
7A
7B
19A
19B
20A
2 OB
21A
21B
22A
22B
1.30
0.86
0.85
2.30
1.00
1.80
0.80
0.67
0.82
0.76
-
1.50
0.46
0.92
0.93
0.60
2.83
1.89
0.84
0.53
0.26
0.52
0.40
0.43
0.23
0.90
0.33
0.20
0.07
0.17
0.18
0.18
0.14
0.86
0.14
0.23
0.27
0.10
0.67
0.68
0.21
0.06
0.12
0.19
0.47
1.39
0.50
0.92
0.50
0.59
1.44
1.11
0.55
0.64
0.93
1.17
-
-
1.38
0.86
0.75
0.54
0.64
1.00
0.48
0.57
0.11
0.35
0
0
0
0.12
0.31
0.33
0.15
0.22
0.26
0.33
-
-
0.33
0.24
0.20
0.16
0.16
0.09
0.19
0.13
160
-------
River transect (stations 19-22) produced the largest phytoplankton population. These
trends can be seen in Table 25 and Appendix C-2. Mean number of individuals/ml were
always less in the St. Clair River than in the Detroit River. The total plankton populations
at the upstream and downstream Detroit River transects were similar (no./ml) when the
means and variance are taken into consideration (Table 25).
Table 25. MEAN NUMBER OF PHYTOPLANKTON INDIVIDUALS/ml + ONE
STANDARD DEVIATION
Date Area Mean
August 73 St. Clair River 392.5 98.9
Detroit River 3137.0 3683.5
Upstream 3466 5383.5
Downstream 2808 2119.5
November 73
St. Clair River
Detroit River
Upstream
Downstream
645.8
934.1
9257
940.5
100.4
T53.4
233.3
103.1
May 74
St. Clair River
Detroit River
Upstream
Downstream
1386.0
2476.8
2274.0
2578.0
241.3
751.4
1213.4
639.6
The dominant group of phytoplankton organisms was the diatoms (Bacillariophyta) in
all cases. This held true at all stations during each collecting period (Table 26). During
August and November 1973 the second and third dominants were the green algae
(Chlorophyta) and blue green algae (Cyanophyta), respectively. The second dominant
group during May 1974 was the Chrysophyta (golden-brown algae exclusive of the diatoms).
The dominant diatom species in the St. Clair River (stations 1-4) during August were
Cyclotella spp., Stephanodiscus astraea, and Tabellaria flocculosa (Appendix C-3).
Pelogloea bacillifera was the dominant blue-green alga while Chlorella vulgaris, Elakatothrix
gelatinosa, and Selenastrum minutum were the dominant green algal species. Dominant
species in the upper and lower St. Clair River were similar during August.
In the Detroit River (August 1973) the domiannt species were Cyclotella spp.,.C. catenata,
Melosira italica, Navjcula spp., Nhzschia spp., and Ste_phanodiscus astraea. Cyanarcus
161
-------
Table 26. DOMINANT GROUPS OF PHYTOPLANKTON BY PERCENT
St. Glair and Detroit Rivers (Aug, Nov 73 and May 74)
Date
August 73
a-.
hJ
November 73
tation Cyanophyta
1
2
3
4
5
6
7
19
20
21
22
1
2
3
4
5
6
7
19
20
21
22
13
4
7
12
7
21
5
13
6
4
23
19
22
16
5
6
3
3
4
2
2
.2
.7
.5
.8
.0
.3
.2
.4
.4
.6
-
.6
.2
.9
.9
.9
.3
.5
.8
.6
.8
.5
Chlorophyta
17.
39,
11.
20.
15.
19.
19.
18.
12.
15.
-
4.
12.
10,
7,
9.
5.
18.
16.
6,
4.
16.
5
3
6
1
0
8
4
9
0
0
7
9
0
7
2
8
0
4
8
7
9
Chrysophyta
2
3
7
5
0
10
2
0
0
2
1
2
2
1
6
2
1
2
2
3
5
.5
,4
.2
.0
.2
,5
.6
,5
.8
.8
-
.0
.3
.2
.4
.9
.0
.8
.2
.4
.2
.2
Bacillariophyta Other
59
46
62
55
77
40
71
66
80
76
68
55
60
70
67
82
69
76
73
81
58
.0
.3
.9
.7
.5
.8
.9
.9
,7
.1
-
.6
.1
.6
.2
.4
.5
.7
.7
.8
,4
.9
7
6
10
6
0
7
0
0
0
1
2
10
4
4
10
3
6
0
12
7
16
.8
.3
.7
.4
.3
.6
.9
.2
.5
.5
-
.2
.4
,3
.3
.6
.4
.6
.8
.3
.8
.1
-------
Table 26. (Cont.). DOMINANT GROUPS OF PHYTOPLANKTON BY PERCENT
St. Glair and Detroit Rivers (Aug. Nov 73 and May 74)
Date Station
May 74 1
2
3
4
5
6
7
19
20
21
22
Cyanophyta
2.5
2.1
3.0
2.3
1.9
2.5
1.0
1.7
2.0
1.5
Chlorophyta
3.5
4.1
4,9
2.9
3.2
3.0
3.7
3,0
4.3
2,9
Chrysophyta
14.2
13,9
16.2
19.9
10.1
14.1
0.4
10,0
13.0
14,3
Bacillariophyta
76.2
65,7
71.3
71.8
82.6
79,4
94.3
84.1
79.9
---81.5
Others
3.6
14.0
4.6
3.3
2.1
1.0
0.6
1.1
0.6
a
-------
hamiforrnis and Marsoniella elegans were the dominant blue-green species, especially at
station 5 of the upstream Detroit River transect. At the downstream transect several
species of blue-green algae were equally abundant and the blue-greens were more diverse
at the downstream transect than at the upstream transect (Appendix C-3). The August
collections in the Detroit River had many green algal species of which Ankistrodesmus
falcatus, A. spiralis, Pianktosphaeria gelatinosa, Scenedesrnus abundans, S. quadrj£auda,
and Selenastrum minutum were common. As with the blue-green algae, the greens appeared
to be more diverse at the downstream stations.
The order of dominance in the St. Clair River during November 1973 was the diatoms,
blue-green, and green algae (Table 26). Of the diatoms Asterionella formosa. Cyclotella
spp., Fragilaria crotonensis, Melosira ijaJlca,,, Stephanodjscus astraea, and SyjTedra_spp. were
equally common at all four St. Clair River stations (Appendix C-3). Fragilaria crotonensis
was the most abundant, equalling between 20 and 30 percent of the total individuals/ml
at the four St. Clair River stations. Coelosphaerium naegelianum, Microcystis aeruginosa,
I mill • • •» ••>••••. .n.. i *ft in.aa.i.... mumn' - —«—•^w-.-B*™**** ,.v „ . ^^.atL^^a*™ '
and Pelogloea bacillifera were the blue-greens which were common to all St. Clair River
stations. Of these, Microcystis aeruginosa was consistently more abundant although an
occassional species dominated this group at specific stations, e.g., Aph anocapsa ejachisla
at station 1. The common green algae species were Ankistrodesmus falcatus, Gojenkjrna,
radiata, and Oocystis gloeocystiformis.
In the Detroit River during November the diatoms were dominant followed by the green
and blue-green algae. The extent to which the diatoms were dominant was slightly higher
in the Detroit River than in the St. Clair River (Table 26). The blue-green algae were
only one-half to one-third as dominant in the Detroit River as in the St. Clair River and
the degree of dominance of the green algae varied between stations. Common and abundant
diatom species included Amphora sp., Asterionella formosa, CycloteMa spp., £ra<3ilaria
crotonensis, Melosira italica, Navicula spp., JNIjtzschia palea, StejihajTOdiscus astraea, and
Synedra spp. (Appendix C-3). Blue-green species which were common included
Chroococcus limneticus, Coelosphaerium naegelianum, Microcystis aeruginosa, and
Oscillatoria minima, although this and other species of Oscillatoria were common at the
downstream transect (stations 19-22). Common species of green algae included
Ankistrodesmus falcatus, A^spiraMs, Scenedesrnus abundans, S. bijuga, S. quadricauda, and
Selenastrum minutum. The species Dinobryon calciformis and C). sertularia of the
Chrysophyta were also common at most stations (Appendix C-3).
Although the diatoms remained as the dominant group during May 1974, the Chrysophyta
were of second importance rather than the Cyanophyta or Chlorophyta. The common
164
-------
diatom species in the St. Clair River were Asterionella formosa, Cyclotella spp., Fragilaria
crptonensis, Rh|^jsolenia eriensis, Synedra spp., and TabeMlaria flocculosa. The common
and abundant species of Chrysophyta were Djjnpbp£on sertularia and D. tabellariae
(Appendix C-3).
Dominant diatom species in the Detroit River (May 1974) were Asterionella formosa,
Cyclotella spp., Fragilaria capucma, F^ crotongQgjg. Mejosj^a varicins, Syjiedra spp., and
Tabellaria flocculosa. In addition to these, CycloteMa glomerata and Riizosolenia eriensis
were abundant at the downstream transect and less so at the upstream transect. Dinobryon
sertulajria^and D. tabel|armejvere the dominant species of Chrysophyta. Of the blue-green
algae the common forms were Oscillatoria hamelii and (D. Ijmnetica. Ankistrodesmus
falcatus and A. spiral is were the common species of green algae in the Detroit River during
May 1974 (Appendix C-3).
At several stations during all three collecting periods there was an abundance (7 to 16
percent) of "other forms" (Table 26 and Appendix C-3). These were phyto-flagellates
and were classified as Rhodomonas lacustus and Chroomonas sp. It should be noted
that those individuals recorded as Chroomonas sp. may not necessarily be of this taxon
and should most probably be labelled as "Unidentified Flagellates".
Richness and Diversity - The data with regards to richness and diversity are summarized
in Appendix C-3 and trends are depicted in Figures 42-47. For these comparisons, two
richness formulas were used which are "ratio-type" expressions of which only one (S-1/lnN)
was plotted as a histogram. In addition to the species richness calculations, species diversity
(H) was determined by the Shannon-Weaver equation which is a "log-proportional"
expression, with the numbers of each species being of relative importance.
Species richness increased from the upper St. Clair River to its downstream area during
August 1973 and greatest richness occurred along the United States shore (Figure 42).
At the upstream Detroit River transect species richness was slightly lower than found
at the downstream St. Clair River transect. Richness was lowest along the United States
shore at the upper Detroit River transect. In the lower Detroit River, species richness
was greatest along the United States shore and lower near mid-channel. Species richness
increased greatly from the upstream to the downstream Detroit River transects during
August (Figure 42).
During November 1973, species richness was higher than during August at most stations
165
-------
Figure 42. Phytoplankton Species Richness (S-l/lnN) - August 73
ower Detroit
River
Flow
United States Shore
Jpp~er Detroit River
Tower St. Glair River
Upper St. Glair River
-------
Figure 43. Phytoplankton Species Richness (S-l/lnN) - November 1973
8
7
6
5
4
Flov >'^*"
United States Shore
•— .
6
-------
Figure 44 . Phytoplankton Species Richness (S-l/lnN) - May 74
CTv
00
8
Lower Detroit
River
Flow "^
United States Shore
Jpper Detroit River
Lower St. Glair River
Upper St. Glair River
-------
Figure 45 . Phytoplankton Species Diversity (3) - August 73
o\
4.0
3.5
3.0
2.5
2.0
1.5
1.0
0.5
0
Flow
United States Shore
Lower Detroit
River
Jpper Detroit River
Lower St. Clair River
Upper St. Clair River
-------
Figure A6. Phytoplankton Species Diversity (d) - November 1973
O
4.0
3.5
3.0
2.5
2.0
1.5
1.0
0.5
0
Flow
United States Shore
Lower Detroit
River
Uppei
jr Detroit River
Lower St. Glair River
Upper St. Glair River
-------
Figure 47 . Phytoplankton Species Diversity (d) - May 74
4.0
3.5
3.0
2.5
2.0
1.5
1.0
Flow _^-
United States shore
..ower Detroit
River
pper
St. Clair River
Lower St. Clair River
IT C> j
-------
(Figure 43). In the St. Clair River species richness increased from the upstream to the
downstream transect, a trend similar to that seen during August. However, rather than
one station exhibiting dominance over another within a transect, derived richness values
within a transect were similar. High species richness occurred at the upstream Detroit
River transect and increased from the United States shore, to mid-channel, to the Canadian
shore. At the lower Detroit River transect the highest richness values occurred nearest
the United States shore, decreased towards mid-channel, and increased again at station
22 (Figure 43). Mean species richness was higher in the upper Detroit River (6.99) than
it was downstream (5.95).
Overall, species richness was lowest during May 1974 and was uniform throughout all
stations with few exceptions (Appendix C-2, Figure 44). Derived richness values from
the upstream Detroit River transect were very similar at the time of this survey, with
a slight increase at the lower Detroit River transect. As occurred in the August and
November collections, species richness values in the lower Detroit River were higher near
the United States shore than at mid-channel.
Species diversity (d) exhibited more uniform trends than did species richness (S-1/lnN).
During August 1973 diversity increased from the upper to the lower St. Clair River,
decreased slightly at the upper Detroit River transect, and dropped to its lowest values
at the lower Detroit River transect (Appendix C-2, Figure 45).
During November 1973, species diversity was higher at most stations than during August.
Similar to the Aigust collections, diversity increased from the upper to the lower St.
Clair River and also increased at the upper Detroit Rver transect (Appendix C-2). In
any comparison between transects diversity was similar. At the downstream Detroit River
transect there was a decrease in diversity, although stations 19 and 22 had values similar
to many of the upstream stations (Figure 46).
Greatest uniformity in species diversity between all stations was observed during May 1974.
The only shift was a slight increase in diversity after the upstream St. Clair River transect.
The Detroit River carried a slightly more diverse phytoplankton population than did the
St. Clair River during May (Appendix C-2, Figure 47). Contrary to the low diversity
seen at the downstream Detroit River transect during August and November, this transect
produced a diverse population during May.
Similarity - There was a low degree of similarity between phytoplankton populations in
172
-------
the St. Clair River (stations 1-4) during August and November 1973 with somewhat higher
similarity during May 1974 (Table 27). Stations 1 and 2 of the upstream St. Clair Rver
transect were less than 50 percent similar (0.431) at the time of the August survey.
Likewise, station pairs 1/3 and 2/3 were less than or equal to 50 percent similar. Greatest
similarity was between station pairs involving station 4.
Parallel trends in similarity were observed in the St. Clair River during November (Table
27). Station pair 1/2 had the lowest similarity (0.522) which approaches the lower limit
of similarity (arbitrarily selected as 50 percent). Station pairs 2/3 and 3/4 were the most
similar, and similarity was highest in paired combinations involving stations 3 or 4 of
the lower St. Clair River.
Highest overall similarity in phytoplankton populations in the St. Clair River was observed
during May 1974. Station pair 1/2 which had no, or low, similarity at earlier dates,
was similar at the 65 percent level (0.657) during May. Downstream station pairs exhibited
higher similarity, and, as before, highest similarity usually involved paired combinations
with stations 3 and 4.
Similarity of phytoplankton populations between stations in the Detroit River was low
during August and November 1973. Values slightly below to slightly above the arbitrary
50 percent level of similarity were not uncommon (Tables 28 and 29). As seen in the
St. Clair River, similarity during August was very low. There appeared to be slightly
higher similarity within the downstream Detroit River transect than within the upstream
transect during August. Cross pairing of stations between upper and lower Detroit River
transects produced very low population similarity (Table 28).
During November there was higher plankton similarity between stations in the Detroit
River than during August. When stations within a transect (upstream or downstream)
were paired similarity was always greater than 50 percent, usually near the 60 percent
level. Furthermore, there was good similarity between station pairs of different transects,
e.g., 5/19, 6/20, 7/20, etc., with no value being less than 55 percent and most being
above 60 percent.
High levels of similarity occurred during May 1974 (Table 30). Since no sample was
obtained from station 7 there are fewer comparisons to make in the Detroit River. At
the downstream transect, adjacent station pairs were more similar than nonadjacent pairs,
i.e., 19/20, 20/21, and 21/22 were more similar than 19/21, 19/22, and 20/22. This
173
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Table 27. PHYTOPLANKTON SIMILARITY - ST. CLAIR RIVER
Piriot's Similarity Coefficient 2c
a+b
A: August 73
Stations 1234
1
2 0.431
3 0.500 0.459
4 0.566 0.619 0.571
B: November 73
Stations 1 2 3 4
1
2 0.522
3 0.579 0.759
4 0.613 0.667 0.729
C: May 74
Stations 1234
1
2 0.657
3 0.627 0.725
4 0.667 0.732 0.647
174
-------
Table 28
Stations
5
6
7
19
20
21
22
PHYTOPLANKTON SIMILARITY - DETROIT RIVER, AUGUST 1973
Pirlot's Similarity Coefficient 2c
20
5
0.464
0.508
0.500
0.454
0.533
0
0
0
0
6
.542
.457
.454
.533
a + b
7 19
0.526
0.500 0.602
0.603 0.500
21
0.554
Table 29.
Stations
5
6
7
19
20
21
22
PHYTOPLANKTON SIMILARITY - DETROIT RIVER, NOVEMBER 1973
Pirlot's Similarity Coefficient 2c
21
0
0
0
0
0
0
5
.660
.589
.653
.690
.611
.636
0
0
0
0
0
6
.602
.602
.630
.550
.583
7
0.
0.
0.
0.
615
645
568
619
a + b
19
0.
0.
0.
624
543
577
20
0.686
0.651
22
0.649
175
-------
Table 30. PHYTOPLANKTON SIMILARITY - DETROIT RIVER, MAY 1974
Pirlot's Similarity Coefficient 2c
a+b
Stations 5 6 7 19 20 21 22
5
6 0.779
7 - -
19 0.729 0.744
20 0.703 0.779 - 0.760
21 0.737 0.711 - 0.643 0.725
22 0.693 0.711 - 0.643 0.622 0.773
176
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same trend was seen during August and November (Tables 28 and 29). During May the
cross-pairings between transects also produced high levels of similarity, none being less
than 69 percent.
Discussion
Benthos -
The St. Clair River is characterized by a benthic community adapted to living in a rapidly
flowing system, with hard substration at the headwaters and somewhat more fines, detritus,
etc. in the lower reaches. The preponderance of the Gastropod Goniobasis sp. at the
headwaters illustrates this fact, as this organism has an extremely heavy shell and is able
to maintain a hold on hard surfaced substratum in high velocity flow situations . The
environmentally critical condition throughout the St. Clair River would seem to be flow
velocity and not pollution, posed on the observed benthic macrofauna. The species collected
are intolerant to mildly tolerant to pollutant additions or presence . The Detroit River,
although influenced by current velocity, evidences major pollutional conditions throughout
the benthic community in several regions. The transect at Peach Island shows a community
unaffected by major pollutional sources. The presence of the Hydorpsychid caddisflies
and Amphipods is characteristic of a healthy southern Michigan river. The lowered total
numbers and diversity during the May survey was undoubtedly due to increased flow
produced by snow melt and spring rains. From these initial stations located at the
headwaters of the river to river mile 20 there is a progressive degradation of the benthic
community. Below the reach associated with the Rouge River confluence to Mud Island
an abrupt change in the benthos is evident. Samples taken between river miles 19.0 and
12.0W had severely limited benthic communities, all of which had population structures
of greater than 70 percent tolerant species. This condition is indicative of severely polluted
environments57 (Figure 48). The fact that samples collected near Mud Island had not
fewer than 98 percent tolerant forms, primarily Limnodrilus, is evidence of a higher
polluted situation. The stations downstream from this area along the United States shore,
and particularly through the headwaters of the Trenton Channel, also had very high levels
of tolerant benthic forms, animals that can grow and develop in a wide range of
environmental conditions. These species are generally insensitive to a variety of
environmental stresses such as the highly organically enriched areas previously mentioned.
The river below station 15 (river mile 12.0W) begins a natural recovery in the benthic
community (Table 19), although this "recovery" is faster along the Canadian shore and
in the main channel. However, at river mile 3.9, which can technically be considered Lake
Erie, the converse is true with respect to presence of tolerant forms. Stations 21 and
22 have high percentages of pollution tolerant or facultative organisms. This condition
is due to the shifting of bottom and not entirely to pollutional enrichment from farther
upstream. The principal animals collected here were the Sphaeriidae, which are capable
of surviving for sustaiped periods the moving and shifting substration by closing the mantle.
The oligohumic Chironomid Tanytarsus was also collected in "this area.
' " * " * •.,
177 • •
-------
Figure 48. Percent tolerant versus intolerant taxa at
Benthos stations in theVpetroit River,
November 1973 and May 1
-intolerant forms
-Trichoptera, Ephememrop
Amphipoda, Gastropoda
-tolerant forms
xxx - no sample
1 73
-------
03
0)
I
-------
The overall pattern of the macrobenthonic community in the Detroit Rver, then, is one
of a relatively healthy and diverse assemblage from near the headwaters to just above
the Rouge River. At this point the influence on the rivers benthos by industrial and
municipal discharges, compounded by natural conditions, is altogether drastic. Low
numbers of species are represented by very high numbers of individuals and the forms
are largely tolerant to environmental stress.
Phytoplankton -
Phytoplankton populations in the Lake Huron-Lake Erie connecting waters (i.e., the St.
Clair and Detroit Rivers) are probably more important in terms of their potential rather
than their present development. The occurrence and abundance of phytoplankton in a
lotic ecosystem (running-water) is dependent upon many factors, and the extent of
development is at most minimal when compared to a lentic system (standing-water).
Limnologists who have studied lotic systems basically agree that rivers are dependent upond
adjoining lakes, pools, backwaters, and tributaries for plankton organisms and that the
development of these populations is affected by current velocity, turbidity, and age of
the water°°'°°'°0 . River plankton is therefore a composite of a pparticular drainage
and will vary, often significantly, with time and distance. Some species are able to
reproduce to significant numbers in rivers depending on rate of flow and nutrient
availability. Common river species are included in the genera Fragilaria, Synedra,
Asterionella, Cyclotella, and Stephanodiscus and the green algae Scenedesmus and
Pediastrum *** ®' . As current velocity slows, and temperature and nutrients increase, there
are shifts in dominant species from diatoms to green and blue-green algae . These
conditions develop near the banks of a river before they do at mid-channel, thus initiating
more "well-developed" plankton populations along the edges of a river (i.e., more total
species and total individuals)^4,59,60
When rivers flow into lake systems, the planktonic organisms are almost immediately
subjected to a different set of conditions and respond accordingly. Some species decline
in numbers while others reach "bloom" proportions depending upon their autecology,
responding to changes in pH, alkalinity, nutrient availability, light penetriation,
temperature, sedimentation, and a wealth of other physical-chemical parameters. This
in part dictates the development of phytoplankton in the St. Clair and Detroit River
systems. Plankton from Lake Huron is subjected first to river conditions, specifically
a fast flow rate as it enters the St. Clair River, and is later subjected to lake conditions
180
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as it enters Lake St. Clair. These same waters, after a relatively short rention time in
Lake St. Clair, are again subjected to lotic conditions in the Detroit River, only to be
eventually deposited in the western basin of Lake Erie.
The use of chlorophyll measurements gives an indication of algal biomass as it represents
about one to two percent of the algal dry weight . Also the amount of different
chlorophyll forms (a, J), andjc) give an indication of the taxonomic group or groups of
fi1 R^ fi*^
algae which are present '' . The data which have been presented show that the
upstream and downstream transects of the St. Clair River supported similar algal biomass
when expressed as chlorophyll a (yg/l), with the downstream transect being slightly lower.
This is the probable result of the fast flow rate and the lack of new sources of plankton
which are occassionally added to any river system. Lake Huron plankton, measured at
the beginning of the St. Clair River, maintains a similar level as it passes to the lower
St. Clair River measured near Algonac, Michigan before it enters Lake St. Clair. This
is not to say that the population remained static. The population probably decreases
and increases as the river descends to Lake St. Clair, however in total, it is not too different
between the upstream and downstream areas.
This is further shown by little difference in the mean number of individuals/ml between
river areas. Species richness, diversity, and population similarity indicate a changing
plankton population from upstream to downstream in the St. Clair River. It appears
as if different populations enter the St. Clair River on opposite shores and becomes mixed
with distance downstream. Dominant species are similar, while there are shifts in the
commona and occassional species. Population similarity stabilization as it nears Lake St.
Clair. At no point did extremely low levels of species richness or species diversity occur
in the St. Clair River. This river relfects Lake Huron phytoplankton and, due to physical
factors, has little potential to develop into a nusiance phytoplankton population.
When chlorphyll data collected on this survey are compared to other studies similar results
prevail. Data for 1973 from the Ontario Ministry of the Environment indicated an overall
mean chlorophyll a_ level of 1.2 yg/l at the beginning of the St. Clair River. At a similar
downstream transect the Ontario data indicates an overall mean chlorophyll a level of
about 1.04 yg/. Analyses from this survey produced chlorophyll jj_values of 1.2 and
1.4 (+0.13) yg/l at the upstream transect and 1.1 and 1.2 (+0.13) ug/l at the downstream
transect. ChlorophyllJ^ levels in this survey and from the Ontario data are in the range
of 0.2-0.6 yg/l.
From two collecting periods in the Detroit River (November and May) it was shown that
181
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the upstream and downstream areas produced similar, yet different, chlorophyll aJevels.
However, when mean values of all samples are considered there was a slight increase at
the downstream area (i.e., 2.04 ug/l chlorophyll ^ upstream as opposed to 2.4 u g/l
downstream). This is contrary to the St. Clair River trend which showed a slight decrease
in chlorophyll a_ with distance downstream. Data from the Ontario surveys of 1973
indicated a decrease in chlorophyll a^ in going from the upstream to the downstream areas
of the Detroit River (mean upstream concentration of 5.9 \i g/l; mean downstream
concentration of 3.4 yi g/l). These data represent many more measurements than this
survey, and extended over a 12 month period. In the current survey the little difference
in chlorophyll b_ did not affect the chlorophyll b/a_ratio which suggests similar plankton
populations in the two areas of the Detroit River.
Species richness, diversity, and similarity support the trends shown by the chlorophyll
data. The lower Detroit River was not greatly different from the upstream area. The
downstream transect was shown to carry slightly more green and blue-green algal species
during August and November. This trend, discussed earlier, occurs as rate of flow begins
to decrease and temperature and nutrient availability increases. Dominant and common
species were characteristic of river plankton as discussed earlier. Species richness and
diversity were low at only one or two stations on different dates but were otherwise
relatively high. Richness was at times greatest along the shore areas, a trend of river
plankton suggested by other researchers54,59,60 ^ anc| va|ues increased slightly in going
downstream, except during November. This is the result of an increase in the number
of species, as the total number of individuals did not change greatly. Shannon-Weaver
species diversity tended to decrease at the downstream Detroit River transect, a trend
usually associated with declining conditions of water quality. The degree of difference
between the upstream and downstream transect was not, however, extreme.
