United States
Environmental Protection
Agency
Environmental Research
Laboratory
Duluth MN 558O4
EPA GOO 3-80-059
Julv 1980
Research and Development
Limnology of
Michigan's Nearshore
Waters of Lakes
Superior and Huron
EP 600/3
80-059
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RESEARCH REPORTING SERIES
Research reports of the Office of Research and Development, U S Environmental
Protection Agency, have been grouped into nine series These nine broad cate-
gories were established to facilitate further development and application of en-
vironmental technology Elimination of traditional grouping was consciously
planned to foster technology transfer and a maximum interface in related fields
The nine series are
1 Environmental Health Effects Research
2 Environmental Protection Technology
3 Ecological Research
4 Environmental Monitoring
5 Socioeconomic Environmental Studies
6 Scientific and Technical Assessment Reports (STAR)
7 Interagency Energy-Environment Research and Development
8 "Special" Reports
9 Miscellaneous Reports
This report has been assigned to the ECOLOGICAL RESEARCH series This series
describes research on the effects of pollution on humans, plant and animal spe-
cies, and materials Problems are assessed for their long- and short-term influ-
ences Investigations include formation, transport, and pathway studies to deter-
mine the fate of pollutants and their effects This work provides the technical basis
for setting standards to minimize undesirable changes in living organisms in the
aquatic, terrestrial, and atmospheric environments
This document is available to the public through the National Technical Informa-
tion Service, Springfield, Virginia 22161
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EPA-600/3-80-059
July 1980
LIMNOLOGY OF MICHIGAN'S NEARSHORE WATERS
OF LAKES SUPERIOR AND HURON
by
R. E. Basch
C. H. Pecor
R. C. Waybrant
D. E. Kenaga
Water Quality Division
Environmental Protection Bureau
Michigan Department of Natural Resources
Lansing, Michigan 48909
Project R005146-01
Project Officer
Nelson A. Thomas
Large Lakes Branch
Large Lakes Research Station
Grosse He, Michigan 48138
GREAT LAKES NATIONAL PROGRAM OFFICE
REGION V
U.S. ENVIRONMENTAL PROTECTION AGENCY
CHICAGO, ILLINOIS 60605
and
ENVIRONMENTAL RESEARCH LABORATORY
OFFICE OF RESEARCH AND DEVELOPMENT
U.S. ENVIRONMENTAL PROTECTION AGENCY
DULUTH, MINNESOTA 55804
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DISCLAIMER
This report has been reviewed by the Environmental Research Laboratory,
Large Lakes Research Station, Grosse lie, Michigan, U. S. Environmental
Protection Agency, and approved for publication. Approval does not signify
that the contents necessarily reflect the view and policies of the U. S.
Environmental Protection Agency, nor does mention of trade names or
commercial products constitute endorsement or recommendation for use.
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FOREWORD
The U. S. Environmental Protection Agency has a great concern for the
nearshore waters of the Great Lakes because most of the pollutants that enter
the Great Lakes pass through the nearshore zone. The processes that disperse
the pollutants are very complex, therefore, a detailed description of the
nearshore water quality is necessary. The nearshore environment is extremely
important to the Great Lakes biota. Degradation of the nearshore environment
is often the only pollutional effect that the general public perceives.
This report describes the water quality and biota of the nearshore
environment along the Michigan shoreline of Lakes Superior and Huron. The
authors of this report have attempted to delineate the condition of these lakes
and indicate areas that have been degraded. It is hoped that the report will
provide material to help design management programs for the enhancement,
improvement, and protection of the nearshore waters of the Great Lakes.
Norbert A. Jaworski, Ph.D.
Director
Environmental Research Laboratory
Duluth, Minnesota
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ABSTRACT
Limnological assessments, including water and sediment chemistry, bacte-
rial densities, zoo- and phyto-plankton and benthic macroinvertebrate commu-
nity structure, and fish contaminants, were performed at 24 locations in
Michigan's nearshore waters of Lakes Superior and Huron in 1974 and 1975.
The nearshore waters of Lake Superior were all oligotrophic with generally
high water quality as reflected by consistently high dissolved oxygen, reac-
tive silica and nitrate, and low phosphorus, total dissolved solids (TDS),
chlorophyll a_ and bacterial densities. Heavy metals and organic contaminants
were low in water and sediments, except at Ontonagon, Upper Portage Entry and
Muni sing. Phytoplankton and zooplankton communities were generally diverse
and low in numbers. Plankton densities reflected seasonal changes throughout
the nearshore waters and indicated nutrient enrichment at Carp River and
Munising. Benthic macroinvertebrate communities indicated localized enriched
areas at Ontonagon, Presque Isle, Marquette Harbor and Munising, with less
extensive effects found at Lower Portage Entry and Carp River. A statistical
trend analysis based on 1974 through 1976 (6LECS) data indicated significant
increases in the concentrations of dieldrin, DDT and mercury in Lake Superior
lake trout. These same data show no statistical changes in PCB concentrations
from 1974 to 1976.
The nearshore waters of Lake Huron were oligotrophic in the northern
section and became mesotrophic at the southern end of the lake. Eutrophic
conditions were found at Alpena harbor and Saginaw Bay. Concentrations of
chlorides, sulfates, total dissolved solids, phosphorus and chlorophyll a^
were higher in the northern nearshore waters of Lake Huron than in Lake
Superior's nearshore waters. These constituents increased from north to south
while silica levels decreased. Areas of severe water quality degradation oc-
cured at Alpena and Saginaw Bay as a result of large inputs of phosphorus and
TDS. Alpena was the only location where bacterial densities were consistently
elevated. Areas to the south of Saginaw Bay were affected by the nutrient-
rich Bay waters moving south to the lower Great Lakes. Organic and metals
contaminants were generally low in water and sediments except for sediments at
Cheboygan, Alpena, and particularly Harbor Beach. Sediments at the mouth of
the Saginaw River were grossly polluted, but in the outer Bay sediments were
unpolluted. Localized blue-green and cryptomonad algal blooms were found in
the southern and very nearshore portions of the lake and in Thunder Bay. The
low percentage of calanoid copepods and the abundance of rotifers and cladocerans
indicated enriched conditions in the southern portions of the lake. Benthic
macroinvertebrate communities indicated enriched conditions at Cheboygan, Alpena,
Tawas and Harbor Beach. Metals and organic contaminants in fish were generally
low or below detection. A statistical analysis based on 1975 through 1978
GLECS data suggested a peak in 1976 for dieldrin, DDT and mercury in Lake Huron
lake trout. The same data showed no statistical changes in PCB concentrations
-iv-
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from 1975 through 1978. The GLECS data revealed no changes in dieldrin,
DDT or mercury concentrations in whitefish between 1974 and 1975, but PCB
concentrations were significantly greater in 1975 whitefish than 1974. The
GLECS data for walleye showed significantly higher DDT and mercury concen-
trations in 1978 than 1974. No walleye data were available for the
intervening years.
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TABLE OF CONTENTS
Page
Abstract ii1
List of Figures vii
List of Tables viii
List of Tables Appended x
Acknowledgments xii
Section
I Conclusions 1
II Recommendations 8
III Introduction 10
IV Methods 12
Sampling Design 12
Physical and Chemical Water Constituents 16
Radioactivity in Water 24
Sediment Chemistry 24
Bacteria 24
Ph.ytoplankton 25
Zooplankton 25
Benthic Macroinvertebrates 25
Organic Chemicals and Heavy Metals in Fish 26
Data Handling 26
25
V Lake Superior 28
Introduction 28
Physical and General Water Chemistry 28
Nutrients and Chlorophyll a_ 31
Heavy Metals in Water 33
Organic Chemicals in Water 35
Radioactivity in Water 35
Sediment Chemistry 35
Bacteria 37
Phytoplankton 37
Zooplankton 42
Benthic Macroinvertebrates 43
Contaminants in Fish 49
Summary 51
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Page
VI Lake Huron 63
Introduction 63
Physical and General Water Chemistry 65
Nutrients and Chlorophyll a^ 66
Heavy Metals in Water 68
Organic Chemicals in Hater 70
Radioactivity in Water 70
Sediment Chemistry 70
Bacteria 71
Phytoplankton 74
Zooplankton 78
Benthic Macroinvertebrates 79
Contaminants in Fish 86
Summary 94
VII Literature Cited 96
VIII Appendices 103
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LIST OF FIGURES
Number Page
1 Sampling stations in the nearshore waters, Lakes Superior 13
and Huron, 1974 and 1975.
2 Sampling array for locations sampled in nearshore waters, 15
Lakes Superior and Huron, 1974 and 1975.
3 Typical summer surface currents in Lake Superior. 29
4 Nearshore phytoplankton standing crop, Lake Superior, 1974. 41
5 Percent composition and density of major benthic macro- 46
invertebrate taxonomic groups in nearshore Lake Superior,
1974 and 1975.
6 Mean PCB and mercury concentrations of lake trout, Lake 55
Superior, 1974.
7 Typical Lake Huron surface currents. 64
8 Nearshore phytoplankton standing crop, Lake Huron, 1974. 75
9a Percent composition of major nearshore algal groups in the 76
spring, Lake Huron, 1974.
9b Percent composition of major nearshore algal groups in the 77
fall, Lake Huron, 1974.
10 Percent composition and density of major benthic macro- 80
invertebrate taxonomic groups in nearshore Lake Huron,
1974 and 1975.
11 Percent composition of the major groups of benthic macro- 85
invertebrates in Thunder Bay, Lake Huron, 1957-1975.
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LIST OF TABLES
Number Page
1 Sampling locations and number of stations per location 14
in the nearshore waters, Lakes Superior and Huron,
1974 and 1975.
2 Methods used to analyze selected water and sediment 17
constituents and fish contaminants in Lakes Superior
and Huron, 1974 and 1975.
3 Collection pattern for sampling locations in the near- 21
shore waters, Lakes Superior and Huron, 1974 and 1975.
4 Sample collection and preservation method for the 23
nearshore waters, Lakes Superior and Huron, 1974 and
1975.
5 Geometric mean bacterial densities in nearshore waters, 38
Lake Superior, 1974.
6 Mean numbers of benthic macroinvertebrate major taxonomic 45
groups at selected locations in nearshore waters,
Lake Superior, 1974 and 1975.
7 Mean concentrations of selected metals in Lake Superior 50
fish, 1974 and 1975.
8 Mean concentrations of selected organic contaminants in 53
Lake Superior fish, 1974 and 1975.
9. Trends of dieldrin in Lake Superior lake trout, 1974-1976. 56
10. Trends of DDT in Lake Superior lake trout, 1974-1976. 57
11. Trends of PCB in Lake Superior lake trout, 1974-1976. 59
12. Trends of mercury in Lake Superior lake trout, 1974-1976. 60
13. Geometric mean bacterial densities in nearshore waters, 72
Lake Huron, 1974.
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Number Page
14. Mean numbers of benthic macroinvertebrate major taxonomic 82
groups at selected locations in nearshore waters,
Lake Huron, 1974 and 1975.
15. Mean concentrations of selected metal contaminants in 87
Lake Huron fish, 1974 and 1975.
16. Mean concentrations of selected organic contaminants in 88
Lake Huron fish, 1974 and 1975.
17. Trends of dieldrin in Lake Huron fish, 1974-1978. 90
18. Trends of DDT in Lake Huron fish, 1974-1978. 91
19. Trends of PCB in Lake Huron fish, 1974-1978. 92
20. Trends of mercury in Lake Huron fish, 1974-1978. 93
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LIST OF TABLES APPENDED
Table Page
A-l Lakes Superior and Huron nearshore sampling locations 103
and associated stations, STORET numbers, latitudes
and longitudes, 1974.
A-2 Lakes Superior and Huron nearshore sampling locations 105
and associated stations, STORET numbers, latitudes and
longitudes, 1975.
A-3 Descriptive statistics for selected physical and 107
chemical constituents in the nearshore waters of Lakes
Superior and Huron, 1974.
A-4 Combined spring and fall correlation coefficients for 122
selected water constituents in nearshore Lake Superior,
1974.
A-5 Combined spring and fall correlation coefficients for 125
selected water constituents in nearshore Lake Huron,
1974.
A-6a Descriptive statistics for chemical and physical 128
constituents in the nearshore waters of Lakes Superior
and Huron., 1975.
A-6b Mean concentrations of heavy metals in unfiltered water 133
samples collected in rivers or very nearshore stations
in Lakes Superior and Huron, 1975. All values are expressed
in ug/1 based on three samples.
A-7 Descriptive statistics for sediment constituents in the near- 134
shore waters of Lakes Superior and Huron, 1974.
A-8 Descriptive statistics for sediment chemical constituents 140
in the nearshore waters of Lakes Superior and Huron, 1975.
A-9 List of phytoplankton species found in nearshore Lake ^43
Superior, spring and fall, 1974.
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Table Page
A-10 Abundance of phytoplankton by class in nearshore Lake 146
Superior, 1974.
A-ll Zooplankton species presence in nearshore Lake Superior, 150
spring and fall, 1974.
A-12 Abundance of zooplankton by major taxonomic groups in 151
nearshore Lake Superior, 1974.
A-13 Macroinvertebrate presence in nearshore Lake Superior, 152
1974 and 1975.
A-14 Summary of benthic macroinvertebrates in nearshore 157
Lake Superior, 1974 and 1975.
A-15 List of phytoplankton species found in nearshore Lake 161
Huron, sorinq and fall, 1974.
A-16 Abundance of phytoplankton by class in nearshore Lake 164
Huron, 1974.
A-17 Zooplankton species presence in nearshore Lake Huron, 166
spring and fall, 1974.
A-18 Abundance of zooplankton by major taxonomic groups in 157
nearshore Lake Huron, 1974.
A-19 Macroinvertebrate presence in nearshore Lake Huron, 168
1974 and 1975.
A-2Q Summary of benthic macroinvertebrates in nearshore 172
Lake Huron, 1974 and 1975.
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ACKNOWLEDGMENTS
Many members of the Biology Section of the Water Quality Division,
Michigan Department of Natural Resources (MDNR), were involved in this
project from its inception and their efforts are greatly appreciated.
Special thanks go to Penny Stockel who typed the various revisions of this
document.
Various groups outside the MDNR took part in this project and their
assistance is acknowledged. The Fisheries Division of the MDNR collected
the fish which the Michigan Department of Agriculture laboratory analyzed
for heavy metals and organic contaminants. The Environmental Laboratory of
the MDNR in Lansing analyzed water and sediment for chemical and physical
constituents throughout the project. In addition, heavy metals in water were
analyzed by J. E. Poldoski of the Environmental Research Laboratory of the
U. S. EPA at Duluth, Minnesota.
The U. S. EPA project officer, Nelson Thomas, deserves special thanks
for his review, assistance and patience throughout this project.
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SECTION I
CONCLUSIONS
Background Locations - Lake Superior
1. Michigan's nearshore Lake_Superior waters were oligotrophic as indicated
by low total phosphorus [x = 0.007 +_ 0.003 mg/1 (mean ± one standard
deviation)], reactive orthophosphate (0.002 +_ 0.001 mg/1) and chlorophyll
(1.55 +_ 0.36 yg/1) and non-limiting concentrations of nitrates (0.27 +^
0.03 mg/1) and dissolved silica (2.4^0.2 mg/1).
2. Most heavy metals and organic contaminant concentrations in nearshore
waters were near detection levels.
3. Concentrations of gamma emitting radionuclides in the nearshore waters of
Lake Superior were below detection levels with total Beta emitters
averaging 2 pCi/1.
4. Sediment quality was generally good with most constituents near detec-
tion levels or less than U. S. EPA dredge spoil criteria for polluted
sediments. Only Presque Isle and Isle Royale sediments exceeded the
EPA criteria for nickel (36 + 52 mg/kg and 58 + 28 mg/kg, respectively)
and manganese (310 + 108 mg/kg and 470 + 240 mg/kg, respectively).
5. Bacterial densities were generally undetectable.
6. Phytoplankton densities were low and dominated by diatoms (especially
Asterionella and Cy do tell a) in the spring. In the fall the percentage of
diatoms decreased due to increases in Chrysophyta (especially Dinobryon)
and Cryptophyta (mainly Rhodomonas).
7. Zooplankton densities were uniformly low and included high percentages of
calanoids and oligotrophic indicator species (especially Senecel1 a
calanoides and Limnocalanus macrurus). Dominant species throughout the
year were Bosmina longirostris, Diaptomus oregonensis, D_. minutus and
Cyclops bicuspidatus thomasi.
8. The calanoid/(cyclopoid plus cladoceran) ratio was reduced in the fall due
to increased numbers of the cladocerans Hoi opediurn gitberum and
Daphnia retrocurva.
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9. The common occurrance of the rotifers Kellicottia, Polyarthra, and
Asplanchna reflected the general oligotrophic nature of the waters.
10. The benthic communities were diverse and included pollution-intolerant
indicator species. Numbers were generally less than 1,000 organisms/m2
and were comprised primarily of Stylodrilus heringianus, Pontoporeia
affinis, Heterotrissocladius and sphaeriids. The exception was Whitefish
Point where average benthic numbers were 3757 +_ 1828 organisms/m2,
comprised primarily of oligochaetes and P_. affinis.
11. Heavy metal and organic contaminants in fish were uniformly low except for
mercury, DDT and PCB. Mercury in fat lake trout exceeded the pre-
January, 1978 USFDA criterion of 0.5 mg/kg at all locations. No location
exceeded the new USFDA criterion of 1.0 mg/kg. DDT and PCB in fat lake trout
exceeded the USFDA criteria only at Black River. Concentrations of PCB's in
all fish except some mottled sculpins exceeded the 1978 Great Lakes Water
Quality Agreement (GLWQA) recommended limit of 0.1 mg/kg.
Impacted Areas
12. Ontonagon
A. Ontonagon mean total phosphorus concentrations in water were in the
mesotrophic range (0.015 +0.021 mg/1) in 1975.
B. Sediments at station 4 exceeded U.S. EPA dredge spoil criteria for
total Kjeldalh nitrogen and total nickel.
C. Mean numbers of benthic macroinvertebrates were relatively low
(2682 +_ 2511 organisms/m2) with pollution-tolerant organisms
(Limnodrilus hoffmeisteri, Aulodrilus limnobius) dominant.
Pontoporeia af finis and Stylodrilus herinnianus were present but in
low numbers.
13. Marquette Harbor
A. Degraded benthic macroinvertebrate communities were found near the shore-
line (6706 orqanisms/m2 with 48 percent oliqochaetes at station 1).
Communities improved further offshore (1322 + 1510 organisms/m2 with 10
to 75 percent oliaochaetes and 2 to 49 percent P_. af finis.
B. Concentrations of mercury in fat lake trout (0.64 mq/kg) exceeded the pre-
January, 1978 USFDA tolerance limits but fell within the new limit of
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1.0 mg/kg mercury in fish flesh. PCB concentrations in fat lake trout
(5.05 mg/kg) also exceeded USFDA tolerance limits at this location.
C. All fish species exceeded the GLWQA criterion for PCB. Lean lake
trout exceeded the GLWQA criterion for total DDT (1.0 mn/kq).
14. Carp River
A. Carp River had elevated mean concentrations of orthophosphate
(0.037 +0.068 mg/1), total phosphorus (0.059 +0.109 mg/1) and
chlorophyll a_ (4.63 +_ 1.74 yg/1) in water in 1975.
B. Diethylhexelphthalate was found in water at one station at 3.8 pg/1.
C. Fecal coliform and fecal streptococci densities were elevated at the
river mouth.
D. Phytoplankton densities were elevated (2698 units/ml) above back-
ground densities with several eutrophic species present.
E. Zooplankton densities were elevated above the background numbers with
6817 organisms/m3 found in the spring and 10,225 organisms/m3 in the
fall. Rotifer numbers were especially high at this location (5201
and 2351/m3 in the spring and fall, respectively), indicating enriched
conditions.
F. The benthic community had more taxa (9-21 per station), greater numbers
(1356 +_ 1405/m2) and more pollution-tolerant forms than found at.
background locations.
15. Munising
A. Sediments were severely degraded with the following location mean values
exceeding U. S. EPA dredge spoil criteria: oil and grease (16,840 +_
24,867 mg/kg); volatile solids (13 +.10.4 percent); lead (80 +44 mg/kg);
arsenic (7.3 + 1.8 mg/kg); copper (96.6 + 37.1 mg/kg); nickel (28 +
9 mg/kg); total Kjeldahl nitrogen (3766 + 691 mg/kg); zinc (134 +
42.5 mg/kg); and chemical oxygen demand ^380,000 +_ 192,561 mg/kgj.
B. The phytoplankton community nearest to the shore was dominated by blue-
green algae throughout the year. Dactylococcopsis was dominant in the
spring and was succeeded by Qscillatoria prolificaf in the fall.
C. Benthic macroinvertebrates at stations nearest shore were dominated by
pollution-tolerant forms with 88 percent of the organisms oliqochaetes.
Especially abundant were Peloscolex ferox, Aulodrilus pluriseta,
Procladius, Microtendipes and Tanytarsiis. At stations further from
shore, oligochaetes decreased to 22 percent and pollution-intolerant
forms (especially P_. affinis and sphaeriids) became dominant (88 percent)
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D. Concentrations of mercury in fat lake trout (0.71 mg/kg) exceeded pre-
January, 1978 USFDA tolerance limits but not the new USFDA limit of
1.0 mg/kg mercury in fish flesh. Levels of PCB in fat lake trout
(5.05 mg/kg) also exceeded USFDA tolerance limits.
E. All fish species except mottled sculpins exceeded the GLWQA
recommended tolerance limit for PCB. Lean lake trout exceeded the
GLWQA limit for DDT.
Background Locations - Lake Huron
1. Nearshore Lake Huron waters were oligotrophic in the northern areas but
approached mesotrophy in the southern portion. Low lakewide concen-
trations of total phosphorus (0.007 +_ 0.001 mg/1), reactive orthophosphate
(0.003 10.002 mg/1) and chlorophyll ^concentrations (2.3 ^ 0.89 yg/1)
reflect the oligotrophic quality of these waters. Nitrates (0.269 +_
0.022 mg/1) and reactive silica (1.2 + 0.4 mg/1) were abundant in the
northern portion with lower concentrations in the southern portion of
the lake.
2. Concentrations of most heavy metals and organic contaminants in water were
near or below detection. The PCB concentration in water at one Harrisville
station was 0.08 ug/1.
3. Sediment quality was generally good with most parameters near or below
detection and within U. S. EPA dredge spoil criteria.
4. Bacterial densities were generally undetectable at background locations.
5. Phytoplankton communities were dominated by diatoms. Algal abundances at
northern Lake Huron locations averaged one-third to one-half the lakewide
mean with an overall north to south increase. Lexington may be classified
as eutrophic, based on algal numbers which were twice the lakewide mean.
6. Spring zooplankton densities (13,444 +_ 145331 oroanisms/m3) were numer-
ically greater than fall densities (4545 +_ 2164 organisms/m3) although
not statistically different. There was a general increase from north to
south. Rotifers were more abundant close to shore (station 1 average
2824/m3) than further offshore (661/m3). The dominant zooplankton species
were Bosmina longirostris, Diaptomus oregonensis, D_. minutus and Cyclops
bicuspidatus thomasi.
7. The benthic macroinvertebrate community at the northernmost location (Detour)
was completely dominated by oligotrophic indicator species (especially
Stylodrilus herinnianus and Heterotrissocladius) and lacked tubificids.
Presque Isle and Harrisville were also dominated by oligotrophic indicator
species but pollution-tolerant or mesotroohic indicator tubificids and
chironomids were present in low numbers. Lexington, south of Saginaw Bay
(and affected by its waters), was completely dominated by mesotrophic
indicator species. Pontoporeia affinis, the primary profundal organism, was
exceptionally sparse in most nearshore waters (not found at Harrisville and
Lexington and only 19/m3 at Detour).
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8. Heavy metals and organic contaminants were generally at or below
detection levels in all fish species at all locations. Concentrations
of PCB and DDT were highest in salmonids, while mercury was highest in
yellow perch.
Impacted Areas
9. Cheboygan
A. The water quality at Cheboygan was enriched as indicated by elevated
chlorophyll a^ (6.6 +_ 8.5 yg/1) concentrations and low nitrates (0.18 +_
0.05 mg/1) and reactive silica (2.0 +_ 1.6 mg/1).
B. In sediments, oil and grease (2600 mg/kg), zinc (140 mg/kg), and TKN
(2500 mg/kg) exceeded U. S. EPA dredge spoil criteria at two, one and
one stations, respectively.
C. Spring phytoplankton communities were dominated by cryptophytes with
lesser numbers of blue-greens and diatoms. In the fall, diatoms were
dominant with the chrysophytes second most abundant.
D. Zooplankton populations were not dominated by calanoids, yielding a
low calanoid/(cyclopoid plus cladoceran) ratio in the sprinn
(0.41) and a very low ratio in the fall (0.28) indicating enriched
conditions.
E. The benthic community at stations nearest shore was diverse and
composed of abundant pollution-tolerant oligochaetes (36 percent) and
chironomids (14 percent). P_. affinis was not present, but at stations
further offshore intolerant species (especially Heterotrissocladius)
were found in low numbers.
10. Saginaw Bay
A. Saginaw Bay was considered eutrophic based on high total phosphorus
(0~018 + 0.011 mg/1), and chlorophyll a_ (60.5 + 46.8 yg/1), and low
nitrate (0.14 +_ 0.11 mg/1) and reactive silica (0.7 +_ 0.4 mg/1).
In addition, 79 percent of the total nitrogen found in Saqinaw Bay was
in the organic form.
B. River-mouth sediments were grossly polluted with copper (46 mg/kg),
arsenic (4.2 mg/kg), chromium (36 mg/kg), zinc (195 mg/kg), nickel
(42 mg/kg), lead (67 mg/kg), manganese (460 mg/kg), COD (87,000 mg/kg),
TKN (2200 mg/kg), and PCB (315 ug/kg).
C. Phytoplankton communities were dominated by green and blue-green algae,
especially Ulothrix and Oscil latoria, respectively.
D. Zooplankton populations were dominated by cyclopoids and cladocerans
yielding low caTanoid/(cyclopoid plus cladoceran) ratios (0.41 spring
and 0.35 fall).
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11. Tawas
A. Water quality was moderately enriched as indicated by chlorphyll a_
(3.6 +_ 1.7 yg/1) and reactive silica (1.2 +_ 0.3 mg/1) concentrations.
B. The phytoplankton community was dominated by abundant eutrophic green
algae (Ulothrix) near the river but improved further offshore.
C. The benthic macroinvertebrate community was dominated by pollution-
tolerant species (especially feloscolex ferox, Pseudochironomus,
Chryptochironomus gr.) at stations nearest shore but at outer stations
oligotrophic indicator species (notably Stylodrilus heringianus)
were present.
D. Whitefish and yellow perch flesh (0.22 and 0.20, respectively) exceeded
the GLWQA recommended tolerance limit for PCB.
12. Harbor Beach
A. Water quality inside the breakwater was moderatley enriched as reflected
by mean chlorphyll a_ (5.4 +_ 1.2 pg/1) and total phosphorus (0.012 _+
0.007 mg/1) concentrations.
B. Sediments exceeded U.S. EPA dredge spoil criteria for TKN (2573 +_
1466 mg/kg), COD (62,000 +_ 22,315 mg/kg), oil and grease (1350 _+
70.7 mg/kg), zinc (126 +_ 57.2 mg/kg), arsenic (5.2 +_ 1.4 mg/kg), nickel
(31 _+ 6 mg/kg), and iron (34,000 +_ 29,720 mg/kg). Copper manganese,
chromium and PCB (18 to 27 yg/kg) were elevated but did not exceed U.S.
EPA dredge spoil criteria.
C. Zooplankton populations indicated enriched conditions by low calanoid/
(cyclopoid plus cladoceran) ratios (0.44 spring, 0.43 fall) and
elevated rotifer numbers (5524/m3 in the fall).
D. The benthic macroinvertebrate community within the breakwall was indic-
ative of degraded water quality with 86 percent by abundance pollution-
tolerant oligochaetes. Stations outside the breakwall were dominated
by oligotrophic indicator species (especially Stylodrilus heringianus).