A general overall trend of increasing numbers of individuals/ml was seen in moving from
the upper St. Clair River to the lower Detroit River. Likewise species richness increased
with distance from the St. Clair River to the lower Detroit River while species diversity
was similar to slightly lower. This is not different from the trend shown in 1966 and
1967 where there was 540 asu/ml at Sarnia and 720 asu/ml at Windsor (1966) and 434
asu/ml and 79 asu/ml (1967) respectively^4. An "asu/ml" is a calculated surface area
of individuals, similar to, but less meaningful than, volumetric biomass determinations (1
asu/ml = 400 u2 ).
At no time was there a plankton population of "bloom" proportions. Sawyer^ has
182
-------
indicated that total inorganic nitrogen levels of 0.30 mg/l and orthophosphate-phosphorus
levels of 0.01 mg/l are sufficient to initiate blooms of nuisance algae. Levels determined
in the present survey were not of this magnitude. As stated earlier, the concern of the
Detroit River and its phytoplankton population is its potential to produce "bloom"
conditions of nuisance algae in Lake Erie. In order to better define this potential and
the acute role of plankton in the Detroit River it is recommended that tests using the
fifi
algal assay procedure00 be pursued. A project of this nature could better predict the
critical levels and ratios of nitrate, phosphate, and carbon.
183
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SECTION VI
MATHEMATICAL MODEL FOR THE DETROIT RIVER
INTRODUCTION
A steady state mathematical model was developed for the Detroit River from its head
at Lake St. Clair to its mouth at Lake Erie. The basic computer program used for this
study is the Steady State Modeling Program (SSMP) developed by Canale and Nachiappan
67
Several assumptions were made during the model construction. The first assumption of
steady state conditions was inherent in the choice of SSMP as a model. This choice
was based on several considerations including the type of river data generated from past
and present monitoring programs; the industrial and municipal loading data available, and
the general characteristic of the river system. As discussed previously in this report, the
monitoring network along the river generally obtains samples once a month for six months
during each year. Industrial surveys are performed by grab samples being taken at various
times during the year. Recently, a self-monitoring program by the industries was initiated
with grab or composite samples being taken a few times each month. Considering this
data base, all simulation runs are based on average steady state conditions for a six month
period in any given year.
SSMP is capable of handling one, two, or three dimensional analysis. A three dimensional
system was chosen for the Detroit model in order to provide maximum flexibility in use
of the model. This system is designed so that, in addition to considering the water
interfaces (lateral and longitudinal) between segments, the sediment-water interface along
the bottom of the river can also be included. As more sediment and sediment exchange
information becomes available, it is hoped that this flexibility will allow the simulation
of the water-sediment boundary exchange conditions for such parameters as nutrients and
metals.
For most of the parameters to be discussed, conservative kinetics (reaction rate = 0) have
been assumed. However, the model is capable of simulating first order reaction kinetics
and a coupled system, such as BOD-DO.
Thus the Detroit River model developed during this study is a three dimensional, steady
state model with an option of choosing a simulation for conservative substances or those
which follow first order reaction kinetics.
184
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MODEL FORMULATION
Theory
The development of the Detroit model is based on the laws of continuity. In examining
the continuity equation (see Equation 1 and 2) it can be seen that two distinct types
of mechanisms are involved in altering the concentration of a chemical or biological
substance. The first mechanism involves the concept of reaction kinetics. Kinetic
expressions can be dependent on a number of parameters including concentration,
temperature, pH etc. The second mechanism involves mass transfer concepts including
advective flow (bulk flow) and dispersive flow (small scale movement and concentration
gradient effects).
It is not possible to solve Equation 2 directly for natural systems. Therefore it is necessary
to make approximations which are equivalent to considering a body of water as a network
of finite interconnected segments as shown in Figure 49. The steady state continuity
equation with first order kinetics can then be reduced to the following:
dC,
vk_Ji =0= n -QkjC«kjck+ ekjcj)+Ekj(Cj-ck)>-vkKkck+wk ^.
where:
C, = concentration of water quality variable in segment
K k, (mg/1)
V, = volume of segment k, (eft)
Q, . = net flow from segment k to segment j (positive
•"* ward) (cubic feet per second)
a, . = finite difference weight given by ratio of flow
3 to dispersion, 0
-------
Rate of Change of i
vith time within a
cell
(weight/time)
Rate of Input of i
by convection» dis-
persionj sedimenta-
tiorii or migration
from adjaceht cells
(weight/time)
Rate of Output of
i by convection»
dispersion, sedi-
roentationj or
migration from
adjacent cells
(weight/time)
Rate of Production
of i by growth»
excretion, or
dissolution tfithin
cell
(weight/time)
Rate of Disap-
pearance of i by
uptake, predation,
respiration, death,
or precipitation
(weight/time)
(1)
Composltiort Change
ilyclrodynamic Mechanism
Reaction Mechanism
00
ACCUMULATION
V-(EVC)-V<(UO
DISPERSION BULK FLOW'
4-
(2)
REACTION
-------
Figure 49. Uniform Rectangular Volume
00
'k3
Jk5
'kl
-------
The above units for the parameters are those commonly used in practice and may be
changed according to user preference.
For a river system represented by n segments (cells) the solution to equation 3 is obtained
by solving a set of n simultaneous equations in n unknowns. There are several numerical
methods for solving such a set of equations. SSMP uses a Gaussian eleimination technique.
Equation three is applicable to single dependent variables, such as chloride, BOD, and
coliform. Other systems, such as dissolved oxygen, are coupled to other quality systems.
The mass balance for a coupled system such as D.O. would be as follows:
dC,
where C^ is the saturation value of D. O., Kgk is the reaeration coefficient in segment
k, K^ is the deoxgenation coefficient, L is the biochemical oxygen demand and +W
is now interpreted as sources and sinks of D. 0. such as benthal demands and
photosynthetic production or respiration. With Lk known from previous calculations,
the final solution of Equation 4 is similar to the solution of Equation 3.
Thus, the river is represented as a three dimensional network of interconnected completely
mixed segments, characterized according to the physical properties of a particular river
system.
A more detailed discussion of the theory and solution techniques is given in the Appendix
D.
River Characteristics and Segmentation
The Detroit River was divided into 73 segments. The resulting system of coupled segments
is represented in Figures 50 and 51. The size, number and placement of the segments
was based on an examination of available water quality data, location of major wastewater
inputs and on the flow pattern of the river. In analyzing this information, it was found
that the Upper Detroit River (Peach Island to Zug Island) was fairly uniform in the
concentration of various pertinent parameters and contained few waste inputs. Therefore,
large segments were used in this section of the river with generally two segments across
188
-------
Figure 50. Model Segmentation
Upper Detroit River
LAKE ST. CLAIR
X
MICHIGAN
Note: Not Drawn to Scale
Approx. only
189
-------
23-26
37-40
HONGUAGOW CREEX
Four Segments
Across Channel
MICHIGAN
56-59
60-63
Note; Not Drawn to Scale
Appro*, only
-------
the river and each segment approximately two miles in length. In the lower river (below
Zug Island) the characteristics changed considerably. There are many waste inputs along
the banks of the river and large concentration gradients were found between shoreline
stations and center channel stations. As a result, a more detailed segmentation was used
in this portion of the river. An example is the Trenton Channel running between the
U. S. shore and Grosse Me. This portion of the river is only 1000-1500 feet wide. However,
because of the large concentration gradients, the river width was divided into four segments.
The segments were also much shorter than the upper segments due to the large number
of waste inputs. This more detailed characterization was followed throughout the Trenton
Channel all the way to Lake Erie. The rest of the river was divided using similar
considerations as discussed above (concentration gradients, waste inputs, flow routing).
Islands located in the river were handled by starting new segments on each side of the
Island and splitting the flow according to the available flow routing information. A few
of the very small islands were incorporated within one segment. Several segments in the
river were designed to contain water-sediment boundary conditions. The choice of these
segments was based on general characteristics of the river (depth, water velocity, proximity
to waste inputs, etc.) and on information gained during the core sampling portion of
the survey program. The cross sectional area of the water-sediment interface was calculated
for these designated segments and incorporated with the physical description in the model.
The schematization was prepared using U. S. Department of Commerce, National Ocean
Survey, Lake Survey Center, navigation chart No. 400, scale 1:15,000. These maps were
used to determine the cell widths, characteristic lengths, depths, and volumes. Flow routing
/^
for the river was obtained from the U. S. Public Health Service report0 .
The flow rate in the Detroit River is exceptionally steady. The average discharge for
the period of 1936 through 1973 was approximately 185,000 cfs. The average flow during
1962 through 1964 was 170,000 cfs. Flow rates have been somewhat higher in the last
few years averaging 200,000 to 220,000 cfs. A table of flow rates used in the model
for various years is given in Appendix D. Flow information was obtained from the U.
S. Department of Commerce Lake Survey Center.
Kinetics
As discussed previously, both conservative substances and substances following first order
reaction kinetics may be simulated using the model. In most cases the parameters chosen
191
-------
in this study were of a conservative nature. The type of kinetics assumed for each of
the specific parameters will be indicated in the discussion with respect to the individual
parameters.
Dispersion
Specific dye tracer studies were not part of this project and consequently it was not
possible to calculate dispersion coefficients from such data. However, the Public Health
Service report contained some dye tracer information on a qualitative basis, and also
included maps indicating zones of pollution and the paths they traveled. Examination
of river water quality information gathered since the Public Health report supported the
various zones and pathways which had been defined earlier. This information, coupled
with the large flow rates and swift velocities characteristic of the river, indicated that
advective (bulk) flow was the major type of mass transfer in the river.
Several dispersion coefficients were tried ranging from .01 to .25 sq. miles/day. A
coefficient of .05 sq. miles/day for lateral dispersion and a coefficient of .10 for longitudinal
dispersion gave good results. These values were tested using chloride data for 1968 and
1969. A further discussion of this procedure is given in the chloride discussion below.
These values appear reasonable in light of the characteristics of the Detroit River mentioned
above.
VERIFICATION
The previous section detailed the Detroit River model in its general form and considered
the physical representation of the river. These characteristics (segmentation, flow rates,
flow patterns, dispersion), when input to the general modeling program (SSMP), define
the model specifically for the Detroit River system. As such, they remain constant
regardless of which chemical parameter (chloride, phenol, etc.) is chosen for simulation.
The following section will discuss the individual parameters which were modeled, and will
consider the input variables which change for each specific parameter. These variables
include input loads, boundary conditions, and reaction kinetics.
The river water quality data used in the verification for each parameter was obtained
from various sources including, Public Health Service report, U. S. Environmental Protection
Agency Storet System, and the Ontario Ministry of the Environment Water Quality
Information System. Data obtained from these sources was averaged for each of the
192
-------
years investigated (i.e. at milepoint 14.6 station, 100 feet from shore, average chloride
concentration, 1968, was 35 mg/l). These average values were then plotted versus distance
from shore for each mile point along the river. Segments defined in the model were
then matched with the appropriate mile points, and the widths of these segments were
marker) on the graphs at the proper intervals. The model treats each segment as a completely
mixed cell and consequently, overall averages were obtained for each appropriate width
by using individual station values, drawing a curve through them, calculating the area under
the curve, and dividing by the width. Ai example is given below to illustrate this procedure.
Average chloride values for 1968 at milepoint 17.4W were obtained from the Storet System.
Information was available for stations located at 100, 200, 400, 800, 1200, 1600, and
1900 feet from the U. S. shore. The average concentration of chloride for each of these
stations was 23.6, 19.6, 14.4, 12.4, 10.8, 10.4, and 10.5 mg/l respectively. These averages
were based on samples taken from April through October, 1968. Using these values,
a plot of concentration versus distance from shore was developed. (See Figure 52). Three
model segments (19, 20, and 21) are located at milepoint 17.4W. These widths were
defined as 900 feet, 800 feet and 700 feet, respectively. Thus segment 19 includes the
area from 0-900 feet from the U. S. shore,segment 20 includes 900-1700 feet and segment
21 includes 1700-2400 feet. These widths are marked on Figure 52. An average value
for each segment was then obtained by calculating the area under the curve and dividing
by the width. Average values were obtained in this manner for all milepoints at which
data was available. These averages were then used to compare the actual river quality
data with the concentrations predicted by the model.
Industrial and municipal waste input data was obtained from various sources, including
the Michigan Water Resources Commission's monitoring programs, the industrial
self-monitoring program. City of Detroit Waste Treatment Plant records, and the Public
Health Service Report. The various industrial and municipal outfalls were located from
maps provided by the Michigan Water Resources Commission. A listing of these outfalls
and the segments into which they flow is given in Appendix D. Each industry contained
one, two or many outfalls. In the case of those industries with several outfalls, the loading
for each outfall was calculated, and then combined into one load for the industry. Loadings
were obtained by averaging available data on a yearly basis. The type of data available
differed widely in frequency of sampling, types of samples, parameters measured, etc.
Where possible, averages were obtained from monthly or semi-monthly reports. For some
cases the data was scattered, but could be used to obtain approximate values. In other
193
-------
Figure 52. Average Chloride Concentration
Detroit River Dt 17.4W 1968
16
bO
E
100
Segment 19
1
Segment 20
1
Segment 21
1
500 1000 1500 2000
Distance from U.S. shore (feet)
-------
cases certain information, such as flow rates, was not available at the precise sampling
time, but information was available from other time periods or other records. In these
cases averages were again approximated and generally reported as ranges of values. Finally,
in some instances little or no information was found, and best estimates had to be made
based on data of previous years or other general information obtained. A complete listing
of loadings used for various runs is given in Appendix D.
Boundary conditions were established from river quality data. In general, the
concentrations found at milepoint 30.8 and milepoint 20.6 were similar, as no major
industrial or municipal plants have outfalls in this section of the river. Consequently,
boundary conditions were determined from data available at these two milepoints. These
boundary concentrations were entered into the model to serve as a starting level of the
various model simulations.
DISCUSSION
Chloride
During 1968 and 1968, a survey of industrial waste discharges along the Detroit River
was conducted by the Michigan Water Resources Commission. This survey indicated that
the major sources of chloride from the United States side of the river were Wyandotte
Chemical Corporation (north and south works) and Pennwalt Chemicals Corporation. Other
major sources were the Detroit Wastewater Treatment Plant, Wayne County Wastewater
Treatment Plant and the Rouge River. The loading data provided by this survey was
used as input data in the model. During the same time period, river water quality data
was being obtained through the monitoring network.
Chloride was assumed to be a conservative substance for all simulation runs. Thus the
reaction coefficient k was set equal to zero (k=0).
Having defined the input loads and kinetics for the system, the only remaining unknown
was the magnitude of the dispersion coefficient. As discussed earlier, some information
was available for use in estimating the lateral and longitudinal dispersion coefficients.
r\
Several coefficients were tried ranging from 0 to .25 miles /day for lateral dispersion
r\
and 0 to 1.0 miles /day for longitudinal dispersion. A reasonable fit of the data was
obtained using .05 miles^ /day for lateral dispersion and .10 miles^/day for longitudinal
dispersion. The results for selected stations are presented in Figures 53-57. A complete
195
-------
cr>
50
40
30
•8 20
•H
o
10
50
40
bO
30
•a
•H
o 20
10
0
&
o
Figure 53 . Model verification - chloride
Detroit River - DT 14.6 and 12.0 - 1968
DT 14.6 W
• average measured concentration
— model predicted concentration
J_
1
100 400 800 1,200
Distance from U. S. shore (ft.)
DT 12.0 W
I
1
1
100 300 600 900 1,200
Distance from U. S. shore (ft.)
1,600
2,000
-------
1— 1
bO
-------
00
bO
E
100
Figure 55. Model verification - chloride
Detroit River DT 20.6 and 17.4W 1969
DT 20.6
• average measured concentration
— Model predicted concentration
I
i}00 800 1200
Distance from U.S. shore (ft.)
100
DT 17.
5
bO
e
~
d
20
16
12
Q
o
n
_ *
•
* • • •
.
II 1 1 1
500 1000 1500
Distance from U.S. shore (ft.)
2000
-------
Figure 56. Model Verification - chloride
•H
M
e
rH
U
rH
M
H
U
50
'
140-
30
20
10
0
V C I/ J. V_l X L- JX-LVCl — 1^ J. J-1 . U W aiiU J.C..UKV J-^U^
DT H.6W
— • average measured concentration
— model predicted concentration
' •
' 1
1 I . , ,
100 500 1000 1500 2000
Distance from U.S. shore (ft.)
50
10
30
20
10
0
DT 12. OW
^»
.
L 1 ,
100 5nA 1000
Distance from U.S. shore (ft.)
-------
NJ
O
O
Figure 57,
bQ
30
20
10
100
50
40
_ 30
rH
j= 2°
o 10
0
1000
Model Verification - chloride
Detroit River DT 8.7 W and 3.9 1969
DT 8.7 W
• average measured concentration
_ model predicted concentration
I
I
500 1000 1500
Distance from U.S. shore (ft.)
DT 3.9
JL
5000 10000 15000
Distance from U.S. shore (ft.)
20000
-------
listing of industrial loads and model results is given in Appendix D. At this point, the
results of the model simulation were quite good. However, for full verification, additional
data; preferably under different loading conditions, needed to be examined.
Additional loading information and river water quality data were available for the years
1972 and 1973. The results for these simulations are presented in Figures 58-60. A
complete listing of loads and model output is given in Appendix D. The comparison
of model output with river data again was quite good. These runs were made without
further adjustments of the dispersion coefficients.
The model was tested for five separate years (1963, 68, 69, 72, 73). In 1963, 68 and
69 the total loadings to the river were much higher than in 1972 and 1973. The reduction
in loading and subsequent water quality improvement has been discussed in the trend
analysis section of this report. The model simulation also reflected this water quality
improvement.
During the test runs for 1963, (see Appendix D), using data from the Public Health Service
Report, it was found that all predicted chloride levels were lower than the measured
concentrations. Upon further examination, however, it was found that this should be
expected. In the Public Health Service Report, a mass balance of chloride was presented
which indicated that the measured loadings accounted for only a portion of the total
chloride measured in the river. Thus, it would be expected that predicted levels using
these loads would be somewhat lower than actual values. The spatial distribution predicted
by the model did follow the general pattern of the measured values. By increasing the
loading levels, to account for the discrepancy in the massbalance, the results correlated
with the river data. This case serves to illustrate the point that a model is only as good
as the data available.The analyst's care in choosing proper input data and the subsequent
interpretation of the results is an important part of using a model as a tool. In this
case, the results of the model indicated a problem, and upon further examination of the
data, the discrepancy between loading data and river levels was found. Thus, the results
of model supported the results of the Public Health Service Report from which the input
data had been taken.
Overall the predicted levels for each year agreed quite well with observed data. In each
case, it was possible to predict the average concentrations of chloride in the river using
only waste input data and the appropriate flow rates. The dispersion coefficent was chosen
based on 1968 data and was not changed in the simulation for other years. This same
201
-------
12
Figure 58- Model Verification - chloride
Detroit River DT 20.6 and 19.0 1972
DT 20.6
50
E
average measured
concentration
Model predicted
concentration
ro
o
to
100
I
MOO 800 1200
Distance from U.S. shore (ft.)
15
10
DT 19.0
0
100
I
I
I
400 800 1200
Distance from U.S. shore (ft.)
-------
bO
E
15
F igure 59. Model verification - chloride
Detroit River - DT 111. 6W and 12. OW 1972
DT 1H.6W
10
• average measured concentration
— model predicted concentration
fo
O
LO
100
JL
_L
500 1000 1500
Distance from U.S. shore (ft.)
2000
bO
2*1
16
DT 12.OW
100
500 1000
Distance from U.S. shore (ft.)
-------
NJ
o
to
Figure 60.
30
20
10
100
Model verification - chloride
Detroit River DT 8.7W and 3.9 1972
DT 8.7W
• average measured concentration
— model predicted concentration
I
_L
500 1000 . 1500
Distance from U.S. shore (ft.)
50 I
DT 3.9
M
^H
H
U
30
20
10
0
•
" 1 •
•
j_ •
i
•
1 |
15000
Distance from U.S. shore (ft.)
20000
-------
model was used for all of the other parameters to be discussed in this section with no
changes in the basic segmentation or dispersion coefficients.
It should be mentioned here that all discussion has centered on the United States shore
and center sections of the river. At the time of verification, Canadian loading information
for the Canadian shoreline was not available. Thus the model at this time has only been
verified for the United States side of the river.
Water quality data for 1973 was received from the Ontario Ministry of the Environment.
Examination of this data and preliminary runs using the model indicated three major
sources of chloride loading to the river. These areas were defined as: near the Canadian
Rock Salt Company Ltd., near the waste beds at the south end of Fighting Island, and
in the Amherstburg Channel near Amherstburg, Ontario. Preliminary estimates for these
loads were made and the results of the model compared favorably with water quality
data. However, these are only preliminary results and must be supported by additional
loading and water quality data. It is hoped that this can be accomplished in the near
future so that a fully verified model for the entire river can be made available.
Phenol
Industrial survey data for the years 1963, 1968, 1969, 1972, and 1973 indicated that
the following industries were discharging phenol: Allied Chemical, Great Lakes Steel,
Pennwalt Chemicals, McLouth Steel and Mobil Oil. The Detroit Wastewater Treatment
Plant and the Rouge River were also sources of phenol loadings to the river.
Phenol is normally considered a non-conservative substance in an aquatic system. However,
the time of passage in the lower Detroit River from Zug Island to Lake Erie is very
short ( 12 hours). Therefore, it was assumed that any degradation of phenol due to
biological activity would probably be small, and treating phenol as conservative substance
(k=0) would be reasonable for this river system. As can be seen in the results, the
assumption proved to be adequate for most sections of the river.
The results for various years at selected stations are shown in Figures 61-67. A complete
listing of model outputs and loadings for the river is given in Appendix D. The initial
verification runs showed good correlation between model results and field data. In each
case, the model predicted increase in phenol concentration below a discharge point
compared closely with the increase measured in the field. However, at two milepoints
205
-------
ho
O
60
3
O
c
12
Figure 61 . Model verification - phenol
Detroit River - DT 1?.4 W and 14.6W 1968
DT 17.4 W
I
• average measured concentration
— model predicted concentration
1
100 400 800 1,200
Distance from U. S. shore (ft.)
1,600
fctO
12
DT 14.6 W
o
c
<1>
a
4
n
•
•
* . •
r 1
II 1 1 1
100 500 1,000
Distance from U.S. shore (ft.)
1,500
2,000
-------
NJ
O
0
c
a
Figure 62 . Model verification - phenol
Detroit River - DT 12.0 W and 8. ?W 1968
DT 12.0 W
_L
J_
• average measured concentration
—model predicted concentration
J.
100 400 800 1,200
Distance from U. S. shore (ft.)
\
20 _
15 -
DT 8.7 W
iH
O
c
0)
a
10
5
0
_
0
.
1
II 1 1
100 500 1,000 1,500
Distance from U. S. shore (ft.)
-------
Figure 63 . Model verification - phenol
Detroit River - DT 3.9 - 1968
10
DT 3.9
• average measured concentration
— model predicted concentration
KJ
o
oo
O
c
d>
o.
6
H
• •
0
I
I
1
1
1,000
5,000 10,000 15,000
Distance from U. S. shore (ft.)
-------
12
M o
a. o
0
§
x;
a
Figure 64 . Model verification - phenol
Detroit River - DT 17.4 W and 14.6 W 1969
100
DT 17.4 W
i
JL
• average measured concentration
— model predicted concentration
_L
400 800 1,200
Distance from U. S. shore (ft.)
TTSSo
12
fan
DT 14.6 W
0
c
0)
JC
4
0
1 ll|,
1,000
Distance from U. S. shore (ft.)
1,500
2,000
-------
Figure 65 . Model verification - phenol
Detroit River - DT 12.0 W and 8.7W 1969
8
x"-v
X 6
faO
3.
rH
O
c
5 2
P.
0
M
DT 12.0 W
— •
• 1
-
II I 1
100 400 800 1,20
o
• average measured concentration
_ model predicted concentration
Distance from U. S. shore (ft.)
20 _
100
DT 8.7 W
rH
bO
rH
O
c
(1)
45
fi,
15
10
5
*s
0
—
*
|
II 1 1
500 1,000
Distance from U. S. shore (ft.)
1,500
-------
12
faO
o
c
0
100
Figure 66 . Model verification - phenol
Detroit River - DT 19.0 and 14.6W- 1972
DT 19.0
• average measured concentration
— model predicted concentration
400 800 1,200
Distance from U. S. shore (ft.)
8
6
to
o
c
2 2
1
DT 14.6 W
1
100 500 1,000
Distance from U. S. shore (ft.)
.
1,500
2,000
-------
ho
O
£ 2
x:
a
Figure 67 . Model verification - phenol
Detroit River - DT- 12.0 W and 8.7 W 1972
DT 12.0 W • average measured concentration
— model predicted concentration
I
_L
I
100 1JOO 800 1200
Distance from U. S. shore (ft.)
iH
*> 8
100
DT 8.7 W
phenol
o j=-
1
•
1
1 1 1
500 1,000
Distance from U.S. shore (ft.)
1,500
-------
(14.6W and 3.9) the model predicted levels were much higher than the measured
concentrations.
An examination of the measured phenol concentrations at milepoints 17.4W and 14.6W
(see Figure 61 and 64) shows that a considerable drop in phenol levels occurs between
there two stations. At the present time there is no documented evidence as to exact
nature of the phenol "sink". There is some information that indicates a
sorption-sedimentation process may be responsible for the drop in concentration. This
section of the river (between 17.4 and 14.6) is wider and shallower than the immediate
upstream sections, and river velocities appear to be slower. The Detroit Wastewater
Treatment Plant, and the Rouge River and Great Lakes Steel are all located just above
milepoint 17.4W. Each of these are sources of suspended solids, iron, and other heavy
metals, in addition to phenol. In analyzing the iron data for this section of the river,
it can be seen that iron concentrations follow a pattern similar to the phenol levels. The
iron concentrations decrease considerably through this section of the river. Core samples
taken during the survey program also indicated an increase of iron and other heavy metals
in the sediment in this area. A more detailed discussion of the sediment condition is
given in the chemistry section of this report.
A similar drop in phenol concentration also occurred between milepoints 8.7W and 3.9.
The decrease in this area was much less than at the upstream sections but river conditions
and sediment samples were similar in both cases.
In order to simulate these decreases in phenol concentrations, negative loads were
introduced for those segments of the model located in the areas discussed above (between
17.4W and 14.6W and between 8.7W and 3.9). A listing of the negative loads used in
given in Table 31. At the present time the choice of appropriate negative loads is an
empirical process. However, in the future, as more information becomes available in these
critical areas, it may be possible to develop a mathematical relationship to define these
processes. This relationship could then be incorporated into the model, and based on the
appropriate input parameters, the model could be used to predict the decreased
concentrations in these areas.
Iron
The program for simulating iron concentrations in the river followed the same general
pattern as for chloride and phenol. Loading information was obtained from survey data
213
-------
Table 31 . NEGATIVE LOADS FOR MODEL - PHENOL AND IRON - DETROIT RIVER
Phenol
Area of river
mile points
17.4 W - 14.6 W
8.7 W - 3.9
17.4 W - 14.6 W
Model segment
23
30
60
61
23
30
Iron
1963
#/day
200
400
600
600
-
1968
#/day
400
650
200
200
60000
100000
1969
#/day
200
400
200
200
50000
100000
1972
#/day
300
500
100
200
40000
80000
1973
#/day
300
500
100
200
40000
80000
-------
which indicated Great Lakes Steel, McLouth Steel, Firestone Tire and Rubber, the Detroit
Wastewater Treatment Plant, Wayne County Wastewater Treatment Plant and the Rouge
River as sources of iron input to the river. Iron was considered a conservative substance
for all areas of the river.
A comparison of the model predicted levels versus field data for several stations is given
in Figures 68-73. As in the case of phenol, the results were quite good except at milepoint
14.6W. The drop in iron concentration between 17.4W and 14.6W paralleled the drop
in the phenol concentrations. This phenomenon was handled in the same manner as phenol.
The negative loads used for iron are given in Table 31.
Ammonia
The Public Health Service Study indicated that the major input of ammonia-nitrogen
to the river was the Detroit Waste Treatment Plant. The Detroit Plant has not monitored
ammonia levels in the effluent during past years, and consequently, the only data found
was from the 1963 Public Health Service Study. Assuming the ammonia-nitrogen
concentration (8.0 mg/l NHg -N) has remained relatively constant, and using flow data
measured at the plant, it was possible to estimate the loading levels for several years.
These estimated values, along with measured loadings from other sources (see Appendix
D), were used in the model. As in the case of phenol, ammonia nitrogen was assumed
to be a conservative substance for this river system. Because of the short time of passage
in the system, the effects of nitrification in the river appear to be small. Several test
runs were made to check this assumption. If the oxidation of ammonia is assumed to
follow first order kinetics, the model can be used to project the effects of this oxidation
on ammonia concentrations. The normal range of the first order reaction coefficient for
ammonia is 0.1 to 0.6/day. A value of 0.6/day was used in the model and the results
were compared with the output using the conservative asssumption. The difference in
concentrations between the two outputs was negligible. Thus the conservative assumption
appears to be adequate for this particular river system. The results of the model projections
compared with measured levels is given in Figures 74-79. As can be seen, the simulated
levels compare quite well with measured levels in the river.
It would appear from this study that the estimated levels for the Detroit Waste Treatment
Plant are reasonable. However, these levels should be verified as data becomes available.
Detroit personnel have indicated that ammonia concentrations will be monitored on a
routine basis in the near future. As this information becomes available, the assumptions
215
-------
hfl
0)
100
Figure 68. Model verification total iron
Detroit River DT 17. 4W and 14.6W 1968
DT 17.
•average measured concentration
— Model Predicted concentration
1
0
1 1 1
A _
1 L_
400 800 1200
Distance from U.S. shore (ft.)
i£oo
bO
(Li
1.2
100
DT 14.6W
1
500 1000
Distance from U.S. shore (ft.)
1500
20SO
-------
1.2
5 -8
Jp
«» .4
100
Figure 69.
I
Model verification total iron
Detroit River DT 12.OW and 8.7W 1968
DT 12. OW
1
• average measured concentration
— model predicted concentration
400 800 1200
Distance from U.S. shore (ft.)
fe
1.2
1-1 D
\ • o
fc>0
100
DT 8.7W
400 800 1200
Distance from U.S. shore (ft.)
-------
00
1.2
. 8
M
Figure 70. Model Verification total iron
Detroit River DT 3-9 1968
DT 3.9
• average measured concentration
— model predicted concentration
I
I
1
1
20000
1000
5000 10000
Distance from U.S. shore (ft.)
15000
-------
100
Figure 71. Model verification total iron
Detroit River DT 17.4W and 14.6W 1969
DT 17. 4W
• average measured concentration
— model predicted concentration
bO
~ 2
0)
&H
0
.
_J 1 • 1 f f-
400 800 1200 1600
Distance from U.S. shore (ft.)
fctC
E
0)
1.2
.8
100
1
DT 14.6W
i
,
500 1000 1500
Distance from U.S. shore (ft.)
2000
-------
1.2
Figure 72. Model verification total iron
Detroit River DT 12.OW and 8.7W 1969
DT 12.OW
100
1.5
1.0
bO
E
(U
I
1
1
400 800 1200
Distance from U.S. shore (ft.)
DT 8.7W
• average measured concentration
_ model predicted concentration
I
I
100
400 800 1200
Distance from U.S. shore (ft.)
-------
1.2
.8
K3
Figure 73 Model verification total iron
Detroit River DT 3.9 196Q
DT 3.9
• average measured concentration
— model predicted concentration
I
I
1
1
1
1000
5000 10000
Distance from U.S. shore (ft.)
15000
2000D
-------
Figure 74 . Model Verification - Ammonia Nitrogen Detroit River -
DT 19.0 and 14.6 W - 1972
N>
bC
e
53
i
m
ffi
53
6
.2
0
DT 19.0
J_
I
100 400 800
Distance from U. S. shore (ft.)
• average measured concentration
model predicted concentration
1200
53
on
53
.6
.4
.2
0
I
DT 14.6 W
100 400
Distance from U. S. shore (ft.)
I
TZUCT
-------
l-o
K3
Figure 75 .
.6
Model verirication - ammonia nitrogen
Detroit River - DT 12.OW and 8.7W 1Q?2
DT 12.0 W
• average measured concentratioi
— model predicted concentration
I
100 400 800 1200
Distance from U. S. shore (ft.)
.6
DT 8.7 W
to '"
I .2
en
S
0
^
1
II 1 1 1
100 400 800 1200 1600
Distance from U. S. shore (ft.)
-------
Figure 76 . Model verification - ammonia nitrogen
Detroit River - DT 3-9 - 1972
K3
NO
-p-
.6
1,000
DT 3.9
• average measured concentration
bO
3 .4
i
on
K
.2
0
w
1
i
— i ... i i i ' i
5,000 10,000 15,000
Distance from U. S. shore (ft.)
-------
NJ
N3
Figure 77 . Model verification - ammonia nitrogen
Detroit River - DT 19.0-and 14.6W- 1973
.6
.4
1 ?
oo • £-
0
DT 19.0
• average measured concentration
— model predicted concentration
_L
100 400 800 1200
Distance from U. S. shore (ft.)
bO
E
I
X
0
DT 14.6 W
JL
100 400 800 1200
Distance from U. S. shore (ft.)
-------
NH3-N (m
g/1)- NH3-N (mg/
'D
o ro -fcs
p-t)
H^
CD
3
c!
CO
o
W o
»
CO
3*
0
t-J
fD
x-^»
l-t) (—1
ct ro
o
•—s O
M
C^
O
o
1
—
""
A
_
0
«•
•
o ro 4=- ON
1
1
0
o
O
01
ct jr
P O
3 o
o
CD
f-^
>-$
O
3
.— 1
<— (
*
a
K-3 co oo
o
CO O
CO
—i 3*
O
s: ^
CD
x-x
1-^
Ct
• 1— '
v-^ ro
0
o
•••
A
""" """^"^
c
J
i
1
* **!
P-
OT
0)
00
.
OS
O
ct CL
4 fD
O M
P-
ct <
/T^
(U
P- P-
O ^ M)
H) fD P-
4 0
i_i p
ro i ct
P-
o GO
h3 3
s:
M 1
ro
. p
0 g
^ o
3
. P H-
* 3 P
3 P D,
O < 3
a- a> OOP-
04 . ct
L_J f\\ 1 l-rf
r~
— **• — >j j
M 5* O
"O CD TO
H
! fD
fD 3 M3
••»
h
lj • fD VO
* P — J
O 01 UJ
ct e
fD ""i
C
•L fD
r^
»-"
O
O 0
3 0
0 3
fl> O
3 fD
ct 3
H
rt
5 Ct
•» t_l
K" ' i
ct p
h
* ct
0 P-
3 0
3
-------
Figure 79 . Model verification - ammonia nitrogen
Detroit River - DT 3-9 - 1973
NJ
NJ
.6
5 .«
60
1
sT -2
0
"~ DT 3«9 • average measured concentration
* — model predicted concentration
1
1
i •
* i , — , •
1 1 1 1*1
1,000 5,000 10,000 15,000
Distance from U. S. shore (ft.)
-------
made during these phases of the modeling programs should be checked and documented.
The model should be run using measured ammonia concentrations and checked with data
generated by the river monitoring network.
Phosphorus
Total phosphorus loading information was available from industrial surveys and municipal
treatment plant operating reports. Using this data, and assuming total phosphorus to
be a conservative substance, the model was run for the years 1971, 1972, and 1973.
The results of these runs are presented in Figures 80-88. Comparisons between model
projected levels and measured concentrations were not as good for phosphorus as for the
parameters discussed previously. For all stations except milepoint 3.9, the predicted total
phosphorus concentrations was higher than measured levels. The largest difference was
at milepoint 19.0 just below the Detroit Waste Treatment Plant outfall. At the present
time, there does not appear to be a plausible explanation for this difference.
The Detroit Treatment Plant is the major contributor of phosphorus to the river at this
time. As such, the phosphorus concentration of all of the downstream segments in the
model are influenced greatly by the Detroit load. If the difference between measured
and predicted concentrations just below the Detroit Plant can be resolved, it appears that
the downstream measured concentrations would agree quite well with the model
predictions.
Application
The steady state model developed for the Detroit River has been tested and verified for
several parameters. The model is capable of projecting the steady state distribution of
parameters such as chlorides, phenol, iron, ammonia and total phosphorous. However,
the use of the model as a tool in evaluating the effects of future waste loads depends
largely on the judgment and skill of the analyst. A thorough understanding of the basic
assumptions inherent in the model development, and recognition of various limitations
and problems which occurred during the verification are of the utmost importance when
using the model for projection purposes.
The model can be a helpful tool in evaluating alternate plans for the management of
the river system. The application of the model for parameters such as chloride is fairly
228
-------
IS5
to
bO
1
E-t
.3
.2
.1
Figure 80- Model verification total phosphorous
Detroit River DT 19.0 and 14.6W 1971
100
DT 19.0
1
±
• average measured concentration
— model predicted concentration
±
400 • 800 1200
Distance from U.S. shore (ft.)
.3
^ '2
to
P-.
I
EH
0
DT 14.6W
100
500 1000
Distance from US shore (ft.)
1500
2000
-------
to
u>
bO
PL4
I
100
Figure 81. Model verification total phosphorous
Detroit River DT 12.OW and 8.7W 1971
DT 12.OW
I
• average measured concentration
— model predicted concentration
400 800 1200
Distance from U.S. shore (ft.)
to
DT 8.7W
1
1
1
100
400 800 1200
Distance from U.S. shore (ft.)
1600
-------
Figure 82. Model verification - Total Phosphorous
Detroit River DT 3-9 1971
1000
DT 3-9
• average measured concentration
— model predicted concentration
^~^
r-i
60
E
(X, . 1
I
EH
0
i
*
p 1 '
""""^""''— I
*
1 1 III
5000 10000
Distance from U.S. shore (ft.)
15000
2000D
-------
OH
i
EH
Figure 83 Model verification Total Phosphorous
.3
^ .2
rH
M
£
^ .1
PH
1
EH
0
Detroit River DT 19.0 an
DT 19.0
~ • avera
MB
. *
« 1
— model
1 L_
average measured concentration
— model predicted concentration
100
100
400 800 1200
Distance from U.S. Shore (ft.)
DT 14.6W
.
1000 1500
Distance from U.S. shore (ft.)
2000
-------
t-o
OJ
OJ
. .3
bO • ^
6
OH
cL .1
100
Figure 84 Model verification - Total Phosphorous
Detroit River DT 19-0 and ll|.6W 1973
DT 19.0
• average measured concentration
— model predicted concentration
i
400 800 1200
Distance from U.S. shore (ft.)
100
DT 14. 6W
rH
W>
F
i
.2
.1
0
—
9
,
, I 1 1 1_
5oo 1000
Distance from U.S. shore (ft.)
1500
2000
-------
Figure 85 Model verification Total Phosphorous
Detroit River DT 12.OW and 8.?W 1972
N3
bO
E
PH
I
EH
.2
.1
100
DT 12.OW
I
I
• average measured concentration
— model predicted concentration
I
400 800 1200
Distance from U.S. shore-(ft.)
DT 8.7W
M
E
I
EH
100
1
1
400 800 1200
Distance from U.S. shore (ft.)
1600
-------
bO
E
PL,
I
.3
.2
.1
Figure 86. Model verification Total Phosphorous
Detroit River DT 12.OW and 8.7W 1973
DT 12.OW
• average measured concentration
— model predicted concentration
S3
-------
Figure 87. Model verification Total Phosphorous
Detroit River DT 3-9 1972
U3
.3
.2
H
bO
.1
1
EH
0
DT 3.9
• average measured concentration
— model predicted concentration
<^^mm"^^^
\
"~ ^" ""* "^ _
• •
II 1 1 1
1000 5000 10000 15000 200QD
Distance from U.S. shore (ft.)
-------
Figure 88. Model verification Total Phosphorous
Detroit River DT 3.9 1973
ho
U)
hO
(X,
I
.3
.2
. 1
1
1000
DT 3.9
• average measured concentration
— model predicted concentration
1
5000 10000
Distance from U.S. shore (ft.)
1
15000
2000
J-
-------
straightforward. Through the use of appropriate input loads, the effects of various loading
levels, outfall placement, and other conditions can be estimated. Proper interpretation
of model output can provide insight not only to the effects of waste discharges on river
water quality, but also to other utlimate effects in the water quality of Lake Erie.
The model can also aid in pinpointing those areas of the river which are most critical
in terms of water quality. The evaluation of phenol and iron conditions in the river
serves as a good example. As discussed earlier, the section of river between milepoints
17.4W and 14.6W showed a decrease in both phenol and iron levels. During the modeling
program it became obvious that this area deserved special attention because of this drop
in concentration and the large effects on the downstream areas. The results of the model
study were substantiated and supported by the biological and chemical data obtained during
the surveys. Thus, this area is considered a special section of the river and should be
considered in more detail during future studies on the river. The end segments of the
model are designed to provide input data for Lake Erie. It is anticipated that the Detroit
model can be used in conjunction with the Hydroscience Model for lake Erie to aid
in evaluating alternative plans for the management of this section of the Great Lakes.
Through the proper use of these models, the changes in water quality due to various
control programs along the Detroit River and changes in the water quality of Lake St.
Clair can be evaluated according to their impact on the Lake Erie system.
As in the case of any model, the Detroit River model should be updated and reverified
as additional data becomes available. A program of continual revaluation will assure that
the model reflects current river conditions and will help establish the model as a valuable
asset in the management of the river system.
238
-------
SECTION VII
WATER QUALITY PROJECTIONS
The water quality projections discussed in this section are based on observed historical
trends in water quality, analytical results obtained during this study, and application of
the developed mathematical model, using tentative effluent limitations provided by the
State of Michigan. Each of these areas has been discussed in previous sections, and serves
as a foundation for the projection of water quality under various control alternatives.
Industrial loadings are based on permits issued by the State of Michigan under the National
Pollutant Discharge Elimination System. While these permits are still under review and
may be altered to some degree, they do provide an indication of future loadings that
can be expected. This loading data, utilized in conjunction with the developed mathematical
model, allows a quantitative projection of future levels for pollutants such as chloride,
phenol, ammonia nitrogen, phosphorus and total iron. Background and loading data for
other parameters such as heavy metals is not sufficient at this time to allow a quantitative
projection of future levels, however, anticipated water quality conditions can be discussed
on a qualitative basis. It should be understood at this time that all of the various projections
made, whether qualitative or quantitative, are based on a set of assumed conditions.
(Flow rates, flow pattern, incoming water quality for Lakes St. Clair and Huron, etc.)
If these conditions change, the resultant water quality may vary appreciably from the
projected levels.
For each of the projections in which the mathematical model was used, several assumptions
were needed. The boundary conditions for the incoming water to the river were set
based on 1973 measured values. The flow rate was assumed to be 175,000 cfs, which
is a low flow compared to recent years. It was felt that a conservative set of conditions
would be best for the projection of critical conditions. The model is based on an established
flow and mixing pattern, thus it is assumed in these projections that no major changes
in the flow pattern will occur.
The segmentation scheme for the model is detailed in the modeling section of this report.
239
-------
For purposes of discussion, the concentrations mentioned will be the average concentration
in one segment. Therefore, when a maximum average concentration is discussed and
compared with a water quality standard, that concentration will represent the highest level
for all segments of the river. In most cases this high level will occur in a shoreline segment
near a major outfall. It should be noted that in most cases the segments in the center
of the river will be much lower in concentration. Also, the entire discussion and projections
using the model are for the U. S. side of the river only. The Canadian side of the river
has not been included as the model was not verified for Canadian shoreline stations nor
was any industrial loading data for the Canadian side available at the time of this report.
Little change in existing quality can be anticipated in the St. Clair River. Generally speaking,
the St. Clair River is presently characterized by high quality water, and compliance with
more stringent effluent guidelines will simply assure that this high quality continues. The
primary parameter of concern with regards to meeting current international water quality
guidelines for the St. Clair River is phenol. In recent years the concentration of this
parameter has failed to meet the established guidelines of 2 yg/l average and 5 yg/l
maximum near the Canadian shore at milepoints SR 30.7 and SR 33.1, and near the
United States shore at milepoints SR 33.9, SR 34.4, and SR 35.0. Compliance by industries
on both sides of the river with the effluent guidelines established in 1972 amendments
is necessary in order to decrease the river concentration of this material to the desired
level.
Similarly, the upstream portion of the Detroit River (above the confluence with the Rouge
River) is presently of such a quality as to meet present standards. The only major sources
of waste loads in this section of the river are combined sewer overflows from the City
of Detroit. In the past these overflows had a large influence on the water quality. In
recent years, however, the City of Detroit has implemented a control system whereby
overflow occurrences have been greatly reduced, and consequently exerted less detrimental
influence on water quality.
The lower section of the Detroit River (Zug Island to Lake Erie) receives the largest waste
loads, and is the area where water quality standards are violated most often. At the
present time, phenol standards of 2.0 yg/l average and 5 yg/l maximum are violated
at shoreline stations from the Detroit Waste Treatment Plant to Lake Erie. As indicated
in the trend analysis, there has been considerable improvement in the river even though
standards are still violated at some stations. This improvement has been due largely to
240
-------
the Industrial Control Program that has been initiated. Many industries are now meeting
effluent guidelines and it is anticipated that more will comply in the future.
The mathematical model was used to project anticipated future levels of five chemical
constituents in the Detroit River. These parameters include chloride, phenol, ammonia
nitrogen, phosphorus and total iron. The projections made with the model are for the
year 1977 and are based on the industrial loadings authorized under the National Permit
Program. Effluent loadings for the Detroit Wastewater Treatment Plant (Det WWTP) were
based on available information where possible, although in the ammonia nitrogen, chloride,
and iron simulations, values had to be assumed. For each case where an estimated
concentration was used, an average flow rate of one billion gallons per day (1 BCD) was
assumed.
As mentioned previously, the chloride standard of 50 mg/l is presently achieved at all
points in the river. Simulation, assuming an average of 175 mg/l in the Det WWTP effluent
and allowed loadings for all industries, showed a maximum average concentration of 48
mg/l. This occurred below the industrial outfalls in the Trenton Channel (Segment 37).
It is important to note that the chloride loadings allowed under the permits are generally
higher than the present discharge levels. Therefore, if it present industrial discharge levels
are maintained the chloride standard will continue to be met.
It was stated earlier that the phenol standard was violated at many near shore areas of
the Detroit River. The new phenol limitations placed on the industries and on the Det
WWTP (93 Ib/day) are much lower than the levels presently being discharged, and were
entered into the model. As discussed in the modeling section it was necessary to insert
a phenol "sink" in the model in order to verify the results. The exact nature of this
sink and its interrelationship with other parameters are not completely understood.
Therefore no loss of phenol to such a "sink" was assumed for projections using the model.
By removing this sink, the projection may be more conservative than the actual conditions
warrant. The results showed that near shore segments at milepoint 8.7W and 3.9 (the
most critical reaches) would average 3.0 ppb of phenol. This would indicate a violation
of the standard at those locations, however, this degree of violation is minimal, and thus
it is difficult to state definitely whether the standard will be violated. Also, any effects
of degradation or sorption-sedimentation of this material will serve to further decrease
its concentration in the aqueous phase. The large reduction in the total pounds of phenol
entering the river will definitely result in a significant improvement in the water quality
241
-------
with respect to phenol contamination should be realized.
Ammonia nitrogen levels should decrease as the new discharge levels are met. The exact
degree of reduction will depend primarily on the removal attained by the Det WWTP.
Little data on the Det WWTP ammonia levels is available, consequently three simulations
were carried out. The first run was based on 1 BCD flow, and 8 mg/l NhU -N from
the Det WWTP and all industries in compliance with the permits. Runs 2 and 3 are based
on a Dat WWTP discharge of 4 and 1 mg/l, respectively. The results from these simulations
show that with .030 mg/l NHo -N entering the river from Lake St. Clair a maximum
average concentration of from 0.41 to 0.21 mg/l can be expected (high level based on
Det WWTP 8 mg/l, low level based on Det WWTP 1 mg/l). This represents a reduction
in the ammonia nitrogen concentration of between 25 and 75 percent in the near shore
areas.
The phosphorus projections were also based on various estimated effluent levels from the
Detroit plant and compliance by the various industries with the permit program. The
present standard for phosphorus for the Det WWTP is 4750 Ibs/day, or 0.56 mg/l at one
billion gallons per day flow. Simulation using this loading along with allowed industrial
discharges showed a maximum average concentration expected of 0.13 mg/l, whereas
presently the value is averaging 0.18 mg/l. A second run with the Detroit plant discharging
at an average level of 1 mg/l, the established international goal, showed an expected
maximum of 0.14 mg/l. Thus the new limitations will definitely decrease the phosphorus
concentrations in the river, and in fact those areas along the shoreline can be expected
to drop by approximately 20-30 percent in phosphorus concentration.
Iron values obtained during the model verification are based on total iron measurements.
The standard for iron is set on filtrable iron concentration, and consequently cannot be
compared directly with model output. Two effluent levels of 4 and 9 mg/l T-Fe were
used as esimates for the Det WWTP. The results of the simulation indicated a substantial
reduction in total iron concentration with a maximum average value of 0.57 or 0.70 mg/l
depending on the assumed Detroit plant loading. This represents a substantial reduction
in iron levels, and while it is not clear whether the 0.03 mg/l filtrable iron standard will
be met, it is anticipated that the river will show a marked reduction in iron concentration.
Graphical representation of the above projections is given in Appendix D-9.
Five-day biochemical oxygen demand (BODg) and total suspended solids were not modeled
in this study. The BOD of the river was not large although the area near the Detroit
242
-------
Wastewater Plant and Rouge River definitely showed a BOD increase. The Detroit plant
has been discharging on the order of one half million pounds per day of BODg . The
new discharge level is expected to be much lower with a standard of 200,000-250,000
Ibs/day. This will definitely aid the river by lowering the oxygen demand. Similarly,
the Det WWTP and the various industries are required to lower the suspended solids
discharged to the river by better than 50 percent in almost all cases. This will enhance
the water quality, not only by an improvement in the aqueous phase, but also by an
improvement in the sediment condition, with fewer solids, along with sorbed materials,
being settled to the bottom.
In summation, it is apparent that the water quality in most cases has improved in recent
years. The new limitations issued for discharges indicate that this trend will continue
and that water quality standards will either be met or approached very closely in the
next few years. The exact fate of some of the trace metals and the role of sediment
chemistry has not been defined adequately to make a complete evaluation at this time.
However, it is hoped that further research in these areas will provide the necessary
information to assess their importance in river management.
243
-------
SECTION VIM
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40. Nargalef, R., Perspectives in Ecological Theory. Chicago, University, of Chicago
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248
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APPENDIX
-------
Table A-l;
Aqueous Phase (Insitu) Data Summary -
August 1973 Survey
Station Depth Dissolved Temp
(ft.) Oxygen (°C)
(rog/1)
Specific
Conductance
(ymho)
6
7
8
0
6
12
18
0
6
12
18
30
0
6
12
18
30
0
6
12
18
0
6
12
18
24
30
0
6
12
0
6
12
18
24
0
6
12
18
30
0
6
12
18
10.2
7.7
6.7
6.1
8.8
8.8
8.7
8.8
8.8
9,3
9.4
9.0
8.2
6.8
9.2
9.2
8.9
7.9
9.3
9.1
6.0
4.8
3.5
1
7
8.
8.
8.4
9.3
9.0
8.8
7.5
6.8
9.1
8.8
8.7
6.6
5.6
8.7
8.3
8.2
8.0
23.0
22.5
22.2
22.3
23.0
23.0
22.7
21.9
21.9
21.0
21.8
21.1
21.2
20.8
20.8
21.0
20.9
20.9
23.5
22.5
22.5
23.0
22.9
23.0
23.1
23.1
23.1
23.3
23.0
23.2
23.1
23.1
23.8
24.0
24.0
23.9
23.5
23.2
23.2
23.3
23.1
200
182
189
202
198
202
201
194
194
203
208
212
209
207
195
194
198
198
240
238
231
225
260
255
257
257
250
250
251
257
253
269
269
269
268
272
260
261
260
261
250
-------
Table A-l: Aqueous Phase (In.situ) Data Summary <-
1973 Survey (continued)
Station
Depth
(ft.)