P. affinis was not found at any station.
13. Alpena
A. Water quality at Alpena was enriched as reflected by elevated total
phosphorus (0.039 +_ 0.039 mg/1 in 1974 and 0.018 +_ 0.009 mg/1 in 1975),
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chlorophyll a^ (8.7 +_ 4.0 yg/1 in 1974 and 11.3 +5.5 yg/l in 1975)
and low nitrates (0.14 +_ 0.11 mg/1 in both years).
B. PCBs in the water were found at one station at 0.02 ug/1.
C. Mean sediment TKN (1033 + 469 m/gkg) and oil and grease (1180 +
783 mg/kg) exceeded U.S. EPA dredge spoil criteria, as did arsenic
at half of the stations sampled.
D. Phytoplankton communities reflected enriched conditions with high
total numbers four times the lakewide mean.
E. Zooplankton communities in the fall indicated enriched conditions
as reflected by a low calanoid/(cyclopoid plus cladoceran) ratio
(0.27).
F. The benthic community was degraded. Sphaeriids decreased from
18 percent of the total population in 1957 to 6 percent in 1975.
Oligotrophic indicator species were present in very low numbers and
only found at the outermost stations.
G. Brown trout, chinook salmon, whitefish and yellow perch in 1974 and
1975 exceeded the GLWQA recommended tolerance limits for PCB.
Trends in Fish Contaminants
1. In Lake Superior, lake trout was the only species with sufficient data for
analysis. The most recent GLECS data covered a period from 1974 to 1976.
The lake trout data in Lake Superior were collected from two subspecies
(fat and lean). Fat lake trout had significantly higher concentrations of all
contaminants than did lean lake trout. The concentrations of dieldrin, DDT
and mercury in the lean and fat lake trout combined were significantly
higher in 1976 than 1974. Concentrations of PCB however, did not change
significantly during this same period.
2. In Lake Huron adequate data were available for analysis of lake trout (1975-
1978), whitefish (1974 and 1975) and walleye (1974 and 1978).
In Lake Huron lake trout, dieldrin, DDT and mercury concentrations appear
to have peaked in 1976 followed by an apparent decline using the most recent
(1975-1978) data. Concentrations of PCB however, did not change signf-
icantly from 1975 to 1978. For whitefish no significant changes occurred
in the concentrations of dieldrin, DDT and mercury in Lake Huron. A signif-
icant increase in PCB concentrations in whitefish occurred from 1974 to 1975.
3. In Lake Huron walleye, a significant increase in DDT and mercury concentrations
in 1978 over 1974 was observed. However, without the intervening years data,
prediction of trends is difficult. The maximum mercury concentration in
walleye collected in the northern portion of Lake Huron nearly exceeded the
action level. Dieldrin and PCB were not tested for in 1974 walleye.
-7-
-------
SECTION II
RECOMMENDATIONS
1. Most impacts found in the nearshore areas of Lakes Huron and Superior were
the result of nutrient inputs from wastewater treatment facilities (WWTP).
Many of these WWTPs have been or are now being upgraded to meet their NPDES
limits. The following areas should have follow-up studies to document
improvements in water quality:
A. Alpena - The municipal WWTP has been upgraded to secondary treatment
with phosphorus removal. In addition, the Abitibi paper company has
changed its treatment process to reduce nutrient inputs. An interim
permit has been issued and further improvements are planned.
B. Cheboygan - The present municipal WWTP has only primary treatment, but
a new facility is under construction and will be on line by 1980.
C. Harbor Beach - The municipal WWTP presently has secondary treatment but
is undersized. A facility plan for a new structure has been submitted
for approval. More efficient treatment should eliminate the present
bacterial contamination.
D. Marquette - The municipal WWTP has impacted the Carp River and Marquette
Harbor. The plant is being upgraded and will be operational in two or
three years.
E. Munising - The present municipal WWTP has been upgraded to secondary
treatment with phosphorus removal. The Kimberly Clark paper company
has improved its treatment facility and is now in compliance with its
NPDES limits.
F. Ontonagon - The municipal WWTP effluent formerly discharged to Lake
Superior now goes to the Hoerner-Waldorf paper company. However, since
Hoerner-Waldorf discharge is not meeting water quality standards, and
is in gross violation of its NPDES permit the problem remains. Recent
negotiations with the company may soon resolve the problem.
G. Tawas - The municipal WWTP presently has primary treatment only, but will
be upgraded within several years,
2. Saginaw Bay is eutrophic and loadings to the ^ay are decreasing. The entire
southern basin of Lake Huron has been impacted by Saginaw Bay. Intensive
efforts should be made to improve the water quality of Saginaw Bay before
the southern basin becomes eutrophic.
-8-
-------
3. New funding for the GLECS studies should be provided to monitor the elevated
PCB and mercury concentrations in fat lake trout from Lake Superior. Other
fish species should be monitored and the remainder of the samples collected
during 1976-1978 analyzed to document the direction of changes in these
residual bioaccumulative contaminants.
4. New fish collections should include area MS-5 in Lake Superior where very
highly contaminated lake trout were previously collected.
5. Fish already collected from Lake Huron in 1976-1978 should be analyzed to
reassess the increase in mercury contamination in walleye. The direction
of changes in the concentrations of DDT, PCB, mercury and dieldrin in lake
trout and whitefish also need verification.
-9-
-------
SECTION III
INTRODUCTION
The Laurentian Great Lakes collectively constitute the world's largest
reservoir of fresh water and are a critical resource for the future develop-
ment of the United States and Canada. While less than four percent of the
United States land area lies within the Great Lakes watershed, it supports
more than 14 percent of the United States population. Increasing population
densities in the watershed will require increased volumes of high quality
water for municipal, industrial, commercial and agricultural expansion. At
the same time, there will be an increasing demand for high quality water for
drinking, swimming, boating, fishing and other recreational pursuits. The
necessity for high quality water to maintain existing natural ecosystems
overlays these interwoven and often conflicting uses.
Future management strategies designed to utilize, protect and, where
needed, improve the Great Lakes water resources must be based on up-to-date
and comprehensive information. To provide such information, the Biology
Section of the Michigan Department of Natural Resources, Water Quality Division
(WQD), conducted water quality surveys in the Michigan nearshore waters of Lakes
Superior and Huron during the spring and fall of 1974 and the summer of 1975.t
The primary objectives of this project were: (1) to establish background levels
of chemical constituents and assess existing biological communities in Michigan's
nearshore Great Lakes waters, and (2) to document cultural influences on the
quality of these waters.
The nearshore waters in this project were roughly defined as those waters
within 5 kilometers (km) of the shoreline. Although they comprise only a small
portion of a lake's volume, nearshore waters are a focal point for limnological
studies because they are the site of complex interactions between the lake's
watershed and the deep water or limnetic zone. The nearshore or littoral waters
are extremely productive and serve as spawning, nursery and feeding areas for
fish and other organisms. Benthic and planktonic animals found in nearshore
waters are vital food chain links and are generally sensitive to changes in water
quality. Physical processes, such as wave-induced mixing, coastal currents and
tThese nearshore surveys were part of a comprehensive assessment of these lakes
performed under the auspices of the Upper Lakes Reference Group of the
International Joint Commission.
-10-
-------
thermal bars, may act in the nearshore waters to disperse or contain watershed
inputs.
Water in sheltered embayments and harbors is isolated in varying degrees
from offshore physical processes and may not readily mix with other nearshore
waters or the open lake. This can cause extensive chemical and physical
variability within these embayments. Therefore, these embayments and harbors
often exhibit physical and chemical characteristics significantly different
from adjacent nearshore and open-water areas.
Consequently the'nearshore waters, especially the embayments, are the
first to be adversely impacted by waste discharges and can thereby serve as an
early warning of impacts on whole-lake water quality.
-11-
-------
SECTION IV
METHODS
Sampling Design
In 1974, twenty-one locations and in 1975, twenty-three locations in the
nearshore waters of Lakes Superior and Huron were sampled (Figure 1). The
locations selected included areas of potential cultural impact and areas outside
direct human influence. The impacted locations were sampled to identify the
extent of degradation from local major discharges which enter the lake via
rivers. The background locations were sampled to determine background values
of water and sediment chemical constituents and the diversity and density of
organisms comprising the biological communities. The term "background" is
defined as locations where man's impact was judged to be minimal when compared
with those locations described as impacted.
In 1974, the locations were sampled in both spring and fall. Spring samples
were collected between June twelve and July third. Fall samples were collected
between August 23 and September 16. One fall station was sampled on
October eighth. Sampling stations were arranged in three tiers at each loca-
tion (Table 1, Table A-l, Figure 2). The first tier consisted of one station.
At impacted locations, attempts were made to locate this station at the interface
of the river and the lake proper. At background locations, this station was
located nearest shore. The second tier of stations, numbered 2 through 4, was
arranged in a line parallel to the shoreline, with station 3 located directly
lakeward from station 1. This tier of stations was located 60-180 meters (m)
from shore at impacted locations and 0.8 to 1.2 km from shore at background
locations. The third tier of stations, numbered 5 through 7, was arranged in
a line parallel to the shoreline, with station 6 directly lakeward from
stations 1 and 3. This tier was located 1.6 to 4.8 km offshore at all locations.
At selected impacted areas, additional stations were established to evaluate
the biological community.
The station arrays at five locations were modified to accomodate special
local conditions. Upper and Lower Portage Entries and Eagle Harbor had four
stations arranged similarly to stations 1 throuqh 4 of the above sampling de-
sign (Figure 2). Isle Royale had four stations located on the northern shore-
line of Amygdaloid Island (Figure 2). The Saginaw Bay sampling design was
reduced because of extensive sampling conducted by other agencies. Four stations
were located along the major axis of the Bay, with station 1 at the interface with
the Saginaw River and stations 2 through 4 extending to the middle of the outer
Bay (Figure 2).
-12-
-------
ISLE
EAGLE HARBOR
UPPER PORTAGE
SHIP CANAL.
LAKE
SUPERIOR
ONTONAGON
BLACK
RIVEI
,WHITEFISH POINT
TAHQUAMENON RIVER
DETOUR
PRESQUE
ISLE
HARRISVILLE
OWER PORTAGE SHIP CANAL
BIG BAY
PRESOUE ISLE
MARQUETTE HARBOR
CARP RIVE
CHEBOYGAN
CALCITE
SAGINAW
BAY / HARBOR
BEACH
Figure I Sampling Stations in the nearshore waters, Lake Superior and Huron ,
1974 and 1975
-13-
-------
Table 1. Sampling locations and number of stations per location in the
nearshore waters, Lakes Superior and Huron,
1974 and 1975.
Location
Number of Stations Sampled
Fall -74 Summer-75
Lake Superior
Impacted
Ontonagon
Upper Portage
Lower Portage
Presque Isle
Carp River
Munising
Background
Black River
Isle Royale
Eagle Harbor
Big Bay
Grand Marais
Whitefish Point
Additional (Sampled only in 1975)
Marquette Harbor
Tahquamenon River
7
4
4
7
7
7
7
4
4
7
7
7
Lake Huron
Impacted
Cheboygan
Alpena
Tawas
Saginaw Bay
Harbor Beach
Background
Detour
Presque Isle
Harrisville
Lexington
Additional (Sampled only in 1975)
Calcite Harbor
Total
132
131
89
-14-
-------
UPPER PORTAGE
LOWER PORTAGE
LEGEND
-I974 STATION
1975 STATION
310092- STORE! NUMBER
EAGLE HARBOR
16 TO 48 Km
2
60-180 m - IMPACTED
O8-I2 Km-CONTROL
3fl_m_D££TH_
CONTOUR
GENERALIZED STATION ARRAY FOR SAMPLES
COLLECTED IN 1974
GENERALIZED STATION ARRAY FOR SAMPLES
COLLECTED IN 1975
Figure 2 Sampling array for locations sampled in the nearshore waters, Lake Superior
and Huron, 1974 and 1975.
-15-
-------
Data collected in the rivers at the interface of the lake in 1974 are not
included in this report, since they do not reflect typical nearshore conditions.
Although these data are not included, they are available upon request. They are
available in the WQD files and on the U. S. EPA STORE! computerized water-quality-
data-storage system. The STORET station numbers for all stations are given in
Table A-l and Table A-2 in the appendix.
In 1975, the locations were sampled only in the summer. Summer samples were
collected from June nine second to August sixteenth. The station array at each
location was reduced to four stations positioned on a transect perpendicular
to the shoreline (Figure 2, Table A-2). At impacted locations, attempts were
made to locate station 1 at the interface of the river and the lake proper.
At background locations, station 1 was located near shore in less than 8-m of
water.
The station arrays at eight locations were modified to accomodate special
local conditions. Upper and Lower Portage Entries, Black River, Big Bay,
Tahquamenon River and Tawas were sampled at only one station. Isle Royale
and Alpena were sampled at six stations.
Additional water samples were taken in 1975 from selected rivers for heavy
metals and organic contaminants analysis (Table A-6).
Physical and Chemical Hater Constituents
In 1974, water samples were collected from 3 depths: Km below the
surface, mid-depth and 1-m above the bottom. Mid-depth collections were deleted
at shallow-water stations. Descriptive statistics for the physical and chemical
water constituents were computed using all stations within a location, excluding
station 1 (Table A-3). Station 1 was not included because it was always close
to the point source (where present) and often did not reflect nearshore water
quality. Detailed correlation coefficient matrices were generated using com-
bined spring and fall data for statistically significant combinations of paired
water quality parameters (Table A-4 and Table A-5).
In 1975, water was collected from 1-m below the surface and 1-m above the
bottom, with all stations included in the calculations of the descriptive
statistics (Table A-6).
For both 1974 and 1975, 8 groups of physical and chemical water quality
variables were determined. These variables are listed in Table 2, along with
descriptions of analytical methods, sensitivity limits and literature citations
for specialized procedures. All samples, except those to be analyzed for heavy
metals contaminants in 1975, were iced and flown to the Environmental
Protection Pureau Laboratory in Lansing for analysis. Table 3 shows the
sampling patterns for all groups of variables surveyed at impacted and back-
ground locations in 1974 and 1975. Table 4 shows the sampling devices, field
preservatives and other information pertinent to sample collection.
-16-
-------
Table 2.
Methods used to analyze selected water and sediment constituents and fish
contaminants in Lakes Superior and Huron, 1974 and 1975
Water variables
Group/Variable
IN-SITU:
Temperature
Dissolved Oxygen
Conductivity
PH
NUTRIENTS:
Ammonia-N
Nitrate-N
Nitn'te-N
Total Kjeldahl-N
Organic-N
Total-N
Reactive orthophosphate
Total Phosphorus
Reactive Silica
Analytical Method Sensitivity
Martek MK II 0.1 °C
Martek MK II 0.1 mg/1
Martek MK II 1 jumho/cm
Martek MK II 0.01 SU
Automated Phenate 1 jug/1
Automated Cadmium Reduction 10jug/l
Di'azotization Colorimetric 1 /ig/1
BlocK digester 2 jug/1
Automated Salicylate
Kjeldahl-N minus Ammonia-N 2 >ig/l
Sum of nitrogen fractions
Automated Single Reagent 2jug/l
Ascorbic Acid Reduction
Block Digester 2 fig/]
Automated Single Reagent 0.1 mg/1
Automatic Molybdosil icate 0.1 mg/1
Reference
EPA p. 168
EPA p. 207
EPA p. 215
EPA p. 256
EPA p. 256
EPA p. 249
Std. Md. p. 302
GENERAL CHEMISTRY
pH
Conductivity
Alkalinity, Total
Hardness, Total
Chemical Oxygen Demand
Turbidity
Total Dissolved Solids
Suspended Solids
Suspended Volatile Solids
Electrometric
Wheatstone Bridge Corrected
to 25°C
Automated Methyl orange
EDTA Titration
Dichromate, Test Tube
Hach Turdibimeter
65% of Sp. Conductance
Sum of Constituents
Gravimetric, Glass Fiber
Filtered, 180°C
Gravimetric, 550°C
0.01 SU
1 iimho/cm
1 mg/1
1 mg/1
0.2 mg/1
0.1 JTU
1 mg/1
1 mg/1
1 mg/1
Std.
A.S.
EPA
Std.
A.S.
EPA
EPA
Std.
A.S.
EPA
Std.
A.S.
EPA
Std.
A.S.
EPA
Std.
EPA
Std.
EPA
Md. p.
T.M. p.
p. 239
Md. p.
T.M. p.
p. 275
p. 5
Md. p.
T.M. p.
p. 68
Md. p.
T.M. p.
p. 21
Md. p.
T.M. p.
p. 295
Md. p.
p. 266
Md. 536
p. 272
500
186
323
128
179
169
495
472
350
231
38
continued
-17-
-------
Table 2, (continued)
WATER VARIABLES
Group/Variable
MAJOR IONS:
Calcium
Magnesium
Sodium
Potassium
Iron
Manganese
Chlorides
Sulfates
CHLOROPHYLL:
Chlorophyll-a
Analytical Method Sensitivity
EDTA Titration 1 mg/1
Atomic Absorption 0.1 mg/1
Atomic Absorption 0.1 mg/1
Atomic Absorption 0.01 mg/1
Flameless AA 0.0004 mg/1
Atomic Absorption 0.005 mg/1
Atomic Absorption 0.001 mg/1
Automated Ferric thiocyanide 0.1 mg/1
Barium Chloride 0.1 mg/1
Turbidimetric
Fluorometric Corrected
Reference
Std. Md. p.
EPA p. 19
Std. Md. p.
A.S.T.M. p.
EPA p. 114
EPA p. 147
EPA p. 143
Std. Md. p.
A.S.T.M. p.
EPA p. 110
Std. Md. p.
A.S.T.M. p.
EPA p. 116
EPA p. 31
Std. Md. p.
A.S.T.M. p.
EPA p. 277
84
210
351
210 (Duluth)
351
210
351
334
428
Std. Md p. 748
HEAVY METALS
Arsenic
Cadmium
Chromium
Copper
Lead
Mercury
Nickel
Selenium
Zinc
nameless AA* 0.0002 mg/1
Atomic Absorption (Gaseous Hydride) 0.001 mg/1
Atomic Absorption Flameless 0.008 ug/1
0.002 ug/1
Flameless AA* 0.0003 mg/1
Atomic Absorption 0.001 mg/1
Flameless AA* 0.0002 mg/1
Atomic Absorption 0.001 mg/1
Flameless AA* 0.0002 mg/1
Atomic Absorption Flameless 0.05 mg/1
Flameless AA* 0.00002 mg/1
Cold Vapor Method 0.0002 mg/1
Flameless AA* 0.0008 mg/1
Atomic Absorption 0.005 mg/1
Atomic Absorption 0.001 mg/1
Gaseous Hydride 0.002 mq/1
Flameless AA* and Atomic Absorption 0.0001 mg/1
Atomic Absorption 0.001 mg/1
*=1975 samples
^Environmental Research Laboratory - see Poldoski, 1975.
Duluth LPL
EPA p. 95
Duluth
Std. Md. p.
uuluth
Std. Md. p.
A.S.T.M. p.
EPA p. 105
Duluth
Std. Md. p.
A.S.T.M. p.
EPA p. 108
Duluth
EPA p. 112
Duluth
A.S.T.M. p.
EPA p. 118
Duluth
A.S.T.M. p.
EPA p. 141
EPA p. 145
EPA p. 145
Duluth
Std. Md. p.
A.S.T.M. p.
EPA p. 155
210
210
351
210
351
344
351
129
351
PLSTICIDES & ORGANIC CONTAMINANTS:
"~ " "Gas Chromatography
Gas Chromatography
DDE
P-P-DDT
Dieldren
1242 PCB
1254 PCB
1260 PCB
DEHP
DBP
Gas Chromatography
Gas Chromatography
Gas Chromatography
Gas Chromatography
Gas chromatoqraphy
Gas Chromatography
Gas Chromatography
0.001 ug/1
0.001 |jg/l
0.001 ug/1
0.001 Mg/1
0.01 ug/1
0.01 ug/1
0.01 uq/ I
l.o uq/l
1.0 ug/1
EPA p.
EPA p.
EPA p.
EPA p.
EPA p.
EfA p.
E^A p.
EPA p.
EPA p.
1973
1973
1973
1973
1973
1^73
19/3
1973
1973
continued
-18-
-------
Table 2. (continued)
Group/Variable
RADIOACTIVITY
Gross Beta
Zinc 65
Zirconium 95
Niobium 95
Cesium 137
Cobalt 60
Mannanese 54
Analytical Method Sensitivity
Low background external proportional 1 oCI/1
alpha/beta counter
Sodiumiodide gamma spectrometer 30 pCi/1
Sodiumiodide gamma spectrometer 13 pCi/1
Sodiumiodide gamma spectrometer 13 oCi/1
Sodiumiodide gamma soectrometer 15 pCi/1
Sodiumiodide qamma spectrometer 15 pCi/1
Sodiumiodide gamma spectrometer 13 nCi/1
Reference
P.H.S 5.2.1.
P.H.S.
P.H.S.
P.H.S.
P.H S.
P.H.S
P.H.S.
5 2 1
5 2 1
5.2.1 .
5 2 1
5 2 1
5.2.1.
SEDIMENT VARIABLES
NUTRIENTS
Ammonid
Nitrate
Total Kjeldahl Nitrogen
Total Phosphorus
GENERAL
Total Solids
Volitle Solids
Chemical Oxygen Demand
HEAVY METALS
Arsenic
Cadmium
Chromium
Copper
Iron
Lead
Manganese
Mercury
Nickel
Selenium
Zinc
ORGANIC CONTAMINANTS
Dieldrin
DDT (TOTAL)
DDD
DDE
PCB (1242, 1254, 1260)
Dibutylphthalate (DBP)
Diethylhexyl phthalate (DEHP)
Automated phenolate analysis 1 yg/1
Automated cadmium reduction 10 yg/1
1974 automated phenolate analysis 2 yg/1
sulfuric-perchloric digestion
on micro-kjeldahl units
1975 automated phenolate analysis
block digestion 2 yg/1
Ascorbic acid reduction 2 ya/1
Moisture determination balance 1 mg/1
Moisture determination balance 1 mg/1
Dichromate reflex method 0.2 mg/1
Gaseous hydride 0.001 mg/1
Atomic absorption 0.008 mg/1
Atomic absorption 0.001 mg/1
Atomic absorption 0.001 mg/1
Atomic absorption 0.005 mg/1
Atomic absorption 0.005 mg/1
Atomic absorption 0.001 mg/1
Cold vapor method 0.0002 mg/1
Atomic absorption 0.005 mg/1
Atomic absorption 0.001 mg/1
Atomic absorption 0.001 mg/1
Gas chromatograph 10 yg/kg
Gas Chromatograph 20 yg/kg
Gas Chromatograph 20 yg/kg
Gas chromatograph 20 yg/kg
Gas chromatograph 200 yg/kg
Gas chromatograph 60 yg/1
Gas chromatograph 90 yg/1
Technicon Industrial
Method 154-71W
Technicon Industrial
Method 100-70W
Technicon Industrial
Method 154-71W
Technicon Industrial
Method 154-71W
Technicon Industrial
Method 155-71W
Std. Md. p. 91, 14th Ed.
Std. Md. p. 95, 14th Ed.
Std. Md. p. 495, 14th Ed.
Method 220
EPA p.
EPA p.
EPA p.
EPA p.
EPA p.
EPA p.
EPA p.
ASTM p.
EPA p.
EPA p.
EPA p.
EPA p.
95
101
105
108
no
112
116
344
118
141
145
155
EPA 1973
FED REG.
EPA 1973
FED. REG.
EPA 1973
38
38
38
FED. REG.
FPA 1973
FED. REG.
EPA 1973
FED. REG.
EPA, 1973
FFD.RER. 38
EPA 1973
38
38
continued
-19-
-------
Table 2. (continued)
FISH PARAMETERS
Group /Variable
ORGANIC CONTAMINANTS
Dieldrin
Lindane
DDT
DDE
ODD
Chlordane
Methoxychlor
Arochlor (PCB)
Polybromated biphenyl (PBB)
Benzene hexac'ilon'de
Hexachlorobeizene
Hexachlorobutadeine
Dibutylphthalate
Di ethyl exyl phthal ate
HEAVY litTALS
Arsenic
Mercury
Cadmium
Chromi um
Copper
Lead
Magnesium
Nickel
Selenium
Analytical Method
Multiresidue method
Gas chromatography
Multiresidue method
Gas chromatography
Multiresidue method
Gas chromatociraphy
Multiresidue method
Gas chromatography
Multiresidue method
Gas chromatography
Multiresidue method
Gas chromatography
Multiresidue method
Gas chromatography
Multiresidue method
Gas chromatography
Multiresidue method
Gas chromatography
Multiresidue method
Gas chromatography
Multiresidue method
Gas chromatograohy
Multiresidue method
Gas chromatography
Multiresidue method
Gas chromatography
Multiresidue method
Gas chromatography
Atomic Absorption
Mercury Analyzer
Atomic Absorption
Atomic Absorption
Atomic Absorption
Atomic Absorption
Atomic Absorption
Atomic Absorption
Atomic Absorption
Sensitivity
(mg/kg)
0.01
0.01
0.02
0.01
0.01
0.04
0.02
0.0'
0.01
n.nl
0.01
0.01
0.20
0.50
1.0
0.01
1.0
1.0
1.0
1.0
1.0
1.0
1.0
Reference
PAH Vol . 1
PAM Vol . 1
PAM Vol . 1
PAM Vol . 1
PAM Vol . 1
PAM Vol . 1
PAM Vol. 1
PAH Vol . 1
PAM Vol. 1
PAn vol . 1
PAM »ol . 1
PAM Vol . 1
PAM Vol . 1
PAM Vol . 1
AOAC Vol . 53, No.
6
Perkins-Elmers^Coleraan
Bull . Env. Cont.
Vol . 3
Bull . Env. Cont.
Vol. 3
Bull . Env. Cont.
Vol 3
Bull. Env. Cont.
Vol. 3
Bull. Env. Cont.
Vol. 3
Bull . Env. Cont.
Vol. 3
Bull . Env. Cont.
Vol. 3
& Tox.
& Tox.
& Tox.
& Tox.
& Tox.
& Tox.
& Tox.
-20-
-------
Table 3.
Collection pattern for sampling locations in the nearshore waters,
Lakes Superior and Huron, 1974 and 1975
IMPACTED
Station/Sample Depth
Variable Group
Water
In-Situ
Nutrients
Gen. Chem
Major Ions
Heavy Metals
Pesticides & Org.
Radionuclides
Chlorophyll a
Sediment
Nutrients
General
Heavy Metals
Pesticides & Org.
Biology
Bacteria
Phytoplankton
Zooplankton
Benthos
Variable Group
Water
In-Situ
Nutrients
Gen. Chem.
Major Ions
Heavy Metals
Pesticides & Org.
Radionuclides
Chlorophyll a
Sediment
Nutrients
General
Heavy Metals
Pesticides & Org.
Biology
Bacteria
Phytoplankton
Zooplankton
Benthos
1 2
S M B t S M B
* *
Composite Composite
& 5m grab & 5m grab
* *
* *
* *
*
Surface Surface
Composite
& 5m grab
Bottom haul
15m haul
* *
1 2
S M B S M B
* * * *
* * * *
* *
Composite
& 5m grab
*
*
*
*
Surface Surface
Composite
& 5m grab
Bottom haul
15m haul
* *
3 4 5
SMB SMB SMB
* * *
Composite Composite Composite
& 5m grab & 5m grab & 5m grab
* * *
* * *
* * *
*
Surface Surface Surface
Composite
& 5m grab
Bottom haul
15m haul
* * *
BACKGROUND
Station/Sample Depth
3 4 5
SMB SMB SMB
* * * * * * *
* * * * * * *
* * * *
Composite
& 5m grab
*
*
*
*
Surface Surface Surface
Composite
& 5m grab
Bottom haul
15m haul
* * *
6
S M B
*
Composite
& 5m grab
*
*
*
*
Surface
Composite
& 5m grab
Bottom haul
15m haul
*
6
SMB
*
*
Composite
& 5m grab
*
*
*
*
Surface
Composite
& 5m grab
Bottom haul
15m haul
*
7
SMB
*
Composite
& 5m grab
*
*
*
Surface
*
7
SMB
* * *
* * *
* *
Surface
*
t S = surface
M = Mid-depth
B = Bottom
* - indicates sample was collected.
continued
-21-
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Variable Group
Uater
In-Situ
Nutrients
Gen. Chem.