Dissolved
Oxygen
(mg/1)
Temp. Specific
(°C) Conductance
(ymho)
10
11
12
13
14
15
16
17
18
30
0
12
18
30
0
12
30
0
6
12
18
30
0
6
12
18
24
0
6
9
30
0
6
12
18
30
0
6
12
18
30
0
6
12
18
30
0
6
12
18
22
5.0
7.4
7.7
8.3
4.4
8.6
8.8
8.0
7.9
7.4
6.3
5.4
4.9
8.3
8.4
8.0
7.2
6.3
8.9
9.2
8.6
7.2
8.2
8.3
8.0
7.0
5.2
8.5
8.2
7.8
8.2
7.8
8.2
7.9
7.2
6.1
5.6
8.6
7.6
7.4
23.1
24.5
24.2
24.0
24.0
23.8
23.9
24.0
23.8
23.8
23.8
23.8
23.8
24.7
24.3
24.0
24.1
24.1
24.0
24.0
24.0
23.9
24.4
24.0
24.0
24.1
24.1
24.0
23.9
23.9
23.9
23.9
24.0
23.0
22.9
22.9
22.8
25.0
24.8
26.0
24.3
24.0
267
307
285
282
284
261
261
263
287
281
281
278
283
282
282
283
282
282
265
262
261
263
283
282
282
282
282
270
268
268
269
272
295
290
285
283
288
287
310
313
312
301
251
-------
Table A-l; Aqueous Phase (Insitu) Data Summary -
August 1973 Survey (continued)
Station
Depth
(ft.)
Dissolved
Oxygen
(mg/1)
Temp. Specific
( C) Conductance
(ymho)
19
20
21
22
0
6
10
0
6
12
0
6
12
0
6
12
18
30
34
6.7
6.3
5.9
8.9
8.1
7.6
8.9
8.6
8.1
8.4
8.1
7.0
4.9
3.4
3.8
26.0
26.0
26.0
25.0
24.9
24.9
24.9
24,8
24,8
24.0
24.0
23.9
24.0
24.0
24.0
342
339
339
308
309
311
299
298
297
298
.293
292
291
292
287
252
-------
Table A-2:
Aqueous Phase (Insitu) Data Summary -
November 1973 Survey
Station
1
2
3
4
5
6
7
8
9
10
11
12
13
14
Depth
(ft.)
6
24
0
12
24
0
12
24
0
12
30
0
12
24
0
12
24
0
12
24
0
12
24
0
12
30
0
12
30
0
12
30
0
12
0
12
24
0
3
Dissolved
Oxygen
(mg/1)
3.0
0.6
11.7
9.4
5.2
11.5
8.3
8.8
11.8
8.4
5.3
12.8
7.2
5.2
12.6
6.4
5.2
12.6
11.6
7.5
12.6
12.4
11.5
12.4
12.4
6.9
11.3
11.3
9.0
12.2
12.1
11.7
12.8
12.8
12.0
11.8
11.8
12.8
12.4
Temp.
Specific
Conductance
(ymho)
10.0
10.0
10.0
10.0
10.0
10.0
10.0
10.0
10.0
10.0
10.0
6.0
7.0
7.5
8.0
8.0
8.0
6.5
6.5
6.5
7.5
7.5
7.5
7.6
7.6
7.8
8.0
8.0
8.0
7.5
7.5
7.5
6.5
6.5
7.0
8.0
8.0
7.0
7.0
142
150
191
189
189
200
192
192
198
198
190
170
172
169
170
173
169
185
185
180
170
170
170
170
170
169
188
170
165
160
160
160
205
220
192
190
192
178
178
253
-------
Table A-2:
Station
15
16
17
18
19
20
21
22
Aqueous Phase (Insitu) Data Summary -
November 1973 Survey (continued)
Temp. Specific
(°C) Conductance
(ymho)
Depth
(ft.)
0
12
30
0
12
24
0
6
0
12
18
0
6
0
12
No data
0
12
Dissolved
Oxygen
(mg/1)
11.5
11.5
12.0
13.2
13.0
13.2
13.4
13.4
11.0
11.4
11.3
11.6
11.6
12.0
-
obtained:
12.8
12.8
8.0
8.0
8.0
7.0
7.0
7.0
6.5
6.5
8.0
8.0
8.5
8.0
8.0
8.0
185
182
175
215
218
218
278
270
205
200
210
170
172
161
Equipment malfunction
7.0 460
7.0 380
254
-------
Table A-3; Aqueous Phase (Insitu) Data Summary ~
May 1974 Survey
Station Depth Dissolved Temp. Specific
(ft.) Oxygen (°C) Conductance
(mg/1) (ymho)
1 0
10
20
30
2 0
10
20
30
3 0
10
20
30
4 0
10
20
30
5 0
10
20
6 0
10
20
30
7 0
10
20
30
8 0
10
20
30
9 0
10
20
30
10 0
10
20
30
11 0
10
20
30
255
12.6
12.4
12.4
12.2
12.8
12.6
12.6
12.6
13.0
12.7
12.6
12.6
12.4
12.2
12.2
12.4
11.8
11.8
11.7
11.7
11.6
11.6
11.5
11.6
11.4
11.3
11.2
11.6
11.4
11.4
11.3
12.0
11.6
11.4
11.4
9.8
9.5
9.6
10.8
11.2
11.3
11.4
11.3
7.0
6.9
6.9
6.8
6.0
6.3
6.3
7.5
7.8
7.0
7.0
7.0
8.0
8.0
7.9
7.8
9.0
8.9
8.8
7.8
7.7
7.6
7.4
7.9
7.7
7.5
7.4
9.0
8.8
8.5
8.5
8.0
8.0
7.9
7.9
10.9
9.8
9.0
9.0
8.5
8.3
8.1
8.1
133
133
133
135
131
132
131
132
167
158
167
160
155
155
153
153
200
200
205
208
208
206
206
231
230
230
230
220
220
218
215
190
190
188
190
270
220
240
215
185
188
188
186
-------
Table A-3: Aqueous Phase (Insitu) Data Summary -
May 1974 Survey (continued)
Station Depth Dissolved Temp. Specific
(ft.) Oxygen (°C) Conductance
(mg/1) (ymho)
12 0 8.8 11.8
13 0 10.4 10.0
10 10.6 10.0
20 10.8 10.5
30 11.1 10.6
14 0 11.4 11.0
15 0 10.4 11.3 201
10 10.4 11.1 200
20 10.4 11.2 199
30 10.6 11.0 193
16 0 11.2 9.9 233
10 11.0 9.2 237
20 11.0 9.2 238
30 11.0 9.0 240
17 0 11.0 10.1 277
18 0 10.5 11.9 233
10 10.3 11.7 230
20 10.4 11.3 228
19 0 10.2 13.0 235
10 10.2 12.5 223
20 0 10.9 11.0 173
10 11.0 11.0 174
21 0 11.2 10.5 170
10 11.2 10.3 170
20 11.2 10.3 170
22 0 11.3 10.5 199
10 11.2 10.4 195
256
-------
Table A-4: Aqueous phase data summary - August 1973 survey
Parameter
Units
Stations
10 11 12 13 14 15 16 17 18 19 20 21
22
Date taken
BOD
COD
Cd
Cr
Cu
Fe
Hg
Mn
Hi
Pb
Zn
"-n Chlorinated
-
mg/1
mg/1
ug/1
Ug/1
Ug/1
Ug/1
.. _ / 1
ug/ 1
ug/1
ug/1
ug/1
ug/1
ug/1
14
0.9
10.2
0.47
4.9
6.3
50
1.7
11
1.7
221
0.66
14
0.9
12.9
0.45
9.9
4.7
70
2.1
11
2.1
66
0.51
14
0.3
9.9
0.35
14.2
3.4
120
4.5
15
2.0
48
0.46
14
1.9
9.2
0.62
10.1
7.9
120
4.0
15
2.3
90
0.50
15 .
2.4
8.0
0.49
9.8
3.9
960
19.0
23
2.3
66
0.30
15
1.2
9.7
0.35
11.8
11.2
420
11.7
19
1.6
72
0.44
15
0.8
8.7
0.35
16.8
3.1
2490
21.8
15
2.1
96
0.25
15
1.8
.10.7
0.29
5.5
4.0
550
14.4
27
1.9
48
0.32
15
1.1
8.2
0.28
27.8
3.4
490
12.4
15
1.7
54
0.48
15
4.6
17.9
0.64
15.1
13.3
2600
30.5
23
4.2
72
0.50
15
1.1
12.9
0.25
7.9
2.3
490
11.8
11
1.7
36
0.58
16
1.5
8.7
0.33
13.0
5.4
2170
26.9
11
1.8
54
0.37
15
3.9
12.9
0.68
21.6
18.8
4750
52.6
23
5.3
96
0.36
15
1.7
12.2
0.30
8.3
3.1
1420
12.9
11
1.4
42
0.54
15
3.9
10.4
0.55
8.3
7.1
2020
26.2
23
3.2
60
0.22
16
1.5
12.7
0.34
18.7
5.2
1150
15.3
19
2.2
60
0.46
16
0.7
10.2
0.35
19.5
4.0
1250
14.6
15
1.9
66
0.38
15
4.2
12.4
0.90
16.3
12.3
2690
27.0
19
5.4
84
0.73
15
2.6
14.2
0.75
21.3
10.7
4850
43.6
47
6.4
78
0.43
15
1.9
8.2
0.53
20.0
6.8
1420
17.9
23
3.5
60
0.53
15
2.6
8.0
0.43
6.2
6.0
1570
16.9
19
3.0
84
0.67
15
0.6
8.0
0.33
21.3
2.8
1040
12.5
15
2.2
48
0.58
-------
OO
Table A-5: Aqueous phase data summary - November 1973 survey
Parameter Units Stations
1 2 3 4 5 6 7 8 9 10 11 12 13 14 15 16 17 18 19 20 21 22
Date taken - 6666777777788878877789
BOD mg/1 1.0 1.0 1.6 1.2 1.2 1.2 1.4 1,4 1.2 3.3 1.0 1.9 3.3 1.9 2.7 1.4 2.0 3.8 2.8 1.2 1.6 1.8
COD mg/1 3.0 4.2 6.0 6.5 6.7 7.5 5.7 4.2 6.2 7.5 4.2 13.4 10.5 6.2 10.0 6.7 10.5 12.2 11.9 6.5 11.9 9.0
Cd yg/1 0.24 0.15 0.19 0.13 0.26 0.37 0.41 0.54 0.27 0.68 0.43 0.31 0.66 0.24 0.81 0.14 0.23 1.58 1.46 0.26 0.23 0.46
Cr ug/1 2.6 5.8 3.4 3.4 3.8 5.1 6.2 6.4 7.4 13.5 6.6 8.4 18.6 7.1 9.7 3.6 10.3 17.1 13,7 5.8 5.0 7.4
C" yg/1 7.0 5.4 8.5 7.2 6.6 4.8 10.5 20.4 10.9 13.3 8.8 9.0 9.0 5.3 9.1 3.5 5.0 13.7 12.7 6.4 4.3 8.9
Fe Vg/1 160 120 300 230 460 490 1000 650 800 1340 720 1320 1120 650 1170 670 1710 1670 980 560 570 1260
Hg yg/1 6.1 9.0 2.4 4.8 4.2 8.3 7.3 6.6 1.1 7.0 7.7 12.0 6.5 2.8 1.6 5.5 6.4 4.1 5.1 5.3 4.6 5.8
Mn Mg/1 3.7 2.8 6.5 5.9 7.8 9.7 14.2 6.8 13.8 22.0 9.0 21.9 18.9 9.7 18.3 9.2 27.5 22.2 18.1 8.6 10.7 20.1
Ni yg/1 11 23 19 15 11 11 15 15 15 23 15 23 27 15 19 11 15 19 23 15 11 15
Pb yg/1 4.2 3.7 3.1 3.2 2.7 3.5 4.6 10.9 5.8 7.2 4.5 4.7 7.7 3.6 6.0 3.2 3.4 10.8 6.5 3.6 3.3 6.4
Zn yg/1 56 35 56 63 63 49 84 155 91 84 70 56 42 42 70 56 70 141 84 70 56 84
-------
Table A-6: Aqueous phase data summary - May 1974 survey
Parameter Units Stations
1 2 34 5 6 7 8 9 10 11 12 13 14 15 16 17 18 19 20 21 22
Date taken - 13 13 13 13 14 14 14 14 14 14 14 15 15 15 14 14 14 14 14 14 14 14
&OD mg/1 1.6 1.3 2.1 1.6 1.8 1.8 1.7 2.1 2.2 3.4 1.5 2.5 1.8 2.6 2.9 1.3 1.6 3.2 3.8 1.6 1.6 1.8
COD mg/1 3.9 5.1 6.7 5.2 5.3 5.4 4.8 6.7 3.5 13.0 6.2 9.8 8.9 7.1 11.8 3.2 7.6 14.2 13.1 7.9 7.0 6.3
Cd ug/1 0.42 0.15 0.13 0.15 0.12 0.28 0.23 0.17 0.18 0.34 0.12 0.19 0.37 0.20 0.35 0.16 0.24 0.53 0.65 0.15 0.67 0.57
Cr ug/1 0.6 0.5 0.6 1.1 0.9 10.5 1.0 1.0 1.2 8.6 1.3 7.2 9.9 4.6 14.3 1.6 1.7 13.0 16.3 4.4 1.8 1.7
Cu ug/1 4.6 4.2 3.2 6.4 3.4 5.4 5.5 6.4 8.5 10.3 6.3 6.0 17,3 40.6 8.6 6,5 8.2 13.4 12.5 6.5 7,0 18.0
Fe yg/1 70 30 200 250 330 350 490 330 330 1410 470 730 940 540 820 500 690 1490 1060 860 350 350
Kg ug/1 0.4 0.1 0.1 <0.1 4.6 0.3 0.6 0.2 0.1 <0.1 0.1 0.8 0.7 0.1 0.1 0.8 0,1 0.3 0.1 0.1 0.1 0.3
Mn Ug/1 3 3 8 5 10 10 15 10 10 6 15 44 37 21 28 13 17 41 33 25 10 10
Ni ug/1 7 27 19 11 15 11 11 11 19 27 31 47 27 27 27 15 23 31 23 15 19 15
Pb VZ/i 0.7 1.0 0.6 0.7 0.9 1.0 1.3 1.3 1.3 7.1 1.3 6.4 15.8 7.3 11.9 4.1 4.1 13.7 14.7 5.8 4.0 6.4
Z° ug/1 57 51 53 93 59 77 86 64 77 84 69 142 130 110 101 107 94 86 90 66 72 95
-------
Table A-7: Aqueous phase (pesticides) data summary - November and May surveys
Parameter Units Stations
1 2 3 k 5 6 7 8 9 10 11 12 13 14 15 16 17 18 19 20 21 22
November 1973 survey
Lindane ng/1
Heptachlor ng/1
Aldrin ng/1
Heptachlor Epoxide ng/1
p, p' DDE ng/1
Dieldrin ng/1 - <20 <20 <20 <20 <20 <20 <20 <20 <20 <20 <20 <20 <20 <20 <20 <20 <20 <20 <20 <20 <20
p, p' TDE (ODD) ng/1 - <30 <30 <30 <30 <30 <30 <30 <30 <30 <30 <30 <30 <30 <30 <30 <30 <30 <30 <30 <30 <30
Endrin ng/1 - <40 <40 <40 <40 <40 <40 <40 <40 <40 <40 <40 <40 <40 <40 <40 <40 <40 <40 <40 <40 <40
p, p' DDT ng/1 - <30 <30 60 60 30 <30 <30 <30 <30 <30 <30 <30 <30 <30 30 51 45 <30 30 <30 <30
May 1974 survey
g Lindane ng/1
-------
Table A-8: Sediment phase data summary - August 1973 survey
Parameter
Date taken
COD
TVS
Kjeldahl-n
N03-N
Total-P
Cd
Cr
Cu
Fe
Hg
Mn
Ni
Pb
Zn
Units
-
mg/g
% Dry Wt.
mg/kg
mg/kg
mg/kg
mg/kg
mg/kg
mg/kg
mg/g
mg/kg
mg/kg
mg/kg
mg/kg
mg/kg
Stations
1
14
NS
NS
SS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
2
14
3
6.0
170
72
370
0.5
20
11
4.3
-
190
10
6
33
3
14
25
9.7
290
124
590
1.4
50
13
7.1
-
280
25
266
61
4
14
40
10.7
820
152
1010
1.7
124
12
17.4
-
650
41
24
95
5
15
13
9.6
310
91
850
1.5
87
10
13.1
-
420
32
15
81
6
15
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
7
15
9
3.6
450
86
600
0.7
47
4
8.2
-
260
17
13
39
8
15
52
7.4
620
79
860
1.5
55
45
8.2
-
330
20
108
86
9
15
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
10
15
157
12.2
1400
34
2090
11.9
473
161
36.9
-
1090
47
242
424
11
15
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
12
16
11
2.4
270
99
500
0.9
33
9
5.5
-
210
13
29
88
13
15
209
21.0
5010
274
7010
16.2
2680
199
38.6
-
730
289
384
444
14
15
28
4.7
650
74
810
0.7
42
5
7.8
-
210
14
14
40
15
15
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
16
16
31
4.3
610
67
610
2.3
61
14
11.2
-
480
26
17
56
17
16
27
9.0
450
87
890
1.2
41
12
6.7
-
300
15
25
63
18
15
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
19
15
197
15.7
1340
331
10000
10.0
795
88
31.6
-
720
87
160
404
20
15
20
6.8
380
323
3420
3.4
328
35
10.2
-
260
39
52
266
21
15
48
9.1
750
135
1090
3.2
186
19
13.6
-
490
31
41
149
2:
15
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
SS
NS
NS - No sample
-------
Table A-9: Sediment phase data summary - November 1973 survey
Parameter
Units
Stations
10
11
12
13
14
15
16
17
18
19
20
21
22
Date taken
COD
TVS
Kjeldahl-N
N03-N
Total-P
Cd
Cr
Cu
Fe
Hg
Mn
Nl
Pb
Zn
»g/g
I Dry Wt.
mg/kg
mg/kg
mg/kg
mg/kg
mg/kg
mg/kg
mg/g
mg/kg
mg/kg
mg/kg
mg/kg
mg/kg
6
18
4.1
420
162
620
2.9
30
16
12.3
0.18
380
32
29
59
6
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
6
47
6.3
820
93
760
2.4
47
11
21.0
0.12
490
41
25
92
6
48
5.0
360
172
910
2.4
35
14
20.8
0.53
510
46
30
87
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
19
5.1
310
93
540
2.1
30
14
12.5
0,50
380
31
30
70
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
109
6.7
960
94
790
3.5
47
21
15,2
4,12
580
43
58
131
7
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
8
35
7.7
650
95
780
2.9
40
13
15.2
8.00
550
36
29
69
8
110
5.5
1000
632
2910
5.3
166
103
21.2
0.43
510
95
144
335
8
31
5.8
590
77
520
2.1
33
14
7.1
0.17
120
20
29
67
7
37
7.0
570
78
930
2.7
40
15
15.0
0.18
560
38
29
70
8
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
8
32
8.4
870
207
1180
2.7
55
12
22.8
0.86
960
45
30
90
7
NS
. NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
7
148
11.9
1450
553
3730
8.2
217
92
21.4
2.32
540
73
125
350
7
109
11.4
1770
267
1440
7.5
180
55
20.7
0.97
480
57
101
266
6
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
8
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS - No sample
-------
Table A-10: Sediment phase data summary - May 1974 survey
ON
Paraneter
Date taken
COD
TVS
Kj eldahl-N
N03-N
Total-P
Cd
Cr
Cu
Fe
Hg
Mn
Nl
Pb
Zn
Units
-
mg/g
% Dry Wt.
mg/kg
mg/kg
mg/kg
mg/kg
mg/kg
mg/kg
mg/g
mg/kg
mg/kg
nig /kg
mg/kg
ing /kg
Stations
1
13
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
2
13
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
3
13
46
9.0
910
65
660
3.1
20
17
22.5
<.01
520
44
21
105
4
13
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
5
14 '
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
6
14
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
7
14
14
3.0 '
420
45
660
2.6
16
14
17.7
0.19
480
30
21
49
8
14
NS
•NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
9
14
5
3.6
360
126
690
3.1
14
14
17.4
0.20
500
29
16
47
10
14
120
14.1
1060
366
1590
3.3
32
78
29.1
0.39
1120
37
152
601
11
14
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
12
15
88
6.8
1740
67
1020
3.1
39
20
11.6
0.31
340
59
54
214
13
15
51
8.0
660
171
1100
4.1
36
47
18.2
0.78
480
43
339
225
14
15
73
5.1
670
73
660
2.6
22
30
8.6
0.20
230
22
38
124
15
14
36
9.7
530
49
930
3.3
26
19
15.1
0.03
550
41
29
124
16
14
85
8.1
1470
89
700
2.8
15
19
13.3
0.40
390
30
42
101
17
14
86
12.1
2280
41
670
2.3
13
9
14.7
«.01
300
29
17
49
18
14
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
19
14
86
5.6
980
78
1740
4.6
48
69
13.2
0.58
330
37
84
284
20
14
76
10.7
1580
93
1350
8.5
56
32
20.2
0.42
480
44
80
278
21
14
40
3.4
630
63
430
2.1
9
12
6.8
0.17
230
15
29
84
22
14
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS - No sample
-------
Table
Survey
August
1973
November
1973
A-ll;
Sample
2
3
4
5
7
8
10
12
13
14
16
17
19
20
21
1
3
4
6
10
12
13
14
15
17
19
20
Sediment
August,
Description -
November and May
Sampling Device Color
Ponar
Ponar
Ponar
Corer
Ponar
Corer
Corer
Ponar
Corer
Corer
Ponar
Ponar
Ponar
Ponar
Ponar
Corer
Corer
Corer
Corer
Corer
Corer
Ponar
Corer
Corer
Corer
Corer
Corer
Vary
Vary
Gray
Gray
Vary
Gray
Gray-
Black
Vary
1 Gray-
Black
Gray
Gray
Vary
Black
Black
Gray-
Black
Vary
Vary
Vary
Vary
Gray-
Black
Gray
Black
Gray-
Black
Gray
Gray
Gray-
Black
Gray-
Brown
De s c r iption
Coarse sand & gravel
Coarse sand & gravel
w/some gray ooze
Ooze w/pea size stones
Ooze w/pea size stones
Sand & coarse gravel
Fine gravel
Ooze
Sand & gravel
Ooze
Very fine sand & gravel
w/some plant materal
Ooze w/pea size stones
Sand w/gray ooze
Sand w/black ooze
Sand w/black ooze
Sand w/ooze
Sand w/coarse gravel
Coarse gravel w/gray
ooze
Fine gray ooze w/sand
& gravel
Coarse gravel w/gray
ooze
Ooze overlain w/black
cinder & gravel
Fine sand w/ooze &
small stones
Ooze
Sand w/small stones,
organic material &
plant material
Ooze w/sand & small
stones
Ooze w/surface layer of
living macrophytes
Ooze w/some fine sand
Ooze
264
-------
Table A-ll:
Sediment Description -
August, November and May Surveys
(continued)
Survey Sample Sampling Device Color
May
1974
3
7
9
10
12
13
14
15
16
17
19
20
21
Corer
Corer
Corer
Corer
Corer
Corer
Corer
Corer
Corer
Corer
Corer
Corer
Corer
Gray
Vary
Vary
Black
Brown-
Black
Black
Brown
Gray-
Brown
Gray-
Brown
Brown-
Black
Brown-
Black
Brown-
Gray
Brown
Description
Ooze w/gravel
Gray ooze overlain by
2 cm of sand & gravel
Gray ooze w/sand &
gravel
Sand & black ooze
Ooze w/some detrital
material
Ooze
Sand & ooze w/some
detrital material
Sand & gravel w/gray
ooze
Sand & ooze
Ooze w/some detrital
material
Ooze w/some sand
Ooze w/some stones
and shells
Sand w/some gray ooze
265
-------
Table A-12: Sediment exchange data summary - August 1973 survey
Parameter
COD
Kjeldahl-N
N03-N
Total-P
Cd
Cr
Cu
Fe
Mn
Ni
Pb
Zn
Units
Z
%
Z
z
z
z
z
z
z
z
z
z
Stations
1
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
2
6.40
4.2
12.2
2.2
2.6
6.8
6.3
3.7
5.8
-
2.5
-
3
0.83
2.7
3.4
0.2
0.7
0.3
2.7
1.1
6.1
<48
0,04
41
4
0.57
3.2
11.8
7.8
0,8
1.7
5.1
4.8
2,9
<49
1.2
45
5
0.30
2.6
8.4
2.0
0,5
0.7
3.9
2.2
1.6
<44
1,6
85
6
NS
NS
NS
NS
NS
NS
NS
NS
NS
N5
NS
NS
7
0.86
4.9
3.3
0.4
2,2
0,5
7.2
<1.0
.2,1
,65
0.8
97
8
0.68
0.8
4.9
0,6
3,7
1,0
2.5
2.9
<2,5
,85
0.2
52
9
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
10
1.18
3.8
23,8
0.5
0,3
0.3
0.8
0.6
0,8
<36
0,08
10
1!
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
12
13
14
15
2,35 0.93 2.52 NS
9.4 14.8 21,9 NS
6.0 9,3 100.0 NS
2.6 0.6 9,8 NS
1,8 0,4 2,9 NS
1,3 0,1 16,1 NS
7.4 1.4 55,2 NS
4.7 2,2 8,6 NS
4.3 4,7 63,3 NS
- 23.2 r- NS
0.5 Q.05 3,5 NS
78 23 <• NS
16
17
18
19
20 21
22
0.40 4.15 NS 0.85 5.90 1.96 SS
1.6 16.8 NS 3.4 17.8 4.1 NS
11.2 79.1 NS 2.7 9.0 6.4 NS
2.5 12.7 NS 0.2 1.7 1.7 NS
1,3 3.5 NS 0.4 6.1 0.7 Nb
l\H 8,4 NS 0,3 2,9 0,8 NS
3.0 33.4 NS 1,4 19.7 3.2 NS
0.8 12.8 3.5 NS
2.2 68.1 NS
1,8 38.3 NS
<69 " NS
0,8 3.0 NS
NS
1.2 6.9 3.9 NS
•< 21 S49 "42 NS
0.1 1.7 0.4 NS
14 60 22 NS
NS - No Sample
Percentages are based on total concentration in dry sediment
-------
Table A-13; Sediment exchange data summary <- November 1973 survey
Parameter
COD
Kjeldahl-N
NO -N
Total-P
Cd
Cr
Cu
Fe
Mn
Ni
Pb
Zn
Units
t
Z
z
z
z
X
z
z
z
z
z
z
Stations
1
0.69
3.8
0.86
2.8
0.7
1,0
0.3
0.23
1.05
< 1.9
2.1
2.4
2
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
3
1.06
1.3
0.22
2.0
0.7
0,6.