Major Ions
Heavy Metals
Pesticides & Org.
Chlorophyll a^
Sediment
Nutrients
General
Heavy Metals
Pesticides & Org.
Biology
Benthos
Table 3. (continued)
Collection patterns for all 1975 sampling locations
1 2 3
River
S M B
S M B
S M B
5m grab
5m grab
5m grab
5m grab
S = surface
M = mid-depth
B = bottom
* = indicates sample was collected
-22-
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In 1975, collections at special river stations (or station 1 when no river
was present) and station 4 were made for heavy metals and organic contaminants.
An exception to this was Isle Royale where stations 2 and 5 were sampled rather
than stations 1 and 4. Additional samples were collected at station 1 at Alpena
and Cheboygan. River samples were taken 0.5-m below the surface. All other metals
samples were taken at mid-depth. Triplicate water samples for metals analysis
were taken at each station with a PVC Kemmerer bottle rinsed with 1:1 nitric acid
and deionized water. These samples were analyzed by the National Water Quality
Laboratory (NWQL) of the U. S. EPA, in Duluth, according to the method outlined
by Poldoski (1974).
In 1975, organic contaminants were analyzed from a 38-liter water sample
collected with a PVC Kemmerer sampler. The sample was filtered through a
polyurethane foam plug which was rinsed with distilled water, acetone and
hexane. The eluate was washed, dried and concentrated before analysis by
gas chromatography (Bedford, 1974).
Radioactivity
During 1974, a four-liter water sample was collected at each location at
station 1 one-meter below the surface with an alpha bottle. Samples were
transported to the Department of Public Health radiological health labo-
ratory and analyzed for gross beta and the gamma emitting radionuclides
shown in Table 2.
Sediment Chemistry
During the fall of 1974, sediment samples were collected at 9 locations
in Lake Huron and 12 locations in Lake Superior (Table A-7). In 1975, sed-
iments were collected at Calcite and Saginaw Bay in Lake Huron and Marquette
Harbor in Lake Superior (Table A-8). All sediments were collected with a
Ponar grab sampler, placed in either a 250-ml glass jar (pesticides) or a
four ounce plastic whirlpac bag, iced and flown to Lansing's Environmental
Protection Bureau Laboratory for analysis. Tables 2, 3 and 4 summarized
sediment parameters analyzed, sampling stations, and collection techniques.
Bacteria
Bacteriological samples were collected only during 1974. Replicate
samples were collected from the surface at designated stations (Table 3)
in sterilized glass bottles. The samples were iced, transported to the
Michigan Public Health Laboratory in Lansing and analyzed within 48 hours.
Samples were analyzed for total coliforms, fecal coliforms and fecal strep-
tococcus using the membrane filter method (APHA, 1971) with detection levels
of 100, 10 and 10 counts/100 ml, respectively.
-24-
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Phytoplankton
Phytoplankton samples were collected at designated stations (Table 3)
during 1974 only. Two types of samples were taken from each site. The first
was a grab sample at a depth of 5-m. The second type was a composite sample
containing equal volumes of water collected from the water column at 5-m depth
intervals, including the surface. Both types of samples were placed in
3.8-liter disposable plastic containers and preserved with formalin and
Lugol's solution. The samples were transported to Bowling Green State
University, Bowling Green, Ohio, for identification and enumeration under the
direction of Dr. Rex Lowe.
One-liter portions of all samples were concentrated by sedimentation and
decantation. A 1-ml aliquot of each concentrated sample was analyzed in a
Palmer-Maioney nannoplankton counting chamber. At least 500 algal units were
counted from each sample, using magnification up to 450x. Algal units consisted
of:
Colonial greens and blue-greens 1 colony/unit
filamentous greens and blue-greens 10 cells/unit
all diatoms and chrysophytes 1 cell/unit
all cryptophytes and dinoflagellates 1 cell/unit
Species identifications were made in the nannoplankton chamber or with a wet
mount using oil emersion (lOOOx). Diatoms were identified to species from
cleared Hyrax mounts.
Zooplankton
Zooplankton samples were collected only in 1974. Two types of zooplankton
samples were collected at designated stations (Table 3) using a 0.5-m diameter,
64-y mesh plankton net. The first sample type was vertical haul from the
bottom and the second was a vertical haul from 15-m, or bottom in depths less
than 15-m. Each sample was washed from the cod end of the net into a sample
bottle and preserved with formalin. The samples were transported to the
University of Wisconsin in Milwaukee, Wisconsin for enumeration and identi-
fication under the direction of Dr. Byron Torke. Results were reported as
organisms/m3.
Benthic macroinvertebrates
Triplicate Ponar grab samples were collected at each of the designated
stations (Table 3) during the fall of 1974 and the summer of 1975. Each
sample was sieved through a U. S. Standard #30 mesh screen and the residue
placed in quart jars. The samples were preserved with buffered formalin and
transported to Lansing where they were sorted, identified and enumerated.
The results were reported as organisms/m2.
-25-
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Organic chemicals and heavy metals in fish
Fish were collected in Lake Superior at 12 and 18 locations in 1974 and
1975 respectively and at 5 and 3 locations in Lake Huron during 1974 and 1975
respectively. Whitefish (Coregonus clupeaformis), herring (Coregonus artedii)
and both fat and lean lake trout (Salvelinus namaycush siscowet and
Salvelinus namaycush namaycush respectively) were collected in 1974 in
Lake Superior. In 1975, only mottled sculpins (Cottus bairdi) were collected
in Lake Superior.
Whitefish, rainbow trout (Salmo gairdneri), brown trout (Salmo trutta)
Chinook salmon (Oncorhynchus tshawytscha), walleye (Stizostedion vitreum)
and yellow perch (Perca flavescensjwere sampled in Lake Huron in 1974. In
1975 only yellow perch were collected in this project. Fish were iced,
transported to Lansing, frozen and analyzed by the Michigan Department of
Agriculture by methods shown in Table 2. Analyses were performed on skinless
fillets of individual fish and in the case of yellow perch, on a composite
of four to six fillets. Sculpins were gutted and analyses conducted on a
composite of six to thirty fish. Several species of fish were analyzed for
dieldrin, DDT, PCB and mercury during 1974 in conjunction with the Great Lakes
Environmental Contaminants Survey (GLECS) program. For some species, the
Upper Lakes Reference Group (ULRG) of the IJC supported additional analyses
for copper, zinc, lead and cadmium and 11 additional organic compounds (Table 2).
In 1975, the ULRG supported only the collection of mottled sculpins in
Lake Superior and yellow perch in Lake Huron, most of which were tested for
the above contaminants. Additional fish were monitored in the GLECS program
in 1975 and succeeding years. The GLECS program began in 1970 with analysis
performed by the U.S. FDA or the Michigan Department of Agriculture (MDA) laboratorie:
Data Handling
When data were reported below the detection limit, one-half of the detection
limit was used in calculation of averages, standard deviations and other
statistics. As a result, some values are reported lower than the detection
level. This was done to make a "reasonable" estimate of the concentrations
of the parameters. This assumption should not result in large errors since
the values below detection level were generally a low percentage of the total
number of observations. Values for pH were "averaged" differently than other
parameters, using proper arithmetical handling of logarithams (Earth, 1975).
In the report the word "significant" indicates that a statistical test has
been preformed. All tests were significant at the P = 0.05 probability level.
Althouth the GLECS data were not collected with the forethought toward
rigorous trend analyses, they are the best data available concerning Great Lakes
fish contaminants. Fish samples were not always collected from the same
-26-
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locations each year, fish age or length and sex were not held constant and
sample size was variable. It is therefore difficult to determine whether or
nor these samples are truly representative of the entire population. However,
the attempt was to describe overall, lake-wide variations in fish contaminants
from year-to-year.
Preliminary examination of the 1974 through 1978 GLECS data indicated that
the concentrations of these fish contaminants were not normally distributed and
therefore would not meet the assumptions of the analysis of variance test.
Using Taylor's power law, the transformation determined was to replace each X
value with x"°-03355. The transformed data were tested at the 0.05 alpha level
by one-way analysis of variance with tests conducted for both year-to-year
and location differences. The Student-Newman-Keuls procedure was used to
determine the order of difference when significance was found.
-27-
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SECTION V
LAKE SUPERIOR
Introduction
Lake Superior is the largest freshwater lake in North America and one of
the largest lakes in the world. It is 82,413 km2 in surface area, approximately
563 km long, 258 km wide, has a maximum depth of 406-m, and a volume of
13,500 km3. It is the uppermost lake in the Great Lakes system and overlies
the relatively insoluble Canadian Shield. The relative insolubility of this
geological formation results in low average total alkalinity (43.5 mg/1) and
calcium concentrations (14.4 mg/1) in Lake Superior, both less than half of
Lake Michigan's averages (Schelske and Roth, 1973).
Historically, there has been little change in the water quality of Lake
Superior based on data collected as early as 1907 (Dole, 1909). Total dissolved
solids, chlorides and sulfates have remained relatively constant since the
early 1900's (Beeton, 1965). Lake Superior is an oligotrophic lake as indicated
by non-depletion of nitrate and silica in the summer surface waters and rela-
tively low total phosphorus concentrations at the surface (Schelske et al.,
1972). The lake is dominated by oligotrophic species of ohytoplankton, zoo-
plankton, benthic macroinvertebrates and fish.
Major currents in Lake Superior have been characterized by a number of
investigators (Yeshe ejt al_., 1972, Adams 1970, Murty and Rao 1970). The overall
water movement in Lake Superior is counter-clockwise around the periphery of the
basin (Figure 3). Contrasting this general movement is a clockwise current
around Isle Royale (Adams, 1970). Current velocities in the lake range from a
few cm/sec to over 50 cm/sec for the coastal current off the Keweenaw Peninsula.
Physical and General Hater Chemistry
Little physical variation occurred in Lake Superior nearshore waters throuahout
the 1974 survey. Mean location temperatures ranged from 6.6° to 10.0°C during
the spring (June) except at Isle Royale, which averaged 3.3°C. Fall
mean location temperatures ranged from 13.5° to 22°C, approximately 7.5 °C higher
than corresponding spring values. During 1975, for samples collected from the
first of June through mid-July, mean temperatures ranged from 4.5°C at Isle
Royale to 11.3°C at Grand Marais. River-lake interface station temperatures
were generally 6° to 8°C warmer than the lake. Although temperatures varied
with depth, no stable thermal stratification was noted.
-28-
-------
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-29-
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Mean dissolved oxygen (DO) concentrations at individual locations during
1974 ranged from 10.1 to 13.2 mg/liter during spring. The higher temperatures
recorded during the fall sampling period may have been the cause of lower DO
levels which ranged from 8.5 to 10.9 mg/1. In 1975, mean dissolved oxygen
concentrations ranged from 11.2 to 13.2 mg/1, with a lakewide mean of 12.4 +
0.6 mg/1. Dissolved oxygen concentrations were near saturation levels at all
locations and depth profiles were orthograde.
In 1974, mean hydrogen ion concentrations (pH) at individual locations
ranged from 7.4 to 8.0 pH units during the spring and from 7.6 to 7.9 during
the fall. Mean spring and fall pH values were nearly identical to the lake-
wide mean of 7.7. In 1974, no significant differences were evident between
sampling periods, locations or depths. In 1975, mean pH values ranged from
7.6 near Grand Marais and Isle Royale, to 7.8 at Marquette Harbor. Because
equipment failure prevented accurate pH measurements at several locations in
1975, pH was not included in the correlations or other statistical analysis.
Total dissolved solids (TDS) did not vary significantly during 1974.
Location means ranged from 52 to 55 mg/1, with a lakewide mean of 53 +_ 1 mg/1.
No sampling period differences or location differences were evident, although
TDS was significantly correlated with nutrients, conductivity and major ions.
In 1975, mean TDS values ranged from 55 to 60 mg/1, with a lakewide mean of
57 +_ 2 mg/1. TDS values from both years were similar to Beeton's (1965)
suggested long-term average value of approximately 60 mg/1, indicating that the
lake's water quality as indicated by this parameter has remained relatively
constant since the early 1900's.
Mean location conductivity measurements in Lake Superior ranged from 85 to
88 ymhos/cm during spring sampling, and from 83 to 92 ymhos/cm in the fall of
1974. The lakewide mean was 88 +_ 1 ymhos/cm. Conductivity measurements varied
little with depth, and no significant sampling period or location differences
were found. During 1975, mean location conductivity measurements ranged from
85 to 101 ymhos/cm with a lakewide mean of 88 +_ 5 ymhos/cm. The location values
were relatively constant with the exception of the Carp River at Marquette
which was 13 ymhos/cm above the lakewide mean reflecting the impact of the river.
Chloride and sulfate mean location concentrations were low throughout 1974,
ranging from 0.9 to 1.4 mg/1 and 2.5 to 3.2 mg/1, respectively. No significant
depth, location, or sampling period differences were noted for these constituents,
Mean location concentrations of chlorides and sulfates were similar during 1975,
ranging from 1.1 to 2.3 mg/1 and 2.9 to 4.7 mg/1, respectively. These values
agree with the mean Lake Superior values reported by Beeton and Chandler
(1963), of 1.9 mg/1 for chloride and 3.2 mg/1 for sulfate. Apparently,
little change has occurred in the concentration of these constituents in
Lake Superior over the last decade. While chlorides and sulfates were most
closely correlated to TDS, they also correlated well with nutrients and the
conservative ions.
-30-
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Nutrients and Chlorophyll a^
Mean annual nitrate (N03-N) concentrations in 1974 ranged from 0.239 mg/1
at Carp River (Marquette) to 0.326 mg/1 near Big Bay, with a lakewide mean of
0.269^0.021 mg/1. The mean fall N03-N concentration (0.277 +_ 0.027 mg/1)
was significantly higher than the mean spring concentration (0.261 +_ 0.018 mg/1).
Since nitrate concentrations generally are reduced through phytoplankton
growth in the late summer. This apparent reversal suggests that changes
have occurred in the fall samples following collections due to improper pre-
servation techniques or contamination. Total nitrogen concentrations were
relatively constant throughout the year, although organic nitrogen values
decreased in most of the fall samples relative to spring values. Along with this
decrease in organic nitrogen, N03-N and NH3-N increased in these same samples,
indicating some degradation of the organic nitrogen to N03-N and NH3-N before
analysis suggesting improper preservation techniques. In the fall, concentrations
of N03-N were significantly lower at the surface than at the bottom probably due
to phytoplankton utilization.
Mean nitrate (N03-N) concentrations in 1974 were low with no significant
differences between locations, sampling periods or depths. Location means
ranged from 0.001 to 0.002 mg/1 with a lakewide mean of 0.002 + 0.002 mg/1.
Three percent of the values were below the detection limit (0.001 mg/1) with
all nondetectable values occurring in the spring.
In 1975, N03-N and N02-N were analyzed together. The lakewide mean was
0.27 +_ 0.03 mg/1, nearly identical to the 1974 results. Location means ranged
from 0.22 mg/1 at Tahquamenon River to 0.31 mg/1 at Upper Portage Entry.
Mean ammonia (NH3-N) concentrations were low at all locations in 1974,
ranging from 0.001 to 0.014 mg/1, with a lakewide mean of 0.005 +_ 0.002 mg/1.
Fourteen percent of the values were below the detection limit (0.002 mq/1.
Maximum NH3-N levels were recorded at station 1 off the Carp River (0.41 mg/1)
but these relatively high levels were not present at stations further off-
shore. The Carp River receives primary treated municipal wastewater from the
Marquette municipal wastewater treatment plant. Previous studies (MWRC 1969a,
MWRC 1973) revealed water quality degradation downstream of the Marquette
wastewater treatment plant in the Carp River and in the nearshore waters of
Lake Superior. Ammonia concentration in Lake Superior was strongly correlated
with the conservative ions, phosphorus and hardness, and negatively correlated
with dissolved oxygen (Table A-4).
In 1975, a similar percentage of NH3-N reading^ was below the detection
limit. The lakewide mean was 0.002 + 0.001 mg/1 excluding the Carp River
location (0.015 +_ 0.021 mg/1) which, as in 1974, was substantially higher than
other locations.
In 1974, mean total nitrogen (total-N) concentrations at individual loca-
tions ranged from 0.36 to 0.46 mg/1 with a lakewide mean of 0.40 +_ 0.003 mg/1
total-N. Big Bay had the highest mean total-N concentration during both
samplings in 1974. The 1975 lakewide mean was 0.37 + 0.04 mg/1 with individual
-31-
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location means ranging from 0.30 to 0.45 mg/1. The highest mean value was
found at the Carp River, Marquette. No significant differences were found
among locations or sampling periods in 1974 or 1975. Total-N was strongly
correlated with N03 and organic-N (Table A-4).
Mean total orthophosphate concentrations were low at all locations in 1974,
ranging from 0.001 to 0.003 mg/1, with 59 percent of the values below the
detection limit of 0.002 mg/1. The lakewide mean was 0.002 + 0.001 mg/1. Fall
concentrations were slightly higher than spring levels but differences between
sampling periods were not statistically significant. Orthophosphate was
correlated with all nutrients, reactive silica and the conservative ions
(Table A-4).
In 1975 orthophosphate concentrations were also low, with location means
ranging from below detection (<0.001 mg/1) to 0.005 mg/1, excluding the Carp
River location which was substantially higher (0.037 + 0.068 mg/1) than other
locations. The lakewide mean excluding Carp River data was 0.001 +_ 0.001 mg/1.
In 1974, location means for total phosphorus (total-P) ranged from below
the detection level (0.002) to 0.012 mg/1 with a lakewide mean of 0.007 +_
0.003 mg/1. Eighteen percent of the values were below the limit of detection
(0.002 mg/1). No significant differences were found between locations or
sampling periods, even though individual stations at Black River and Carp River
had total-P concentrations considerably higher than the lakewide mean (0.020
and 0.150 mg/1, respectively). Both rivers receive municipal wastewater dis*
charges which might explain these elevated total-P values. Unpublished 1973-
1974 data from Michigan Water Resources Commission (MWRC, 1975) show total-P
levels near the mouth of the Black River averaging approximately 0.04 mg/1. High
levels of total-P (0.400 mg/1) were also found near the mouth of the Carp
River in 1972 (MWRC, 1973). Correlations of total phosphorus with other
parameters were similar to those for orthophosphate.
In 1975, location total-phosphorus means ranged from below the detection
level (0.002 mg/1) at Tahquamenon River to 0.015 mg/1 at Ontonagon, with a lake-
wide mean of 0^.005 +_ 0.003 mg/1 excluding Carp River data, and 0.008 + 0.118 mg/1
including Carp River data. The Carp River location mean for total-P was 0.059
+^0.109 mg/1, reflecting the inputs from the wastewater treatment plant.
In 1974, mean dissolved silica concentrations ranged from 2.0 to 2.8 mg/1,
with a lakewide mean of 2.4 +_ 0.2 mg/1. Differences between surface and bottom
concentrations were not significant, nor were differences between locations.
Fall concentrations were significantly lower than those taken in the spring,
probably reflecting utilization by diatomaceous phytoplankton. Silica
concentrations were positively correlated at a low level with nutrients
(except nitrate) and conservative ions and negatively correlated with
temperature and nitrates (Table A-4).
In 1975, dissolved silica location means ranged from 2.0 to 2.5 mg/1, with
a lakewide mean of 2.2 + 0.2 mg/1. All concentrations during both years were
well above limiting levels for diatomaceous phytoplankton production (Schelske
and Roth, 1973).
-32-
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In 1974, Lake Superior mean chlorophyll ^concentrations ranged from
1.09 to 2.27 yg/1, with a lakewide mean of 1.55 +_ 0.36 yg/1. No significant
differences were found between locations or sampling periods. These concen-
trations are similar to levels obtained by Schelske and Roth (1973). They
found chlorophyll ^concentrations usually less than 0.5 yg/1 in the open
lake, but in bay areas values ranged from 1.2 to 1.7 yg/1, about two or
three times those in open waters. No correlations were found between
chlorophyll a^ and other parameters.
In 1975, chlorophyll ^values were slightly higher. Means ranged from
1.49 yg/1 at Isle Royale to 4.63 yg/1 at Carp River (Marquette) but no
significant differences were found between locations. The lakewide average
was 2.70 +_ 1.10 yg/1 with Carp River values included, and 2.40 +_ 0.83 yg/1
without them.
Heavy Metals in Water
Heavy metals concentrations in Lake Superior were generally very low and
frequently were below detection. Total selenium concentrations were below the
detection level (1.0 yg/1) at all locations in 1974, and in 1975 no selenium
analyses were made.
Total mercury was below the 1974 detection level (0.2 yg/1) at all loc-
ations. In 1975, total mercury concentrations were also below the detection
level (0.02 yg/1) except at Grand Marais (<0.03 yg/1) and Whitefish Bay
(<0.04 yg/1), both Within the 0.05 yg/1 criterion tor orotection of aquatic
life (U. S. EPA 1976).
In 1974, total cadmium was below detection level (2.0 yg/1) at all locations.
In 1975, total cadmium detection level was lowered to 0.02 yg/1. The 1978
Great Lakes Water Quality (GLWQA) has an objective for total cadmium in
unfiltered samples of 0.2 yg/1 to protect aquatic life (GLWQA, 1978). All
locations except Big Bay (0.23 yg/1) and Grand Marais (0.48 yg/1 in the unfiltered
and 0.32 yg/1 in the filtered samples) met this criterion. Poldoski (1975)
suggested that the variability of the Grand Marais sample was probably due to
Steps prior to analysis but the real cause of this cadmium concentration is
unexplained.
In 1974, total nickel was above the detection level (5 yg/1) only at Big
Bay (7 yg/1) and Black River (6 to 9 yg/1). In 1975, the detection level was
lowered to 0.8 yg/1, with 64 percent of the samples below detection. Individual
samples ranged up to 0.9 yg/1, with all values well below all water quality
criteria.
Total lead was found above the 5 yg/1 detection level at only three loc-
ations in 1974. Presque Isle and Munising were below and Grand Marais equalled
the 10 yg/1 total lead criterion for Lake Superior for aquatic life (GLWQA, 1978).
In 1975, the detection level for total lead was lowered to 0.2 yg/1. Loca-
tion mean concentrations in 1975 were 0.8 yg/1 or less, with a lakewide mean
of 0.4 +_ 0.2 yg/1. The highest values occurred at Grand Marais but all detect-
able concentrations were less than 1/10 of the GLWQA (1978) objectives.
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Total arsenic concentrations in Lake Superior were below the detection
level (1 yg/1) at all locations in 1974. In 1975, the total arsenic detection
level was lowered to 0.2 yg/1. Location means in 1975 ranged up to 1.0 yg/1,
with a lakewide mean of 0.78 + 0.2 yg/1. All detectable values were well below
the 50 yg/1 criterion for public water supply (U. S. EPA 1976).
Althouth total manganese concentrations were consistently detectable
during 1974, they were very low, ranging from below the 1 yg/1 detection limit
at Big Bay to 3 yg/1 at Black River, Ontonagon and Carp River. In 1975, the
total manganese detection level was reduced to 0.05 yg/1, with mean concen-
trations ranging from 0.3 to 1.1 yg/1. All values were well below the 50 yg/1
criterion for public water supply (U. S. EPA 1976).
Total chromium detection level in 1974 was 1.0 yg/1, with the majority
of values below the concentration. All 1974 location means were 1 yg/1 or
less but individual station concentrations at Grand Marais and Eagle Harbor
ranged to 3 yg/1. In 1975, the total chromium detection level was reduced to
0.3 yg/1, with most values at or near this concentration. The 1975 total
chromium lakewide mean was 0.42 +_ 0.26 yg/1, with Big Bay having the highest
mean concentration (1-3 yg/1). All detectable values were well below the
50 yg/1 total chromium criterion for public water supply (U. S. EPA 1976) and
the Michigan hexavalent chromium Water Quality Standard for aquatic life
(25 yg/1) (MWRC, 1978).
Mean total iron concentrations ranged from 18 to 64 yg/1 in 1974. Only
at Big Bay (330 yg/1) and Munising (320 yg/1) did individual values exceed
the drinking water criterion for public water supplies (EPA 1976). The
detection level for iron in 1975 was 0.4 yg/1, with location means ranging from
5 to 81 yg/1, and a lakewide mean of 21 +_ 23 yg/1. All values were well below
the water quality criterion of 300 yg/1 for aquatic life protection (U. S.
EPA 1976).
In 1974, location means for copper ranged from 3 yg/1 at several locations
to 8 yg/1 at Lower Portage Entry. While differences between location means were
not significant, fall values were significantly lower than spring values. The
annual location means for copper exceeded the Great Lakes Water Quality
Agreement of 5 yg/1 for aquatic life (GLWQA 1978) at Lower Portage Entry
(8 yg/1), Eagle Harbor (6 yg/1) and Big Bay (6 yg/1). These concentra-
tions probably do not reflect unnatural inpdts due to natural copoer deposits
in these areas. The 1975 copper concentrations were comparable to the
fall concentrations of 1974. Location means in 1975 ranged from 1.0 to 2.6 yg/1,
with a lakewide mean of 1.5 +_ 0.4 yg/1. Mo copper values in 1975 exceeded the
GLWQA objective of 5 yg/1 (GLWQA 1978).
In 1974, mean zinc concentrations ranged from 4 yg/1 at Upper Portaqe Entry to
11 yg/1 at Big Bay, with a lakewide mean of 8 +_ 2 yg/1. All values were well
within the GLWOA objective of 30 yg/1 (GLWQA 1978). No significant differences
were found between locations, but fall values were significantly higher than
spring values. Several elevated zinc concentrations were observed in the
water samples collected near the bottom which may have been contaminated with
sediments. The zinc detection level in 1975 was 0.1 yg/1. Location means
ranged from 1.0 to 2.7 yg/1, with a lakewide mean of 2.0 +0.9 yg/1. No 1975
zinc values exceeded the above objectives.
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Organic Chemicals in Water
In 1974, water samples were analysed for dieldrin, polychlorinatert
biphenyls (PCB), and several other organic chemicals (Table 2). In this
study, PCB's are reported as total PCB's which is the sum of the three
major forms, Arochlor 1242, Arochlor 1254 and Arochlor 1260. Also within
this report the total DDT analogs are reported as DDT or total DDT which
is a summation of ortho para (o.p.), and para para (p.p.) DDT and their
metabolites ODD and DDE. No PCB, dibutylphthalate (DBP), or dieldrin were
found above the detection level of 0.01, 1.0, and 0.001 yg/1, respectively.
Diethylhexalphthalate (DEHP) was detected at one station at Carp River
(Marquette) (3.8 yg/1). No source could be determined although DEHP is
used in many products, including some farm chemicals and orchard spray.
DDT and DDE were found only above detection levels (0.001 yg/1) in
individual samples from Eagle Harbor (0.004 yg/1), Big Bay (0.002 yg/1),
Presque Isle (0.002 ug/1) and Carp River (Marquette) (0.002 yg/1).
In 1975, a more sensitive analytical method developed by Musty (1974)
was used for organic chemicals. In this method, two and one half liters of
water were filtered through a foam plug and the filtrate-plug extracted
with hexane. Interference occurred from the foam plug and/or other sources.
As a result, the various organic chemicals in the water and the interfering
substance could not be differentiated. Consequently, all values for 1975
were reported as below the level of detection.
Radioactivity
Samples for radioactivity analysis were collected only in the spring and
fall of 1974. Zinc 65, zirconium 95, niobium 95, cesium 137, cobalt 60 and
manganese 54 were all below the minimum detectable activity (MDA) levels 30, 13,
13, 15, 15 and 13 pCi/1 respectively. Correspondingly low gross beta activities
also occurred ranging from below the MDA to 5 pCi/1. The lakewide average was
2,0 pCi/1.
Sediment Chemistry
In 1974 and 1975, most sediments from the nearshore waters of Lake Superior
had very low levels of pesticides, polychlorinated biphenyls (PCB), metals,
nutrients and chemical oxygen demand (COD).
Arochlor 1242, 1254 and 1260, o.p. DDT, o.p. DDT, and ODD were below the
detection level of 3 yg/kq at all locations with the exception of ODD at one
station in Munising Bay in 1974. Dieldrin and DDE were below the detection
level of 1 yg/kg at all locations.
Dibutylphthalate (DBP) was detected in the sediment from all Lake Superior
locations except Isle Royale in concentrations ranging from less than 60 to
540 yg/kg. Concentrations of diethylhexalphthalate (DEHP) in sediment ranged
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from below detection (90 yg/kg) at Black River and Isle Royale to an average
of 4994 +_ 6855 yg/kg at Muni sing.
A 1974 wastewater survey indicated the Kimberly Clark paper company was
discharging 2.3 yg/1 -DEHP from its facility and is the only known source of
phthalates in Munising sediments. However, phthalates, which are plasticizers, are
widely used in many industrial processes and are found in numerous house-hold products
Hexane extractable oil and grease concentrations in sediments exceeded U.S.
EPA dredge spoil criteria at Munising (16,804 +_ 24,867 mg/kg), Upper Portage Entry
(5400 + 0.0 mg/kg) and Whitefish Point (6000 + 3997 mg/kg). Elevated concen-
trations of hexane extractables in the Munising sediments probably are the
result of the past sulfite-pulp paper process at Kimberly Clark. This process was
utilized prior to the Company's conversion to specialty paper products.
Upper Portage Entry sediments were probably contaminated by mining
wastes or discharges from ship traffic through this passage. The source
of the oil and grease in the sediments at Whitefish Point (one station)
is unknown.
Concentrations of nickel in sediments exceeded the dredge spoil criterion
at Ontonagon, Upper Portage Entry, Eagle Harbor, Isle Royale, Presque Isle
and Munising.
Copper exceeded the dredge spoil criterion at Upper Portage Entry,
Eagle Harbor and Munising. Copper and nickel in the sediments at Upper
Portage Entry were probably the result of past mining activities and natural
ores in the bedrock and glacial till.
Concentrations of manganese exceeded the dredge spoil criterion at Isle
Royale and Presque Isle.
Total chromium exceeded the dredge spoil criterion only at Presque Isle.
Levels of lead, zinc, arsenic, and volatile solids exceeded dredge spoil
criteria only at Munising.
Concentrations of total phosphorus, TKN, and COD were elevated at
Munising, Untonagon and Carp River. This probably was due to organic enrich-
ment from wood processing and paper mill plants as well as wastewater from
municipalities.
The principal sources of degradation at Munising were wood fibers
previously deposited from the Kimberly Clark pulp mill (MWRC, 1969), several
other now-defunct saw mills and pulping operations, storm sewers and the
Munising wastewater treatment plant effluent discharged to the Anna River.
Woody material was still evident in the sediment samples collected in 1974,
even though the pulp mill stopped operation and the company's paper mill
discharges were greatly reduced in 1962. Cellulose fibers are relatively
inert and may cover the sediments for many years, as evidenced by samples
collected at other locations in the Great Lakes.
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Bacteria
Densities of total and fecal coliforms and fecal streptococci have been
used to indicate pollution because these organisms are associated with the
feces of warmblooded animals. Total coliform concentrations, however, vary
as a result of inputs from several sources, and thus may not reflect human
degradation of water quality. Prior to Rao and Henderson's (1974) baseline
bacteriological survey of Lake Superior, bacteriological data were limited
to miscellaneous nearshore studies for permit enforcement and public health
concerns.
Samples taken in 1974 from Michigan's nearshore Lake Superior waters
generally had low bacterial densities, reflecting high water quality. A total
of 106 water samples were analyzed with 69, 90 and 90 percent, respectively,
of the total coliform, fecal coliform and fecal streptococci counts below
detection levels (100, 10 and 10 organisms/100 ml).
Total coliforms were elevated at the nearshore stations in the spring
at Munising and Presque Isle, and in the fall at Black River, Ontonagon, Carp
River and Munising (Table 5).
The maximum fecal coliform value observed, 17,138 organisms/100 ml at
Carp River, exceeded the Michigan water quality standard of 200 organisms/100 ml
(MWRC, 1977). This high value probably resulted from the wastewater treatment
plant discharge from Marquette.
Fecal streptococci values were consistently below detection levels in both
spring and fall, except for Carp River and moderate spring levels at Munising.
At Carp River, station 1 had high levels of fecal streptococci, reflecting
discharges from the Marquette wastewater treatment plant.
Phytoplankton
Historical information on the phytoplankton of Lake Superior is limited
and usually restricted to studies of net plankton. Holland (1965) found an
oligotrophic diatom assemblage in 1964 dominated by small forms of
Cyclotella (C_. glomerata, C_. Stell igera, C_. ocellata, and C_. kutzingiana).
Schelske et al. (1972) in both nearshore and offshore samples reported a
dominance~of~diatoms, especially of the genus Cyclotella. Other common
diatoms (Asterionella, Tabellaria and Synedra) were reported by Schelske and
Roth (1973^Dinobryon and Fragilaria have also been often reported (Davis,
1966). Lake Superior was classed as oligotrophic based on phytoplankton in a
review by Vollenweider, ejb aj_. (1974).
The nearshore waters of Lake Superior were sampled for phytoplankton in
June and August through September, 1974. Diatoms were the dominant algal
group at all locations in June, averaging 57 percent by abundance. In June,
dominant species at all 12 locations were Asterionella formosa, four species
of Cyclotella (C_. compta, C_. glomerata, C_. kutzingiana and C_. ocellata),
Rhodomonas minuta, Synedea tenera, and Melosira granulata (Table A-9).
-37-
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-39-
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In late August and September, the numerical dominance of diatoms was
reduced to 29 percent from the spring value of 57 percent. Although present
at relatively low numbers, diatoms still were slightly more abundant than
other classes (Table A-10). This change was due primarily to an increase in
Dinobryon which shifted the Chrysophyta from 5 percent in the spring to
22 percent in the fall. The Cryptophyta increased from 15 to 21 percent in
the fall, while blue-greens and greens remained about the same. Fewer dominant
species were found than in the spring. In the fall, Rhodomous minuta and
Dinobryon ranked first and second in numbers at eight locations. Other
dominant species included Fragilaria crotonensis, Cyclotella compta, C_.
Glomerata, Asterionella formosa and Oscillatoria prolifica which was especially
abundant in Whitefish Bay.
Mean values for total algal numbers in the spring ranged from 338 units/ml
at Isle Royale to 2214 units/ml at Carp River. Fall means ranged from
533 units/ml at Whitefish Bay to 4587 units/ml at Eagle Harbor. Statistical
comparisons between composite samples and 5-m grab samples showed no sig-
nificant differences between number of species or number of algal units
collected. The lakewide mean algal abundance and number of species was 1655 +_
628 units/ml and 28+6 species in the 5-m grab sample and 1689 +_ 831 units/ml
and 30+6 species in the composite samples (Figure 4).
Variations in the algal community were found for individual stations
within each location. This was expected since stations at a particular
location included river-mouth stations, relatively shallow lake stations
and lake stations located up to 3.2 km offshore in 30-m of water. Although
variations in species composition were present, generally the abundant
species at a location were found at all stations within that location.
However, this trend was not consistent at two locations. Blue-green
algae were abundant in the shallow South Bay stations at Munising but
not further offshore. In the spring, Dactylococcopsis fascicularis, were
abundant at station 1, near the Anna River mouth, but it was succeeded by
Oscillatoria prolifica in the fall. At Carp River, large numbers of
Stephanodiscus invisitatus, a common eutrophic rivor plankton (Lowe 1974),
were found only near the river mouth. The other algae abundant at this
station, however, were also present at the other stations.
Rhodomonas minuta was one of the two most abundant forms found during the
spring at all locations e/.cept Lower Portage Entry, Eagle Harbor, Isle Royale and
Grand Marais. In the fall .R. minuta was very abundant at all locations except
Isle Royale and Whitefish Bay. Mean !R. minuta percentages ranged from 0 to 34
percent in the spring and 6 to 38 percent in the fall. Isle Royale was the only
location where F*. minuta did not comprise at least 10 percent of the total algal
numbers during both sample periods.
Dinobryon was the most abundant chrysophyte found and one of the two most
abundant algae in the fall samples.
Several species of blue-green algae were present in most samples but were
found in abundance only at Muni sing and Whitefish Bay.
-40-
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Chlamydomonas globosa, a green alga, was the second most abundant species
at Eagle Harbor in the spring.
Zooplankton
The crustacean zooplankton of Lake Superior are generally dominated by
diaptomids (Diaptomus sicilis and 13. ashlandi) the cyclopoid Cyclops
bicuspidatus thomasi, and the cladoceran Bosmina longirostris (Patalas, 1972).
Schelske and Roth (1973) found that Diaptomus and Limnocalanus dominated the
zooplankton with Cyclops and Senecella often present but in lower numbers.
They found total zooplankton densities ranging from 1200 to 16,000 organisms/m3,
with an average of approximately 4600 organisms/m3. Selgeby (1975) described
the seasonal variation and abundance of crustacean zooplankton in Lake Superior
during 1971 and 1972. He found C_. bicuspidatus thomasi, D_- ashlandi, D_- silicis,
L_. macrurus and Senecella present throughout the year.
Rotifers of Lake Superior were reviewed by Watson (1974) and studied by
Nauwerck (1972) who collected about 20 taxa during the summer and autumn of 1970.
Kellicottia longispina, Conochilus unicornis and Polyarthra vulgaris were the
most common species with Gastropus stylifer, Collotheca mutabillis, and
Conochiloides dossuarius also often found. Nauwerck suggested the following
trophic classifications: Kelicottia, Notholca, and Synchaeta are generally
coldwater oligotrophic genera; Conochilus, Collotheca, and Gastropus are
warmwater oligotrophic genera; Polyarthra and Asplanchna are mestrophic genera;
and Brachionus, Filinia and Keratella are coldwater eutrophic genera.
The most common crustacean zooplankton in 1974 were the cladoceran,
Bosmina longirostris, the calanoid copepods, Diaptomus oregonensis and D_.
minutus, and the cyclopoid copepod Cyclops bicuspidatus thomasi. In the fall,
three additional species were abundant: the cladocerans, Hoi opedium gibberum
and Daphnia retrocurva, and the calanoid copepod Epischura lacustris. In the
spring Diaptomus sicilis was also commonly found (Table A-lTT
During 1974, mean numbers of crustacean zooplankton ranged from 859/m3
at Isle Royale in June to 7874/m3 at Carp River in the fall, with a lakewide
mean of 2270 /m3 (Table A-12). About 40 percent of those collected were
nauplii, 10 percent unidentified cyclopoid copepods and 15 percent unidentified
diaptomid copepods.
Senecella calanoides and Limnocalanus macruru-s are two oligotrophic relic
species found in 1974. S_. calanoides was found in low numbers (one to nine
organisms/m3) during both sampling periods at Isle Royale, and in the spring at
Carp River and Whitefish Point. L_. macrurus was found at 8 of 12 locations,
ranging from one to nine organisms/m3^It occurred during both sampling periods
at Eagle Harbor, Big Bay and Grand Marais. The abundance of L_. macrurus is
probably under-estimated since it generally occurs below 50-m depths (Patalas
1972, Conway, 1977) which were not sampled in this study. It was not abundant
in the nearshore areas sampled and, when found, was generally at depths greater
than 12 meters.
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Diaptomus minutus was common at all stations at all locations in this
survey except station 1. Although Watson (1974) stated that EL minutus
was excluded from shallow waters, it was identified from samples taken at
depths less than five meters in 1974.
Patalas (1972) suggested that the ratio of calanoid copepods to cyclopoid
copepods plus cladocera was inversely related to increasing nutrients in the
oligotrophic Great Lakes. In 1974, substantially lower ratios of calanoid/
(cyclopoid plus cladocera) occurred in September than in June (35 percent vs.
67 percent) at every location except Lower Portage Entry and Isle Royale. The
only location that did not have at least 50 percent calanoid copepods in the
spring was Lower Portage Entry (28 percent), which may indicate nutrient
enrichment at this location. Isle Royal e had a higher percentage (66) of
calanoids in the fall. If Isle Royale is considered apart from other Michigan
nearshore waters, the 1974 data indicate Michigan's nearshore Lake Superior
waters are enriched during late summer. This enrichment appears to be a
natural characteristic of nearshore waters resulting from seasonal increases
in water temperature and nutrient runoff from adjacent land and atmospheric
inputs.
The numbers of rotifers in the nearshore Lake Superior waters during the
summer of 1974 were highly variable. The location means for rotifers ranged
from 401 and 451 rotifers/m3 at Isle Royale in August and June, respectively,
to 5201/m3 at Carp River during June.
The most common rotifers at all locations were Asp!.anchna, Keratella,
Filinia and Polyarthra. Kellicottia, Braehionus and Conochilus were usually
present but in lower numbers. Gastropus was found at three of twelve locations
but only in the fall. The occurrance of Polyarthra, Asplancha. Filinia and
Kerate1_1a_, which Nauwerck (1972) classified as mesotrophic and coldwater
eutrophic genera, indicates some enrichment in the nearshore waters. However,
the frequent occurrence of Kellicottia reflects the general oligrophic nature
of these waters. Although there were no statistically significant differences
between early-and late-summer rotifer numbers, some species changes were noted.
Differences within stations did occur. Rotifers were more abundant (3 to 10
times) at stations nearest the shore at all locations except at Ontonagon during
both seasons, and at Isle Royale in fall. The mean number of rotifers found
at station 1 was 3250 +_ 3049/m3 while the mean of all other stations was 920 +_
652/m3.
Benthic Macroinvertebrates
Only a limited amount of benthic macroinvertebrate literature is available
for Lake Superior, most of which has been reviewed by Cook and Johnson (1974).
Hiltunen (1969), Adams and Kregear (1969), and Schelske and Roth (1973) found
benthic macroinvertebrate assemblages in the profundal zone of Lake Superior
typical of deep cold oligotrophic lakes. Organisms found generally belonged to
four major taxa: Oligochaeta, Chironomidae, Sphaeriidae, and the glacial
marine relict amphipod, Pontoporeia affinis. £_. affinis was reported by Henson,
-43-
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et al_. (1973) to be the single most important benthic organism in Lake Superior.
They believed any reduction in P_. affinis numbers could disrupt the entire
ecosystem of the lake.
The oligochaetes, chironomids and sphaeriids have only recently been
taxonomically described at the generic or specific level by Brinkhurst (1964,
1965), Brinkhurst, et al_. (1966, 1968, 1971), and Hiltunen (1969). The
lumbriculid, Stylodrilus heringianus; the tubificids, Limnodrilus profundicola,
Tubifex kersleri americanus, Peloscolex variegatus, P_. superiorensis and
Rhyacodrilus montanus; and many Naididae are restricted to oligotrophic lakes
such as Lake Superior (Hiltunen, 1969, Cook and Johnson, 1974). S_. heringianus
is the dominant profundal oligochaete in Lake Superior and the naidid Stylaria
lacustris is an important component of the deep-water benthos of Lake Superior
(Adams and Kregear, 1969).
Typical oligotrophic chironomid assemblages include Heterotrissocladius,
Protanypus, Paracladapelma, Monodiames^, Potthastia cf. longimanus,
Paralauterborniel 1 a, Stictochironomus and Micropsectra. Heterotrissocladius
and Protanypus were reported to be the primary profundal chironomids in
Lake Superior (Schelske and Roth, 1973 and Henson, 1966).
Because the Sphaeriidae are difficult to identify, the ecological
significance of this group has not been adequately documented. Pisidium
conventus and Sphaerium nitidum are coldwater species (Brinkhurst, et al.
1968) and have been reported in western Lake Superior (Hiltunen, 1969).
Studies of benthos in nearshore harbor and embayment areas of Lake
Superior have been conducted primarily to assess the impact of municipalities,
pulp mills and mining operations (German 1967, 1968; German and Pugh, 1969;
Henson et_ al_. 1973; Winter 1968; MWRC 1957, 1969; and Aquatic Research Group
1975). Since most studies are in impacted areas, the distribution and ecology
of the benthos in unaffected nearshore waters are not adequately known. Cook
and Johnson (1974) stated the nearshore fauna had a greater species diversity
than the profundal zone due to a wider range of microhabitats in the nearshore
waters. Although Pontoporeia affinis is the dominant profundal species, in
the nearshore waters, the fauna is dominated by oligochaetes and chironomids
(Hiltunen 1969).
During 1974, twelve locations along Michigan's Lake Superior shoreline
were sampled for benthic macroinvertebrates. These locations were specifically
chosen because of their particular characteristics. Areas of high water quality
were chosen to serve as background references for areas which were impacted.
From 1 to 13 stations per location were sampled, the number depending on prior
knowledge of direct or indirect discharges to Lake Superior from industry or
municipalities. In 1975, Carp River (Marquette Harbor) was sampled at four
stations and Munisinq Harbor was resampled at four stations.
Five Taxonomic groups Pontoporeia affinis, sphaeriids, oligochaetes,
chironomids and "other" taxa were used to identify major changes in benthic
macroinvertebrates in the areas. The assumption was made that the presence of
high numbers of P_. affinis and sphaeriids, coupled with low numbers of total
organisms (number/mz) would indicate background or non-impacted areas (Table 6). Con
-44-
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versely, impacted areas would have lower densities of P_. affinis and
sphaeriids as well as large numbers of total organisms/m2. Tables A-13 and
A-14 summarize the benthic macroinvertebrate data collected from the nearshore
waters of Lake Superior during 1974 and 1975.
With one exception (Whitefish Point), the background locations were dom-
inated by oligotrophic indicator organisms, principally Pontoppreia affinis; the
oligochaetes Stylodrilus heringianus, enchytraeids and Aulodrilus limnobius; the
naidids, Stylaria lacustris and Piguetiella michiganensis; and the chironomids
Heterotrissodalius, Micropsectra, Paracladapelma and Monodiamesa. Other taxa
included the pelecypod, Pisidium; representatives of the trichopteran family,
Hydroptiliidae; the ephemeropteran, Baetis; and the coleopteran, Macronychus
glabratus. Only P_. af finis and Pisidium were common at all background stations
(Figure 5).
The background locations had low numbers of taxa and organisms, generally
averaging less than 1000 organisms/m2, except at Whitefish Point which averaged
3757 organisms/m2. The benthic macroinvertebrates at Whitefish Point were
dominated by oligotrophic indicator forms such as Pontoporeia affi nis, Stylodrilus
heringianus, Monodiamesa, and Heterotrissocladius. Increased numbers of organisms
(3757 mean total organisms/m2) and taxa (46), including pollution-tolerant forms
such as Peloscolex ferox and Limnodrilus hoffmeisteri may indicate nutrient
enrichment or an unusually rich habitat at this location.
The benthic macroinvertebrate communities at the impacted locations had
significantly higher numbers of taxa, more than 1,000 organisms/m2, and were
dominated by oligochaetes and chironomids with a corresponding decrease in
Pontoporeia affinis and sphaeriids. One exception was Upper Portage Entry. The
benthic community at this location was dominated by chironomids (Chironomus and
Polypedilum); had low numbers averaging 134 organisms/m2, and had few taxa (18).
This impact is probably due to past Coppermine wastes (Aquatic Research Group
1975).
Lower Portage Entry and Carp River appear to be areas of moderate nutrient
enrichment as shown by changes in the numbers and taxa of oligochaetes and
chironomids, as well as the greater abundance of Pontoporeia affinis and other
taxa. Compared to the background locations, these two locations have more taxa,
greater numbers/m2 and more pollution-tolerant forms. Enrichment at Lower
Portage Entry has not excluded intolerant forms, indicating less enrichment to
this oligotrophic system than at the Carp River location.
Marquette Harbor, Munising, Ontonagon and Presque Isle were dominated by
oligochaetes and midges, both in numbers of taxa and organisms/m2. The
Marquette Harbor samples indicated a degraded benthic macroinvertebrate community
near the shore that improved further offshore. The mean total number of organisms
was 2639 organisms/m2, dominated by oligochaetes (78 percent). The breakwall
at this site restricts open lake water from mixing, and increases the accumulation
of organic materials and nutrients contributed by the Dead River. The resulting
enriched conditions are reflected i,n the large percentage of oligochaetes (48%)
and elevated numbers of organisms (x = 6706/m2) at station 1 at the Dead River
mouth. Lakeward of the breakwall, the community was less degraded as shown by
-47-
-------
lower densities of pollution-tolerant forms (Cryptochironomus, Cricotopus and
Polypedilum cf. laetum) at station 3 and the dominance of Pontoporeia affinis
(47 percent), one of the primary oligotrophic indicator species, at station 4.
In 1974, Munising had the highest density (10,540 organisms/m2) of all Lake
Superior locations. The benthic community offshore from the Anna River was
dominated by pollution-tolerant forms, reflecting inputs of nutrients from
municipal sewage and paper mill waste discharges and restricted water circulation.
The benthic community throughout the bay was dominated by oligochaetes
(Peloscolex ferox, Aulodrilus pluriseta and immature oligochaetes), the isopod
Asell us and the chironomids Procladius, Ablabesmyia, Microtendipes, and
Tanytarsus. Intolerant species such as Stylodrilus heringianus, Pontoporeia
affinis and Heterotrissocladius were present but not dominant. Benthic
macroinvertebrates were sampled in 1975 at four stations, two of which were in
the degraded zone indicated by the 1974 data, and two further lakeward but
within the bay. Similar organisms were present in the duplicated 1974 stations.
The river-mouth station was severely degraded with 88 percent oligochaetes
(23,864/m2) and no intolerant forms were found. Stations further offshore
showed improved conditions, with oligochaetes ranging from 19 to 22 percent
(247 to 410/m2), and pollution-intolerant forms (F\ affinis and sphaeriids)
comprising 74 to 88 percent of the organisms. The total numbers of organisms
were relatively low, ranging from 1293 to 2058 organisms/m2.
In 1957, the benthic community in South Bay at Munising was biologically
depressed (MWRC, 1957). In 1968, as in 1974 and 1975, offshore stations had
diverse benthic communities, while stations in the vicinity of Kimberly Clark
and the mouth of the Anna River (which receives the effluent from the municipal
wastewater treatment plant) had a very limited benthic community dominated by
pollution-tolerant midges (Procladius, Prodiamesa) and oligochaetes
(Limnodrilus) (MWRC, 1968). Comparisons between the 1974-75 benthic data and
data collected over the past 18 years indicated no apparent improvement of
the benthic macroinvertebrate community in Munisinq Harbor.
Ontonagon and Presque Isle did not have as many taxa (67 and 84,
respectively) or numbers of organisms/m2 (2682 and 2847, respectively) as were
found at Munising, but oligochaetes and chironomids dominated the benthic
community at the former locations. The benthic macroinvertebrates at Ontonagon
included naidids (Uncinais uncinata, Piquetiella michiganenis), tubificids
(Limnodrilus hoffmeisteri, Aulodrilus limnobius and immature forms), low numbers
of the limbriculid, Stylodrilus heringianus, and chironomids (Potthastia,
Stictochironomus, Chironomus, Monodiamesa tuberculata and Heterotrissocladius).
The amphipod, Pontoporeia affinis, although present at all but one station, was
not abundant.
The benthic macroinvertebrate community at Presque Isle was dominated by
oligochaetes and chrionomids, with Pontoporeia affinis and Heterotri ssocladi us
abundant. Oligochaetes present at nearly all stations included Stylodrilus
heringianus, Arcteonais lomondi, Piquetiella michiganensis, Uncinais uncinata,
Limnodrilus hoffmeisteri,Peloscolex ferox and immature forms. The isopod
Asellus was also present in low numbers. Chironomids present at nearly every
-48-
-------
station included Procladius, Monodiamesa depectinata, M_. tuberculata,
Potthastia cfr. longimanus, Heterotrissocladius, Chironomus, Paracladapelma,
Phaenopsectra, PolypediTurn, and Tanytarsus.
Contaminants in Fish
Excessive levels of metals and organic contaminants have been found in fish
of the Great Lakes. Elevated mercury levels in fish from Lake St. Clair led to
a ban on commercial fishing in that lake. High polychlorinated biphenyls (PCB),
DDT and dieldrin concentrations in lake trout, coho salmon and chubs have
resulted in a ban on commercial fishing of certain age classes of these species
in Lake Michigan. High levels of DDT and PCB have been identified as the cause
of reduced reproductive success of fish, fish-eating birds and animals; as a
result, tolerance limits for various contaminants have been set by both the
United States and Canadian governments to protect public health and wildlife.
The Canadian Food and Drug Directorate (CFDD, 1972) set the following
maximum allowable levels for heavy metals in freshwater animal products:
arsenic, 5 mg/kg; lead, 10 mg/kg; copper, 100 mg/kg; mercury, 0.5 mg/kg; and
zinc, 100 mg/kg. The United States Food and Drug Administration (USFDA) has
also set the tolerance-limit for human consumption of mercury in edible fish
fillets at 0.5 mg/kg. A court ruling raised this concentration to 1.0 mg/kg
mercury as of June 1978.
The GLWQA has an objective for total PCB level in whole fish of 0.1 mg/1 for
the orotection of fish-eatinq birds and animals, and 1.0 mg/kg for DDT in whole
fish (GLWOA 1978). The USFDA has set a tolerance-limit of 5.0 mg/kg for PCB and
5.0 mg/kg for total DDT in edible fish tissues. A tolerance limit of 2.0 mg/kg
for PCB in edible fish tissue was set by the Canadian Food and Drug
Directorate in 1972. The tolerance-limit recommended by the USFDA for
dieldrin and the Great Lakes Water Quality Agreement for aldrin plus
dieldrin in fish flesh is 0.3 mg/kg (GLWQA 1978).
Concentrations of heavy metals in Great Lakes fish have been discussed by
Lucas et a]_. (1970), Uthe and Bligh (1971), Beal (1974), and Thommes, et al_.
(.1972). Thommes et_ aj_. (1972) reported mercury concentrations in burbot and
lake trout which exceeded the pre-June 1978 USFDA action level of 0.5 mg/kg.
In Lake Superior there are two distinct subspecies of lake trout which are
recognizable from exterior morphological characteristics. Within the context
of this report Salvalinus namaycush namaycush are described as lean lake trout
and Salvalinus namaycush siscowet are described as fat lake trout.
In Lake Superior, concentrations of heavy metals were generally low.
Copper, zinc, lead and cadmium concentrations were well below GLWQA criteria
for all fish (Table 7). However, over 40% of the lake trout analyzed in
1974 exceeded the pre-January 1978 USFDA action level for mercury. Only 3.0%
exceeded the new action level of 1.0 mg/kg. Actual location means were
variable, ranging from 0.01 mg/kg in mottled sculpins to 0.71 mg/kg in lake
trout.
-49-
-------
Table 7. Mean concentrations of selected metals in Lake Superior fish, 1974 and 1975. Entries exoressed
as mg/kg vot weight basis for edible fillets, except for mottled sculpin which were composites
of gutted fish. All species, except mottled sculoins were collected in 1974.
Location
Whitefish Point
Grand Marais
Muni sing
Marquette
Big Bay
Lower Portage Entry
Bete Grise
Copoer Harbor
Upper Portage Entry
Black River
Isle Royale
Little Girls Pt.