0.3
0.10
O.A9
<1. 5 <
2.3
0.8
4
0.03
1.7
0.58
1.8
0.8
0,7
0.3
0.07
0.33
1.3
1.9
0.9
5
NS
NS
NS
NS
NS
us
NS
NS
NS
NS
NS
NS
6
2,49
3.6
0,32
1.2
1.1
i?
0.4
0.14
1.31
< 1.9
2.1
1.1
7
NS
NS
NS
NS
N5
NS
NS
NS
NS
NS
NS
NS
a
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
9
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
10
0.09
5,5
1.49
1.7
0,4
M
0.2
0.26
0.33
2,1
1.0
1.3
11
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
12
0,66
1,8
0,21
1.6
QV6
0X5
0.3
0.14
1.07
< 1.7
2,1
1.4
' 13
0,48
3.8
27.2
0.8
0,7
QV2
0.03
0.33
1.36
2.1
0.4
1.3
14
2,05
3.1
2.08
4,6
0,7
*,*
0.09
0.65
4.27
3,5 <
2.2
1.6
15
0,78
3,5
2,18
1,4 '
0V5
0,6
0.1
0.12
0.88.
1.6
1.9
1.1
16
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
17
1.88
2,5
0.28
1,1
0,4
-------
Table A-14; Sediment exchange data summary r- May 1974 survey
Parameter
COD
KJeldahl-N
N03-N
Total-P
Cd
NJ
£ Cr
Cu
Fe
Mn
Nl
Pb
Zn
Units
Z
Z
Z
Z
Z
Z
Z
%
Z
Z
Z
Z
Stations
1
NS
NS
NS
NS
NS
NS
NS
N3
NS
NS
NS
73
2
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
US
rr.
3
0.60
2.6
7.23
4.6
1.0
3.3
0.2
0.70
0.81
4.3
2.7
l.C
4
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
»tc»
5
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
MO
6
NS
NS
NS
NS
NS
N5
NS
NS
NS
NS
NS
MC
7
0.92
1.0
8.67
1,0
0.7
1,6
0,1
0.25
0,25
2,0
3.0
1.2
8
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
MS
9
3.2
3.1
4.21
1.9
0.6
0,1
0.38
0.50
<2.1
3.9 '
J.,3
10
0.19
1,3
2.43
0.2
1.2
1,6
0.02
0.19
0.81
2.2
0.6
0,3
1
NS
NS
NS
NS
US
NS
NS
NS
NS
NS
NS
NS
12
13 14
15 16
17
18
0,65 0,52 0,36 0.81 0.35 1.41 NS
5.2 3.8 3.0 1.9 3.0 5.1 NS
4,48 1,46 4.93 24.7 5.62 27.8 NS
1.9 0.5 2.0 0.7 3.4 3.5 NS
2.3 0.7 0.9 1.1 1.1 1.7 NS
0,8 1,4 2,2 1,3 7,8 16.9 NS
0.08 0,04 0,07 0.09 0.08 0.5 NS
0.23 0,10 0.71 0.32 0.43 3.50 NS
3.56 1.25 0.39 0.18 0.21 2.33 NS
2.2 1.6 2.7 <1.5 <2.0 4.8 NS
1.1 0.2 1.9 2.0 1.5 4.0 NS
0.4 0.3 1,2 0.6 0.6 5.9 NS
19
20
21
22
0.37 0.45 0.34 NS
5.8 3.0 6.1 NS
3.46 3.98 5.71 NS
0.4 1.2 3.1 NS
0.5 0.5 1.1 NS
0.5 0.7 3.6 NS
0.02 0.06 0.2 NS
0.24 0.24 0.75 NS
1.27 1.33 0.30 NS
1.6 il.4 /<4.0 NS
0.7 0.8 2.4 NS
0,4 0.5 1.2 NS
NS - no sample
Percentages are baaed on total concentration In dry sediment
-------
APPENDIX B-l
14
DETROIT RIVER BENTHOS
November 1973
15
17
B
Trlchoptera
Hydropsychldae
Chcumatopsychae (Wallengren)
HTdropsyehae (Piecet)
Hacroncmuia (Bummeister)
Brachycenrridae
Bracnycentrus (Curtis)
Lepcocerldae
Athripsodes (Billbarg)
Acari
Tromb i di forma
Parasitengona
HygrobaCidaa
Hygrobates (Koch 1837)
Ephemeroptera
Heptageniidae
Stenonema Ithaca
Amphipoda
Talitridae
Hyalella azteca
(Saussure)
Gammaridae
Gamma rus faseiatus (Say)
Gastropoda
Pleuroceridae
Goniobasis (Lea) sp, 1
Coniobasis (Lea) sp, 2
Planorbidae
Helisoma (Swainaon)
Amniocolidae
Bithinla tencaeulaea L,
Valvatidae
ValvaCa sp.
Physidae
Physa (Draparnaud)
Lymnaeldae
Lymnaea sp.
Ancylidae
Femssia (Walker)
Pelecypoda
Sphaerildae
Snhaerium (Scopoli)
FTsidium (Pfaiffer
CoelenteraCa
Hydridae
Hydra sp.
Annelida
OllgochaeCa
Tubificidae
LiCTiodrilus eervica
Fsacimoryecides ealiforr.ianus
_ ^
Hirudinea
Erpobdellidae
Dina microstoma
Dipcera
Chironomldae
Tanypodinae
Tanypus (Meigen)
Porlfera
(5 x 3 nm)
Turbellaria
y.acroatomtda
Macroscomidae
Macroatomura (0. Schmidt)
Taxa
Individuals
X Blomaaa/m (wee weight)
X Indlvlduals/m2
Shannon-Weaver Diversity
Richness (X) (S-l/lnN)
14
12
31
970
16
542
2
6
1000
4
559
5
20
Richneas fx") (S//"R)
13.33
14735
0.16
0.6B
0.19
5
16
22.10
340
0.43
1.37
1.19
4
30
6.10
567
1.23
0.90
0.76
1
31
269
1.13
378
8:88
0.26
-------
L
APPENDIX B-l
DETOOIT RIVES BENTHOS
Novemb«r 1973
19
20
r
Trichoptera
Hydropsychidae
Chcumncopsyehae (Wallengren)
Hvclropsvchae (Piecat)
Hacronegium (Burnmeiatar)
Brachycencridaa
BrachvcenCTua (Curtia)
L«pcacerida«
Achripsodes (Billberg)
Acari
Trombidlfozma
Parasicengooa
Hygrobatidaa
Hygrobates (Koch 1837)
Ephemeroptara
H«D:agenilda«
Scenonema Ithaca
Amphipoda.
Talicridaa
Hyalella aztaca (S«ua»ura)
Gaomaridae
Sanaa raa faaciacua (Say)
Caacropoda
?leuroc3ridae
Goniobaais (L«a) jp, 1
p, 2
?lanortaidaa
Halisoma (Suainaon)
Aatniocolidae
Bichinia ;er.caculaea L.
Valvacidaa
Valvaea sp.
?hyiidae
?hvaa (Draparaaud)
L/nmaaidaa
L'nanaea sp .
Ancylidaa
Ferris a la (Walkaw)
Palacypoda
Sphaeriidaa
Sphaorl.um (Scopoli)
~
15
5
9
12
16
23
21
17
CoeleaceraCa
Hydridaa
Hydra «p.
Annelida
Oligochaaca
Tubificidae
Liamodrilua ggrvlca
ea
fornianua
Hirudinea'*
Erpobdellida*
Dina aieroseoma
Diptara
Chironomidaai
Tanypodina*
Tanvous
Porifara
(5 x 3 on)
Turb«llaria
Macrostomida
Macroacomida«
Macroscomum (0.
29
13
Schmidt)
Taxa
Individual*
X 31ornaai/m (wet weight)
X IndividualWm2
Shannon-W«aver Diversity (X)
Rlchnei* (X) (S-l/lnH)
Richneaa (X) (S/
-------
L
APPENDIX B-l
DETROIT RIVER BENTHOS
November 1973
6 7 8 9
A B AS AfB A 8
Tricnopcera
Hydropaychidae
Cheuma cop sye has (Wallengren) 11 3 2 IS 1
Hydropayehae (Pictee) 7 5 10 122
Macronemuin (Burnaeiatar) 126 42 1 I 62
Brachycen cri daa
Srachyeer.gjua (Curtia) 10
Lepcocerldaa
Athripaodea (Sillberg)
Acari
Trombidiforaa
Parasitengoaa
Hygrobacidae
Hygrobaeea (Koch 1337) I
Ephemeroocera" ..
Hcpcageniida*
Scenonema Ithaea 4
Amphipoda
Talicridaa
Hyalalla aztaea (S«uj«ur») 2
Saaciacua (S»y) 72 1
Gastropoda
Fleuroccrlda*
Goniobasia (Laa) sp, 1 10 2 4 1
Goniooasis (Lea) sp. 2 331 1
Planocbida*
Helisoma (Sw-ainson)
Aumicolidae
tstiraculata t.. 1
Valvatidaa
Valvaca ap.
Physidae
Physa (Brapamaud)
Lyvnaeida*
Lymnaea sp.
Ancylidaa
Peleeypoda
Sohaeriidac
Sohaeri'jm (Scopoli) ^ ^ 3 2
ftJTaI™~(?faiffer) 12 1
Coelancarata
Sydridaa
Hydra ap.
Annelida
Oligochaaca
Tubificidae
Lianodrllua ceTvlea 46
P s ammo >ycc ice's californianua
Hirudin««'*
Ercobdailidaa
Sina aleroacoiaa ^
Dipcera3
Chironomldae 24 7
Tanypodinae
Porif era
(5x3 mm)
Turbellaria
Macros coral da
Macros com! dae
Macroarotmaa (0. Schmidt)
_ Individual.
X aiomaas/a (wee weight)
X Individuals /a
Shannon-Weaver Diversity (X)
Richness (X) (S-l/lnM)
!Uchn«»!i (X) (S/
-------
L
APPENDIX B-l
DETROIT RIVER BENTHOS
November 1973
Trichoptera
H'/dropsychidae
Cheumatopsyehae (Wallengren)
Hydropsychae (Pietet)
Macronemum (Bummaister)
Brachycentridae
Brachyeentrus (Curtis)
Leptoceridac
Athripsodea (BUlberg)
Ac art
Trombldifora*
Parasitengona
Hygrobatidae
HygrobatesOCoch 1837)
Ephemeropteral-
Heptageniidae
SEenonema Ithaca
Amphlpoda
TaliCridae
Hyalella azteca (Saussure)
Gananaridae
Gammarua fasciarus (Say)
Gastropoda
Pleuroceridae
Goniobasls (Lea) ap. 1
GoniobasT? (Lea) sp. 2
Planorbidae
Helisoma (Swainson)
Anmtcolidae
Bithinia tentaculata L.
Valvatidae
Valyata sp.
Physida*
Physa (Draparnaud)
Lyonaeidaa
Lymnaea sp.
Ancylldae
Ferrissia (Walker)
Pelecypoda
Sphaeriidae
Sphaerlum (Scopoli)
Pisidiuai (Pfeiffer)
Coelenterata
Hydridaa
Hydra sp.
Annelida
Oligochacca
Tubificidae
Linmodrilus cerviea
Fsammoryctides califomianus
Hirudinea
Erpobdellidas
Dina microstoma
Olptera
Chironomldae
Tanypodinae
Tanypus (Melgcn)
Porifera
(5 x 3 an)
Turballaria
Macrostoolda
Macrostorn!dae
Macroscomum (0. Schmidt)
Taxa
Individuals
X Biomass/m (wee weight)
X Individuals/m2
Shannon-Weaver Diversity <
Richness (X) (S-l/ln»)
Richness (X) (S//TT)
56
19
21
41
21
17
24
8
18
1
21
1
17
5
13
5
10
7
111
11.5
66
0.00
0.00
o.so
62.00
359
0.00
0.00
0.22
19.28
217
1.39
1.65
1.49
6.62
1947
1.47
1.24
0.45
11
95
272
-------
APPENDIX B-l
10
DETROIT RIVER
November 1973
11
B A B
12
13
Triehoptera
Hydropsychidae
Cheumatopsychae (Wallengren)
Hydropaychae (Pietet)
Racronemum (Burnmeister)
Brachycentridae
Braehycentrus
(Curtis)
Leptoceridae
Athripsodea (Billberg)
Acari
Tromb i di forme
Paraaitengona
HygrobaCidae
Hygrobates (Koch 1837)
Ephemeroptera
Heptageniidae
Stenonema Ithaca
Amphipoda
Talitridae
Hyalella azteca (Saussure)
Gammarldae
Gammarus faseiatua (Say)
Gastropoda
Pleuroceridae
Coniobasis (Lea) sp. 1
Goniobasis (Lea) sp. 2
Planorbidae
Helisoma (Suainson)
Amniocolidae
Bithinia tentaculata L.
Valvatidae
Valvaca ap.
Phystdae
Physa (Draparnaud)
Lymnaeidae
Lymnaea sp.
Ancylidas
Ferrissia (Walker)
Pelecypoda
Sphaeriidae
Sphaerium (Scopoli)
PiTidlum (Pfeiffer
Coelenterata
Hydridae
Hydra sp.
Annelida
Oligochaeta
Tubificidae
Liamodrilua cervlca
Fsanmoryctidea ealifornianua
Hirudinea
Erpobdellidae
Dina microstoma
Diptera
Chironomidae
Tanypodinae
Tanypus (Meigen)
Porifera
(5 x 3 mm)
Turbellaria
Macrostomida
Macrostomidae
Macrostomum (0. Schmidt)
Taxa
Individuals
X Biomass/m (wet weight)
X Individuals/m2
Shannon-Weaver Diversity (!t)
Richness (X) (S-l/lnN)
Richness (X)
21
3
14
17
26
12
1
14400 28900
97 142
17
103
6
36
16
6
69
3
44
5
19
4
74
2
112
3
14499
3
290S9
31.10
993
1.64
1.29
0.86
1.66
596
0.92
0.95
0.80
2.54
1753
0.30
0.48
0.33
133.70
411701
0.04
0.20
0.02
273
-------
Trichopeera
Hydropaychidaa
Cheumatopayehag (Wallengrtn)
ilydropsyehaa
BrechycentTida*
Braehycencrug (Curtla)
Lapcoceridaa
(Btllb«rg)
APPENDIX B-2
13
* b
DETROIT RIVER BENTHOS
.nay 1974
13
• b
16
a b
Ac»ri
Troobidi.forsM
Para«it«ngon»
Hygrobatida*
HygTQbacaa (Koch 1937)
Ephemeropcera
Eph«me.rlda«
Ephemera alaulana (tJa_Lk»r)
Hexagenia (Mala
Anphipod*
Haustoriida*
Poncaoor-ia affinis CLindaeroai)
Gastropoda
Plaurocerida*
Conxobasls (!.«») 3p. 1
Goniooas:.3 (La») su, 2
?lanorbida«
HelljQtna (Swainson) 3 3
PTiysida*
Phyaa (Braparaaud) 15 1
Amnicolida*
Pyr^-aiooaia sp.
Bichinia cancaculaca CL.) 43 1
Pelecypoda
Sphaeriida«
Sohaeravon (Scoooli)
Pisidium (Pfeiffar) 1
Anna 11 da
Olijochaaca
Tufaificida*
Lipnodrilua eervieii 12237 5860 280
Linnoanlus ansjuscioenis 4102 1606
PsamraoT^ccides calf ironianua 21
lubiiex cubirax
Hir-jdine»
Dina aieroatoma 139 198 1 13
Hcmiptara
Corixida* (i-nmatmr*)
Chironomida*
Chiro-noniina*
TanytaTs-ua 07an der Wulp)
Chironomua (Xeigen)
Tax* 7 S 33
Individual* 1SS37 7693 282 22
!f 3iomaa»/m2 (wet««ight> 66.35 9.58
X Individual* /a2 229017 2873
Shannon-Weaver Diveralcy (T) Q-43 0.32
Richncs* (X) S-l/lnH 0-59 0.50
Rlchnes* (3t5 S/YTT 0.06 0.41
2
10
2
3 9
1 21
14 33
1 34 14 12
5.43 2.91
330 246
0.47 0.81
0.43 0.78
0.85 0.83
r
274
-------
L
, APPENDIX B-2
OETKOIT RIVER BENTHOS
May 1974
9 .10 11 12
Trtchoptara ' « b a . b a b •
Hydropaychldaa
Cheufflgtopsyehae (Wallengran) 1
Hydropsycfaae (flctae) 3
Braehyeentrida*
Brachycenerua (Curtii)
Lepcocerida«
Athrlpsod«» (Billbarg)
Acari
Troobidifora»
Paraaitangon*
Hygrobatida*
Hygrobatea fltoca 1937)
Epheaarldae
Ephemera simulans (V«lkar)
Hexaggnij. (Walafa)
Aaiphipoda
Hauacoriida.«
?oncoporeia affinls (Linda trom)
Gaacropoda
?leurocer±da«
Goniobasia (Laa) «p. 1
Goniobasia (L«a) ap. Z
?lanorbida«
Hellaoma, (Suainson)
Fhysida*
?hyaa (Draparnaud)
Aonicolidac
Pyrguloosia ap.
£«ntacalac» (L.)
Pslecypoda
Spha«riidae
Sohaerium (Scopoli) 29 9
Pisidimn "(Pf alffer) 1
Annslida
Oligochaaca
lubificidaa
Limodrilug eaTVica 99 15 I 102 33
Limnodrilua Anirusciaenia 9
Fsamnoryccidaa ealjlronianm
Tubifex cubifax , , 21
Hirudinea
Olnj aieroatoma 24 2
^
Hemipcara
Corixidae (Immacura) l_
Chiroaomidaa
Chlronooinae
Wulp)
Chironomus (Maigaa)
Tax*
Individual*
X Biomaaa/o2 (v«e weight)
5t lndiviiiu«la/m2
Shannon-Weaver Div*t»iC7 (X)
Rlchneaa (X) S-1/lnH
Richneaa
-------
APPENDIX B- 2
Trlchopt.r.
Hydropsychidaa
Cheumntopavehaa (Wallengran)
Hvdropayehao CyieeaO
Br»chyc«ntTidaa
Brachveentrm (Curti*)
L«ptoctrlda«
Athrlpsodaa (Billbars)
Aearl
Tramb t diforaa
?«rmiic«ngon4
Hygrob«cida«
Hyf.Tob«ia« CKoch 1937)
DETROIT RIVER BENTHOS
May 1974
Ephem«rld««
Sphemera simulana (Valkar)
Hexagania (Waiaqj
AmpbjLpo4a;
H«u«coriida«
Poncooorala afiinis (Liadstnram)
?l»uroc*rid»«
Conlobasia a«») §p. 1
GonioOasj.3 (L««) rp. 2
Planorbida*
(Swainson)
?hysa (Dr»p«rn*ud)
Amnicolida*
Pyrgulopaia sp.
3ichinid cencaculata (t. ) •
?«l«cypoda
Sphaarildaa
Sphaeriua (Scopoli)
FiaTdium (Pfeiffar)
Annelida.
Oligochacca
Tubificida*
Llamodrllua
Liamoonlus
ar^rica
FsamiEoryerj.dea galzironianq*
Tublfex cuoliex
31rudin««
Dina Bicroatoam
Hcaiptara
Corlzldaa (imuoxra)
Qironoroidaa
Chironominaa
Tanytarsua (Van d«r Wilp)
Chironomua
-------
Trichopcera
Hydropaychidae
§heuBijcop8ye- ,
ydropsychae (Pictec)
(Wallengisn)
Brachycenerida*
Braehycentrua (Curtia)
Leptoceridae
Aehripsodea (BUlberg)
Acarl
Troml ulfoniM
Paraaicangooa,
Hygrobacid««
Hygrpbatea (Koch 1937)
Ephemeropcera
Epheffleridae
Ephemera aiaulana (Walk«r)
ffexagenia (Waj.
-------
APPENDIX B-2
Trichoptor*
Hydropsychidae
Choum.iconsychae (Wallongrtn)
llYdropavchac. (f'leect)
Brachycentrida*
Brachyeenerua (Curtis)
L«pcocerida»
Athripsodea (Blllb«rg}
Acari
Troobtdifom*
Parasitangooa
Hygrobatida*
Hygrobacea (Koch 1937)
Eph«meropc«ra
E?h«merida«
Ephemera aiaulana (WaiJwr)
Hexagenia
Asphlpoda
Eaustorlida*
PonCoporeia afjfinia
Gaatrapoda
Pleuroceridaa
Goniobasla (L«*) Jp. 1
GonioqasT? (L«a) »^, Z
Planorfaida*
HeJUaoma (Swainaoa)
17
DETROIT RIVER BENTHOS
May 1974
x . 18 v
Physa (Orapamaud)
Acmicalidaa
Pyr^ul-oosia sp
Hsmiptara
Corixidaa (immacur*)
Chironomidaa
Chironooina*
Tjnytarsua CVan der Wulp)
Chxronomua (Meigen)
Tax*
Individual*
X Biomasa/m2 (wet weight)
Z Individuala/a2
Shannon-Weaver Dlversley (2)
Richnosa (3f) S-l/lnU
Rlchncsa (X)
r
278
a «• b
Sichinia cencaculaCa, (I.)
Sphaeriidaa
Sphaerium (Scopoli)
PlsnUum (Pfeiffer)
Annelida
Oligochaeea
Tubificida*
Lianodrllua eerv-tea
Liinnodr^lus ^n^uacioenia
i*3cinnorvccides calnronianua
Tup;.^ex :ufai.£ax
Hlrudine*
Dina microstoma
1
5 4-
13 3
3 4 1
1 41
12
1
2
L L
1 6
4 9
0.94
123
0.84
1.14
0.35
3 0
12 0
1.26
226
0.37
0.30
O.S7
6 6
23 28
9.39
529
1.43
1.50
1.13
1
1
5.42
38
0.32
0.46
1.08
2
3
-------
Appendix C-l
Detroit River Phytopigments -
Chlorophylls a, b, and £ (ug/1)
November 1973 and May 1974
Sample
Number
1A
IB
2A
2B
3A
3B
4A
4B
5A
5B
6A
6B
7A
7B
19A
19B
20A
20B
21A
21B
22A
22B
Chi. a
1.0
1.4
1.3
1.0
1.2
0.5
1.5
1.2
1.1
1.7
0.7
0.6
3.5
1.3
1.5
1.0
0.6
1.9
1.9
1.7
3.4
2.7
November 1973
Chi. b
0.4
0.6
0.3
0.9
0.4
0.1
0.1
0.2
0.2
0.3
0.1
0.7
0.5
0.3
0.4
0.1
0.4
1.3
0.4
0.1
0.4
0.5
Chi. c
1.3
1.2
1.1
2.3
1.2
0.9
1.2
0.8
0.9
1.3
-0.1
0.9
1.6
1.2
1.4
0.6
1.7
3.6
1.6
0.9
0.9
1.4
Chi. a.
1.8
2.3
0.4
1.2
0.4
1.7
1.6
0.9
4.0
3.6
2.7
1.2
-
-
2.4
2.1
4.0
3.7
2.5
1.1
2.7
2.3
May 1974
Chi. b
0.2
0.8
0.0
0.0
0.0
0.2
0.5
0.3
0.6
0.8
0.7
0.4
_
-
0.8
0.5
0.8
0.6
0.4
0.1
0.5
0.3
Chi.
0.9
3.2
0.2
1.1
0.2
'' i.o
2.3
1.0
2.2
2.3
2.5
1.4
_
-
3.3
1.8
3.0
2.0
1.6
1.1
1.3
1.3
279
-------
00
o
APPENDIX C-2
PHYTOPLANKTON SUMMARY
Total Species (S)
1
31
St.
2
20
Clair
3
41
River
4
22
Detroit River
August 1973
5 6
28
28
7
31
19
64
20
69
21
32
22
-
Mean total individuals/
ml (N)
Richness (S/ VN)
Richness (S-l/lnN)
Diversity (d)
400
1.55
5.01
2.65
527
0.87
3.03
2.51
345
2.21
6.85
2.90
298
1.27
3.69
2.71
9695
0.28
2.94
1.29
277
1.68
4.80
2.59
427
1.50
4.95
2.89
2018
1.42
8.28
2.43
5209
0.96
7.95
1.93
1197
0.92
4.37
2.17
-
-
-
-
November 1973
Total Species (S)
33
36
43
42
43
51
52
52
41
29
45
Mean total individuals/
ml (N)
Richness (S/ YN)
Richness (S-l/lnN)
Diversity (d)
Mean Chlorophyll a
(yg/D
Total Species (S)
601
1.35
5.00
2.53
1.2
34
526
1.57
5.59
2.82
1.2
36
741
1.58
6.36
2.90
0.8
33
715
1.57
6.24
2.82
1.4
May
35
682
1.65
6.44
3.12
1.4
1974
38
948
1.66
7.29
2.86
0.6
39
1147
1.54
7.24
3.94
2.4
-
963
1.68
7.42
2.97
1.2
47
803
1.45
5.98
2.64
1.2
53
944
0.94
4.09
2.43
1.8
38
1052
9.39
6.32
3.08
3.0
37
Mean total individuals/
ml (N)
Richness (S/V~&)
Richness (S-l/lnN)
Diversity (d)
1700
0.82
4.44
2.63
1346
0.98
4.86
2.61
1113
0.99
4.56
2.71
1385
0.94
4.70
2.55
3132
0.68
4.60
2.76
1416
1.04
5.24
2.64
-
-
-
-
3208
0.83
5.70
2.68
3032
0.96
5.49
2.97
2174
0.81
4.81
2.72
1899
0.85
4.77
2.54
Mean Chlorophyll a
(yg/D
2.0 0.8 1.0
1.2
3.8 2.0
2.2
3.8
1.8
2.5
-------
Cyanophyta:
Anabaena flos-aquae (Lyngb.)
Uulirebisson
A_^ schcremctiovt Elcnkin
A. spiroidos var. crassa Lemm.
Annbnonopsis elcnkinil Miller
Aphanocapsa elnchlsta West & West
Aphnnothece fioljL?A5°M (Hcnn.) Lemm.
A. microspora (Mcncgh.) Rabenhorst
Arthrospira goraontiana Setchell
Chroococcus dispcrsus (Kelssl.)
Lemm.
C_._ limneticus Lemra.