Whitefish Point
Grand Marais
Munising
Harquette
Presque Isle
Big Bay
Huron Bay
L 'Arise
Lower Portage Entry
Grand Traverse Bay
Copper Harbor
Eagle Harbor
Eagle River
Uoner Portage Entry
Carver's Bay
Big Iron River
Fish Species
Lake trout
Fat lake trout
Lake trout
Herring
Lake trout
Fat lake trout
Whitefish
Lake trout
Fat lake trout
Whitefish
Lake trout
Herring
Lake trout
Whitefish
Lake trout
Lake trout
Lake trout
Fat lake trout
Fat lake trout
Lake trout
Herring
Whitefish
Mottled sculpin
Mottled sculpin
Mottled sculpin
Mottled sculpin
Mottled sculpin
Mottled sculpin
Mottled sculpin
Mottled sculpin
Mottled sculpin
Mottled sculpin
Mottled sculoin
Mottled sculpin
Mottled sculnin
Mottled sculpin
Mottled sculpin
Mottled sculnin
N
13
10
14
3
22
19
2
25
12
3
23
6
15
6
12
12
5
17
12
3
1975
18
28
13
10
13
18
28
27
20
22
30
13
13
27
40
28
Mercury
mg/kg
0.30
0.50
0.39
0.18
0.44
0.71
0.04
0.32
0.64
0.07
0.26
0.12
0.21
0.16
0.36
0.45
0.33
0.58
0.58
0.22
0.61
0.06
0.04
0.03
0.07
0.02
0.04
0.05
0.05
0.02
0.02
0.02
0.03
0.02
0.04
0.05
0.03
0.03
Copoer
mg/kg
0.54
0.35
0.36
0.35
0.40
0.29
0.56
1.1
0.82
0.82
0.66
0.95
0.75
0.66
0.72
0.90
1.22
O.S3
0.90
Zinc
mg/kg
3.80
2.87
3.11
0.34
3.44
3.12
6.16
22.45
8.0
11.90
11.70
12.3
12.15
11.73
11.86
11.92
12.45
11.81
12.13
Lead
mg/kg
0.39
0.45
-
0.26
0.30
0.36
0.28
0.25
0.39
0.23
1.5
1.4
1 1.2
1.3
1.4
1.2
1.3
1.5
1.2
1.4
Cadmium
mg/kg
0.02
0.02
0.03
0.02
0.02
0.04
0.02
0.22
0.05
0.09
0.07
0.12
0.10
0.08
0.10
0.11
0.13
0.11
0.11
-50-
-------
Table 7. (continued)
Location_ Fish Species
Mercury
Copper
Zinc
Lead
Cadmium
Black River
Isle Royale
mg/kq mg/kg mg/kg mg/kg mg/kg
Mottled sculpin 9 0.03
Mottled sculpin - 0.06 1.3 34.8 0.15 0.05
GLWQA Tolerance Limit (whole fish) 0.5
Pre-Jon. 1978 USFDA Tolerance Limit (edible portions) 0.5
New USFDA Tolerance Limit (edible portions) 1.0
100
100
10
= No sample analysis for this parameter
-51-
-------
Pesticides and other organic contaminants in fish have been discussed by
Reinert 0970), Swain (1975) and the Great Lakes Environmental Contaminants
Survey (GLECS) (1973), 0974) and (1975). Reinert (1970) reported DDT and
dieldrin levels of various Lake Superior fish species and the GLECS reports
showed the concentrations of dieldrin, DDT, PCB and mercury. Swain discussed
persistent organics and heavy metals in nearshore western Lake Supieror
(Swain, 1975).
In Lake Superior, concentrations of chlordane, methoxychlor, benzene,
hexachloride (BHC), hexachlorobenzene (HCB), hexachlorobutadiene (HCBD,
dibutyl-n-phthalate (DBP), diethyl hexylphthalate (DEHP) and polybrominated
biphenyl (PBB) were below detection levels in all samples collected (Table 2).
However, low concentrations of chlordane, BHC, HCB, HCBD and DBP were detected
by Swain using more sensitive techniques (Swain 1975).
Average dieldrin concentrations were well below USFDA action levels for lake
trout, and whitefish collected in 1974 and mottled sculpins collected in 1975.
In 1974, total DDT was present in all samples with location averages
ranging from 0.17 mg/kg in herring at Munising to 5.10 mg/kg in fat lake trout
at Black River Harbor.
The mean total DDT concentration for fat lake trout at Black River Harbor
exceeded the USFDA 5.0 mg/kg action level (Table 8), as did some individial
fat and lean lake trout from the Lower Portage Entry, Copper Harbor, Marquette
and Munising. The highest value was 26.02 mg/kg in a fat lake trout collected
near Munising. Although nearly 20% of the fat lake trout values exceeded the
USFDA limit, total DDT was significantly lower in lean lake trout even though
they exceeded the GLWQA at more than half of the locations sampled (Table 8).
Average total DDT concentrations in lean lake trout ranged from 0.47 to
3.31 mg/kg similar to other authors (Swain 1975).
Whitefish and herring also had low levels of total DDT in 1974 and only
herring at Lower Portage Entry exceeded the GLWQA objectives of 1.0 mg/kg
total DDT.
Mottled sculpins collected in 1974 contained very low levels of total DDT
ranging from below detection to 0.32 mg/kg. This maximum concentration is
less than 10 percent of the current USFDA action level for DDT and the
upper levels found in fat lake trout. DDT residues were not detectable in
sculpins from L'Anse, Lower Portage Entry or Huron Bay. Carver's Bay,
Eagle River and Whitefish Bay were the only locations where DDT levels in
sculpin were over 0.20 mg/kg. Sculpins from these three locations, as well
as those from Big Bay, also contained measurable dieldrin concentrations.
In 1974, mean PCB levels were highly variable between species, ranging
from 8.37 mg/kg in fat lake trout at Black River to 0.22 mg/kg in herring
from Munising. Concentrations within species were variable, as indicated
by lean lake trout from Lower Portage Entry, where 7 of 15 lake trout had
less than detectable PCB levels while others in the same location ranged
as high as 6.81 mg/kg PCB. Grand Marais, Big Bay, Bete Grise and Little
Girls Point were the only locations where no fish exceeded the tolerance
-52-
-------
Table 8. Mean concentrations
Entries expressed as
composites of gutted
Location
Whitefish Point
Grand Marais
Munising
Marquette
Big Bay
Lower Portage Entry
Bete Grise
Cooper Harbor
Uooer Portage Entry
Black River
Isle Royale
Little Girls Pt.
Whitefish Point
Grand Marais
Munising
Marquette
Presque Isle
Big Bay
Lower Portage Entry
Grand Traverse Bay
Copper Harbor
Eagle Harbor
Eagle River
Carvers Bay
Big Iron River
Slack River
of selected organic contaminants in
mg/kg we* weight basis for edible
fish. All species except mottled
1974
Fish Soecies
Lake trout
Fat lake trout
Lake trout
Herring
Lake trout
Fat lake trout
Whitefish
Lake trout
Fat lake trout
Whitefish
Lake trout
Herring
Lake trout
Whitefish
Lake trout
Lake trout
Lake trout
Fat lake trout
Fat Lake trout
Lake trout
"lottled sculpin
Mottled sculpin
Mottled sculpin
Mottled sculpin
Mottled sculpin
Mottled sculpin
Mottled sculpin
Mottled sculoin
Mottled sculpin
Mottled sculoin
Mottled sculpin
Mottled sculpin
Mottled sculpin
Mottled sculpin
fi
13
10
14
3
22
19
25
12
3
23
6
15
6
12
12
5
17
12
3
1975
18
28
18
10
13
18
20
22
30
13
13
40
23
9
Lake Superior fish, 1974
fillets. Mottled sculoin
sculnin were collected in
Total
DDT PCB
mg/kg
0.74
1.82
1.03
0.17
3.31
3.46
0.19
1.35
3.89
0.29
0.85
1.18
1.35
0.69
2.44
0.98
1.51
5.11*
2.10
0.47
0.23
0.10
0.03
0.06
0.03
0.09
0.09
0.02
0.04
0.10
0.43
0.45
0.05
0.02
mg/kg
0.98
3.18
1.61
0.22
3.11
5.10*
0.27
1.95
5.05*
0.31
1.13
1.03
1.06
0.89
2.99
1.17
2.09
8.37*
2.33
1.25
0.44
0.29
0.09
0.15
0.15
0.14
TR
0.09
0.15
0.46
0.37
U.09
and 1975.
were
1974.
Dieldrin
mg/kg
0.03
0.05
0.02
0.01
0.04
0.04
0.19
0.02
0.08
0.02
ND
0.02
0.08
0.02
0.02
0.03
0.07
ND
0.03
0.02
0.01
0.03
0.03
GLWQA objective (whole fish)
USFDA Tolerance Limit (edible oortions)
ND = not detectable
= ,10 sample analysis for this parameter
1.0 0.1 0.3**
5 0 5.0 0.3
* = exceeds USFDA tolerance limit
TR = trace
** = aldrin plus dieldrin
-53-
-------
limit. Mean location PCB levels exceeded the 5.0 mg/kg tolerance limit in
fat lake trout at Munising, Marquette, and Black River (Table 8) (Figure 6).
In 1974, the lakewide averaae for lake trout was 3.57 mq/kq PCB.
The highest mean PCB levels in lean lake trout occurred in Munising and
Copper Harbor, but these locations were not significantly different from the
other location. While fish containing high levels of PCB were found
at these two locations, there were also many fish collected which had low
levels. PCB concentrations in whitefish and herring from all locations were
lower than lake trout, averaging 0.54 mg/kg.
In 1975, low PCB levels were found in mottled sculpin with mean values
ranging from less than detection to 0.46 mg/kg. Sculpins at four locations,
Carver's Bay, Eagle River, Grand Marais, and Whitefish Point had levels
higher than 0.20 mg/kg (Table 8), while levels at all other locations were
very low.
The levels of DDT and PCB were generally higher in the larger fish, as
demonstrated by a linear regression analysis performed on lake trout data.
Lake trout were used because they were captured at nearly all locations:
and in most size groups. Other authors CSwain 1975) have indicated that
bioaccumulation may be more related to exposure experience and lipid
content than to fish size.
An analysis of the trends of these fish contaminants based on the GLECS
data were completed only for lake trout in Lake Superior in 1974, 1975 and
1976. Insufficient data for other fish collected during tnese years prevented
analysis. Fat and lean trout were tested separately in 1975 and 1976 but not
in 1974, when those subspecies were not separately coded and subsequently
could not be differentiated by the computer.
Lean lake trout contained significantly lower concentrations of dieldrin
than fat lake trout based on combined 1975 and 1976 data (Table 9). Dieldrin in
lean lake trout was significantly higher in 1976 and 1975, while fat lake trout
dieldrin levels were not significantly different in these two years. None of
the average concentrations exceeded the U.S. FDA action level, but 7.7
percent of the individual lean lake trout sampled in 1976 exceeded this value.
The trend showed an increase in dieldrin in Lake Superior lake trout based on
data from 1974 through 1976.
Concentrations of DDT in fat lake trout were significantly greater than
in lean lake trout based on combined 1975 and 1976 data (Table 10). Lean
lake trout DDT concentrations were significantly greater in 1976 than in 1975
and in 1976, 11.5% of lean lake trout exceeded the U.S. FDA action level.
There were no significant differences in the DDT concentrations in fat
lake trout between 1975 and 1976. However, 44.2 and 19.0 percent of the
individual fish exceeded the U.S. FDA action level in 1975 and 1976,
respectively. The average concentration of DDT in fat lake trout in 1975 was
3.35 mg/kg above the action level while the 1976 mean value was below this
value (Table 10). The data showed an increase in DDT concentrations in Lake
Superior lake trout based on data from 1974 to 1976.
-54-
-------
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-57-
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Concentrations of PCB in fat lake trout were significantly higher than
lean lake trout for the combined 1975 and 1976 data (Table 11). Lean lake
trout PCB levels were significantly higher in 1976 than the 1975 values.
Only 2.5 and 15.4 percent of the individual fish analyzed exceeded the U.S.
FDA action level in 1975 and 1976, respectively. There were no significant
differences in fat lake trout during 1975 and 1976, but mean values exceeded
the U.S. FDA action level in 1975 and approached this value in 1976. In
addition, 67.3 and 47.6 percent of the fat lake trout exceeded this level during
the respective years. Maximum values ranged up to 61.56 mg/kg in 1975. The
data indicated no increase or decrease in the PCB concentrations in Lake
Superior lake trout from 1974 through 1976.
Fat lake trout had significantly higher mercury concentrations than lean
lake trout based on the combined 1975 and 1976 data (Table 12). Concentrations
of mercury in lean lake trout were significantly higher in 1976 than in 1975.
Fat lake trout were not significantly different, but 9.6% of the fat lake
trout collected in 1975 exceeded the U.S. FDA action level. The data showed
that mercury concentrations in Lake Superior lake trout were significantly
higher in 1976 than 1974. Concentrations of mercury in 1975 were significantly
lower than both other years. None of the yearly means exceeded the 1.0 mq/kq
U.S. FDA action level for mercury, but 3.0 and 2.8 percent of the individual
fish collected in 1974 and 1975, respectively, exceeded this value.
-58-
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Summary
In general, Michigan's nearshore waters of Lake Superior were of high
quality. Temperature, dissolved oxygen and nutrient profiles varied little
with depth, indicating thorough mixing.
In relation to the other Great Lakes, low levels of dissolved solids,
chlorophyll a^ and phosphorus were present, while nitrate and silica concen-
trations were high. Heavy metal concentrations were well within the criteria
for aquatic life and drinking water, although in exceptions various parameters
were noted at Big Bay, Grand Marais, Lower Portage Entry and Eagle Harbor.
Organic chemicals were generally not detectable in Lake Superior nearshore
waters except for diethylhexel-phthalate at one Carp River station. Low con-
centrations of DDT and DDE were detected everywhere, but PCBs were not detectable
in any water samples, apparently because detection limits were not low enough.
Scans for gross beta and gamma emissions in water indicated very low activity or
levels below the minimum detectable activity.
Nearshore sediments were generally uncontaminated except at Munising.
Sediment contamination at Ontonagon, Upper Portage Etnry, Eagle Harbor, Presque
Isle, and Isle Royale was due to past mining activities and/or natural deposits
of metals. Organic contamination at Ontonagon, Carp River, and Munising was
primarily due to past wood and paper mill industries and municipal waste treat-
ment plant discharges.
Biological populations also reflected high water quality. The nearshore
Lake Superior waters were relatively free from fecal contamination except the
river mouths at Carp River and Munising. Standing crops of phytoplankton were
low, as indicated by algal densities and chlorophyll
-------
Elevated levels of these contaminants were evident in fat lake trout, with
higher concentrations found in larger fish at Munising, Black River, Marquette,
Isle Royale and Copper Harbor. Concentrations of PCB in most lake trout exceeded
the GLWQA objectives. Mercury in fat lake trout also exceeded the pre-
January, 1978 USFDA guidelines and the GLWQA objectives at all locations where
they were collected. Approximately 10 percent of the fat lake trout also
exceeded the new USFDA action level of 10 tug/kg.
The GLECS reports were available for limited trend analysis. The most
recent GLECS data for lake trout, which was the only species in Lake Superior
with sufficient information, covered a period from 1974 to 1976. Two sub-
species were found (fat and lean) and fat lake trout had significantly higher
concentrations of all contaminants than did lean lake trout.
In Lake Superior the concentrations of dieldrin, DDT and mercury in the
lean and fat lake trout combined were significantly higher in 1976 than 1974,
the years for which data is available. Concentrations of PCB however, did
not change significantly during this same period.
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SECTION VI
LAKE HURON
Introduction
Lake Huron is the third largest of the Great Lakes in volume (3535 km3)
and second largest in surface area (59,570 km2). It ranks second in water-
shed population density and first in total shoreline length (5088 km)
(Chandler, 1964). The chemical composition of Lake Huron waters is largely
determined by two factors. First, Lake Huron is a large mixing basin for
the outflows from Lakes Superior and Michigan. Schelske and Roth (1973)
report conservative element concentrations from northern Lake Huron which
approximate a mixture of 40 percent Lake Michigan and 60 percent Lake Superior
waters. Second, large amounts of dissolved solids enter lower Lake Huron
through Saginaw Bay via the Saginaw River, significantly increasing concen-
trations of dissolved materials in the lower lake.
The general flow of water in Lake Huron is from the Straits of Mackinac
and the St. Marys River southeast along the Michigan coast to the outlet at
Port Huron (Figure 7), although winds create short-term flow modifications
(Ayers, 1962). Saginaw Bay currents generally move past Port Austin and
south to Port Huron, but occasionally switch to the north toward Thunder Bay
(Schelske and Roth, 1973). Many relatively shallow bays and harbors in
Lake Huron are isolated from the main lake, resulting in distinct physical and
chemical characteristics due to inputs from river mouths, other localized
watershed influences, and the lack of water circulation.
The physical and chemical characteristics of Lake Huron generally indicate
oligotrophic waters. Lake Huron generally has low specific conductance, low
total dissolved solids, high transparency, high dissolved oxygen, and uniform
reactive phosphate throughout the water column. A trend toward mesotrophy
has been reported by Schelske and Roth (1973) and Dobson, et^ al_. (1974).
Schelske and Roth (1973) found somewhat reduced silica and nitrate concen-
trations in surface waters relative to bottom waters. They also found that
chlorophyll a^ levels in Saginaw Bay averaged nine times greater than
concentrations at other Lake Huron locations. Dobson ejt al_. (1974) found
that productivity was increasingly seasonally variable, indicating mesotrophic
conditions. They considered Saginaw Bay to be eutrophic and limnologically
distinct from Lake Huron.
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Physical and General Water Chemistry
Mean temperatures during 1974 ranged from 12.0° to 18.8°C in the spring
with maximum temperatures recorded at Saginaw Bay. Fall mean temperatures
ranged from 9.8° to 19.8°C. In 1975 mean location temperatures ranged from
8.8° to 21.2°C, with the highest temperatures (9°C greater than any other
location) again found at Saginaw Bay. No stable thermal stratification was
observed during either year.
Annual mean DO concentrations in 1974 ranged from 9.1 to 11.6 mg/1, with
an overall lake mean of 10.4 +_ 0.8 mg/1. Differences in oxygen concentrations
between sampling periods and between locations were not significant. Dissolved
oxygen was negatively correlated with some conservative ions, selected
nutrients, temperature and chlorophyll a_. Mean DO concentrations were similar
in 1975, ranging from 10.7 to 13.3 mg/1, with a lakewide average of 11.0 +_
0.9 mg/1. Dissolved oxygen concentrations were near saturation levels at
all locations during both years, with orthograde depth profiles which reflect
oligotrophic waters.
In 1974, mean pH levels ranged from 7.8 to 8.2; however, in 1975, equip-
ment failures prevented accurate pH measurement. There were no consistent
variations with season, and differences between locations were not significant.
Depth profiles reflected more alkaline waters at the surface due to uptake
and incorporations of C02 by phytoplankton.
Mean total dissolved solids (IDS) concentrations ranged from 92 to
136 mg/1 in 1974. No significant differences were found between sampling
periods, but there were significant differences between locations. Background
locations.were not significantly different from each other. The impacted areas
(Cheboygan, Alpena, Saginaw Bay and Harbor Beach) were not significantly
different, but TDS concentrations at Alpena were substantially higher than at
the background areas. The primary sources of TDS in Alpena were the Thunder Bay
River and the Abitibi Corporation. The Lake Huron mean TDS concentrations
(.111 mg/1) for the background locations were approximately twice those for
the Lake Superior mean (54 mg/1). Lake Huron background values indicate a general
southerly increase in TDS throughout the nearshore Lake Huron waters.
Thus, a general north to south increase in TDS and a corresponding decline
in Lake Huron water quality appeared to occur and may be related to the
southward increase in population and industrial activity.
During 1975, a similar TDS relationship existed, but the north to south
trends were not as evident. The lakewide average was 127 +_ 19 mg/1, with
individual location means ranging from 88 to 144 mg/1. Total dissolved solids
were strongly correlated with alkalinity, hardness, conductivity, calcium
and magnesium; however, TDS were less correlated with phosphorus, ammonia, sodium,
-65-
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potassium, sulfate, silica, chlorophyll ^ and COD, and negatively correlated
with nitrate.
In 1974, mean conductivity values ranged from 154 to 225 ymho/cm with
a higher value in the spring than the fall. Significant differences were
found between locations. Significantly lower values at Detour reflected
the input of Lake Superior water from the St. Marys River, while those
industrialized areas located at river mouths (Alpena, Cheboygan and Saginaw Bay)
had significantly higher values. The increased conductivity values in the
southern portion of the lake correspond to the observed change in IDS, both
indicating that inputs from the industrialized watershed of Cheboygan, Alpena,
and Saginaw Bay have a cumulative effect on Lake Huron water quality.
Conductivity correlations were similar to those for IDS except for non-signif-
icant correlations with chlorophyll a^ and nitrate.
Chlorides and sulfates also reflected the north to south trends reported
for total dissolved solids and conductivity. The location means for 1974
ranged from 3.8 to 9.9 mg/1 and 10.8 to 20.4 mg/1 for chlorides and sulfates,
respectively, with sulfate concentrations highest at Alpena, and chloride
highest at Saginaw Bay. Chlorides were moderately correlated with copper,
magnesium, TDS and chlorophyll a^ and negatively correlated with dissolved
silica. Sulfates were also moderately correlated with copper, magnesium, TDS,
and chlorophyll a, in addition to phosphorus, nitrogen and COD, and negatively
correlated with nitrates. In 1975, location means from chlorides and
sulfates ranged from 4.0 to 16.0 mg/1 and 11.0 to 22.0 mg/1, respectively,
while lakewide means were 7.0 +_ 4.0 mg/1 chlorides and 15.0 +_ 3.0 mg/1 sulfate.
The Saginaw Bay location mean was significantly higher than other location
means for both ions in 1975.
Nutrients and Chlorophyll a^
In 1974, nitrate concentrations in Lake Huron were lower and more variable
than the Lake Superior levels. Mean N03-N concentrations at individual locations
ranged from 0.140 to 0.264 mg/1. Nitrate levels were significantly lower in
the surface waters than near the bottom, but there were no differences between
spring and fall data. Nitrate was negatively correlated with the major ions,
dissolved silica, alkalinity and hardness, and was positively correlated with
total nitrogen. In 1975, N03-N means ranged from 0.142 to 0.280 mg/1, with a
lakewide mean of 0.226 +_ 0.040 mg/1. Cheboygan, Alpena and Saginaw Bay had
significantly lower concentrations than the other locations during both
years. The mean concentration for these three locations was Q.154 + 0.012 mg/1
in 1974, and 0.165 + 0.021 mg/1 in 1975, while the 1974 and 1975 mean for the
five background locations was 0.232 + 0.019, and 0.256 + 0.018 mg/1, respectively.
The mean N03-N concentration for the latter five locations was similar to the
lakewide average for Lake Superior (0.269 + 0.022 mg/1). Apparently, increased
primary production in the vicinity of Cheboygan, Alpena, and Saginaw Bay is
sufficient to reduce nitrate concentrations, but not to low enough concentrations
to limit algal growth.
In 1974, mean ammonia concentrations ranged from 0.002 to 0.029 mg/1 with
a lakewide mean of 0.011 +0.007 mg/1, approximately 1.5 times greater'than the
corresponding Lake Superior value. Only 8 percent of the ammonia values were
below the detection limit (0.001 mg/1). Differences between locations
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and sampling periods were not significant, although Alpena, Saginaw Bay and
Harbor Beach did have numerically higher concentrations. Ammonia was
correlated with nutrients, chlorides and turbidity, and negatively correlated
with dissolved oxygen.
In 1975, the average lakewide ammonia concentration was 0.005 +_ 0.005 mg/1,
with individual location means ranging from below detection to 0.016 mg/1 at
Alpena, which had the only elevated concentration in 1975.
Total nitrogen annual means ranged from 0.32 to 0.47 mg/1 in 1974, with a
lakewide average of 0.43 +_ 0.06 mg/1. There were no locations or sampling
period differences in 1974. In 1975, location means ranged from 0.32 to
0.71 mg/1, with a lakewide mean of 0.44 + 0.12 mg/1. These concentrations were
similar to Lake Superior's lakewide mean (0.40 + 0.003 mg/1). Values for the
Saginaw Bay location were significantly higher than other locations in 1975.
At Saginaw Bay, most of the nitrogen occurred at organic nitrogen.
In 1974, reactive orthophosphate levels in Lake Huron were slightly higher
and more variable than Lake Superior levels. Mean concentrations at individual
locations ranged from 0.003 to 0.007 mg/1 P with highest concentrations at
Alpena. Approximately 35 percent of the values were below the detection level
(0.002 mg/1). In 1975, mean concentrations ranged from less than 0.001 to
0.004 mg/1 with a lakewide mean of 0.002 + 0.001 mg/1, which reflects good
water quality. Saginaw Bay had the highest reactive orthophosphate concen-
tration, with Alpena second highest at 0.003 mg/1.
Mean total phosphorus concentrations in 1974 ranged from 0.004 to 0.022 mg/1,
with significant difference between locations. Alpena had the highest
concentration, followed by Saginaw Bay and Harbor Beach. Harbor Beach is
periodically affected by water masses from Saginaw Bay.
The National Eutrophication Survey (EPA, 1974) reported that total phos-
phorus concentrations less than 0.010 mg/1 were indicative of oligotrophic
waters. Concentrations between 0.01 and 0.02 mg/1 were mesotrophic and waters
with total phosphorus over 0.020 mg/1 were eutrophic. Therefore, according to
these classifications Alpena (0.028 mg/1) was eutrophic, and Saginaw Bay
(0.018 mg/1) and Harbor Beach (0.012 mg/1) were in the mesotrophic range.
Total phosphorus was moderately correlated with chlorophyll a^, calcium, sulfate,
TDS, organic N, ammonia, turbidity, conductivity and COD and less correlated
with reactive silica, alkalinity and hardness. During 1975, location means
ranged from 0.003 to 0.032 mg/1, with a lakewide mean of 0.009 +_ 0.010 mg/1.
In 1975, Saginaw Bay (0.032 mg/1) would be considered eutrophic and Alpena
(0.018 mg/1) would be considered mesotrophic.
Reactive silica levels in Lake Huron in 1974 were lower and more variable
than silica levels in Lake Superior. The mean location concentrations ranged
from 0.7 to 1.7 mg/1. The Lake Huron lakewide mean (1.0 +_ 0.4 mg/1) was
approximately one-half the Lake Superior mean concentration. Fall levels were
lower than spring levels, even though there were no significant differences
between sampling periods, locations or depths. Reactive silica was moderately
correlated with calcium, magnesium, TDS and alkalinity, less strongly
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correlated with reactive and total phosphorus, organic nitrogen, conductivity
and hardness, and negatively correlated with nitrate and chlorides (Table A-5).
In 1975, mean reactive silica concentrations ranged from 0.6 mg/1 in the
southern portion of the lake to 2.0 mg/1 at the northern locations, with a
lakewide average of 1.2 ^0.5 mg/1. Thus, a north to south decrease in silica
was evident in 1975.
In 1974, mean chlorophyll a, ranged from 1.7 to 10.6 yg/1 with a lakewide
mean of 4.8 +_ 4.7 yg/1. Significant differences occurred between locations,
but not between sampling periods. Alpena had the highest mean chlorophyll a_
concentration (10.6 yg/1) which was significantly higher than the mean concentra-
tions for three locations north of Detour, Cheboygan and Presque Isle.
A significant north to south increase in chlorophyll a^was observed during
1974. A linear regression of the control location mean chlorophyll ^values
on the approximate distance from Detour on the north to south axis was
significant. Chlorophyll a_ was strongly correlated with COD, potassium,
sulfate, TDS and hardness; moderately correlated with other major ions, total
phosphorus, organic nitrogen, turbidity, alkalinity and temperature; and
negatively correlated with dissolved oxygen (Table A-5).
In 1975, mean chlorophyll a_ ranged from 1.8 to 11.3 yg/1 with a lake wide
mean of 4.5 +_ 3.2 ug/1. Cheboygan and Alpena had elevated concentrations of
6.6 and 11.3 yg/1, respectively. The Saginaw Bay location was not included in
the calculations of these means, because the three stations there were within
the immediate influence of the river, as reflected by their chlorophyll a^
concentration of 60.5 +^46.8 yg/1. The influence of sampling locations within
the Bay on chlorophyll a_ concentration is indicated by the 1974 values which
were exceptionally low compared to our 1975 data and that of other researchers
(Smith 1977; IJC 1977). The 1974 stations were located in the upper middle and
outer portion of the bay. Data from both years indicate significant enrichment
at Alpena and Saginaw Bay. Enrichment at Alpena is primarily the result of
discharges from the Abitibi Corporation, while the enrichment of Saqinaw Bay
is due to numerous point (e.g. Saginaw River) and non-point sources.
Heavy Metals in Water
Heavy metals were very low in Lake Huron waters during 1974 and 1975. In
1974, with the exception of Saginaw River, total arsenic, cadmium ajnd mercury
were at or just above their detection levels of 1.0, 2.0 and 0.2 yg/1,
respectively. In 1975, arsenic and mercury concentrations were consistently
just above the detection level (0.2 and 0.02 yg/1, respectively) at all locations
but below the criteria to protect aquatic life. Cadmium concentrations were
lowest in the northern portion of the lake and increased from Alpena south to
Harbor Beach. At Lexington, the southern most location, cadmium returned to
background levels. None of the values approached the lowest aquatic life
criterion for cadmium of 0.4 yg/1.