C_^ turgidus (KueCz.) Naegeli
Coolosphaeriun naegclianum Unger
Cyanarcus haipiformis Pascher
DacCylococcopsijL acicularls Lemm.
D^_ fascicularis Lemm.
D_._ rhaphidioides Hansgirg
5L smithli Chodat & Chodat
Lyngbya sp. Agardh
L. Itranetica Letnm.
Marssoniella elegans Lemm.
Mcrlsmopedia glauca (Ehr.) Naegeli
M. tenuissima Lemm.
Mlcrocystis aeruginosa Kuetz.
Oscillatorla sp. Vaucher
0. aRardhii Gomont
0^ annusta, Koppe
0. h.-imclil Frcmy
CK_ limnetica Lemm.
0. minima Gicklhorn
Pelor'.loea bncillifera Lauterborn
Rhnphidiopsis curvata Fritsch & Rich
Chlorophyta:
Actinastrum hantzsehii var. fluviatile
Schroeder
Ankistrodesmus braunii (Naeg.) Brunnthaler
A^ convolutus Corda
A^ falcatus (Corda) Ralfs
A_^ spiralis (Turner) Lemm.
Characiura falcatum Schroeder
C. linmeticum Lemm.
Chariopsis longisslma Lemm.
Chlorella yulgaris BeyerincK
Chlorococcum humicola (Naeg.) Rabenhorst
Clostcriopsis longisslma var. tropica
West & West
Closterium sp. Nitzsch
Coclastrum cambricum Archer
C. microporum Naegeli in A. Braun
C. scabrum Reinsch
£^ sphnoricum Naegeli
Cosmarium sp. Corda
Crucigenia quadrata Morren
DETROIT RIVER PHYTOPLANKTON
(mean number of individuals/ml from replicate samples)
August 1973
1 2* 3 It*
15
35
18
15
39
114
37
281
-------
DETROIT RIVER PHYTOPLANKTON
(mean number of individuals/ml from replicate sample)
continued August 1973
12* 3 4
C^. Cctrapcdia (Kirch.) West Si West 22 6
Elakatothrix p.elattnosa Wille 4 30 6 15
GolenkliUa radiaca (Chod.) Wllle *
Kirchnericlla elon^ata G. H. Smith
K^ subsolitaria G. S. Smith
Laserhelmla ciliaca (Lag.) Chodat
L. lonniseca (Lemm.) Printz
L._ quadrisoca (Lemm.) G. M. Smith 2
L. subsala Lenm.
Mougeotia sp. (C.A. Agardh) Wtttrock 4
Nephrocytium agardhianum Naegeli
Oedogonium sp. Link
Oocystis gloeocystiformis Borge
0^. lacustris Chodat
O_._ novae-semliae Wille 2
0. pusilla Hansgirg
0_._ submarina Lagerheim '
Pediascrmn boryanum (Turp.) Meneghini
P. duplex var. clathratum (A. Braun)
Lagerheim
?_._ simplex var. duo
-------
DETROIT RIVER PHYTOPLANKTOU
(mean number of Indtvlduals/ml from rrplicace samples)
August 1973
continued , +
1 2 3 4
M. caudata Iwanoff
H. urnafonnls Prescott .
Ophioeytiuin copitatum Wolle
Synura uvclla Ehr. 2 i ,
—i — / ^
Bacillariophyta:
Achnauthgs spp. Bory 26 2
Amphora sp. Ehr.
Asterionella formosa Hassall 01 .„
a 19 i
Chaetoceras sp. Ehr.
Cocconeis sp. Ehr. ,
Coscinodiscus rothii (Ehr.) Grun.
Cyclotella spp. Kuetz. H3 go IQQ
C^ catcnata Brun.
Cymatopleura solea (Breb.) W. Smith
Cymbella spp. Agardh .
Diatoma tenue var. elongatum (Lyngb.)
D. vulgare Bory
Diploneis sp. Ehr.
Epithemia zebra (Ehr.) Kuetz.
Frafiilaria spp. Lyngbye 15 jc
F_^ brcvistriata var. inflata (Pant) Hust.
F. capucina Desm.
F. crotonensis Kitton 22 8 ?fi
F._ inflata
F. pinnata Ehr.
Gomphonema spp. Agardh
Gyrosifima sp. Hassall
Molosira pranulata (Ehr.) Ralfs
IL. islandica 0. Muell.
Hi. italics (Ehr.) Kuetz.
M^ varians C. A. Ag.
Navicula spp. Bory 472 4
N. pupula Kuetz. -
N^ tripunctata (0. F. Muell) Bory
Hitzschia spp. Hassali 2
N^ acicularis W. Smith
?L_ dj.ssipa.ta (Kuetz.) Grun.
N^_ frustulum Kuetz.
?L- linearts W. Smith
N. palea (Kuetz.) W. Smith .
IT. sigmoidea (Ehr.) W. Smith
N^. tryblionella Hantzsch
Opephora martyi Heribaud
Pinnularia sp. Ehr.
Rhizosolenia eriensis H. L. Smith
Rhoicosphenia curvata (Kuetz.) Grun. «
Rhopalodia gibba (Ehr.) 0. Muell. 2
Stephanodiscus asEraea (Ehr.) Grun. 19 30 20 30
Surirella sp. Turpin
Synedra spp. Ehr. 43 47
S. actinastroides Lemm.
£._ ulna (Nitz.) Ehr.
Tabcllaria flocculosa (Roth) Kuetz. 19 96 26 22
283
-------
DETROIT RIVER PHYTPPI.ANKTON
(mean number of iiuiividvi.il.s/nil from replicate samples)
. August 197J *
1 2* 3 4
continued
Pyrrhophyta:
Ceratlum hirundinclla (0. F. Muell.) 4
Dujardin
Glenodintum ponnrdlformc (Linde.) 474 4
Schiller
G^ pulvisculus (Ehr.) Stein
Euglenophyta:
Colacium arbuscula Stein
Euglena sp. Ehr.
Tracholomonas sp. Ehr. 2
T. robusta Swirenko
T^ yolvoclna Ehr.
Other Flagellates:
Chroomonas sp. Hansglrg 4
Chrysococcus sp. Klebs
Cryptomonas sp. Ehr. 6 9
Nephroselmis olivacea Stein 4 26 9 15
Rhodomonas lacustris Pascher 9 13
Total Number of Species (S) 31 20 41 22
Mean Total Individuals/ml (N) 400 527 345 298
Richness (S/VTl) 1.55 0.87 2.21 1.27
Richness (S-l/lnN) 5.01 3.03 6.85 3.69
Shannon-Weaver Diversity (I) 2.65 2.51 2.90 2.71
*indicates single samples rather than replicates
284
-------
DETROIT RIVER PHYTOPLANKTON
(mean number of individuals/ml from replicate samples)
August 1973
Cyanophyta: 5* 6 7* 19 20 21* 22**
Anabaena flos-aquae (Lyngb.)
DeBrebisson
A^ schorcmetievi Elenkin 2 8
A. spiroides var. crassa Lemm. 49
Anabaenopsls elcnkinii Miller 4
Aphanocapsa elachista West & West
Aphanothece gelatinosa (Henn.) Lemm.
A. microspora (Menegh.) Rabenhorst 48
Arthrospira gomontiana Setchell 4
Chroococcus dlspersus (Keissl.)
Lemm. 25 42
-------
continued
5*
C^ tctrapedia (Kirch.) West & West
Elakatothrix eclntinosa Wille 25
Golcnklnla radlata (Chod.) Wille
Kirchncriella clonf.ata G. M. Smith
K^ subsolitaria G. S. Smith
Lagerhoimia ciliata (Lag.) Chodat
LJ. long!seta (Lemm.) Printz
L. quadriseta (Lemm.) G. M. Smith
L. subsala Lemm.
Mougeotia sp. (C.A. Agardh) Wittrock
Nephrocytium agardhianum Naegeli
Oedogonium sp. Link 62
Oocystis gloeocystiformis Borge
0. lacustris Chodat
-------
continued
DETROIT RIVER PHYTOPI.ANKTON
(mean number of individuals/ml from replicate samples)
August 1973
5* 6 7* 19
20
21*
22**
M. caudata Iwanoff 12
M. urnaformis Prescott
Ophiocytium capltatum Wolle
Synura uvella Ehr.
Bacillariophyta:
Achnanthes spp. Bory
Amphora sp. Ehr.
Asterionella 1'ormosa Hassall 25
Chaetoceras sp. Ehr.
Cocconeis sp. Ehr.
Coscinodiscus rothii (Ehr.) Grun.
Cyclotella spp. Kuetz. 7134
C_._ catenata Brun.
Cymatopleura solea (Breb.) W. Smith
Cymbella spp. Agardh
Diatoma tenue var. elongatum (Lyngb.)
D_._ vulgare Bory
Diploneis sp. Ehr.
Epithemia zebra (Ehr.) Kuetz.
Fragilaria spp. Lyngbye
t\ brevistrlata var. InfLata (Pant) Hust.
F. capucina Desm.
t\ crotonensis Kitton
H inflata
F_._ pinnata Ehr.
Gomphonema spp. Agardh
Gyrosigma sp. Hassall
Melosira granulata (Ehr.) Ralfs
£L_ islandica 0. Hue 11.
M_^ italica (Ehr.) Kuetz. 209
M._ varians C. A. Ag.
Navicula spp. Bory 25
N. pupula Kuetz.
N^ tripunctata (0. F. Muell) Bory
Nitzschia spp. Hassall 111
?L- acicularis W. Smith
ft_. dissipata (Kuetz.) Grun.
N_^ frustulum Kuetz.
N^ linearis W. Smith
N^ palea (Kuetz.) W. Smith
N^ siRmoidea (Ehr.) W. Smith
N^_ tryblionella Hantzsch
Opephora martyi Heribaud
Pinnularia sp. Ehr.
Rhizosolenia eriensis H. L. Smith
Rhoicosphenia curvata (Kuetz.) Grun.
Rhopalodla Ribba (Ehr.) 0. Muell.
Stephanodiscus astraea (Ehr.) Grun.
Surirella sp. Turpin
Synedra spp. Ehr.
S. actinastroides Letnm.
S^ ulna (Nitz.) Ehr.
Tabellaria flocculosa (Roth) Kuetz.
33
75
30
2
10
66
41
55
41
19
1
2
2
17
167
961
17
79
4
41
2
6
2
23
9
2
2
6
8
2
2
10
1918
1992
92
9
21
59
17
17
4
553
37
4
37
18
184
11
7
26
15
287
-------
continued
DETROIT RIVER PHYTOPLANKTON
(mean number of Individuals from replicate samples)
Auf.ust 1973
5* 6 7* 19 20
21*
22**
Pyrrhophyca:
Ceratiurn hirundinella (0. F. Muell.)
Dujarjin
Glenodinium penardiformc (Linde.)
ScnTller
G^_ pulvtsculus (Ehr.) Stein
Euglenophyta-
Colacium arbuscula Stein
Euglena sp. Ehr.
Trachelomonas sp. Ehr.
T. robusta Swirenko
T^ volvocina Ehr.
Other Flagellates:
Chroomonas sp. Hansgirg
Chrysococcus sp. Klebs
Cryptamonas sp. Ehr
Nephroselmis olivacea Stein
Rhodomonas lacustris Pascher
25
3
16
2
2
22
18
Total Number of Species (S)
Mean Total Individuals/ml (N)
Richness (S/V~N)
Richness (S-l/lnN)
Shannon-Weaver Diversity (d)
28
9695
0.28
2.94
1.29
28
277
1.68
4.80
2.59
31
427
1.50
4.95
2.89
64
2018
1.42
8.28
2,43
69
5209
0.96
7.95
1,93
32
1197
0.92
4.37
2.17
*indicates single samples rather than replicates
**no samples from this station
288
-------
DETROIT RIVER PIIYTOl'LANKTON
(mean number of individuals/ml from replicate samples)
November 1973
1234
Cyanophyta:
Anabaona flos-aquac (Lyngb.)
DoBrebisson
A. scheremotlevi Elenkin
A. spiroidos var. crassa Lemm.
Anabaenopsis elenkinil Miller
Aphanocapsa elachista West & West 63
Aphanothoce geiatinosa (Henn.) Lcinm.
A. microspora (Menegh.) Rabenhorst
Arthrospira gomontiana Setchell
Chroococcus dispersus (Keissl.)
Lemm. 11 30 8
C. limneticus Lemm. 4
£i. turgidus (Kuetz.) Naegeli 9 4 11
Coelosphaerium naegelianum Unger 9 11 6 2
Cyanarcus hamiformis Pascher 2
Dactyloooccopsis aeicularis Lemm.
D_._ faseicularis Lemm.
D^_ rhaphidioides Hansgirg
!L_ smithii Chodat & Chodat
Lyngbya sp. Agardh 4
ku limnetlca Lemm. 7 8 10
Marssoniella elegans Lemm.
Merismopodia glauca (Ehr.) Naegeli
M. tenuissima Lemm.
Microcystls aeruginosa Kuetz. 17 61 52 34
Osctllatoria sp. Vaucher
0^ agardhii Gomont 10 11 6
0. angusta Koppe ^
2_u hamelii Fremy
0_._ limnctica Lemm.
0_._ minima Gicklhorn
Pelogloea bacillifera Lauterborn 26 2 70 42
Rhaphidiopsis curvata Fritsch ft Rich
Chlorophyta:
Actinastrum hantzschii var. fluviatile
Schroeder
Ankistrodesmus braunii (Naeg.) Brunnthaler
A. convolutus Corda
A. falcatus (Corda) Ralfs 32 11 8
A. spiralis (Turner) Lemm. 2
Characium falcatum Schroeder
C. limnoticum Lemm.
Chariopsis lonp.issima Lemm.
Chlorclla vulgaris Beyerinck
Chlorococcum humicola (Naeg.) Rabenhorst
ClostGriopsis longissima var. tropica
West & West ~ 22
Closterium sp. Nitzsch
Coelastrum cambricum Archer
C. microporum Nac(;eli in A. Braun
C. scabrum Reinsch
C. sph;icricum Naegeli
Cosmarium sp. Corda 222
Crucif.eriia quadrata Morren 15 8
289
-------
continued
DETROIT RIVER 1'HYTOPl.ANKTON
(mean number of indiviilu^ls/ml from replicate samples)
November 1973
C^ tctrapcdta (Kirch.) West & West
Elakatothrix flnl.itinosa Wille
Golenklnia rodiata (Chod.) Wille
Kirchneriella elongata G. M. Smith
L. subsolitaria G. S. Smith
Lagerheimia cillata (Lag.) Chodat
L. longtseta (Lemm.) Printz
L. quadriseta (Lerara.) G. M. Smith
L. subsala Lemm.
Mougeotia sp. (C. A. Agardh) Wittrock
Nephrocytium agardhianum Naegeli
Oedogonium sp. Link
Oocystis gloeocystiformis Borge
0_._ lacustris Chodat
!L_ novae-semliae Wille
0^ pusilla llansgirg
0. submarina Lagerheim
Pediastrum boryanum (Turp.) Meneghini
P. duplex var. clathratum (A. Braun)
Lagerheim
P. simplex var. duodenarium (Bailey)
Rabenhorst
L. tetras (Ehr.) Ralfs
Phymatodoci s sp. Nordstedt
Planktosphacria gelatinosa G, M. Smith
Pleurotaenium sp. Naegeli
Polyblopharidcs sp. Dangeard.
Rhiy.oclonium sp. Kuetz.
Scencdosmus abundans (Kirch.) Chodat
S. bijuRa (Turp.) Lagerheim
S. dcnticulatus Lagerheim
•L. dimorphus (Turp.) Kuctz.
S. incrassaculus Eohlin
§_._ opoliensis P. Richter
S_._ quadricauda (Turp.) de Brebisson
Schrooderia sctiqera Lemra.
Selenastrum F_i_nm.um (Naeg.) Collins
§-^ yestii G. M/ Smith
Staurastrum sp. Meyen
Tetradesmus vjl'jeonsinpnse G. M. Smith
Tetraodrgn cnu^itum (Corda) Hansgirg
T^ duosplniim Ackley
T^ lunula (Reir.bch) Vlille
T. minimum (A. ;H-aun) llansgirg
T._ rpgul are Kuetz.
T. trtj'.ouuni vur firnrtle (Reinsch) DeLoni
TetraHjpora 1 i^"-,hris Lemm.
TotraHtrum sj: '.':tTEc'ni.icforme (Schroedcr) Lemm.
Trcub.rria t_r_i.i_r;)-ndiciil_ata Bernard
Ulothrlx sp. K''Utz.
Chrysophytar
Dtcor.is ph.-^f.f.lj^s Fott
up. rhr.
13
10
10
11
2
2
2
2
2
290
-------
continued
D^ bnvaricum Imhof
D^ cnlciformis Bach
D^ dtvcrKons Imhof
D. sortularta Ehr.
D^ tabollarino (Letran.) Pascher in
Pascher & Lcmm.
Kophyrion ovum Pascher
Lap.ynion ampullaceum (Stokes) Pascher
Mallomonas acaroides Perty
M. caudata Iwanoff
M. urnaformis Prescott
Ophiocytiura capitatum Wolle
Synura uvella Ehr.
Bacillariophyta:
Achnanthes spp. Bory
Amphlpleura sp. Kuetz.
Amphora sp. Ehr.
Asterionella formosa Hassall
Chaetoceras sp. Ehr.
Cocconeis sp. Ehr.
Coscinodiseus rothii (Ehr.) Grun.
Cyclotella spp. Kuetz.
C^ glomerata Bachmonn
C. catenata Brun.
Cymatopleura elliptica (Breb.) W. Smith
C^ solea (Breb.) W. Smith
Cymbella spp. Agardh
Diatoma tenue var. elongatum (Lyngb.)
D. vulgare Bory
Diplonois sp. Ehr.
Epithemia zebra (Ehr.) Kuetz.
Fraftilaria spp. Lyngbye
F_^ brevistriata var. inflata (Pant) Hust.
F. capucina Desm.
F_._ crotonensis Kitton
j\_ inflata
F_^ pinnata Ehr.
Gomphonema spp. Agardh
Gyrosigma sp. Hassall
Melosira distans (Ehr.) Kuetz.
M^ granulata (Ehr.) Ralfs
M^ islandica 0. Muell.
M^ italica (Ehr.) Kuetz.
M. varians C. A. Ag.
Navicula spp. Bory
N._ pupula Kuetz.
N^ scutelloides W. Smith
N^ tripunctata (0. F. Muell) Bory
Nitzschia spp. Hassall
N_^ acicularis W. Smith
IL. dissipata (Kuetz.) Grun.
N. frustulum Kuetz.
DETROIT RIVER PHYTOPLANKTON
(mean number of individuals/ml from replicate samples)
November 1973
1234
15
76
6
19
2A
6
207
113
30
6
23
4
2
78
83
4
21
150
28
6
15
10
50
32
17
212
35
8
2
13
4
291
-------
continued
1L Hnonrla w- Smlch
N. palca (Kuctz.) W. Smith
?L sir.moidca (Ehr.) M. Smith
N_._ tryblionella Hantisch
Opephora martyi Hcribaud
Pinnularia sp. Ehr.
Rhizosolenia orionsis H. L. Smith
Rhoicosphenia eurvaca (Kuetz.) Grun.
Rhop.-Uodia gibba (Ehr.) 0. Muell.
Stephanodiscus astraea (Ehr.) Grun.
Surirella sp. Turpin
S_._ an,°ustata Kuetz.
S_^ oval is Breb.
Syneara spp. Ehr.
S. actinastroides Lemn.
S^_ ulna (Nitz.) Ehr.
Tabellaria flocculosa (Roth) Kuetz.
Pyrrhophyta:
Certatium hirundinella (0. F. Muell.)
Dujarain
Glenodinium penardiformc (Linde.)
Schiller
£._ pulvisculus (Ehr.) Stein
Gymnodinium fuscum-(Ehr.) Stein
Euglenophyta:
Colacium arbuscula Stein
Euglona sp. Ehr.
E. convoluta Korshikov
Phascus sp. Dujardin
Lepocinclis glabra Drezepolski
Trachclomonas sp. Ehr.
T. robusta Swirenko
T._ volvocina Ehr.
Other Flagellates:
Chroraulina sp. Cienkowski
Chroomonas sp. Hansgirg
Chrysococcus sp. Klebs
Cryptomonas sp. Ehr.
Nephroselmia olivaeea Stein
RhodoF.onas lacustris Pascher
Unidentified flagellate
Total Number of Species (S)
Mean Total Individuals/ml (N)
Richness (S/ V~H)
Richness (S-l/lnN)
Shannon-Weaver Diversity (of)
DETROIT RIVER PHYTOPLANKTON
(mean number of individuals/ml from replicate samples)
November 1973
13
33
601
1.35
5.00
2.53
15
63
47
36
526
1.57
5.59
2.82
3
24
30
24
43
741
1,58
6.36
2.90
22
2
72
17
24
42
715
1,57
6.24
2.82
292
-------
CyanophyCa:
Annh.non_A flos-aquae (Lyngb.)
DcBrcbisson
A^ schcremcticvi Elenkln
A. splroidus var. crassa Lonun.
Anabacnopsis elcnklnil Miller
Aphanocapr.a clachista West & West
Aphanothccc >'.elatinosa (Henn.) Lemtn.
A. microspora (Mcnegh.) Rabenhorst
Arthrospira Romontiana Setchell
Chroococcus dispersus (Keissl.)
Lemro.
C. llmneticus Lemm. g
C_._ turfiidns (Kuetz.) Naegeli n
Coelosph.iGrium n.iegelianum Unger 2
Cyanarcus hamiformls Pascher
Dactylococcopsis aeicularis Lemm.
D. fascicularis Letnra.
D. rhaphidloides Hansgirg
D^_ smithii Chodat & Chodat
Lyngbya sp. Agardh
L. limnetlca Lemm.
Marssoniella elegans Lemm.
Merlsmopcdla glauoa (Ehr.) Naegeli
M. tenutssima Lenun.
Microcystis aeruginosa Kuetz. 19
Oscillatorla sp. Vaucher
0. apardhli Gomont
0^_ anr.usta Koppe
0. hamclil Fremy
0^_ Hjanetlca Lomm.
O. minima Gicklhorn
Pelogloea bacillifera Lauterborn
Rhaphicliopsis curvata Fritsch & Rich
Chlorophyta:
Aetinastrum hantzschii var. fluviatile
Schroeder
Ankistrodesmus braunii (Naeg.) Brunnthaler
A. convolutus Corda
A. falcatus (Corda) Ralfs 15
A. spiralis (Turner) Lemm. g
Characium falcatum Schroeder 2
C. lirnncticum Lemm.
Chariopsis lonsissima Lemm.
Chlorclla vulgaris Beyerinck
Chlorococcum humicola (Naeg.) Rabenhorst
Clostcrjxipsis lonsissima var. troplca
West & West
Closterium sp. Nitzsch
Coelar.trum cambricum Archer
C. microporum Naegeli in A. Braun
C. scabrum Rcinsch
C. sphaericum Naegeli
Cosmqrtum sp. Corda
Cruclf.enia qnndrata Morrcn
DETROIT RIVER PHYTOPLANKTON
(mean number of individuals/ml from replicate samples)
November 1973
6 7 19 20 *21 22
5
2
26
4
17
17
4
15
10
2
11
4
9
6
9
2
26
46
30
20
9
10
2
11
4
43
35
293
-------
continued
CL tetropcdia (Kirch.) West & West
Elakatothrix gelatinosa Wille
Golenklnia radiata (Chod ) Wille
Kirchncriclla elonf.ata G. M. Smith
K_._ subsolitaria G. S. Smith
Lagerheimia ciliata (Lag.) Chodat
L. Icagiseta (Lemm.) Printz
ki. q^adriseta (Lemm.) G. M. Smith
L. subsala Lemm.
Mougeotia sp. (C. A. Agardh) Wittrock
Nephrocytium ap.ardhianum Naegeli
Ocdogonium sp. Link
Oocystis gloeocystiformis Borge
0. lacustris Chodat
0. novae-semliae Wille
0. pusilla Hansgirg
0. submarina Lagerheim
Pediastrum boryanum (Turp.) Meneghini
^- duplex var. clathratum (A. Braun)
Lagerheim
P_; simplex var. duodenarium (Bailey)
Rabenhorst
Ei tetras (Ehr.) Ralfs
Phycatodocis sp. Nordstedt
Plar.ktosphaeria Re latinos a G.
Pleurotaenium sp. Naegeli
PolyblopharjLdes sp. Dangeard.
Bhizoclonium sp. Kuetz.
Seer.edesrous abundang (Kirch.) Chodat
S_._ bijuga (Turp.) Lagerheim
S. denticulatus Lagerheim
S._ cimorphus (Turp.) Kuetz.
S. incrassatutus Bohlin
S_._ opolionsis P. Richter
•L- guadricauda (Turp.) de Brebisson
Schroederia sotif'cra
Smith
Selenastrum miniitum (Naeg.) Collins
•L. yestii G. K.' Smith
DETROIT RIVER 1'IIYTOI'LANKTON
(mean number of individuals/ml from replicate samples)
November 1973
5 6 ? 19 20 *21
10
6
Sta'jrostrum sp. Meyen
Tetradosmus wi-iconsincnse G. M. Smith
Tetraedron caudptun (Corda) Hansgirg
T,_ duospinum Ackley
"L- !"""!? (Rcinsch) Wille
T_._ ainlmum (A. Braun) Hansgirg
T._ regularc Kuetz.
T. trif.onim var. gracllc (Reinsch) Detoni
Tctraapora lacu', t-_ri s Lemm.
Tctrastrum HI .T.IT o^cninoforroo (Schroeder) Lemm.
Trc'Aqria trj/ir.ii!'nd.iculata Bernard
Ulothrtx sp. Kcutz.
Chrysophyta:
Dtcorjj; phru-.po),;^ Kott
Dinobrygn ap. F.hr.
22
13
30
17
2
8
6
21
2
7
35
2
4
2
22
15
4
9
15
2
2
28
6
2
2
294
-------
DETROIT RIVF.R PHYTOI'LANKTON
(mean number of individuala/ml from replicate samp lea)
November 1973
continued
D. bavai'icum Imhof
D. calclformts Bach
D. divcrr.cns Imhof
5i. sertularta Ehr.
iL tabcllariae (Leram.) Faschcr in
Pascher & Lemm.
Kephvrion ovum Pascher
Lap.ynion ampullaceum (Stokes) Pascher
Mallomonas acaroides Perty
M;_ caudata Iwanoff
M^ urnaformis Prescott
Ophiocyclum capitatum Wolle
Synura uvclla Ehr.
Bacillariophyta:
Aehnanthes spp. Bory
Amphipleura sp. Kuetz.
Amphora sp. Ehr.
Asterionella formosa Hassall
Chaetoceras sp. Ehr.
Cocconeis sp. Ehr.
Coscinodiscus rothii (Ehr.) Grun.
Cyelotella spp. Kuetz.
C_^ glomerata Bachmann
C_._ catenata Brun.
Cymatopleura elliptica (Breb.) W. Smith
£._ solea (Breb.) W. Smith
Cymbella spp. Agardh
Diatoma tcnue var. elongatum (Lyngb.)
D._ vulr.are Bory
Diploncis sp. Ehr.
Epitheala zebra (Ehr.) Kuetz.
Fragilaria spp. Lyngbye
F_^ brevistriata var. inflata (Pant) Hust.
F. capuclna Desm.
F. crotoncnsis Kitton
F_^ inflata
¥^_ pinnata Ehr.
Gomphonema spp. Agardh
Gyrosi?,ma sp. Hassall
Helosira distans .(Ehr.) Kuetz.
*L. Rranulata (Ehr.) Ralfs
H_^ islandica 0. Muell.
M^ italica (Ehr.) Kuetz.
5L. yarians C. A. Ag.
Navicula spp. Bory
N. pupula Kuetz.
N._ scutolloidcs W. Smith
N._ tripunctata (0. F. Muell) Bory
Nitzschia spp. Hassall
?L. acicularis W. Smith
tL_ dlnslpata (Kuetz.) Grun.
N. frustulum Kuetz.
5
15
26
6
15
7
17
19
8
11
.35
6
30
21
8
2
4
234
15
2
4
96
24
2
17
2
118
21
9
28
2
19
4
2
22
81
76
4
2
52
4
9
6
2
2
11
20
A
9
6
*21
30
22
30
21
11
8
52
2
68
15
8
2
15
30 6 11 4 15
133 152 85 113 277
4
267 9
96 216 131 95 114
8
8 6
2
4
4
6
17 6 19
2
170
2
41
2
37
233
170
131
22
7
22
41
18
4
59
26
33
295
-------
continued
N^_ lincnris W. Smith
*L- Paloa (Kuetz.) W. Smith
NL_ sir.moidea (Ehr.) W. Smith
N. tryblionclla Hantzsch
Opophora m.irtyt Heribaud
Pinnul.irJa sp. Ehr.
Rhizosolcnla eriensis H. L. Smith
Rhoicosphcnia curvata (Kuetz.) Grun.
Rhopalodia gibba (Ehr.) 0. Muell.
Stephanodlscus astraea (Ehr.) Grun.
Surirella sp. Turpin
S. angustata Kuetz.
S_._ ovalis Breb.
Synedra spp. Ehr.
S. actinagtroides Lemm.
S_._ ulna (Nitz.) Ehr.
Tabellaria flocculosa (Roth) Kuetz.
Pyrrhophyta:
Certatium hirundinella (0. F. Muell,)
Dujardin
Glenodinlum penardiforme (Linde.)
Schiller
G_._ pulvisculus (Ehr.) Stein
Gymnodinium fuscunr(Ehr.) Stein
Euglenophyta:
Colacium arbuscula Stein
Euglena sp. Ehr.
E^_ convoluta Korshikov
Fhascus sp. Dujardin
Lepoeinclis glabra Drezepolski
Trachelomonas sp. Ehr.
T\_ robusta Swirenko
£_._ volvocina Ehr.
Other Flagellates:
Chromulina sp. Cienkowski
Chroomonas sp. Hansgirg
Chrysococcus sp. Klebs
Cryptomonas sp. Ehr.
Nephroselmis olivacea Stein
Rhodomonas lacustris Pascher
Unidentified flagellate
Total- Number of Species (S)
Mean Total Individuals/ml (N)
Richness (S/ VTl)
Richness (S-l/lnN)
Shannon-Weaver Diversity (3")
*indicates single samples rather than replicates
DETROIT RIVKR PHYTOPI.ANKTON
(mean number of individuals/ml from replicate samples)
November 1973
6 7
5
4
19
21
26
10
26
22
28
24
24
70
7
2
39
59
11
65
19
186
22
32
20
8
4
17
48
41
56
*21
7
15
22
41
74
22
17
28
21
39
68
93
43
682
1.65
6.44
3.12
51
948
1,66
7,29
2,86
52
1147
1,54
7.24
3.04
52
963
1.68
7,42
2,97
41
803
1.45
5.98
2,64
29
944
0,94
4.09
2.43
45
1052
9.39
6.32
3,08
296
-------
DETROIT RIVER PHYTOPLANKTON
(mean number of individuals/ml, from replicate samples)
May 1974
Cyanophyta:
Aiialxien.-i flos-aquac (Lyngb.)
Dcllrebisson
A^ schoremetievt Elenkin
AL splroides var. erassa Lemra.
Anabacnopsis elenklnii Miller
Aphanoc.ipsa elachiata West & West
Aphanothccc Rolatinosa (Henn.) Lemm.
A. microspora (Henegh.) Rabenhorst
Arthrospira Kornonti.ina Setchell
Chroococcus dispersus (Keissl.)
Lemm.
C_._ limneticus Lemm.
C. turgldus (Kuetz.) Naegeli
Coelosphaerium naegelianum Unger
Cyanarcus hamiformis Pascher
Dactylococcopsis acicularis Lemm.
D. faseicularis Lemm.
D^_ rhaphidioldes Hansgirg
IL. smithii Chodat & Chodat
Lyngbya sp. Agardh
L. limnetica Lemm.
Marssoniella elesans Lemm.
Merismopedia glauc'a (Ehr.) Naegeli
M. tenutssima Lemm.
Microcystis aeruainosa Kuetz.
Oscillatoria sp. Vaucher
O. agardhii Gomont
0. anRusta Koppe
O_._ hamelii Fremy
0. limnotica Lemm.
0_._ minlna Gicklhorn
Pelogloca bacillifera Lauterborn
Rhaphidiopsis curvata Fritsch & Rich
Chlorophyta:
Actinastrum hantzschii var. fluviatile
Schroeder
Ankistrodesmus braunii (Naeg.) Brunnthaler
A. eonvolutus Corda
A. falcatus (Corda) Ralfs
A. spiralis (Turner) Lemm.
Characium falcatum Schroeder
C. limneticum Lemm.
Chariopsis longissioa Lemm.
Chlorella vulgaris Beyerinck
Chlorococcum humicola (Naeg.) Rabenhorst
Closteriopsis lon^lssima var. tropica
West & West
Closterium sp. Nitzsch
Coelastrum cambricum Archer
C. microporum Naegeli in A. Braun
C. scabrum Reinsch
C. sphaoricum Naegeli
Cosmarium sp. Corda
Cruclp.cnla guadrata Morren
8
35
16
2
2
18
15
4
9
32
2
35
4
37
7
26
2
297
-------
DETROIT RIVi:R HIYTOPLANKTON
(mean number of individu,,l«/ml from replicate
May 1974
continued
£j. tetrapodta (Kirch.) West & West
Elnkatothrlx i;c latinos a Wille
GolenkJnia radlata (Chod.) Wille
Kirchncriclla elongata G. M. Smith
K^ subsolitaria G. S. Smith
Lagcrheimia ciliata (Lag.) Chodat
L. longiscta (Lemm.) Printz
L. quadriseta (Lemm.) G. M. Smith
L. subsala Lemm.
MouRcotia sp. (C. A. Agardh) Wittrock
Hephrocyttum a^ardhianum Naegeli
Oedogonlum sp. Link
Oocystis glococystiformis Borge
0^_ lacustris Chodat
0. novae-semliae Wille
OL_ pusilla Hansgirg
0. submarina Lagerheim
Pediastrum boryanum (Turp.) Meneghini
P_._ duplex var. clathratum (A. Braun)
'duodenarium (Bailoy)
L. tetras (Ehr.) Ralfs
Phymatodocis sp. Nordstedt
Planktosphacria gelattnosn G. M. Stnith
Pleurotaenium sp. Naegeli
Polyblepharides sp. Dangeard. _
Rhizoclonium sp. Kuetz.
Sccnedesmus abundans (Kirch.) Chodat _
S^_ bijuga (Turp.) Lagerheim ,
S^_ denticulatus Lagerheim
S. dimorphus (Turp.) Kuetz.
£L_ incrassatulus Bohlin
S_^ opoliensis P. Richccr
S^ quadricauda (Turp.) de Brebisson
Schroederia setlgera Lemm.
Selenastrum minutum (Naeg.) Collins
S_^ westii G. M. Smith
Staurastrum sp. Meyen
Tetradesmus wisconsinensc G. M. Smith
Tetraedron caudatum (Corda) Hansgirg
T._ duospinum Ackley
"L. lunula (Reinsch) Wille
T^ minimum (A. Braun) Hansgirg
T^_ rcgularc Kuetz.
T^ trlgonum var. gracile (Reinsch) Detoni
Tctraspora lacustris Lemm.
Tctrastrum staurof.eniaoforme (Schroeder) Lemm.
Treubaria tri.-ippondiculata Bernard
Ulothrix sp. Keutz.
Chrysophyta:
Diccras phnsoolus Fott
Dinohryon sp. Ehr.
298
-------
continued
IL. bny.irlcum Imhof
D^ calrtformis Bach
D^_ divi'fp.ens Imhof
D^ scrmlnrla Ehr.
D^ tnliollariae (Lcmm.) Pascher In
Pascher & Lemm.
Kephvrion ovum Pascher
Lap.ynion ampullaceum (Stokes) Pascher
Mallomonas acaroidcs Perty
M. caudata Iwanoff
M. urnaformis Prescott
Ophiocytium eapitatum Wolle
Synura uvella Ehr.
Baclllariophyta:
Achnanthes spp. Bory
Amphipleura sp. Kuetz.
Amphora sp. Ehr.
Asterionella formosa Hassall
Chaetoceras sp. Ehr.
Cocconcis sp. Ehr.
Coscinodiscus rothil (Ehr.) Grun.
Cyclocella spp. Kuetz.
C. glotnerata Bachmann
C. catenata Brun.
Cymatopleura elliptlca (Breb.) W. Smith
C_._ solea (Breb.) W. Smith
Cymbella spp. Agardh
Diatoma tenue var. elonp,atum (Lyngb.)
D. vulj'.are Bory
Diploneis sp. Ehr.
Epithcmia zebra (Ehr.) Kuetz.
Fraflilaria spp. Lyngbye
F._ brevistriata var. inflata (Pant) Hust.
F. capucina Desm.
F._ crotonensis Kitton
F._ inflata
F. pinnata Ehr.
Gomphonema spp. Agardh
Gyrosigma sp. Hassall
Melosira distans (Ehr.) Kuetz.
M. granulata (Ehr.) Ralfs
M^ islandica 0. Muell.
M.. italica (Ehr.) Kuetz.
M. varians C. A. Ag.
Navicula spp. Bory
H. pupula Kuetz.
N^ seutelloides W. Smith
N_^ tripunctata (0. F. Muell) Bory
Nitzschia spp. Hassall
N_._ acicularis W. Smith
N. dissipata (Kuetz.) Grun.
N. frustulum Kuetz.
DETROIT RITCR PHYTOPLANKTON
(mean number of individuals/ml from replicate samples)
1
4
78
98
61
2
2
104
30
33
41
216
81
7
11
May 1974
2
15
6
115
50
2
11
19
4
79
245
22
4
15
139
41
50
59
13
155
24
57
4
2
13
4
35
207
32
54
47
2
4
26
15
146
24
17
299
-------
continued
linoarls W. Smith
?L
_
-------
*5
Cyanophyta:
Aiiobacn.i flos-aquau (Lynch.)
~~ Deiu-cbisuon
A. schoronipficvi Rlcnkin
A. spiroidcr. var. £tvu\sn^ Leinm.
Anabacnopsis eleiikinil Miller
Aphancc.ipn.i elachistj West & '..'ost
Aphanotheco Rol.it uuria (Honn ) Lcmin.
A. micros per a (Mencgh.) Rabonl'orst
Arthrosplra gomontiana Setchell
Chroococcus dispersus (Kcissl.)
Lemm.
C, limneticus Letnm.
C^_ turpidus (Kuetz.) Naegcli
Coelosphaorium nao^olianum Ungcr
Cyanarcus hamlformis Pascher
Dactylococcopsis acicularis Leirjn.
D. fasciculnris Lcmm.
EL_ rhaphldioldes Hansgirg
D^_ smithii Chodat & Chodat
Lyngbya sp. Agardh
L. limnetica Lemm.
Marssoniclla elo^.ana Lemin.
Merismopt-dia glauca (Chr.) N.tegell
M. tcnuissima Leram.
Microcysuis agrup.inosa KueLz.
Oscillatoria sp. Voucher
QL_ agardhii Gomorit
0. anfjusta Koppe
0^_ hamcliji Fremy
0. llmnctica Lemm.
0_^ min i ma Gicklhoin
Pelogloea bacilli foi.i LauCerborn
Rhaphidiopnis curv.iL.i FriLr.cli & Rich
Chlorophyta:
Aetinastrum hantzschii var. fluviatile
Schroeder
Ankistrodesmus braunii (Naeg.) Brunnthaler
A. convolutus Corda
A. falcatus (Corda) Ralfs
A. spiralis (Turner) Lemm.
Characium falcatrum Schroeder
C. limneticum Lemm.
Charlopsis longissima Lemm.
Chlorella vulRarls Beyorinck
Chlorococcum humleola (i!aeg.) Rabenhorst
Clostoriopsls lonslssima var. troplca
West & West
Clostorlum sp. Nitzsch
Coclastrum cambricum Archer
C. microporum Nacgeli iri A. Braun
C. scnhrum Rcinsch
C. sph.icrlcum Nacgeli
Cosmarjjjm sp. Corda
Cruel p.r'tiia quadra I:a Morren
DETROIT RIVER PIIYTOPLANKTON
(mean number of individuals/ml from replicate aamolcu)
May 197A V
6 **7 19 20 21
22
18
39
2
11
15
6
15
A
19
13
15
22
9
13
19
55
18
22
2
59
37
2
45
24
61
7
26
15
301
-------
DETROIT RIVER PHYTOPLANKTON
(mean number of iiulivlilu.il •,/ml from i i>pl i c.i to s/imp lea)
continued
May 1974
*5 6
**7
19
20
21
22
C. tetrapcdta (Kirch.) West & West
Elakatothrix fielatinosa Wille
Colenkinla radiat.i (Chod.) Wille
Klrchneriella elonfiata G. M. Smith
K^ subsolitaria G. S. Smith
Lagerheimia cillata (Lag ) Chodat
L. longiseta (Lemm.) Printz
L. quadriseta (Lemm.) G. M. Smith
L. subsala Lemm.
Mougeotia sp. (C. A. Agardh) Wittrock
Nephrocytlum agardhianum Naegeli
OedoRonium sp. Link
Oocystis gloeocystifomiis Borge
0. lacustris Chodat
0. novae-semliae Wille
0. pus i11a Hansgirg
0. submarina Lagerheim
Pediaatrum boryanum (Turp.) Meneghini
P. duplex var. clathratum (A. Braun)
Lagerheim
P. simplex var. duodenarium (Bailey)
Rabenhorst
P_^ tetras (Ehr.) Ralfs
Phymatodocis sp. Nordstedt
Planktosphaeria gelatinosa G. K. Smith
PIeurotaeniura sp. NaegelJ
Polyblepharides sp. Dangeard.
Rhizoclonium sp. Kuetz.
Scenedestnus abundans (Kirch.) Chodat
S. bijuga (Turp.) Lagerheim
S, denticulatus Lagerheim
S. dimorphus (Turp.) Kuetz.
S. incrassatulus Bohlin
S. opoliensis P. Richter
S. quadricauda (Turp.) de Brebisson
Schroederia sotigc.ra Lenrni.
Selenastrum minutum (Naeg.) Collins
S_._ westii G. M. Smith
Staurastrum sp. Meyen
Tetradesmus visconsinense G. M. Smith
Tetraedron caudatum (Corda) Hansgirg
T. duospinum Ackley
T^ lunula (Reinsch) Wille
T. minimam (A. Braun) Hansgirg
T. regulare Kuetz.
Zj. trigonum var. gracile (Reinsch) Detoni
Tetraspora lacustria Lemm.
Tetrastrum ataurogeniaeforme (Schroeder) Lemm.
Treubaria triappendiculata Bernard
Ulothrix sp. Keutz.
Chryaophyta:
Diceras phascolua Fott
Dinobryon sp. Ehr.
11
302
-------
continued
D^_ bavaricum Imhof
Si calciformis Bach
D. divorfiens Imliof
D^ sertularia Ehr.
D^_ tabellariae (Letnm.) Pascher in
Pascher & Lemm.
Kephyrion ovam Pascher
Lagynion ampullaceum (Stokes) Pascher
Mallomonas acaroides Perty
M^ caudata Iwanoff
M. urnaformis Prescott
Ophiocytium capitatum Wolle
Synura u\'ella Ehr.
Bacillariophyta:
Achnanthes spp. Bory
Amphipleura sp. Kuetz.
Amphora sp. Ehr.
Asterionella formosa Hassall
Chaetoceras sp. Ehr.
Coeconels sp. Ehr.
Coscinodiscus rothii (Ehr.) Grun.
Cyclotella spp. Kuetz.
C^ glomerata Bachmanri
C_._ catenata Brun.
Cymatopleura elliptica (Breb.) W. Smith
C. solea (Breb.) W Smith
Cymbella spp. Agardh
Diatoma tenue var. elongatum (Lyngb.)
EL_ vulgare Bory
Diploneis sp. Ehr.
Epithemia zebra (Ehr.) Kuetz.
Fragilaria spp. Lyngbye
Ei brevistriata var. inflata (Pant) Hust.
F. capucina Desm.
F. crotonensis Kitton
DETROIT RIVER PHYTOI'LANKTON
(mean number of individuals/ml from replicate samples)
May 1974
*5 6 **7 19 20
7 13
218
92
145
48
358
22
55
273
343
F. pinnata Ehr.
Gomphonema spp. Agardh
Gyrosigma sp. Hassall
Melosira distans (Ehr.) Kuetz.
M. granulata (Ehr.) Ralfs
M^ islandica 0. Muell.
M._ italica (Ehr.) Kuetz.
M. varians C. A. Ag.
Navicula spp. Bory
N_^ pupula Kuetz.
N^ scutelloides W. Smith
?L_ tripunctata (0. F. Muell) Bory
Nitzschia spp. Hassall
N^ acicularis W. Smith
N_._ disslpata (Kuetz.) Grun.
N. frustulum Kuetz.
59
295
8
7
59
4
130
57
31
2
50
32
32
249
46
8
6
9
35
2
10
13
142
65
203
760
2
24
6
196
255
59
54
316
19
6
6
35
264
41
10
9
148
31
6
71
181
57
170
362
67
74
30
185
28
2
6
9
11
41
2
21
2
233
46
13
6
98
26
17
152
249
13
50
70
76
6
2
6
50
207
52
8
4
4
92
22
2
2
8
187
122
4
63
30
2
30
30
303
-------
continued
DETROIT RIVKR PIIYTOI'LANKTON
(mean number of individuals/ml from replicate samples)
May 1974
N^ Uncarts W. Smith
N^ palea (Kuetz.) W. Smith
NL_ sigmoiden (Ehr.) W. Smith
fL_ tryblionel la Hantzsch
Opephora ma r t y 1 Herlbaud
Plnnularla sp. Ehr.
Rhlzosolenig crlensls H. L. Smith
Rholcosphcnia curvata (Kuetz.) Grun.
Rhopalodia aihba (Ehr.) 0. Muell.
Stephanodl scus astraea (Ehr.) Grun.
Surlrella sp. Turpin
S. angustata Kuetz.
S_._ oval is Breb.
Synedra spp. Ehr.
§_._ actlnastroides Lemm.
S_^ ulna (Nitz.) Ehr.
Tabellaria f locculosa (Roth) Kuetz.
Pyrrhophyta:
Certatlum hirundlnella (0. F. Muell.)
Dujardin
Glenodinium penardiforme (Linde.)
Schiller
G_._ pulvisculus (Ehr.) Stein
Gymnodlnium fuscum (£hr.) Stein
Euglenophyta:
Colacium arbuscula Stein
Eufllena sp. Ehr.
£_._ convoluta Korshikov
Phaseus sp. Dujardin
Lepocinclis glabra Drezepolski
Trachelomonas sp . Ehr.
T_._ robusta Swirenko
T\_ volvocina Ehr.
Other Flagellates:
Chromullna sp. Cienkowski
Chroomonas sp. Hansgirg
Chrysococcus sp. Klebs
Cryptomonas sp . Ehr .
Nephroselmls olivacea Stein
Rhodomonas lacustris Pascher
Unidentified flagellate
Total Number of Species (S)
Mean Total Individuals/ml (N)
Richness (S/ VT)
Richness (S-l/lnN)
Shannon-Weaver Diversity (3)
*indicates single samples rather than replicates
**no samples from this station
*5
11
15
63
11
391
409
52
38
3132
0,68
4.60
2,76
6
4
19
6
92
2
6
223
266
**7
8
39
1416
1,04
5,24
2,64
19
4
15
8
20
32
17
7
21
4
35
10
22
9
4
115
56
4
304
351
131
2
26
369
447
13
11
10
100
15
386
354
142
23
2
349
408
47
3208
0,83
5,70
2,68
53
3032
0,96
5.49
2,97
38
2174
0.81
4.81
2.72
37
1899
0.85
4.77
2.54
304
-------
APPENDIX D-l
Modeling Theory
A general methodogy for modeling biological production in
aquatic systems has been described in an earlier report by
Canale (1970). This work emphasized the transient behavior
of relatively complex ecosystems in single homogeneous
zones. The ultimate goal of the project was to suggest how
the annual cylce of phytoplankton and nutrient behavior
might be simulated mathematically. The report described the
complex kinetics of the system as characterized by nonlinear
reaction terms and time-variable rate coefficients.
A relatively simpler class of problems is also of interest.
These problems are concerned with the steady state distri-
bution of species whose decay or production tendency can be
decribed b^j first order kinetic formulations . The following
list of water quality variables has been traditionally
analyzed using such assumptions:
1) Total dissolved solids or conductivity
2) Chlorides
3) Any Conservative Chemical Species
4) Total Coliform Bacteria
5) Dissolved Oxygen
6) Biological Oxygen Demand
7) Radioactive Isotopes
8) Nitrogen (Nitrification Process)
This report describes a general user-oriented program capable
of calculating the three-dimensional steady state distribu-
tion of the above water quality variables in aquatic systems.
Mathematical models which can be useful for informed manage-
ment of water resources must be based on the diverse
chemical, physical, and biological mechanisms active in the
system. These mechanisms are recognized by appropriate
terms in equations of continuity for each chemical or
305
-------
APPENDIX D-l
biological element of interest. Essentially, two distinct
types of mechanisms are recognized. First, are those pro-
cesses which alter the concentration of material within a
closed system due to departures of the state from a chemi-
cal equilibrium state. The study of the rate of changes
toward or away from this equilibrium state is called kine-
tics. The kinetic expressions may be dependent on species
concentration, temperature, light intensity, and pH.
A second process which can bring about changes in the con-
centration of species results from the mechanical action of
the fluid circulation and the subsequent dilution of con-
centration gradients. The bulk behavior of the circulation
is characterized by gross convective transfer, while the
random small-scale fluid movement is accounted for by
dispersion coefficients and transfer due to concentration
gradients alone. The above ideas are summarized by Equation
1'which is a descriptive statement of the continuity law
for any material. Equation 2'expresses this same law in
mathematical form for a general three-dimensional system.
A direct solution of Equation 2'for natural systems is not
possible. Therefore in practice it is necessary to use
approximations which are equivalent to considering a con-
tinuous body of water as a series of finite interconnected
segments as shown in Figure \.'. In this case, the steady-
state continuity equation with first order kinetics reduces
to the following:
dC
Vlv rt-_. r- f C\ / f* _1_ n /"* \ I Tn f f^ /"i \ i T T "\7 (~* l.T.T
=y= £ { _M . (a . L, -r 6, . U . )T~EM . 1 G . ~Lt ) } - V, K, U. ~rW,
If if ~\ l^T If l/"~l "I U* TT If IF if K U*
K-J*. i K-J !*"J K- K-J J K.J J K. is. IX K. tv.
where:
C, = concentration of water quality variable in segment
* k, (mg/1)
V, = volume of segment k, (eft)
306
-------
APPENDIX D-l
Q, . = net flow from segment k to segment j (positive
-' ward) (cubic feet per second)
a, . = finite difference weight given by ratio of flow
•* to dispersion, 0
-------
APPENDIX D-l
akk " J^kj+V+W-Qkk kk+Ekk (50
and
Wk - Wk+CB <6'>
where Cg is the boundary concentration of the variable C and
must be known.
If Qkk is negative then,
a, , = E (Q. . o. .+E. :)+V. K, +Q, , B, , +E, ." ,-,^
kk . vxkj kj kj k k xkk kk kk (7 )
and
Wk =
The n equations would then be given by:
3-T i «i "•" 3-1 oGr> °T~ ~<~3-i C =
11 1 12 2 In n
a ^CT + a 0C0 + +a C - W
nl 1 n2 2 nn n n
where the boundary conditions are incorporated into W, 's.
There are a number of numerical procedures for solving such
a set of n simultaneous equations in n unknowns. The SSMP
uses an MTS subroutine called SLE1 which uses the Gaussian
elimination technique.
Equation 3 is suitable for single dependent variables that
are not forced by outputs from other quality systems. Examples
of such a type are chloride, coliform, and BOD. Other water
quality variables such as dissolved oxygen are coupled to
other systems. The utilization of oxygen depends on the dis-
tribution of BOD, and therefore it is necessary to first
308
-------
APPENDIX D-l
obtain the distribution of BOD and then use these results
in a continuity equation for D.O,
Thus, the mass balance equation for D,0, is:
(10-)
V, dCk =0=E { -Q . (0, . C, +B, . C . )+K '. (C . -C. ) +V, K , (C . -C, ) -V, K ,, L. + W.
k~3tf j kj kJ k kJ J kJ J k k akv sk k' k dkTc- k
where C ^ is the saturation value of D.O. , K , is the reaera-
tion coefficient in segment k, K,, is the deoxygenation
coefficient, L is the biochemical oxygen demand and +W is
now interpreted as sources and sinks of D.O. such as ben thai
demands and photosynthetic production or respiration. With
L, known from previous calculations, the final solution of
Equation 10" is similar to solution of Equation 3".