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Selenium was below the detection limit (1.0 yg/1 at all stations in
1S74, and was not analyzed during 1975.
Most total chromium levels were below detection (1.0 yg/1) with 2.0 yg/1
being the highest concentration reported in 1974. In 1975, the detection
level for total chromium was lowered to 0.3 yg/1, with all location means less
than 1.0 yg/1, well below the 50 yg/1 criterion for public drinking water, and
100 yg/1 for aquatic life (U. S. EPA 1976).
Individual copper values ranged from below detection (1.0 yg/1) at
Presque Isle and Alpena in the spring of 1974, to 28 yg/1 at Tawas in the fall.
Location means ranged from 1.0 yg/1 at Lexington, to 13 yg/1 at Tawas, with
a lakewide annual mean of 3.6 +_ 2.9 yg/1. There were no significant dif-
ferences between locations or sampling periods. In 1975, location means ranged
from 0.7 to 3.4 yg/1, with a lakewide mean of 1.6 +_ 0.8. No values exceeded
the criterion of 1000 yg/1 for public drinking water (U. S. EPA 1976). Detour,
Cheboygan and Tawas exceeded the recommended GLWQA 5.0 yg/1 objective in the
spring of 1974, as did Presque Isle in the fall of 1974; however, no annual
means exceeded this objective in either 1974 or 1975, except at Tawas in 1974.
In 1974, means for iron ranged from 12 to 228 yg/1, with a lakewide average
of 68 +_ 63 yg/1. While no sampling period differences were found, significant
iron dTfferences occurred among locations, with Harbor Beach values being
significantly higher than Harrisville, Tawas and Cheboygan. Individual samples
were highly variable, but no location means exceeded the water quality criterion
of 300 yg/1 for iron in drinking water (U. S. EPA 1976). Collection methods
partially account for the elevated values reported for Harbor Beach. During
1975, location means ranged from 8 to 24 yg/1 with a lakewide average of
18+6 yg/1.
Manganese was found above the detection limit (1.0 yg/1) in all Lake Huron
samples during 1974 with location means ranging from 2 to 15 yg/1, and a lake-
wide mean of 5 +_ 4 yg/1. The Alpena mean was significantly higher than that of
Harrisville, but other location or sampling period differences were not signif-
icant. Individual samples at Alpena exceeded the 50 yg/1 criterion for manganese
in public water supply (U. S. EPA 1976). In 1975, manganese detection limits
were reduced to 0.05 yg/1, with all location means less than 2.0 yg/1.
In 1974, lead was frequently below the detection limit (5.0 yg/1). Although
location means ranged up to 8 yg/1, most were below detection. No statistical
analysis was performed because of the lack of detectable values for lead. In
1975, lead detection levels were lowered to 0.2 yg/1, with location means ranging
from 0.4 to l.OPg/1. All values during both years were much lower than the
20 Pg/1 GLWQA objective for Lake Huron.
Total nickel levels (5 yg/1) were detectable in only five individual samples
taken during 1974: three at Harbor Beach, and one each at Alpena and
Presque Isle. No values exceeded the 25 yg/1 criterion for the protection of
aquatic life (GLWQA 1978). In 1975, location means ranged from 0.8 to 1.4 yg/1
total nickel, indicating no excessive nickel levels in Lake Huron waters.
7inc concentrations were variable in 1974, with location means ranging from
5 yq/1 at Harrisville to 29 yo/1 at Detour in the fall, with a lakewide'average
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of 10 +_ 6 yg/1. The Detour mean approached the 30 yg/1 criterion for zinc
(IOC, 1977). There is no known source of zinc at this location. In 1975,
zinc concentrations were substantially lower, with means ranging from below
1.3 to 4.9 yg/1 and a lakewide average of 2.5 j^l.O yg/1. There were no
elevated values at Detour in 1975, indicating no long-term sources at that
location.
Organic Chemicals in Water
In 1974, organic chemicals in Lake Huron were at very low levels or below
detection levels. ODD and DDE were below detection levels (0.001 ya/1)
at all locations. DDT was detected in five samples, ranging from 0.002 to
0.004 yg/1. Detour, Cheboygan, and Presque Isle each had one sample with
measurable DDT levels, and Lexington had two. Polychlorinated biphenyls
(PCB, Arochlor 1242, 1254 and 1260) were found above detection levels of
0.01 yg/1 in single samples at Alpena (0.02 yg/1) and Harrisville (0.08 yg/1).
No known sources of PCB occur at these locations, although both areas have
industries which used PCB in the past. However, the concentrations of PCB
were below detection in samples taken prior to this lake survey in these
industrial effluents.
Dieldrin was above the detection limit (0.001 yg/1) in only one sample from
Detour, and diethylhexel phthalate was found above detection levels (1.0 yg/1)
at Presque Isle (2.6 yg/1), Harrisville (2.0 yg/1) and Saginaw Bay (1.4 yg/1).
Phthalates are used as plasticizers in innumerable products, and samples may
have been contaminated by collecting and processing equipment. Also, low
levels of phthalates are relatively common in wastewater discharges.
In 1975, all concentrations of organics in water were reported as below the
limits of detection due to interference during the laboratory analysis, as
explained in the Lake Superior section of this report.
Radioactivity
Samples for radioactive analysis were collected only in the spring and fall
of 1974. Based on the gamma scan, zinc 65, zirconium 95, niobium 95, cesium 137,
cobalt 60 and manganese 54 were all below the minimum detectable activity levels
of 30, 13, 13, 15, 15 and 13 pCi/1, respectively. Gross beta activity was also
low ranging from orve to five pCi/1 with a lakewide average of 2.7 pCi/1.
Sediment Chemistry
In 1974, the nearshore sediments at background locations in Lake Huron had
low levels of pesticides, PCB, metals, nutrients and COD. However, measurable
total DDT residues were found in samples at two background areas, Presque Isle
(16.3 yg/kg) and Harrisville (3.0 yg/kg). Lexington exceeded EPA dredge spoil
criteria for arsenic but this result was based only on one sample.
Impacted areas generally had higher concentrations of all sediment contam-
inants than background areas. However, mercury, cadmium and selenium were
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below levels of detection, and lead was within background levels at all
locations.
Cheboygan sediments averaged 72 yg/kg total DDT. Cheboygan also
exceeded the EPA dredge spoil criteria for oils and grease at two stations,
and TKN and zinc at one station.
The Alpena stations had total DDT concentrations ranging from 3.9 to
30.7 yg/kg and exceeded EPA dredge spoil criteria for TKN, oils and grease,
and arsenic.
Detectable levels of PCB were found only in the sediments at Harbor Beach
(18 to 27 yg/kg) where these values interfered with the analysis of pesticides.
Total Kjeldahl nitrogen, COD, oil and grease, zinc, arsenic, nickel and iron
in the Harbor Beach sediments were above the EPA dredge spoil criteria.
There were also elevated concentrations of copper, manganese and chromium.
These heavy metal concentrations have been attributed to Hercules, Incorporated,
whose sludge contained these metals.
In 1975, location means for sediments sampled at Calcite and the open
waters of Saginaw Bay were within EPA dredge spoil criteria. However, the
sediments near the mouth of the Saginaw River would be classified as grossly
contaminated.
Bacteria
The bacteriological quality of the nearshore waters of Lake Huron was
high with most locations sampled relatively free from fecal contamination,
except in the near to shore areas surrounding municipal and industrial dis-
charges.
Bacterial densities at the background locations in the spring (July) and
fall of 1974 were generally below detection levels except at the two southern
most locations, Harrisville and Lexington. Geometric mean total coliform counts
at these two locations in the fall ranged from 141 to 741 organisms/100 ml
(Table 13). Similar increases in fecal coliform or fecal strepococci were not
observed.
Elevated bacterial densities were observed at all impacted locations.
Bacterial densities in Saginaw Bay were elevated only during the fall of
1974 with densities below detection levels except for total coliforms at
station 1 (Table 13).
Geometric means for replicated samples from river-mouth stations exceeded
the Michigan criterion for fecal coliforms at Cheboygan and Alpena during the
1974 spring sampling period (Table 13).
Alpena was the only location with consistently elevated total coliform
counts during both 1974 sampling periods. Spring counts exceeded 1000/100 ml
as far as 1000-m southeast of the river mouth, and counts greater than 500/
100 ml were found at stations 2000-m from the river mouth. The fall cruise
showed a similar offshore gradient but the mean coliform count found in the
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river mouth exceeded 15,000/100 ml (Table 9). Fecal coliform counts were above
200/100 ml only in the spring and fecal streptococci were not above 30 counts/
100 ml at any time.
Phytoplankton
Few studies of the phytoplankton communities in Lake Huron have been
undertaken. In a 1971 survey, Vollenweider et_ al_. (1974) noted low biomass in
the offshore stations with the diatoms Cyclotella, Tabellaria, Stephanodiscus,
Melosira, and Synedra dominating the community. At times, various phyto-
flagellates and cryptomonads, including Cryptomonas erosa and Rhodomonas
minuta, accounted for up to 20 percent of the biomass.
Schelski ejt a]_. (1974) described phytoplankton assemblages in western
Lake Huron. They found populations north of Saginaw Bay were dominated by
diatoms including Cyclotella stelligera, C_. michiganiana, C_. comta, C_.
gperculata, C_. ocellata, Frag ill aria crotonensis, Rhizosolenia gracil is and
Asterionella formosa while only £. stelligera and C^. michiganiana were
dominant south of Saginaw Bay.
The phytoplankton community in Michigan's nearshore waters of Lake Huron
were sampled during spring and fall of 1974. The species list for Lake Huron
included approximately 300 phytoplankton taxa with diatoms generally dominant
(Table A-15). The diatoms, primarily Tabellaria fenestrata, Fragillaria
crotonensis, Cyclotella glomerata, C^. comensis, and Asterionella formosa were the
dominant algal group during June. Abundant species other than diatoms included
Rhodomonas minuta, Dinobryon sp., Chrysosphaerella longispina and Aphanocapsa
delicatissima.
The phytoplankton data from Alpena and Lexington indicated the presence of
nutrient enrichment at these locations (Figures 8 and 9). Alpena had very high
phytoplankton standing crops in the spring, about 4 times the lakewide mean,
with samples dominated by a large bloom of the blue-green algae Dactylococcopsis
fascicularis (Table A-16). The total numbers of algae at Alpena were also above
the lakewide mean in September, when collections were dominated by the eutrophic
diatoms, Melosira granulata and Fragillaria crotonensis, although there was a
shift back to more oligotrophic forms, especially Tabellaria fensestrata and
Cyclotella glomerata.
Lexington would be classified as eutrophic based on the high standing crop of
phytoplankton. The fall samples at this location were dominated by Fragill aria
crotonensis and Cyclotella comensis, with total numbers about twice the lakewide
mean.
Algal abundance at the northern Lake Huron stations were one-third to one-
half the lakewide mean. There appeared to be an overall north to south increase
in algal abundance in Lake Huron, but this trend was masked by within-location
variability.
Statistical comparisons made between the composite and the 5-meter grab
samples indicated no significant differences (P<0.05) between either species
-74-
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SAMPLING
LOCATIONS
Figure 8 Nearshore phytoplankton standing crop, Lake Huron, 1974
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found, or mean number of algal units. Most locations showed no major species
changes with depth. Generally, from two to five species were abundant at a
station with only relatively minor ranking changes, although Saginaw Bay and
Tawas varied from this pattern. At Tawas, Ulpthrix, a green alga indicative
of eutrophic conditions, was abundant close to shore (station 1), but not at
stations further offshore. In Saginaw Bay, a decrease occurred from the inner
to the outer bay in the blue-green alga, Oscillatoria. and the green alga,
Ulothrix. Nutrient dilution and distance from shore appears to have caused
species shifts at these impacted locations.
Zooplankton
Only a few studies have been published describing the populations of
Lake Huron zooplankton. Schelske and Roth (1973) found Diaptomus, Bosmina,
and Cyclops to be most abundant in Lake Huron north of Saginaw Bay, with many
genera represented. Ratal as (1972) found 23 crustacean taxa with Cyclops
bicuspidatus thomasi, Diaptomus sicilis, D_. ashi andi and D_. minutus the most
abundant copepods, while Hoi opediurn gibberurn and Bosmina longirostris were the
most abundant cladocerans. Nauwerck (1972) reported approximately 30 species
of rotifers from Lake Huron with Kellicottia, Notholca, Synchaeta, Polyarthra,
Conochilus, Keratella, and Gastropus stylifer common in the open lake. Watson
(1974) reported eighteen common species of rotifers in Lake Huron.
Zooplankton were collected in the spring and fall of 1974. In the spring,
mean zooplankton densities averaged 13,444 +_ 14,331 organisms/m3. In the fall,
densities decreased to 4545 j^ 2164 organisms/m3, but no statistically significant
differences were found between seasons. This pattern was similar at both back-
ground and impacted locations, and although impacted locations appeared to have
greater numbers, no significant differences (P<0.05) were found between locations.
The ratio of calanoid copepods to cyclopoids and caldocerans has been related to
nutrient enrichment in the Great Lakes (Patalas, 1972) with a large ratio (a
large percentage of calanoid copepods) reflecting low nutrients. This ratio was
over 0.65 during the spring at Detour, Presque Isle and Harrisville, while the
other locations had ratios below 0.55. In the fall, Cheboygan and Alpena had
ratios below 0.30, indicating significantly enriched conditions.
The most abundant species were the cladoceran Bosmina longirostris, the
calanoid copepods Diaptomus oregonensis and EL minutus and the cyclopoid copepod
Cyclops biscuspidatus thomasi (Tables A-17 and A-18). In addition, Diaptomus
sicilis, Epischura lacustris and Daphnia retrocurva were present at most loca-
tions and occasionally reached relatively high numbers. Holopedium gibberum
was found at all locations in the fall (ranging from 9 to 17/ma) but occurred only
atDetour and Presque Isle in the spring (7/m3 and 9/m3, respectively). Daphnia
retrocurva was present at all locations in the fall and at 7 of 9 locations in
the spring.
Low numbers of Ceriodaphnia lacustris, generally considered a summer
plankter, were found during June at Lexington, and in the fall at Cheboygan,
Alpena and Tawas City. While not abundant, it appears to be widespread in
Lake Huron at locations having extensive reaches of shallow water. Other
crustacean zooplankton numbers were also generally higher at station 1.
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Daphnia galeata mendptae and Bpsmina coregoni were found only at station 1
in the fall. Diaptomus ashi andi, however, was not found at station 1 at
any location.
Eight genera of rotifers were identified with Keratella, Polyarthra,
Asplanchna, and Filinia abundant at all locations in all samples. Another
commonly occurring form, Gastropus, was found at 3 of 9 locations in soring, and
2 of 9 in the fall, but no location had Gastropus during both sampling periods.
The total numbers of rotifers varied considerably, from 381/m3 at Detour, to
9494/m3 at Harbor Beach. There were no significant differences between spring
and fall abundances. A significant difference was noted between rotifer
densities at station 1 (nearest to shore or the river mouth) and the other
stations further offshore. This difference occurred even when no river was
present, such as at Presque Isle, where the mean for station 1 was 2822/m3
while the mean was 661/m3 for stations further offshore. Since no difference
in community structure was apparent at the generic level, the shallow nearshore
areas appear to provide a more productive habitat for rotifers.
Benthic Macroinvertebrates
During the past two decades, several authors have reported on the benthic
macroinvertebrate communities in Lake Huron. Significant accounts of the com-
munities in the main basin are those of Teter (1960), Schuytema and Powers (1966),
Schelske and Roth (1973), Shrivastava (.1974), and Mozley (1975). Schneider
et al. (1969) surveyed the benthic community in Saginaw Bay, and Brinkhurst
TT969) reported on oligochaetes from the same samples. Quantitative comparisons
with older studies may not be valid due to dissimilarity of collection tech-
niques. In earlier studies, usually only one sample per station was collected
with no estimate of variance given. For this reason, results from older studies
in the vicinity of stations sampled in 1974 and 1975 were only qualitatively
compared.
Cook and Johnson's (1974) review of the benthic literature showed that the
open waters of Lake Huron are dominated by Pontoporeia affinis, oligochaetes,
chironomids and sphaeriids. Mozley (1975) reported that P_. af finis, Stylodrilus
heringianus and Enchytraeidae were the most numerous taxa at depths greater than
30 m with Peloscolex variegatus and Heterotrissocladius cf. subpilosus also
typical members of the profundal benthic fauna.
The taxonomy of the benthic communities of the Great Lakes is incomplete
and knowledge of the ecology of many important species is limited, preventing
the development of a complete list of indicator species. Recent papers
discussing nearctic chironomids as indicators of lake typology may clarify
the present chironomid lake classification scheme (Saether, 1975a, Saether, 1975b)
In 1974, Michigan's nearshore waters of Lake Huron were sampled at four
background locations (Detour, Presque Isle, Harrisville and Lexington) and four
impacted locations (Cheboygan Alpena, Tawas and Harbor Beach). During 1975,
an additional background location (Calcite) was evaluated, and two impacted
locations (Alpena, Harbor Beach) were re-evaluated (Figure 10).
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Total benthic communities at the background locations ranged from
397 organisms/m2 at Calcite, to 7573 organisms/m2 at Presque Isle. The
communities were dominated by chironomids and oligochaetes, except at
Presque Isle where the total population of 7573 organisms/m2 was dominated
by Pontoporeia affinis and sphaeriids (Table 14).
The sample at Detour, collected at 23-m, had a community of 1083
organisms/m2, 81 percent of which were the oligotrophic indicators
Stylodrilus heringianus and Heterotrissoclad^us cf. changi. Other abundant
species included Monodiamesa cf. tuberculata, Protanypus, Micropsectra,
Paracladopelma cf. camplolabis and Tanytarsus (Tab!es A-l 9 and A-20).
The benthic collections at Presque Isle were unique because of an excep-
tionally high density of organisms (7573 organisms/m2). Pontoporeia affinis
and Pisidium formed 79 percent (6011 organisms/m2) of the total population.
The samples were collected from depths 9 to 27-m deeper than the average depth
at other locations, which may account for the high densities. Teter, (1960) and
Schelske and Roth (1973) found similar densities of P o n to pore i a aff i n is
in profundal samples with low numbers of sphaeriids. Shrivastava"(T974) and
Schuytema and Powers (1966) indicated that high mean densities of P. affinis
(600-800/m2) occurred between 20 and 40~m which includes the sample depth
at Presque Isle (33-m).
Chironomids and oligochaetes at Presque Isle formed only 1.7 and 18.6
percent of the total population, respectively. The oligotrophic indicator forms,
Stytodrilus heringianus and Heterotris soc1 ad i u s cf. changi, dominated these groups
but the more pollution-tolerant tubificids, Limnodrilus hoffmeisteri and
Potamothrix vejdovskyi, were also present.
The total benthic communities at the other two background locations,
Harrisville and Lexington, were 515 and 580 organisms/m2, respectively, with
communities dominated by nearly equal numbers of chironomids and oligochaetes.
The oligochaetes had a low diversity of species with Stylodrilus heringianus
abundant at both locations, but dominant only at Harrisville. Pinuetiella
michiganensis was dominant at Lexington. Unidentifiable immature tubificids
and Potamothrix vejdovskyi were also abundant at both locations.
The chironomid community at Harrisville was composed primarily of the
pollution-intolerant forms Heterotri ssocladius cf. changi, Paracladopelma
undine, Potthastia cf. longimanus, Tanytarsus, and Micropsectra, while the
chrionomid fauna at Lexington consisted of a number of pollution-tolerant forms,
Chironomus anthracinus gr., Pseudochironomus and Procladius. The primary
oligotrophic indicator species were not found at Lexington.
Calcite, located northwest of the 1974 sampling location at Presque Isle,
was a background location in Lake Huron during 1975. The total benthic pop-
ulation at Calcite averaged 397 organisms/m2 and consisted of similar numbers
of oligochaetes and chironomids. Stylodrilus heringianus was the dominant
oligochaeie (70 organisms/m2). Of the eight chironomid taxa found,
Parakiefferiella and Cricotopus were the most abundant (32 and 19/m2,
respectively) with Heterotri s soc1 ad i u s cf. changi present in low numbers (6/m2)
The amphipod Pontoporeia affTnis (6/mT] was also found.
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The four impacted locations, Cheboygan, Alpena, Harbor Beach and Tawas, had
high benthic populations (4418, 5721, 3796 and 979 organisms/m2, respectively).
The mean total abundance of benthic organisms at the four impacted locations was
3763 organisms/m2. Mean densities of oligochaetes, chironomids, P_. affinis,
sphaeriids and other taxa were 2666, 391, 4, 161 and 541 organisms/m^
respectively. Although differences occured in local benthic assemblages,
the high numbers of tubificids found at each impacted location indicated
nutrient enrichment.
Fifty-three percent of the benthic fauna at Cheboygan was comprised of
oligochaetes, chironomids and sphaeriids, (36.1, 13.0 and 3.0 percent, respect-
ively). The remaining forty-seven percent consisted primarily of isopods,
Asellus and Lirceus, and amphipods, Gammarus and Hyalella azteca. These four
taxa accounted for 37.2 percent of the total benthic community. Lirceus and
Q. azteca were the most abundant of this group, reaching maximum densities of
2552 and 2413/m2, respectively, at station 6 in 1974. The amphiood, Pontoporeia
affinis, was not found at Cheboygan.
The oligochaete community at Cheboygan contained 22 species of which 13
were tubificids. Maximum oligochaete densities (3437/m2) were found at the
mouth of the harbor, indicating significant enrichment from the river.
Unidentifiable immature tubificids dominated the oligochaete numbers, account-
ing for 60 percent of the total. Significant differences were apparent
between stations with the pollution-tolerant oligochaetes, Aulodrilus
pluriseta, Limnodrilus cervix and L_. hoffmeisteri dominant only at stations 1
and ^. both located near the mouth of the Cheboygan River and the offshore stations.
The chironomid fauna at Cheboygan was highly diverse with 31 taxa rep-
resented. The abundant species were primarily pollution-tolerant forms found
near the river mouth, including Procladius, Chironomus anthracinus gr.,
Cryptochironomus, Microtendipes, Phaenopsectra (Tribelos), Polyped'ilum scalaenum
gr., Pseudochironomus, and Tanytarsus. The pollution-intolerant forms
Heterotrissocladius, Monodiamesa cf. depectinata. Potthastia cf. longimanus
and Paracladopelma were present in very low numbers, primarily at stations
farther from the river mouth.
Both the presence of pollution-tolerant forms in high numbers and the
abundance of isopods and amphipods at the harbor mouth indicate a high degree
of organic enrichment at Cheboygan.
Tawas had a diverse assemblage of oligochaetes (19 species) and chironomids
(27 species). The oligochaete community was dominated by immature tubificids
which made up greater than 40 percent of the community, Peloscolex ferox, a species
tolerant of moderate pollution, and Stylodrilus heringianus, generally considered
an oligotrophic species, were also dominant. Peloscolex ferox, was common
at all stations, and the dominant species at station 1, whereas Stylodrilus
heringianus was dominant only at station 7, further offshore.
The most abundant chironomids found at Tawas, Pseudochironomus and
Cryptochironomus gr., are considered pollution-tolerant. The oligotrophic forms
Heterotrissocladius and Paracladopelma were found in relatively low numbers only
at stations furthest from shore indicating water quality improvement with dis-
tance from the river mouth. The diversity and predominance of mesotrophic
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and eutroohic benthic forms demonstrates the influence of Saginaw Bay on the
water quality at Tawas.
Historical data for Thunder Bay at Alpena reflect changes occurring in
the nearshore waters of Lake Huron as a result of organic enrichment. In
1957, a highly diversified benthic community containing many pollution-
intolerant forms with 12,260 organisms/m2, was found. By 1965, this community
had been almost exclusively replaced by one of pollution-tolerant forms with
only 2260 organisms/m2 (MWRC, 1965a). In 1974, the mean benthic densities
ranged from 2223 to 12,333 organisms/m2, with an overall average of
5721 organisms/m2. In 1975, mean densities ranged from 1610 to 7731 organisms/
m2. Oligochaetes comprised 72 percent of the total population during 1957, 89
percent during 1965, 95 percent during 1974 and in 1975, drooped to 60 oercent
(Figure 11). In 1974, maximum oligochaete densities of more than 12,000/mz
were found near the mouth of the Thunder Bay River, with unidentifiable im-
mature tubificids accounting for 71 percent of oligochaete numbers. The most
abundant of the 23 oliqochaete species found during both years were Nais,
Aulodrilus americanus, A. piqueti, A_. pluriseta, Limnodrilus hoffmeisteri,
Pel os col ex ferox, P_. multisetosus and Potamothrix vejdovskyi, all considered
pollution-tolerant organisms.
Chironomids remained relatively constant at 3 to 5 percent, during the
past 18 years, until in 1975 they increased to 33 percent. In 1975, these
chironomids considered primarily of the pollution-tolerant forms, Cryptochironomus,
Procladius, Tanytarsus, and Harn_ish_T_a. In 1974, chironomid species consisted of
Procladius, Chironomus anthracinus gr., Chironomus fluviatilis gr., Chironomus
plumosus, Cryptochironomus and Tanytarsus.
Sphaeriids which accounted for 18 percent of the total population during
1957, decreased to 2, 1 and 6 percent during 1965, 1974 and 1975, respectively.
The percentage of "other taxa" showed a similar decrease from 5 to 1 percent
since 1957. The oligotrophic indicator species Pontoporeia af finis, Stylodrilus
heringianus and Heterotrissocladius were present in very low numbers in 1974,
and then only at the outermost stations. S_. heringianus was found at very low
numbers only at two intermediate stations in 1975.
Harbor Beach was the only impacted location without a major river discharge,
but the harbor was confined by an extensive breakwall. In 1974, the benthic
community was sampled at seven stations within the harbor and one station about
350 meters west of the main entrance; in 1975, samples were taken at two
stations inside the harbor and one outside the harbor.
In 1974 and 1975 benthic communities were dominated by oligochaetes
(87.8 and 86 percent, respectively), with the pollution-tolerant tubificids,
Limnodrilus cervix, L_. maumeensis, and L_. hoffmeisteri abundant. The pollution-
tolerant chironomids, Chironomus anthracinus and Chironomus plumosus gr. were
the most abundant midges.
In 1974, benthic densities at stations within the harbor ranged from 1973/m2
to 7189/m2, while densities outside the harbor were only 386 organisms/m2.
Although the station further offshore was also dominated by pollution-tolerant
forms and would be classified as mesotrophic, the low populations and the limited
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presence Stylodrilus heringianus, Peloscolex variegatus and Paracladopelma
undine suggest improved water quality outside the harbor.
The Harbor Beach total communities showed no consistent pattern based on
1958, 1965, 1974 and 1975 samples, with 5343, 989, 3796 and 5657 organisms/m2,
respectively. The percentages of oligochaetes and chironomids in 1958 and
1974-5 were similar, 86 and 88 percent for oligochaetes, and 13 and 12 percent
for chironomids. The 1965 survey had 77 percent oligochaetes and 22 percent
chironomids (MWRC, 1965b). Pontoporeia affinis was absent, and sphaeriids and
"other" taxa never exceeded 1 percent of the total population during any of
the surveys.
The 1965 report concluded that water quality had decreased since 1958 even
though there was a decrease in the percentage of oligochaetes (MWRC, 1965b).
Based on the 1974 and 1975 results there appears to have been little change in
the Harbor Beach benthic community since the 1965 study.
Contaminants in Fish
Heavy metal concentrations werexgenerally very low in all areas of Lake
Huron for all species of fish. No values exceeded the CFDD or new U.S. FDA
tolerance limits. The only metal to approach these levels in 1974 samples was
mercury, while all other metal concentrations were less than 10 percent of the
tolerance limits. The highest mean mercury values were in yellow perch at
all locations (Table 15) with the maximum individual mercury value of 0.49 mg/kg
in a yellow perch from Hammond Bay.
All the metal levels in yellow perch during 1974 were low. Mercury ranged
from 0.18 to 0.40 mg/kg with mean values for Thunder Bay and Tawas Bay of 0.26 +_
0.04 mg/kg and 0.27 +_ 0.03 mg/kg, respectively. Values for Harbor Beach and
Lexington were slightly higher (0.33 and 0.34 mg/kg, respectively). Areas south
of Saginaw Bay appeared to have sliglitly higher mercury values than areas to the
north, but no significant differences were found for mercury concentrations in
yellow perch or whitefish.
Pesticides and other organic contaminants in all species were generally low
(Table 16). In 1974 chlordane, lindane, methoxychlor, hexachlorobenzene,
hexachlorbutadiene, dibutyl-n-phthalate, diethylhexylphthalate and polybrominated
biphenyl were not detectable in any fish analyzed at detection levels shown
in Table 2.
Concentrations of dieldrin were well below the U.S. FDA action level in all
samples during 1974 and 1975. There were no significant location differences in
dieldrin concentrations for any of the fish tested.
Total DDT during 1974 and 1975 were generally found above detection levels
with the highest location mean concentration (0.97 mg/kg) occurring in a chinook
salmon from Alpena. The lowest location mean was in yellow perch from Hammond
Bay, where total DDT was not detected in any sample. The salmonids, including
whitefish, had mean levels greater than 0.2 mg/kg, while percids (yellow perch
and walleye) means were below 0.07 mg/kg.
-86-
-------
Table 15. Mean concentrations of selected metal contaminants in
Lake Huron fish, 1974 and 1975. Entries expressed as
mg/kg wet weight basis for edible fillets.
1974
Location
Hammond Bay
Alpena
Tawas
Harbor Beach
Lexington
Hammond Bay
Alpena
Tawas
Fish Species
Brown trout
Yellow perch
Rainbow trout
Walleye
Whitefish
Brown trout
Chinook salmon
Yellow perch
Whitefish
Whitefish
Yellow perch
Yellow perch
Lake trout
Yellow perch
Yellow perch
GLWQA objectives (for whole fish)
Pre-Jan. 1978 USFDA
(edible portion)
Action Level
New USFDA Action Level
Mercury
mg/kg
0.13
0.31
0.10
0.17
0.04
0.13
0.22
0.15
0.03
0.03
0.34
0.33
1975
0.15
0.26
0.27
0.05
0.05
1.0
Copper
mg/kg
0.74
0.56
0.61
0.28
0.64
0.33
0.37
0.31
0.24
0.29
0.27
100
Zinc
mg/kg
3.46
4.60
3. 73
3.80
3.59
2.90
4.69
7.70
7.12
,
8.12
7.64
100
Lead
mg/kg
0.11
0.26
0.07
0.23
0.71
0.10
0.18
0.40
0.32
0.77
7.64
10
Cadmium
mg/kg
0.03
0.10
0.03
0.30
ND
0.01
0.03
0.03
0.03
0.04
0.03
ND = not detectable
--- = no sample analysis for this parameter
-87-
-------
Table 16. Mean concentrations of selected organic contaminants in Lake Huron
fish, 1974 and 1975. Entries are expressed as rug/kg wet weight
basis for edible fillets.
1974
Location
Hammond Bay
Alpena
Tawas
Harbor Beach
Lexington
Hammond Bay
Alpena
Tawas
GLWQA objectives
Fish Species
Brown trout
Yellow perch
Rainbow trout
Walleye
Whitefish
Brown trout
Chinook salmon
Yellow perch
Whitefish
Whitefish
Yellow perch
Yellow perch
Lake trout
Yellow perch
Yellow perch
(whole fish)
USFDA action level (edible portions'
Total
DDT
0.57
ND
0.32
0.03
0.26
0.50
0.97
0.03
0.35
0.12
0.13
0.05
1975
0.81
0.04
0.07
1.0
) 5.0
PCB
1.13
ND
0.94
ND
ND
1.10
2.30
ND
0.34
0.22
0.03
0.13
1.61
0.13
0.23
0.1
5.0
Dieldrin
0.02
ND
0.03
ND
0.05
0.04
0.05
TR
0.05
0.03
ND
ND
0.05
ND
ND
0.3*
0.3
ND = not detectable
TR = trace
* = aldrin plus dieldrin
-88-
-------
PCB concentrations were generally low in 1974 and 1975 in the Lake Huron
fish, with brown trout and Chinook salmon having the highest levels. The
mean for six chinook salmon from Alpena was 2.30 mg/kg, while brown trout from
Hammond Bay and Alpena had mean values of 1.13 and 1.09 mg/kg, respectively.
The U.S. FDA action level for PCB was not exceeded in any individual fish, and
yellow perch, walleye, and whitefish contained less than 1/10 of the tolerance
limit. However, all fish analyzed for PCB with the exception of yellow perch
from Harbor Beach in 1974, exceeded the GLWQA objective of 0.1 mg/kg for PCB.
Concentrations of DDT, PCB and mercury were generally higher in larger
fish as demonstrated by a linear regression analysis performed on whitefish
and chinook in 1974. Mercury was also correlated with fish length in yellow
perch. In 1975, a significant linear relationship of DDT and PCB but not
mercury or dieldrin with length was found in lake trout.
No significant location mean differences were found for PCB or DDT in
whitefish at Detour, Tawas or Lexington or in yellow perch from Detour,
Alpena, Tawas, Lexington or Harbor Beach.
An analysis of the trends of these fish contaminants based on the GLECS
data was completed for lake trout, whitefish and walleye. Lake trout data
were available from 1975 through 1978. In addition, data were available for
whitefish from 1974 and 1975 and for walleye from 1974 and 1978. In addition
to year to year comparisons, location differences were tested, but these
differences were inconclusive.
Lake trout dieldrin concentrations were significantly higher in 1976 than
1975 and 1978. All years were significantly higher than 1977 (Table 17).
Only one lake trout was above the U.S. FDA action level of 1.0 mg/kg for dieldrin.
Concentrations of dieldrin in whitefish were available only for 1974 and 1975
and no significant differences found. Walleye were only analyzed for dieldrin
in 1978. No walleye or whitefish exceeded the U.S. FDA action level for
dieldrin. The data suggest a decline in dieldrin after 1976 in lake trout based
on data from 1975 through 1978. No decline or increase for whitefish based on
1974 and 1975 concentrations was apparent.
The lake trout had significantly higher concentrations of DDT in 1976 than
1975 and 1977. The 1978 DDT concentrations were significantly lower than all
other years (Table 18). There was no significant increase or decrease in DDT
concentrations in whitefish in 1974 and 1975. The 1978 walleye had significantly
higher DDT concentrations than 1974. The 1978 concentrations increased 10 fold
over the 1974 concentrations. The data suggest a decline in DDT concentrations
in lake trout after 1976 based on data from 1975 through 1978. A small increase
in DDT concentrations occurred in walleye based on data for only 1974 and 1978.
Without data for the intervening years, trends are difficult to predict. Only
one lake trout exceeded the U.S. FDA action level of 5.0 mg/kg DDT.
The most recent data show that PCB did not significantly decline or increase
in Lake Huron lake trout from 1974 to 1978 but increased in whitefish from 1974
to 1975 (Table 19). Walleye tested only for PCB in 1978 had mean and maximum
-89-
-------
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PCB concentrations similar to those for whitefish in 1975. Only one lake
trout exceeded the U.S. FDA action level of 5.0 mg/kg PCB in 5.3 and 3.3%
of the lake trout in 1975 and 1977, respectively.
The data for mercury indicate that concentrations may have peaked in
lake trout by 1976 or 1977 based on data from 1975 through 1978 (Table 20).
Mercury concentrations did not change in whitefish from 1974 to 1975. Mercury
concentrations were significantly greater in Lake Huron walleye in 1978 than
in 1974 and appear to be approaching the U.S. FDA action level of 1.0 mg/kg.
However, without data for the intervening years, it is difficult to predict
trends.
Summary
Lake Huron is composed of water originating in Lake Superior and Lake
Michigan but its water quality is substantially affected by inputs from within
the basin. Temperature and dissolved oxygen profiles in Lake Huron varied
little with depth. The absence of thermal stratification and orthograde
dissolved oxygen depth profiles indicate a thorough mixing of the nearshore
waters. Total dissolved solids in Lake Huron averaged twice the levels of Lake
Superior with corresponding increases in chlorides and sulfates. Based on
background locations, there was a general north to south increase in total
dissolved solids, chlorides, sulfates, phosphorus and chlorophyll a^ levels
with corresponding decreases in silica levels.
Areas of lower water quality were found at Cheboygan, Alpena, Saginaw Bay
and Harbor Beach. Cheboygan had elevated suspended solids and conservative
ions while Alpena and Saginaw Bay were the major sources of phosphorus to
Lake Huron. Heavy metals were generally low with some slightly elevated levels
detected in 1974, but not in 1975. DDT, DDE and PCBs were generally below
detection levels in the Water. PCBs were found at 0.02 and 0.08 yq/1 at
Alpena and Harrisville, respectively. Wastewater surveys of industrial effluents
in the vicinity of these locations did not detect the source of these PCBs
Although scattered individual stations were above detection limits, no
location exceeded water quality criteria.
Sediment quality in the lake was good at all locations except Cheboygan,
Alpena, and especially Harbor Beach, which exceeded U. S. EPA dredge spoil
criteria for several metals and organic contaminants. Sediment oualitv was
siqnificantly worse in several of the river mouths, especially Saginaw River,
reflecting degraded water quality inputs from rivers.
Bacterial densities were generally low, except at Alpena where total coliform
counts were consistently elevated. Other areas, near municipal and industrial
wastewater discharges, occasionally exceeded criteria but most nearshore
Lake Huron waters had low or nondetectable bacterial densities.
Phytoplankton populations were dominated by diatoms although localized
blooms of blue-greens and Cryptophyta were found in the southern portions of
the lake, the very nearshore waters, and at Alpena. Zooplankton densities
-94-
-------
increased from north to south with noticable increases at impacted locations.
These locations also had a reduced proportion of calanoids, indicating enriched
conditions.
Analysis of benthic macroinvertebrate data indicated a gradual change from
oligotrophic conditions at the northern most location (Detour) to a mesotrophic
condition at the southern most location (Lexington). Species abundance was
affected by depth, bottom type and ambient water quality. Oligotrophic indicator
species characterized all background locations. The abundance of Pontoporeia
affini^s at Presque Isle was assumed to be due to the greater depth at which samples
were collected. All impacted locations had diverse, abundant, pollution-tolerant
communities, reflecting nutrient inputs from local sources.
Heavy metals in fish were low in all areas for all species and no values
exceeded USFDA tolerance limits. Organic contaminants in fish were below
detectability, except for PCB and DDT which, when found, were present in relatively
low concentrations compared to Lake Superior. The highest concentrations of PCB's
were found in chinook salmon and brown trout from Alpena, but no source was found
in wastewater surveys of industrial effluents in the vicinity. Nearly all species
collected exceeded the GLWQA objective for PCB.
The GLECS reports were available for limited trend analyses. In Lake
Huron adequate data were available for analysis of lake trout (1975-1978),
whitefish (1974 and 1975) and walleye (1974 and 1978).
In Lake Huron lake trout, dieldrin, DDT and mercury concentrations appear
to have peaked in 1976 followed by an apparent decline using the most recent
(1975-1978) data. Concentrations of PCB however, did not change significantly
from 1975 to 1978.
For whitefish, no significant changes in the concentrations of dieldrin, DDT and
mercury in Lake Huron were detected. A significant increase in PCB concentrations
in whitefish from 1974 to 1975 did occur.
In Lake Huron walleye, a significant increase in DDT and mercury
concentrations in 1978 over 1974 was observed. However, without the intervening
years data trends are difficult to predict. The maximum mercury concentration in
walleye collected in the northern portion of Lake Huron nearly exceeded the
action level. Dieldrin and PCB were not tested for in 1974 in walleye.
-95-
-------
SECTION VII
LITERATURE CITED
Adams, C. E., Jr. 1970. Summer circulation in Western Lake Superior. Proc.
13th Conf. Great Lakes Res. p. 862-879.
, and R. D. Kregear. 1969. Sedimentary and faunal environments in
eastern Lake Superior. Proc. 12th Conf. Great Lakes Res. p. 1-20.
American Public Health Association. 1971. Standard Methods for the examination
of water and wastewater. Thirteenth edition, New York. 874 p.
American Society of Testing and Materials. 1975. Annual Book of Standards,
Part 31, Water. 1975. Philadelphia. 673 p.
Anonymous. 1974. Great Lakes environmental contaminants survey. Unpublished
Report. Mich. Dept. of Ag. 41 p.
. 1975. Great Lakes environmental contaminants survey. Unpublished
Report. Mich. Dept. of Ag. 43 p.
. 1976. Great Lakes environmental contaminants survey. Unpublished
Report. Mich. Dept. of Ag. 23 p.
. 1977. Great Lakes environmental contaminants survey. Unpublished
Report. Mich. Dept. of Ag. 15 p.
. 1978. Great Lakes environmental contaminants survey. Unpublished
Report. Mich. Dept. of Ag.
Aquatic Research Group. 1975. Analysis Report: Keweenaw waterway maintenance
dredging. St. Paul Dist., U.S. Army Corps of Eng.
Ayers, J. C. 1962. Great Lakes waters, their circulation and physical and
chemical characteristics. In: Great Lakes Basin, Pub. 71 Amer. Assoc.
Advancem. Sci. p. 71-89.
Barth, E. F. 1975. Average pH Calculations. Jour. Water Poll. Cont. Fed.
47(8): 2191-2192.
Beal, A. R. 1974. A study of selenium levels in freshwater fishes of Canada's
central region. Tech. Rpt. Series No. CEN/T-74-6. Dept. of the Env.
Fish, and Marine Serv.
-96-
-------
Bedford, J. W. 1974. The use of polyurethane foam plugs for extraction of
polychlorinated biphenyls (PCBs) from natural waters. Bull. Env. Cont.
and Tox. 12(5): 622-625.
Beeton, A. M. 1965. Eutrophication of the St. Lawrence Great Lakes.
Limnol. Oceanogr. 10:240-254.
and D. C. Chandler. 1963. St. Lawrence Great Lakes. In: D. G.
Frey (ed.), Limnology in North America. Univ. of Wis. Press, Madison.
p. 535-558.
Brinkhurst, R. 0. 1964. Studies on the North American aquatic oligochaeta.
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Dole, R. B. 1909. The quality of surface waters in the United States.
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-102-
-------
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-106-
-------
Table A-3. Descriptive statistics for selected physical and chemical constituents in the
nearshore waters of Lakes Superior and Huron, 1974
Temperature (c)
Lake Superior
Black River
Outonagon
Upper Portage Entry
Lo-jar Portage Entry
Enple Harbor
Isle RojMle
Big Hr.y
i'rrsqjo Isle (Marquette)
Carp River (Marquette)
K'uiising
Gr.-md Harais
Whltefish Point
l.qke Huror
Detour
Cheboygan
Presque Isle
Alpena
Harrisville
Tawas
Saginaw'Bay
Harbor Beach
Lexington
Lake Superior
Black River
OrLoiiagon
Upper Portage Entry
Lowet Portage Entry
Eagle Harbor
Isle Koyale
Big »>
Prcsque Isle (Marquette)
Cnrp River (Marquette)
Kunising
Grand Marais
White fish Point
Lake Huron
Dec our
Cneboygan
Presqu^ Isle
Alpena
Karrisville
Tawas
Saginaw'Bay
Harbor Beach
Lexington
n
18
18
9
9
9
6
18
17
15
18
18
15
18
18
17
18
18
16
8
16
18
n
16
18
9
9
9
6
18
17
T5
18
18
14
18
18
17
18
17
17
3
16
18
SPRING
X
9.3
10.2
7.8
6.8
8.1
3.3
6.8
6.6
9.9
8.1
7.3
9.3
12.0
14.8
12.9
16.9
13.9
12.4
18.8
15.1
12.9
SPRING
X
10.2
10.2
10.9
10.9
13.0
11.5
13.2
10.8
10.2
11.3
12.6
11.9
11.5
10.8
9.6
9.7
11.4
11.2
9.2
8.6
9.1
SD
1.8
1.1
0.4
1.8
1.5
0.3
0.7
1.7
0.3
0.4
0.5
1.3
3.7
0.4
1.7
1.2
1.4
0.5
6.3
1.1
0.9
Dissolved
SP
1.0
0.2
0.2
0.3
0.2
0.2
0.1
0.?
0.1
0.6
0.2
0.1
1.2
0.5
0.5
0.3
0.4
0.3
1.4
0.4
0.3
n
18
18
9
9
7
3
17
14
15
18
18
15
18
18
17
18
18
18
8
15
18
Oxygen
n
17
18
9
9
7
3
17
14
15
18
18
15
18
18
17
18
18
18
8
15
18
FALL
X
14.3
14.8
15.0
14.0
15.4
13.7
15.7
14.1
14.9
13.5
17.2
17.0
9.8
14.3
15.2
17.3
18.8
19.2
11.3
19.8
19.6
(mg/1 }
FALL
X
8.9
8.7
8.9
9.4
8.5
8.°
10.7
10.0
10. P
10.8
10.1
9.7
11.7
10.4
19.2
11.0
10.5
10.1
11.7
9.7
10.0
SD
0.6
0.6
0.1
2.2
0.9
0.3
1.9
1.6
0.3
3.5
0.1
0.1
3.0
0.4
0.3
0.3
0.3
0.2
0.4
1.0
0.1
SD
0.3
0.1
0.1
0.5
0.4
0.1
0.<5
0.5
0.1
0.7
0.1
0.2
0.3
0.1
0.2
0.2
0.2
0.1
0.5
0.2
0.1
n
36
36
18
18
16
9
35
31
30
36
36
30
36
36
34
36
36
34
16
31
36
n
33
36
18
18
16
9
35
31
30
36
36
29
36
36
34
36
35
35
11
31
36
ANNUAL
X
11.8
12.5
11.4
10.4
11.3
6.7
11.1
10.3
12.4
10.8
12.5
13.1
10.9
14.5
14.0
17.1
16.3
16.0
15.0
17.4
16.3
ANKUAL
X
9.5
9.4
9.T
10.2
11.0
10.fi
12.0
10.8
10.4
11.0
11. '
10.7
ll.fi
10.5
9.9
10.4
11.0
11.0
11.0
9.1
9.6
SD
2.8
2.4
3.6
4.1
3.8
5.2
4.6
4.0
2.5
3.6
4.9
3.9
3.5
0.4
1.6
0.8
2.6
3.4
5.8
2.5
3.4
SD
1.0
0.8
1.0
0.9
2.3
1.3
1.3
0.4
0.2
0.7
1.3
1.1
1.0
0.4
0.5
0.7
0.5
0.3
1.5
0.6
0.5
-107-
-------
Table A-3 (continued)
pH
Lal'e Superior
Black River
Outonagon
Upper Portage Entry
Lower Portage Entry
Eagle Harbor
Isle Royale
Big Bay
Presque Isle (Marquette)
Carp River (Marquette)
Munising
Grand Marais
Whirefish Point
Lake Huron
Detour
Cheboygan
Presque Isle
Alpena
Harrisville
Tawas
Saginaw Bay
Harbor Beach
Lexington
Lake Superior
Black River
Ontonagon
Upper Portage Entry
Lower Portage Entry
Eagle Harbor
Isle Royale
Big Bay
Presque Isle (Marquette)
Carp River (Marquette)
Munising
Grand Marais
Whitefish Point
Lake Huron
Detour
Cheboygan
Presque Isle
Alp';n a
Harrisville
Taw as
Saginaw Bay
Harbor Beach
Lexington
n
4
12
6
_
2
6
-
_
11
9
4
4
4
12
4
12
4
12
6
12
4
n
4
12
6
6
2
6
6
12
11
11
4
4
4
12
4
12
4
12
6
12
4
SPRING
X
7.7
7.7
7.8
_
7.6
7.4
-
_
7.7
7.-
7.7
8.0
7.8
8.3
8.1
8.1
8.0
8.2
7^9
7.9
SPRING
X
2.0
1.8
1.5
1.0
2.0
0.8
0.7
0.8
0.8
1.2
0.6
0.7
1.0
1.0
1.0
2.7
0.6
1.1
2.4
3.2
1.4
SD
Turbidity
SD
1.2
0.6
0.3
0.6
0.0
0.1
0.0
0.1
0.1
0.7
0.0
0.1
0.6
0.2
0.3
3.1
0.1
0.3
1.3
1.6
0.3
n
4
12
6
6
2
4
4
6
12
12
4
4
4
12
4
12
4
12
6
12
4
(J.T.U.
n
4
12
6
6
2
4
4
12
12
12
4
4
4
12
4
12
4
12
6
12
4
FALL
X
7.7
7.7
7.8
7.7
7.7
7.6
7.9
7."
7.6
7.6
7.7
7.-,
7.8
8.1
8.0
8.2
8.2
8.3
8.2
8.1
8.3
FALL
X
1.0
1.6
1.1
0.6
0.5
0.5
0.5
0.5
0.6
1.0
0.6
0.5
1.4
1.3
1.1
2.3
1.0
0.7
6.2
3.3
0.8
SD
SD
0.2
1.0
0.7
0.1
0.0
0.0
0.1
0.1
0.1
1.9
0.1
0.1
0.4
0.3
0.8
0.6
0.3
0.1
5.4
3.2
0.0
n
8
24
12
-
4
10
-
-
23
21
8
8
8
24
8
24
8
24
12
24
8
n
8
24
12
12
4
10
10
24
23
23
8
8
8
24
8
24
8
24
12
24
8
ANNUAL
X
7.7
7.7
7.8
-
7.7
7.5
-
-
7.7
7.6
7.7
7.9
7.8
8.2
8.0
8.2
8.1
8.2
8.2
8.0
8.1
ANNUAL
-
1-6
1.7
1.3
0.8
1-5
0.7
0.6
0.7
0.7
1.1
0.6
0.6
1.2
1.1
1.0
2.5
0.8
0.9
4.7
3.2
1.0
SD
SD
1.0
0.8
0.6
0.5
0.8
0.2
0.1
0.2
0.1
1.4
0.0
0.1
0.5
0.3
0.6
2.2
0.3
0.3
4.4
2.5
0.3
continued
-108-
-------
Table A-3 (continued)
Alkalinltv (mq/1)
Lake Superior
Black River
Ontonagon
Upper Portage Entry
Lower Portage Entry
Eagle Harbor
Isle Royale
Big Bay
Presque Isle (Marquette)
Carp River (Marquette)
Munising
Grand Marais
Wliitefish Point
Lake Huron
Detour
Cheboygan
Presque Isle
Alpena
Harrisvllle
Tow as
Saginaw Bay
Harbor Beach
Lexington
Lake Superior
Black River
Ontonagon
Upper Portage Entry
Lower Portage Entry
Eagle Harbor
Isle Royale
Big Bay
Presque Isle (Marquette)
Carp River (Marquette)
Munising
Grand Marais
Whitefish Point
Lake Huron
Detour
Cheboygan
Presque Isle
Alpena
Harrisville
Tawas
Saginaw Bay
Harbor Beach
Lexington
n
4
12
6
6
2
6
6
12
11
12
4
4
4
12
4
12
4
12
6
12
4
n
4
12
6
6
2
6
6
12
11
12
4
4
4
12
4
12
4
12
6
12
4
SPRING
X
42
42
43
42
41
44
43
42
40
45
43
44
65
96
82
100
79
80
91
82
83
SPRING
X
44
44
45
45
45
45
45
44
45
45
45
45
79
117
103
119
98
99
145
104
103
SD
0
1
1
1
0
1
1
2
2
2
1
6
1
4
8
2
2
7
1
2
HarHnoct
SD
1
1
1
1
0
0
2
^
1
2
1
1
15
2
4
13
2
1
14
2
2
n
4
12
6
6
2
4
4
12
12
12
4
4
4
12
4
12
4
12
6
12
4
: (mn/1 1
n
4
12
6
6
2
4
4
12
12
12
4
4
4
12
4
12
4
12
6
12
4
FALL
-
41
44
43
43
4?
43
43
42
42
43
42
41
65
95
78
87
79
83
81
81
80
FALL
Ic
46
48
46
45
46
46
45
45
46
45
47
46
80
115
95
106
97
100
100
102
98
SD
1
1
0
2
1
1
1
1
1
0
1
1
8
2
0
3
2
1
4
1
1
SD
0
1
1
1
1
1
1
1
1
1
2
1
10
1
0
3
1
2
6
2
1
n
8
24
12
12
4
10
10
24
23
24
8
8
8
24
8
24
8
24
12
24
8
n
8
24
12
12
4
10
10
24
23
24
8
8
8
24
8
24
8
24
12
24
8
ANNUAL
X
41
43
43
4?
41
43
43
42
41
43
42
43
65
96
80
93
79
81
87
8?
81
ANNUAL
X
45
46
46
45
45
45
45
45
45
45
46
45
79
116
99
113
97
100
122
103
100
SD
1
1
1
1
]
1
1
2
1
2
1
1
6
2
3
9
0
2
7
1
2
SD
1
1
1
1
1
0
2
l
1
1
2
1
13
2
"5
9
2
1
25
2
1
continued
-109-
-------
Table A-3 (continued)
Magnesium (mg/1)
Lake Superior
Black River
Ontonagon
Upper Portage Entry
Lower Portage Entry
Eagle Harbor
Isle Royale
Big Bay
Presque Isle (Marquette)
Carp River (Marquette)
Munising
Grand Marais
Whitefish Point
Lake Huron
Detour
Cheboygan
Presque Isle
Alpena
Harrisville
Taw as
Saginaw Bay
Harbor Beach
Lexington
Lake Superior
Black River
Ontonagon
Upper Portage Entry
Lower Portage Entry
Eagle Harbor
Isle Royale
Big Bay
Presque Isle (Marquette)
Carp River (Marquette)
Munising
Grand Marais
Whitefish Point
Lake Huron
Detour
Cheboygan
Presque Isle
Alpena
Harrisville
Tawas
Saginaw Bay
Harbor Beach
Lexington
n
4
12
6
6
2
6
6
12
11
11
4
4
4
12
4
12
4
12
6
U
4
n
4
12
6
6
2
6
6
12
11
12
4
4
4
12
4
12
4
12
6
12
4
SPRING
X
3.0
3.0
3.0
3.0
3.3
3.2
3.0
3.0
3.1
3.1
3.1
3.1
6.3
10.0
8.1
8.9
8.0
7.8
9.7
8.0
8.4
SPRING
X
13
13
14
13
14
13
14
14
14
13
14
13
22
31
27
33
27
28
27
29
29
SD
0.1
0.1
0.1
0.0
0.0
0.1
0.0
0.1
0.1
0.1
0.1
0.1
0.7
0.0
0.3
0.5
0.1
0.1
1.1
0.1
0.1
Calcium
SD
0
0
0
0
0
0
0
0
0
0
0
0
2
1
1
2
1
1
3
1
1
n
4
12
6
6
2
4
4
12
12
12
4
4
4
12
4
12
4
12
6
12
4
(mg/1)
n
4
12
6
6
2
4
4
12
12
12
4
4
4
12
4
12
4
12
6
12
4
FALL
X
3.3
3.4
3.1
3.2
3.2
3.2
3.2
3.3
3.3
3.2
3.1
3.2
6.4
9.9
7.8
8.3
7.7
7.7
8.4
7.8
7.7
FALL
X
13
14
14
14
14
14
13
Id
14
14
13
13
22
30
26
29
28
27
30
28
27
SD
0.0
0.1
0.1
0.0
0.0
0.0
0.1
0.0
0.1
0.0
0.0
0.0
1.0
0.1
0.1
0.2
0.1
0.0
0.5
0.2
0.0
SD
0
0
1
0
0
1
0
0
1
1
0
1
3
0
0
0
1
1
2
0
n
8
24
12
12
4
10
10
24
23
23
8
8
8
24
8
24
8
24
12
24
8
n
8
24
12
12
4
10
10
24
23
24
8
8
8
24
8
24
8
24
12
24
8
ANNUAL
X
3.2
3.2
3.0
3.1
3.3
3.2
3.1
3.2
3.2
3.2
3.1
3.1
6.4
10.0
7.9
8.6
7.8
7.8
9.0
7.9
8.0
ANNUAL
X
13
14
14
14
14
14
14
la
14
13
13
13
22
31
27
31
28
28
28
28
28
SD
0.1
0.2
0.1
0.1
0.1
0.1
0.1
0.1
0.1
0.1
0.0
0.1
0.9
0.1
0.3
0.5
0.2
0.1
1.0
0.1
0.3.