As spatial approximations to derivatives have been used in
Equations 3" and 10", some error are introduced into the
analysis. One of the errors is "psuedo or numerical disper-
sion." It appears due to the assumption of completely mixed
finite volumes. Numerical dispersion is defined by Equation
11-.
When akj = 1/2, E is zero.
On the other hand, it can be shown that for a positive solu-
tion the terms off the main diagonal in the left-hand side of
Equation 9 should be non-positive. This condition is
satisfied if
Writing Equation 12 in another way, it is seen that L, . must
^J
be chosen such that,
r
Lkj<
309
-------
APPENDIX D-l
For the case of zero numerical dispersion a, . = 1/2 and
2E, .A, .
If a, . is set equal to 1/2 and L, . is chosen in such a way
KJ KJ
as to satisfy Equation 14', then it may be necessary to
handle many segments. However, if a, . differs very much
KJ
from 1/2, then numerical dispersion would be high. Further,
making a, . = 1/2 does not imply the best solution for the
KJ
case of unequal-sized segments.
In SSMP a, . is first set equal to
KJ
L.
akj _J
T 4- T
k + Lj
In other words, the segment whose center is nearer to the
interface would have more weightage in determining the con-
centration at the interface in Equation 3", The value of
a, . is then checked against Equation 12', If it is not
KJ
satisfied, then
£
a, . is made equal to 1 - _k1
~ ~
*• ^kj
Choosing proper spatial grids for approximations to the
differential equations is still very much an art. The more
numerous the segments in a model, the more accurate the
resulting solution. However, in such cases the computer
costs may be very high, so a compromise is necessary. Con-
siderations of computer size, nature of problems, degree of
accuracy, simplicity of the resulting finite difference
equations, and availability of verifying field data all in-
310
-------
APPENDIX D-l
fluence the choice. For additional details concerning these
questions the reader is referred to Thomann (1971),
311
-------
APPENDIX D-2
Industrial Outfalls - Detroit River
Industry Model Segment
U.S. Rubber Co. 5
Anaconda - American Brass 9
Allied Chemical (W-100, W107) 11
Great Lakes Steel (W47-53, 56, 101) 15
Allied Chemical (¥113,114) 15
Great Lakes Steel Hot Strip (W43) 19
Great Lakes Steel Rolling Mill (W32-Hl,70) 19
Wyandotte Chemical - North Works 31
Wyandotte Chemical - South Works 37
Pennwalt Chemicals 37
Firestone Tire and Rubber 37
McLouth Steel (W8-11) 49
Mobil Oil Company 56
Chrysler Corp. (W2, 2a, 3, 6) 60
Monsanto (W4, 5, 139) 60
McLouth Steel (Wl) 60
*OUTFALLS DESGINATED W - are according to
Michigan Water Resources System
312
-------
APPENDIX D-3
Flow Rates - Detroit River Model
Year Flow (cfs)
1963 175,000
1968 180,000
1969 180,000
1971 200,000
1972 200,000
1973 200,000
Note: These are the average flow rates
used to obtain the results for
the Detroit Model.
313
-------
APPENDIX D-4
Chloride Loads - Detroit River
1963 1968 1969 1972 1973
Allied Chemical 45
Great Lakes Steel
Main Plant 18
Detroit Waste
Treatment Plant 562 1050* 1100* 1180* 1280*
Rouge River 310 270 245 120 120
Wyandotte-North 1300 1500 1400 30 30
Wyandotte-South 65 560 370 100 60
Pennwalt 510 30 20 230 200
Wayne Co. Treat-
ment Plant 35 50* 60* 90* 95*
All loads as thousands (1000) of #/day
*estimated using increase flow rates and concentration measured
in 1963
314
-------
APPENDIX D-4
Chloride Concentrations (U. S. Public Health Loadings)
Detroit River - 1963
Mile Point
20.6
17.4 W
14.6 W
12.0 W
8.7 W
3.9
3.9
-------
Mile Point
20.6
17.4 W
14.6 W
12.0 W
8.7 W
3.9
APPENDIX D-4
Chloride Concentrations (estimated loadings)
Detroit River - 1963
Model Segment
Numbers
11-13
19-21
31-33
37-39
56-59
67-70
3.9 (cont.) 71-73
AMC
MFC
AMC
MFC
AMC
MPC
AMC
MPC
AMC
MPC
AMC
MPC
AMC
MPC
8
8
19
16
29
29
48
47
50
44
40+
44
12
9
8
8
10
8
14
13
25
23
28
24
40
39
12
_
8
8
10
8
10
10
18
13
20
14
22
23
35
-
13
16
All values as mg/1
AMC - average measured concentration based on stations located
within corresponding model segment
MPC - model predicted concentration
316
-------
APPENDIX D-4
Chloride Concentrations
DETROIT RIVER - 1968
Model Segment
Numbers
Mile Point
20.6
17.4 W
14.6 W
12.0 W
8.7 W
3.9
3.9 (cont.)
All values as mg/1
AMC - average measured concentration based on stations located
within corresponding model segment
MPC - model predicted concentration
9-11
19-21
31-33
37-39
56-59 *
67-70
71-73
AMC
MPC
AMC
MPC
AMC
MPC
AMC
MPC
AMC
MPC
AMC
MPC
AMC
MPC
9
9
14
14
30
29
45
44
42
40
45+
40
10
10
9
9
11
9
13
12.4
18
22
22
23
41
35
20
-
9
9
10
9
10
10
13
13
14 '
14
22
22
40+
-
14
15
317
-------
APPENDIX D-4
Chloride Concentrations
DETROIT RIVER - 1969
Mile Point
20.6
17.4 W
14.6 W
12.0 W
8.7 W
3.9
Model Segment
Numbers
9-11
19-21
31-33
37-39
56-59
67-70
3.9 (cont.) 71-73
AMC
MPC
AMC
MPC
AMC
MPC
AMC
MPC
AMC
MPC
AMC
MPC
AMC
MPC
8
8
13
13
26
27
35
37
35
34
40+
34
9
9
8
8
8.5
8
11
11
15
21
20
21
34
31
16
-
8
8
8.5
8
10
9
12
12
12
13
19 12
20 14
35+
-
All values as mg/1
AMC - average measured concentration based on stations located
within corresponding model segment
MPC - model predicted concentration
318
-------
APPENDIX D-4
Chloride Concentrations
DETROIT RIVER - 1972
Model Segment
Numbers
Mile Point
20.6
17.4 W
14.6 W
12.0 W
8.7 W
3.9
3.9 (cont.)
All values as mg/1
AMC - average measured concentration based on stations located
within corresponding model segment
MPC - model predicted concentration
9-11
15-17
31-33
37-39
56-59
67-70
71-73
AMC
MPC
AMC
MPC
AMC
MPC
AMC
MPC
AMC
MPC
AMC
MPC
AMC
MPC
8
8
13
13
13
13
20
21
20
20
25+
19
9
9
8
8
8
8
11
11
12
12
13
12
22
18
17
16
8
8
8
8
9
9
10
11
11
11
15 10
13 11
30+
26
319
-------
APPENDIX D-4
Chloride Concentrations
DETROIT RIVER - 1973
Mile Point
20.6
17.4 W
14.6 W
12.0 W
8.7 W
3.9
Model Segment
Numbers
9-11
15-17
31-33
37-39
56-59
67-70
3.9 (cont.) 71-73
AMC
MPC
AMC
MPC
AMC
MPC
AMC
MPC
AMC
MPC
AMC
MPC
AMC
MPC
9
9
14
14
15
14
20
21
16
20
25
20
10
10
9
9
9
9
11
12
13
13
13
14
18
18
18
17
9
9
9
9
10
10
10
12
12
12
13 12
14 12
30+
27
All values as mg/1
AMC - average measured concentration based on stations located
within corresponding model segment
MPC - model predicted concentration
320
-------
APPENDIX D-5
Phenol Loads
Detroit River
Allied Chemical
Great Lakes Steel
Main Plant
Detroit Waste
Treatment Plant
Rouge River
Wyandotte-North
Pennwalt
Wayne Co. Treat-
ment Plant
Mclouth Steel
Mobil Oil
1963
2
370
1260
400
34
300
12
20
350
1968
74
150
1390*
60
-
85
20
-
240
1969
62
130
1400*
70
-
22
20
-
260
1972
65
80
1600
20
-
16
25
-
3
1973
50
110
1750
20
-
25
-
3
All loads in #/day
^estimated values
321
-------
APPENDIX D-5
Phenol Concentrations
DETROIT RIVER - 1963
Mile Point
20.6
17.4 W
14.6 W
12.0 W
8.7 W
3.9
Model Segment
Numbers
9-11
15-17
31-33
37-39
56-59
67-70
3.9 (cont.) 71-73
AMC
MPC
AMC
MPC
AMC
MPC
AMC
MPC
AMC
MPC
AMC
MPC
AMC
MPC
2
2
11
10
8
8
16
17
30
25
6
8
2
3
2
2
3
2
6
5
16
7
12
8
5
6
1
3
2
2
2
2
3
3
10
5
8
5
4
4
1
2
4
4
All values as mg/1
AMC - average measured concentration based on stations located
within corresponding model segment
MPC - model predicted concentration
322
-------
APPENDIX D-5
Phenol Concentrations
DETROIT RIVER - 1968
Mile Point
20.6
17.4 W
14.6 W
12.0 W
8.7 W
3.9
Model Segment
Numbers
9-11
19-21
31-33
37-39
56-59
67-70
3.9 (cont.) 71-73
AMC
MFC
AMC .
MPC
AMC
MPC
AMC
MPC
AMC
MPC
AMC
MPC
AMC
MPC
2
2
9
8
5
5
6
6
11
12
6
6
2
2
2
2
5
2
3
3
5
4
5
4
5
5
2
2
2
2
4
2
2
2
4
3
4
3
3 2
3 3
2
2
All values as mg/1
AMC - average measured concentration based on stations located
within corresponding model segment
MPC - model predicted concentration
323
-------
APPENDIX D-5
Phenol Concentrations
DETROIT RIVER - 1969
Mile Point
20.6
17.4 W
14.6 W
12.0 W
8.7 W
3.9
3.9 (cont.)
Model Segment
Numbers
9-11
19-21
31-33
37-39
56-59
67-70
71-73
AMC
MPC
AMC
MPC
AMC
MPC
AMC
MPC
AMC
MPC
AMC
MPC
AMC
MPC
2
2
9
9
7
6
6
7
13
13
8
8
2
3
2
2
3
2
4
4
5
5
5
5
7
7
2
2
2
2
3
2
2
2
4
4
4
4
4 3
4 4
2
2
All values as mg/1
AMC - average measured concentration based on stations located
within corresponding model segment
MPC - model predicted concentration
324
-------
APPENDIX D-5
Phenol Concentrations
DETROIT RIVER - 1972
Mile Point
20.6
17.4 W
14.6 W
12.0 W
8.7 W
3.9
Model Segment
Numbers
9-11
15-17
31-33
37-39
56-59
67-70
3.9 (cont.) 71-73
AMC
MPC
AMC
MPC
AMC
MPC
AMC
MPC
AMC
MPC
AMC
MPC
AMC
MPC
1.5
1.5
7
8
5
5
6
6
8
7
6
5
1
2
1.5
1.5
2
2
3
3
5
4
5
4
4
4
1
2
1.5
1.5
1
1
2
2
4
3
4
3
2 1
3 3
1
2
All values as mg/1
AMC - average measured concentration based on stations located
within corresponding model segment
MPC - model predicted concentration
325
-------
APPENDIX D-5
Phenol Concentrations
DETROIT RIVER - 1973
Model Segment
Numbers
Mile Point
20.6
17.4 W
14.6 W
12.0 W
8.7 W
3.9
3.9 (cont.)
All values as mg/1
AMC - average measured concentration based on stations located
within corresponding model segment
MFC - model predicted concentration
9-11
15-17
31-33
37-39
56-58
67-70
71-73
AMC
MPC
AMC
MPC
AMC
MPC
AMC
MPC
AMC
MPC
AMC
MPC
AMC
MPC
i
1
7
8
5
5
5
6
5
6
5
4
1
2
1
1
1
1
3
3
4
4
4
4
3
3
1
1
1
1
1
1
1
2
4
3
3
3
2 2
3 2
1
1
326
-------
Great Lakes Steel
(Zug Island)
Detroit Waste Treatment
Plant
Rouge River
Great Lakes Steel
Rolling + Hot Strip
Wayne County
Firestone
McLouth Steel
APPENDIX D_6
Iron Loads
Detroit River
1968
1969
8
1972
1973
67*
11
220
.35*
.25
5
75*
7
170
.35*
.25
15*
180
6
4
.5
.2
5
180
6
4
.
.
5
5
2
All loadings in thousands (1000) of #/day
*estimated values
327
-------
Mile Point
20.6
17.4 W
14.6 W
12.0 W
8.7 W
3.9
APPENDIX D-6
Total Iron Concentrations
Detroit River - 1968
Model Segment
Numbers
9-11
19-21
31-33
37-39
56-58
67-70
3.9 (cont.)
71-73
AMC
MFC
AMC
MFC
AMC
MPC
AMC
AMC
MPC
AMC
MPC
AMC
MPC
.35
.35
2.0
1.6
.87
.96
1.0
.97
1.1
1.1
1.2
1.1
.45
.46
.35
.35
.40
.37
.56
.66
.78
.83
1.0
.83
1.0
1.0
.50
.42
.35
.35
.40
.35
.45
.46
.55
.67
.80
.70
.80 .60
.81 .71
.60
.40
All values as mg/1
AMC - average measured concentration based on stations located within
corresponding model segment
MPC - model predicted concentration
328
-------
APPENDIX D-6
Total Iron Concentrations
Detroit River - 1969
Mile Point
20.6
17.4
14.6 W
12.0 W
8.7 W
3.9
Model Segment
Numbers
9-11
19-21
31-33
37-39
56-58
67-70
3.9 (cont.)
71-73
AMC
MPC
AMC
MPC
AMC
MPC
AMC
MPC
AMC
MPC
AMC
MPC
AMC
MPC
.35
.35
1.5
1.4
.87
.85
.85
.84
1.4
1.3
1.0
1.3
.50
.43
.35
.35
.40
.37
.56
.56
.70
.72
1.2
.74
.80
1.1
.40
.40
.35
.35
.40
.35
.45
.45
.48
.58
.72
.60
.70
.74
.60
.39
.60
.61
All values as mg/1
AMC - average measured concentration based on stations located within
corresponding model segment
MPC - model predicted concentration
329
-------
Mile Point
20.6
19.0
14.6 W
12.0 W
8.7 W
3.9
APPENDIX D-6
Total Iron Concentrations
Detroit River - 1972
Model Segment
Numbers
9-11
15-17
31-33
37-39
56-58
67-70
3.9 (cont.)
71-73
AMC
MFC
AMC
MPC
AMC
MPC
AMC
MPC
AMC
MPC
AMC
MPC
AMC
MPC
.40
.40
1.0
1.0
.66
.65
.76
.67
.86
.76
1.2
.76
.45
.40
.40
.40
.40
.40
.45
.47
.73
.57
.80
.60
1.1
.71
.45
.38
.40
.40
.40
.40
.43
.40
.62
.48
.67
.49
,80
,57
.50
.38
.60
.50
All values as mg/1
AMC - average measured concentration based on stations located within
corresponding model segment
MPC - model predicted concentration
330
-------
Mile Point
20.6
19.0
14.6 W
12.0 W
8.7 W
3.9
3.9 (cont.)
APPENDIX D-6
Total Iron Concentrations
Detroit River - 1973
Model Segment
Numbers
9-11
15-17
31-33
37-39
56-58
67-70
71-73
AMC
MPC
AMC
MPC
AMC
MPC
AMC
MPC
AMC
MPC
AMC
MPC
AMC
MPC
.35
.35
1.0
1.0
.66
.65
.66
.66
.75
.75
.80
.75
.40
.40
.35
.35
.25
.36
.45
.47
.55
.57
.50
.57
.80
.70
.30
.38
.35
.35
.25
.35
.40
.40
.50
.48
.48
.48
.60 .50
.56 .50
.50
.38
All values as mg/1
AMC - average measured concentration based on stations located withii
corresponding model segment
MPC - model predicted concentration
331
-------
APPENDIX D-7
AMMONIA LOADING
DETROIT RIVER
1972 1973
Great Lakes Steel Main Plant 18 20
Detroit Waste Treatment Plant 51* 59*
Rouge River 1 1
Wyandotte - North 3 3
Pennwalt 0.5 0.5
Wayne County 3* 4*
McLouth Steel 1 1
All loadings in thousand's (1000) of #/day
^estimated values
332
-------
Mile Point
APPENDIX D-7
Ammonia Nitrogen Concentrations
Detroit River - 1972
Model Segment
Numbers
20.6
19.0
14.6 W
12.0 W
8.7 W
3.9
3.9 (cont.)
9-11
15-17
31-33
37-39
56-58
67-70
71-73
AMC
MFC
AMC
MPC
AMC
MPC
AMC
MPC
AMC
MPC
AMC
MPC
AMC
MPC
.04
.04
.29
.29
.40
.30
.35
.36
.35
.37
.46
.36
.10
.07
.04
.04
.06
.05
.15
.17
.15
.24
.20
.24
.35
.33
.05
.06
.04
.04
.06
.04
.05
.07
.10
.17
.15
.18
.20
.23
.05
.05
.13
.19
All values as mg/1
AMC - average measured concentration
corresponding model segment
MPC - model predicted concentration
- based on stations located within
333
-------
APPENDIX D-7
Ammonia Nitrogen Concentrations
Detroit River - 1973
Mile Point Model Segment
Numbers
20.6 9-11
19.0 15-17
14.6 W 31-33
12.0 W 37-39
8.7 W 56-58
3.9 67-70
3.9 (cont.) 71-73
All values as mg/1
AMC - average measured concentration based on stations located within
corresponding model segment
MFC - model predicted concentration
AMC
MPC
AMC
MPC
AMC
MPC
AMC
MPC
AMC
MPC
AMC
MPC
AMC
MPC
.03
.03
.33
.32
.34
.33
.40
.41
.38
,41
.40
.40
.02
.08
.03
.03
,03
.03
.08
.19
.20
.27
.20
,27
.40
.37
.03
.06
.03
.03
.03
.03
.05
.08
.10
.19
.13
.20
.15 .04
,26 .21
.04
.05
334
-------
APPENDIX D-8
Total Phosphorous Loadings
Detroit River
1971 1972 1973
Detroit Waste Treatment
Plant 27,000 37,000 48,000
Wayne County 3,000 3,000 3,000
All values as #/day
335
-------
APPENDIX D_8
Total Phosphorous Concentrations
DETROIT RIVER - 1971
Mile Point Model Segment
Numbers
20.6 9-11
19. Q •: 15-17
!i
14.6 W 31-33
12.0 W 37-39
8.7 W 56-58
3.9 67-70
3.9 (cont.) 71-73
All values as mg/1
AMC - average measured concentration based on stations located
within corresponding model segment
MPC - model predicted concentration
AMC
MPC
AMC
MPC '
AMC
MPC
AMC
MPC
AMC
MPC
AMC
MPC
AMC
MPC
.03
.03
.10
.14
.10
.13
.14
.19
.19
.13
.22
.18
.04
.06
.03
.03
.02
.03
.08
.09
.11
.12
.15
.12
.20
.17
.03
.05
.03
.03
.02
.03
.05
.06
.07
.09
.12
.10
.15
.12
. .03
.05
.09
.10
336
-------
APPENDIX D-8
Total Phosphorous Concentrations
DETROIT RIVER - 1972
Model Segment
Numbers
Mile Point
20.6
19.0
14.6 W
12.0 W
8.7 W
3.9
3.9 (cont.)
All values as mg/1
AMC - average measured concentration based on stations located
within corresponding model segment
MPC - model predicted concentration
9-11
15-17
31-33
37-39
56-58
67-70
71-73
AMC
MPC
AMC
MPC
AMC
MPC
AMC
MPC
AMC
MPC
AMC
MPC
AMC
MPC
.04
.04
.09
.17
.10
.17
.12
.23
.14
.21
.20+
.21
.07
.06
.04
.04
.03
.04
.07
.11
.07
.14
.12
.15
.20
.20
.05
.05
.04
.04
.03
.04
.03
.06
.05
.11
• .08
.11
.12
.14
.04
.05
337
-------
APPENDIX D_8
Total Phosphorous Concentrations
DETROIT RIVER - 1973
Mile Point Model Segment
Numbers
20.6 9-11
19.0 15-17
14.6 W 31-33
12.0 W 37-39
8.7 W 56-58
3.9 67-70
3.9 (cont.) 71-73
AMC
MPC
AMC
MPC
AMC
MPC
AMC
MPC
AMC
MPC
AMC
MPC
AMC
MPC
.05
.05
.13
.22
.13
.21
.13
.26
.18
.25
.17+
.25
.06
.08
.05
.05
.04
.05
.07
.14
.10
.18
.10
.19
.16
.23
.04
.07
.05
.05
.04
.05
.06
.08
.06
.14
.07
.15
.11 .07
.18 .15
.04
.06
All values as mg/1
AMC - average measured concentration based on stations located
within corresponding model segment
MPC - model predicted concentration
338
-------
APPENDIX D-9
ASSUMED LOADINGS FOR WATER QUALITY PROJECTIONS
OJ
Source
Chloride
1 OOP// /day
1460a
120
1300
550
509*
95
Phenol
///day
37
161
93
20
3.8*
25
26
20
0.5
Ammonia Nitrogen
///day
125
9034*
8340b
33000^
67000
1000
3486*
352
65
4000
834
Phosphorus
///day
4750
400
875*
3000
33*
16.7*
520
Iron
///day
2250***
330006
6000
3700***
1300***
500
50*
3050***
Allied Chemical Semet Solvay Division
Great Lakes Steel - Blast Furnace Div.
Detroit Wastewater Treatment Plant
Rouge River**
Great Lakes Steel - Hot Strip Mill
Great Lakes Steel - Rolling Mill
Wyandotte Chemical North Works
Wyandotte Chemical South Works
Pennwalt Chemical
Wayne County Waste Treatment Plant**
Firestone Tire and Rubber
McLouth Steel - Trenton Plant
Mobil Oil Company
Chrysler Corporation
Monsanto Company
McLouth Steel - Gibraltar Plant
* max. allowable loads, average value not available
** estimated values based on 1972-1973 values
*** permit loading given in mg/1, assumed load based on total plant flow est. and 3 mg/1 average
27
a based on 1 BCD and 175 mg/1 ave.
b,c,d based on 1 BCD and 1,4 and 8 mg/1 respectively
e based on 1 BCD and 4 mg/1 average
-------
APPENDIX D-9
Water Quality Projections - Chloride
Detroit River - 1977
CO
-O
o
15
10
bO
6 5
J_J L
100 200 300
500
800 1000
Feet from U.S. shore
Dt. 19.0
1500
2000
50
40
30
20
oo
6 10
TW"
500
1000 1200
Feet from U.S. shore
Dt, 12,OW
1500
-------
APPENDIX D-9
Water Quality Projections - Chloride
Detroit River - 1977
iH
0
t-l
oo
e
50
40
30
20
10
0
— Dt, 8.7W
—
Ill II
10&
500 700 1000 1200
Feet from U.S. shore
rH
U
i-l
00
e
50
40
30
20
10
0
Dt. 3,9
1
%
II II
1,000 5,000 10,000 15,000
Feet from U.S. shore
-------
APPENDIX D-9
Water Quality Projectioas >- Phenol
Detroit River - 1977
Dt, 19.0
o
a
-------
APPENDIX D-9
Water Quality Projections - Phenol
Detroit River - 1977
u>
*-
UJ
o
I 3
OC
3.
1
0
Dt. 8.7W
I I I
I
100 200 300
500
1,000
Feet from U.S.
1,200
shore
O
c
a)
.c
2
1
0
Dt. 3.9
J
1,000
5,000
J
10,000
15,000
-------
APPENDIX l)-9
Water Duality Projection - Ammonia Nitrogen
Detroit River - 1977
.50
.40
.30
.20
.10
0
_
Dt. 19.0
~~ Detroit WWTP - 8 mg/1 ave.
—
lit 'i
| | | | ( , __
1UU 200 300 500 1000 1500
Feet from U, S, shore
.50 __
1,000
5,000
10,000
Feet from U.S. shore
Dt, 3.9
a
on
§ .30
rH
If .20
.10
0
1
II 1 1
15,000
-------
APPENDIX D-9
Water Quality- Projection - Ammonia Nitrogen
Detroit River - 1977
.30
.25
.20
S5
5zT -15
•H
"« .10
0
.05
0
CJ
t
— Dt, 19,0
Detroit WWTP - 4.0 mg/1 avg
—
—
1
—
1 1 1 1 I 1
100 200 300 500 1000 1500
m Feet from U.S. shore
.30
.25
.20
2
sf *15
l-i
~M .10
0
.05
0
'
1
Dt. 3.9
-,
-
i —
—
II 1 1
1,000
5,000 10,000
Feet from U.S. shore
15,000
-------
APPENDIX D-9
Water Quality Projection - Ammonia Nitrogen
Detroit River - 1977
CO
.£>
,15
.10
^ -05
^ °
~ob
0
Dt, 19.. 0
__ Detroit WWTP - 1,0 mg/1 ave, d
— •
till 1 1
100 200 300 500 1000 1500
Feet from U.S. shore
K
00
a
.25
.20
.15
.10
.05
0
Dt. 3.9
1,000
5,000 10,000
Feet from U.S. shore
15,000
-------
APPENDIX D-9
Water Quality Projections - Iron
' Detroit River - 1977
d
0
M
"S
.7
.6
.5
.4
.3
.2
.1
0
—
__ Dt. 19.0
—
i
—
—
till 1 1
100 200 300 500
Feet from U.S. shore
1000
1500
CO
.fs
a
o
M
H
r-i
00
&
.6
C
. 3
.4
.3
.2
,1
0
—
1
__ Dt. 12. OW
—
•
—
I 1 1 1 II
100 200 300 500
Feet from U.S. shr>r*>
1000
1200
-------
.6
.5
° .«
'APPENDIX D-9
Water Quality Projections - Iron
Detroit River - 1977
Dt. 8.7W
.2
.1
n
—
—
1
100
CO
1 1 1
200 300 500
Feet from U.S. shore
1
1000
1
1200
A
.6
.5
g .4
oo
e
.3
.2
.1
0
1,000 5,000
Feet from U.S. shore
10,000
\ ''"1
Dt. 3.9
15,000
------- |