SD
0
1
0
0
0
0
1
0
0
0
0
0
)
1
1
3
1
1
3
1
1
continued
-110-
-------
Table A-3 (continued)
Potassium (mg/1)
Lake Superior
Black River
Ontonagon
Upper Portage Entry
Lower Portage Entry
Eagle Harbor
Isle Royale
Big Bay
Presque Isle (Marquette)
Carp River (Marquette)
Munis ing
Grand Marais
Whitefish Point
Lake Huron
Detour
Cheboygan
Presque Isle
A]pen a
Harrisville
Tawas
Saginaw Bay
Harbor Beach
Lexington
Lake Superior
Black River
Ontonagon
Upper Portage Entry
Lower Portage Entry
E.igle Harbor
Isle Royale
Big Bay
Presque Isle (Marquette)
Carp River (Marquette)
Munj.si.ng
Grand Marais
Whitefish Point
Lake Huron
Detour
Cheboygan
Presque Isle
Alpena
Harrisville
Tawas
Saginaw Bay
Harbor Beach
Lexington
n
4
12
6
6
2
6
6
12
11
11
4
4
4
12
4
12
4
12
6
12
4
n
4
12
6
6
2
6
6
12
11
11
4
4
4
12
4
12
4
12
6
12
4
SPRING
X
0.40
0.41
0.45
0.49
0.46
0.42
0.47
0.47
0.44
0.42
0.41
0.38
0.58
0.81
0.66
0.85
0.68
0.76
1.05
0.80
0.79
SPRING
X
1.3
1.4
1.5
1.3
1.7
2.3
1.2
1.3
3.1
1.3
1.2
1.2
3.7
4.9
3.9
4.5
4.1
4.3
5.8
5.0
5.5
SD
O.Ol
0.01
0.08
0.06
O.Ol
0.03
0.01
0.03
0.02
0.04
0.02
0.01
0.05
0.03
0.02
0.21
0.01
0.03
0.16
0.02
0.04
Sodium
SD
0.1
0.1
0.3
0.1
0.1
0.4
0.1
0.1
0.1
0.1
0.0
0.1
0.4
0.3
0.2
0.5
0.2
0.2
1.4
0.2
0.1
n
4
12
6
6
2
4
4
12
12
12
4
4
4
12
4
12
4
12
6
12
4
(mg/1)
n
4
12
6
6
2
4
4
12
12
12
4
4
4
12
4
12
4
12
6
12
4
FALL
X
0.52
0.56
0.51
0.46
0.54
0.52
0.58
0.45
0.45
0.57
0.47
0.44
0.64
0.86
0.76
0.79
0.72
0.87
0.90
0.84
0.85
FALL
X
1.6
1.9
1.7
1.6
1.9
1.4
1.6
1.8
1.6
1.6
1.5
1.3
2.6
4.1
3.2
3.6
3.3
3.8
4.6
3.8
3.4
SD
0.06
0.10
0.06
0.02
0.09
0.02
0.10
0.01
0.01
0.15
0.01
0.01
0.09
0.02
0.01
0.02
0.01
0.12
0.08
0.08
0.03
SD
0.2
0.5
0.3
0.1
0.4
0.1
0.3
0.3
0.2
0.3
0.1
0.1
0.5
0.1
0.1
0.1
0.1
0.3
1.0
0.5
0.1
n
8
24
12
12
4
10
10
24
23
23
8
8
8
24
8
24
8
24
12
24
8
n
8
24
12
12
4
10
10
24
23
23
8
8
8
24
8
24
8
24
12
24
8
ANNUAL
X
0.47
0.49
0.48
0.48
0.50
0.46
0.52
0.46
0.44
0.51
0.44
0.4]
0.61
0.84
0.71
0.82
0.70
0.82
0.98
0.82
0.82
ANNUAL
3c
1.4
1.6
1.6
1.5
1.8
1.9
1.3
l.b
2.4
1.4
1.3
1.3
3.2
4.6
3.b
4.0
3.7
4.1
5.2
4.4
4.5
SD
0.07
0.10
0.08
0.04
0.08
0.06
0.08
0.02
0.02
0.14
0.03
0.03
0.08
0.04
0.05
0.15
0.02
0.10
0.15
0.06
0.04
SD
0.2
0.4
0.3
0.2
0.3
0.6
0.3
0.4
0.8
0.3
0.1
0.1
0.7
0.5
0.4
0.6
0.4
0.4
1.4
0.7
1.1
continued
-111-
-------
Lake Superior
Black River
Ontonagon
Upper Portage Entry
Lower Portage Entry
Eagle Harbor
Isle Royale
Big Bay
Tresque Isle (Marquette)
Carp River (Marquatte)
Munising
Grand Marais
Kiitefish Point
Lake Huron
Detour
Cheboygan
Presque Isle
Alpen a
Harrisville
Tawas
Saginaw Bay
Harbor Beach
Lexington
Superior
Black River
Ontonagon
Upper Portage Entry
Lower Portage Entry
Eagle Harbor
Isle Royale
Big Bay
Presque Isle (Marquette)
Carp River (Marquette)
Munising
Grand Marais
Whitefish Point
Lake Huron
Detour
Cheboygan
Presque Isle
Alpena
Harrisville
Tawas
Saginaw Bay
Harbor Beach
Lexington
Table A-3 (continued)
Chloride (mg/1 }
n
4
12
6
6
2
6
6
12
11
12
4
4
4
12
4
12
4
12
6
12
4
n
4
12
6
6
2
6
6
12
11
12
4
4
4
12
4
12
4
12
6
12
4
SPRING
X
1.3
1.5
1.0
1.2
1 4
1.1
0.9
0.6
1.5
1.3
1.4
1.0
3.5
6.2
4.3
4.8
5.2
5.6
11.0
7.0
6.7
SPRING
X
2.8
3.1
2.9
2.3
2.8
3.2
2.7
3.1
2.6
3.2
2.9
2.8
11.2
16.6
13.8
26.7
14.0
14.0
18.7
17.5
17.0
SD
0.1
0.3
0.0
0.4
1.0
0.0
0.2
0.2
0.1
0.3
0.1
0.1
0.6
0.1
0.2
0.?
0.2
0.2
3.6
0.2
0.7
Sulfate
SD
0.2
0.3
0.2
0.4
0.1
0.1
0.2
0.4
0.2
0.4
0.2
0.5
2.3
0.7
0.5
2.0
0.0
0.9
2.5
0.5
0.8
n
4
12
6
6
2
4
4
12
12
12
4
4
4
12
4
12
4
12
6
12
4
(mg/1)
n
4
12
6
6
2
4
4
12
12
12
4
4
4
12
4
12
4
12
6
12
4
FALL
3c
1.2
1.4
1.2
1.2
1.1
1.2
1.1
1.3
1.3
1.1
1.3
1.1
4.0
7.5
5.8
5."
5.8
6.8
8.8
6.c
5.8
FALL
X
2. 9
2.9
2.0
3.0
3.5
3.3
2.5
3.0
2.a
2.9
2.6
2.4
10.4
16.3
12. R
14.1
14.8
15.0
19.0
16.2
13.8
SD
0.0
0.1
0.0
0.1
0.0
0.1
0.1
0.1
0.2
0.1
0.1
0.0
0.9
0.1
0.1
0.1
o.';
0.8
2.5
0.2
0.1
SD
0.?
0.3
0.1
0.2
0.4
0.4
0.2
0.3
0.1
0.3
0.3
0.2
2.8
0.5
0.5
1.0
0.5
0.4
2.1
0.4
0.5
n
8
24
12
12
4
10
10
24
23
24
8
8
8
24
8
24
8
24
12
24
8
n
8
24
12
12
4
10
10
24
23
24
8
8
8
24
8
24
8
24
12
24
8
ANNUAL
X
1.3
1.4
1.1
1.?
1.2
1.1
1.1
0."
1.4
1.2
1.3
1.1
3.8
6.8
5.3
5.3
5.5
6.2
9.0
C.8
5.2
ANNUAL
X
2.8
3.0
2.5
3.0
3.1
3.2
2.6
3.1
2.8
3.0
2.8
2.6
10.8
16.5
13.3
20.4
14.4
15.5
18.9
16.8
15.4
SD
0.1
0.2
0.1
0.3
0.1
0.1
0.2
0.4
0.2
0.3
0.1
0.0
0.8
0.7
0.5
0.6
0.3
0."
3.3
C.3
0.6
SD
0.2
0.3
0.5
0.3
0.4
0.3
0.2
0.3
0.3
0.3
0.3
0.4
2.6
0.6
0.7
6.5
0.5
0.8
2.3
0.8
1.8
continued
-112-
-------
Table A-3 (continued)
Total Dissolved Solids (mg/1)
Lake Superior
Black Paver
Ontonagca
Upper Portage Entry
Lower Portage Entry
Eagle Harbor
Isla Royale
Big Bay
Presque Isle (Marquette)
Carp River (Marquette)
Munis ing
Grand Marais
Wh J re fish Point
Lake Huron
Clioboygan
Prcsque Isle
Alp?na
H.irrisville
Tawss
Saginaw Bay
Harbor Beach
Lexington
Lake Superior
Black River
Chtonagon
Upper Portage Entry
Low?r Portage Entry
Eagle Harbor
Isle Royale
Big Bay
Presque Isle (Marquette)
Carp River (Marquette)
Munis ing
Grnnd Marais
Whitefish Point
Lake Huron
Detour
Ch<3boygan
Prefque Isje
Alpena
Karrisville
Tsvas
Sagitiaw'Bay
Harbor Beach
Lexington
n
4
12
6
6
2
6
6
12
11
11
4
4
4
12
4
12
4
12
6
12
4
n
18
18
9
9
9
6
18
M
15
18
18
14
18
18
17
18
18
17
8
16
18
SPRING
X
53
53
54
53
54
55
53
52
52
55
54
53
93
135
115
149
113
116
136
124
124
SPRING
X
87
88
86
85
85
87
85
85
87
88
87
87
155
228
191
224
190
195
232
202
207
SD
1
1
1
2
0
1
1
1
1
2
1
1
10
1
4
8
2
2
16
2
3
Conductivity
SD
2
2
1
3
3
1
1
1
1
3
1
1
11
4
6
n
6
1
29
4
9
n
4
12
6
6
2
4
4
12
12
12
4
4
4
12
4
12
4
12
6
12
4
FALL
X
52
55
53
54
54
54
54
53
53
53
53
51
91
134
111
121
114
118
129
119
113
SD
0
2
0
1
1
1
1
1
1
1
1
1
13
2
1
3
1
2
11
1
1
n
8
24
12
12
4
10
10
24
23
23
8
8
8
24
8
24
8
24
12
24
8
ANNUAL
X
52
54
53
54
54
55
53
53
53
54
53
52
92
135
113
135
114
117
133
121
119
SD
0
2
1
1
1
1
1
1
1
2
1
1
12
2
4
15
2
3
14
3
6
(u-mho/cm)
n
17
18
9
9
7
3
17
14
15
18
18
15
18
18
17
18
18
18
8
15
18
FALL
X
89
92
88
83
88
88
87
88
88
87
87
87
153
222
86
203
190
196
205
145
189
SD
1
5
0
1
1
3
1
2
1
2
1
1
18
2
2
4
2
2
12
3
0
n
35
36
18
18
16
9
35
31
30
36
36
29
36
36
34
36
36
35
16
31
36
ANNUAL
X
88
90
87
86
86
87
86
87
88
88
87
87
154
225
189
213
190
196
219
199
198
SD
2
4
2
3
^
2
j
2
1
3
1
1
15
4
5
13
5
2
26
5
n
continued
-113-
-------
Table A-3 (continued)
Total Phosphorus (mg/1)
Lake Superior
Black River
ChiLonagon
Upper Portage Entry
Lcwer Portage Entry
Eagle Harbor
Isle Royale
Big Bay
Presquc Isle (Marquette)
Carp River (Karquette)
tlvnlsing
Grand Marais
Whitefish Point
Lake Huron
Detour
Cheboygan
1'resque Isle
Alpena
Harrisville
Taw as
Saginaw Bay
Harbor Beach
Lexington
Superior
EJ.ick River
Onfonagon
Upper Portage Entry
Lower Portage Entry
Eagle Harbor
IrJe Royale
Big Bay
Presque Isle (Marquette)
Carp River (Marquette)
Mun is ing
Grand Marais
Whitefish Point
Lake Huron
Detour
Cbeboygan
Piesque Isle
AJpona
Horri&ville
Tawas
Sagir.iw'Bay
Harbor Beach
Lexington
n
18
18
9
9
9
9
18
17
16
18
18
18
18
18
18
18
18
18
8
15
18
SPRING
X
0.006
0.006
0.004
CONTh. ,.,,, *.
SD
0.005
0.012
0.001
OMTNATCn
0.004 0.002
0.004
0.005
0.004
0.006
0.010
0.002
<0.002
0.007
0.005
0.006
0.036
0.005
0.010
0.018
0.016
0.011
0.005
0.009
0.002
0.002
0.013
0.001
0.002
0.004
0.006
0.053
0.002
0.003
0.011
0.006
0.004
n
18
18
9
9
9
6
18
14
15
17
18
l ft
1 O
18
18
17
18
18
18
8
15
18
FALL
-
0.007
0.004
0.002
0.005
0.005
0.008
0.005
0.012
0.007
0.004
n find
u . uu*t
0.008
0.005
0.003
0.021
0.007
0.006
0.021
0.008
0.006
SD
0.002
0.002
O.OOI
n om
U . UU I
0.006
0.003
0.003
0.003
0.003
0.005
0.002
n nno
o.ooi
O.OOI
0.002
0.005
0.002
O.OOI
0.018
0.004
O.OOI
n
36
36
18
1 8
1 O
18
15
36
33
31
35
36
qc
JO
36
36
35
36
36
36
16
30
36
ANNUAL
X
0.006
0.005
0.003
0.005
0.005
0.007
0.004
0.009
0.008
0.003
0.007
0.005
0.005
0.028
0.008
0.008
0.019
0.012
0.008
SD
0.004
0.009
0.005
0.004
0.004
0.006
0.003
0.004
0.010
0.002
0.002
0.003
0.005
0.039
0.003
0.003
0.015
0.007
0.004
Total Ortho-Phosphate (tnq/1)
n
18
18
9
9
9
9
18
17
15
18
18
18
18
18
18
18
18
18
8
16
18
SPRING
X
0.001
0.003
0.003
SD
0.000
0.006
0.001
CONTAMINATED?
0.001
0.001
0.001
0.001
0.001
0.002
0.001
0.001
0.003
0.001
0.001
0.007
0.001
0.002
0.003
0.005
0.004
0.001
0.000
0.001
n.nnn
0.001
0.002
0.000
0.001
0.001
0.001
0.001
0.010
0.000
0.001
0.002
0.001
0.001
n
18
18
9
9
9
6
18
14
15
18
18
18
18
18
17
18
18
18
8
14
18
FALL
X
0.003
0.002
0.001
0.001
0.001
0.001
0.003
n.nnj
0.002
0.001
0.002
0.002
0.003
0.002
8.002
0.007
0.002
0.001
0.006
0.002
0.103
SD
0.002
O.OOI
0.000
0.000
0.000
O.OOI
O.OOI
n.fW|
O.OOI
O.OOI
O.OOI
O.OOI
O.OOI
O.OOI
O.OOI
0.002
o.ooi
O.OOI
O.OOI
O.OOI
O.OOI
n
36
36
18
18
18
15
36
31
30
36
36
36
36
36
35
36
36
36
16
30
36
ANNUAL'
X
0.002
0.003
0.002
0.001
o.ooi
0.002
0.001
0.002
0.001
0.002
0.002
0.003
0.002
0.001
0.007
0.006
0.002
0.004
0.004
0.004
SD
0.002
0.004
0.001
-_
0.001
0.000
0.002
n.nn1!
0.001
0.001
o.ooi
0.001
0.002
0.001
0.001
0.007
0.001
0.001
0.002
0.002
0.001
continued
-114-
-------
Table A-3 (continued)
Nitrite-Nitrogen (mg/1
Lake Superior
Black River
Ontonagon
Upper Portage Entry
Lower Portage Entry
Eagle Harbor
Isle Royale
Big Bay
Presque Isle (Marquette)
Carp River (Marquette)
Munislng
Grand Marais
White fish Point
Lake Huron
Uctour
Cheboygan
Presque Isle
Alpena
Harrisville
Tawas
Saginaw Bay
Harbor Beach
Lexington
Lake Superior
Black River
Ontonagon
Upper Portage Entry
Lowar Portage Entry
Eajle Harbor
Isle Royale
Big Bay
Presque Isle (Marquette)
Carp River (Marquette)
Munising
Grand Marais
Whiteflsh Point
Lriko Huron
Detour
Cneboygan
Presque Isle
Alpona
Harrisville
Tawas
Saginaw Bay
Harbor Beach
Lexington
n
18
18
9
9
9
9
18
17
15
18
18
18
18
18
18
18
18
18
8
16
18
SPRING
X
0.001
0.001
0.001
0.002
0.002
0.001
0.001
0.002
0.002
0.001
0.002
0.001
0.001
0.002
0.002
0.002
0.001
0.002
0.007
0.005
0.004
SD
0.001
0.001
0.001
0.001
0.001
0.000
0.000
0.001
0.001
0.000
0.001
0.000
0.000
o.ooi
0.000
0.002
0.001
0.001
0.001
0.001
0.000
n
18
18
9
9
9
6
18
14
15
18
18
18
18
18
17
18
18
18
8
14
18
Nitrate-Nitrogen
n
18
18
9
9
9
9
18
17
15
18
18
18
18
18
18
18
18
18
8
16
18
SPRING
X
0.255
0.248
0.268
0.261
0.250
0.263
0.31!
0.274
0.236
0.252
0.272
0.251
0.263
0.167
0.227
0.138
0.216
0.211
0.172
0.256
0.264
SD
0.028
0.008
0.006
0.012
0.007
0.005
0.109
0.012
0.009
0.006
0.004
0.005
0.028
0.015
0.044
0.016
0.060
0.014
0.061
0.006
0.010
n
18
18
9
9
9
6
18
14
15
18
18
18
18
18
17
18
18
18
8
14
18
FALL
X
0.002
0.002
0.002
0.001
0.002
0.002
0.002
0.001
0.001
0.002
0.001
0.004
0.004
0.002
0.002
0.001
0.002
0.002
0..006
0.003
0.002
(mg/D
FALL
3c
0.273
0.240
0.260
0.287
0.272
0.296
0.341
0.282
0.242
0.277
0.264
0.291
0.265
0.165
0.207
0.142
0.215
0.226
0.143
0.213
0.231
SD
0.000
0.001
0.00]
0.001
0.000
0.001
0.000
0.000
0.000
0.000
0.000
0.000
0.002
0.001
0.001
0.001
0.000
0.001
0.001
o.ooo.
0.00?
SD
0.069
0.019
0.052
0.046
0.026
0.054
0.181
0.023
0.005
0.046
0.058
0.047
0.020
0.019
0.019
0.014
0.024
0.055
0.086
0.009
0.042
n
36
36
18
18
18
15
36
31
30
36
36
36
36
36
35
36
36
36
16
30
36
n
36
36
18
18
18
15
36
31
30
36
36
36
36
36
35
36
36
36
16
30
36
ANNUAL
lc
0.002
0.002
0.002
0.002
0.002
0.002
0.002
0.002
0.001
0.002
0.002
0.003
0.003
0.002
0.002
0.002
0.002
0.002
0.006
0.004
0.003
ANNUAL
X
0.264
0.244
0.264
0.274
0.261
0.277
0.326
0.278
0.239
0.265
0.268
0.272
0.264
0.166
0.218
0.140
0.216
0.219
0.158
0.237
0.248
SD
0.001
0.001
0.001
0.001
0.001
0.001
0.000
0.001
0.000
0.007
0.001
0.002
0.002
0.001
0.000
0.001
o.ooi
o.ooi
o.ooi
0.001
0.001
SD
0.053
0.015
0.037
0.036
0.021
0.038
0.150
0.018
0.007
0.035
0.041
0.038
0.024
0.017
0.035
0.015
0.045
0.040
0.075
0.022
0.034
continued
-115-
-------
Table A-3 (continued)
Ammonia-Nitrogen (mq/1)
Lake Superior
Black River
Ontonagon
Upper Portage Entry
Lower Portage Entry
Eagle Harbor
Isle Royale
Big Bay
Presque Isle (Marquette)
Carp River (Marquette)
Munising
Grand Marais
Whitefish Point
Lake Huron
Detour
Cheboygan
Presque Isle
Alpena
Harrisville
Tawas
Saginaw Bay
Harbor Beach
Lexington
Lake Superior
Black River
Ontonagon
Upper Portage Entry
Lower Portage Entry
Eagle Harbor
Isle Royale
Big Bay
Presque Isle (Marquette)
Carp River (Marquette)
Munising
Grand Marais
Whitefish Point
Lake Huron
Detour
Cheboygan
Presque Isle
Alpena
Harrisville
Tawas
Saginaw Bay
Harbor Beach
Lexington
n
18
18
9
9
9
9
18
17
15
18
18
18
18
18
18
18
18
18
8
16
18
n
18
18
9
9
9
9
18
17
15
18
18
18
18
18
18
18
18
18
8
16
18
SPRING
X
0.006
0.006
0.003
0.012
0.005
0.003
0.001
0.001
0.005
0.004
0.005
0.002
0.012
B.QQ3
u. UOo
0.006
0.004
0.005
0.022
0.038
0.032
SPRING
X
0.11
0.12
0.19
0.15
0.12
0.12
0.15
0.09
0.14
0.18
0.12
0.08
0.28
0.14
0.14
0.36
0.16
0.21
0.29
0.28
0.22
SD
0.002
0.002
0.002
0.007
0.001
0.001
0.002
0.000
0.002
0.005
0.001
0.002
0.009
0.002
0.002
0.005
0.001
0.001
0.018
0.011
0.014
Organic
SD
0.03
0.04
0.02
0.06
0.10
0.07
0.04
0.04
0.03
0.08
0.04
0.06
0.10
0.02
0.05
0.08
0.05
0.06
0.09
0.09
0.18
n
18
18
9
9
9
6
18
14
15
18
18
18
18
18
17
18
18
18
8
14
18
Nitrogen
n
18
18
9
9
9
6
18
14
15
18
18
18
18
18
17
18
18
18
8
15
18
FALL
X
0.002
0.006
0.003
0.007
0.005
0.009
0.006
0.008
0.008
0.008
0.007
0.014
0.014
0.004
0.001
0.022
0.006
0.011
0.008
0.012
0.005
(mg/1)
FALL
Ic
0.09
0.10
0.10
0.13
0.13
0.08
0.11
0.11
0.12
0.11
0.11
0.11
0.18
0.16
0.15
0.25
0.24
0.20
0-29
0.11
0.24
SD
0.001
0.002
0.002
0.002
o.ooi
0.002
0.001
0.003
0.103
0.005
0.002
0.003
0.006
0.002
0.001
0.007
0.102
0.003
0.005
0.009
0.001
SD
0.02
0.03
0.02
0.02
0.02
0.02
0.06
0.04
0.05
0.05
0.02
0.03
0.05
0.04
0.04
0.03
0.04
0.08
0-13
0.04
0.03
n
36
36
18
18
18
15
36
31
30
36
36
36
36
36
35
36
36
36
16
30
36
n
36
36
18
18
18
15
36
31
30
36
36
36
36
36
36
36
36
36
16
31
36
ANNUAL
X
0.004
0.006
0.003
0.010
0.905
0.006
0.005
0.005
0.007
0.006
0.006
0.010
0.013
0.004
0.002
0.016
0.005
0.008
0.016
0.029
0.023
ANNUAL
X
0.10
0.08
0.14
0.14
0.13
0.10
0.13
0.10
0.13
0.15
0.11
0.10
0.23
0.15
0.14
0.21
0.20
0.21
0.29
0.20
0.23
SD
0.002
0.002
0.002
0.006
0.001
0.003
0.003
0.004
0.003
0.006
0.002
0.007
0.008
0.002
0.002
0.010
0.002
0.003
0.015
0.016
0.017
SD
0.03
0.04
0.05
0.05
0.07
0 06
0.05
0.04
0.04
0.08
0.03
0.05
0.09
0.03
0.05
0.08
0.06
0.07
0.11
0.11
0.13
continue^
-116-
-------
Table A-3 (continued)
REACTIVE SILICA (mg/1)
Lake Superior
Black River
Ontonagon
Upner Portage Entry
Lower Portage Entry
Eagle Harbor
Isle Royale
Big Bay
Presque Isle (Marquette)
Carp River (Marquette)
Munising
Grand Marais
Uhitefish Point
Lake Huron
Detour
Cheboyqan
Presque Isle
Aloena
Harrisville
Tawas
Saginaw Bay
Harbor Beach
Lexington
Lake Superior
Black River
Ontonagon
Upper Portage Entry
Lower Portage Entry
Eagle Harbor
Isle Royale
Big Bay
Presque Isle (Marquette)
Carp River (Marquette)
Muni sing
Grand Marais
tfhitefish Point
Lake Huron
Detour
Chebcygan
Presque Isle
AJpena
Harrisville
Tawas
Saginaw Bay
Harbor Beach
Lexington
N
4
12
6
6
4
6
6
12
11
12
5
4
4
12
3
12
4
11
6
13
4
n
18
18
9
9
9
9
18
17
15
18
18
18
18
18
18
18
18
18
8
16
18
SPRING
X"
2.5
2.8
2.6
2.4
3.4
2.6
2.6
2.6
2.3
2.5
2.0
2.4
1.5
0.6
1.2
1.0
1.3
1.2
0-6
0.9
0.9
SPRING
X
0.37
0.38
0.45
0.42
0.37
0.39
0.46
0.36
0.38
0.44
0.39
0.32
0.56
0.32
0.37
0.51
0.38
0.43
0.49
0.58
0.45
SD
0.2
0.1
0.1
0.4
0.1
0.0
0.2
0.2
0.0
0.3
0.9
0.1
0.2
0.2
0.3
0.2
0.4
0.3
0.1
0.1
0.3
Total
SD
0.04
0.04
0.02
0.05
0.10
0.07
0.12
0.04
0.03
0.08
0.05
0.04
0.10
0.02
0.08
0.08
0.09
0.05
0.05
0 09
0 05
N
4
12
6
6
2
4
4
12
11
12
4
4
4
12
4
12
4
12
5
12
4
Nitrogen
n
18
18
9
9
9
6
18
14
15
18
18
18
17
18
17
18
18
18
8
15
18
FALL
I
2.1
2.4
2.1
2.2
1.7
2.1
2.3
2.2
2.2
2.3
2.1
2.8
1.8
0.9
0.8
2.4
0.7
0.7
1.0
0.6
0.4
(mg/1)
FALL
X
0.36
0.38
0.36
0.43
0.41
0.39
0.46
0.40
0.38
0.39
0.38
0.44
0.46
0.33
0.36
0.42
0.47
0.42
0.44
0.34
0.47
SD
0.1
0.3
0.1
0.0
0.8
0.1
0.1
o.o
0.0
0.1
0.0
0.1
0.1
o.o
0.1
0.8
0.1
0.0
0.2
0.1
0.0
SD
0.09
0.03
0.06
0.06
0.03
0.06
0.23
0.05
O.OS
0.06
0.07
0.12
0.05
0.05
0.05
0.03
0.05
0.06
0.05
0.04
0.05
N
8
24
12
12
4
10
10
24
22
24
9
8
8
24
7
24
8
23
11
25
8
n
36
36
18
18
18
15
36
31
30
36
36
36
35
36
35
36
36
36
16
31
36
ANNUAL
J
2.1
2.6
2.4
2.5
2.5
2.5
2.5
2.4
2.3
2.4
2.0
2.3
1.6
0.8
1.0
1.7
1.0
1.0
0.9
0.7
0.7
ANNUAL
X
0.37
0.36
0.41
0.42
0.39
0.39
0.46
0.38
0.38
0.42
0.39
0.38
0.51
0.32
0.36
0.46
0.42
O.a3
0.47
0.46
0.46
SD
0.2
0.3
0.3
0.5
1.1
0.2
0.2
0.3
0.0
0.3
0.6
0.1
0.2
0.2
0.3
0.9
0.4
0.3
0.2
0.2
0.3
SD
0.07
0.04
0.06
0.05
0.08
0.07
0.18
0.05
0.04
0.08
0.06
o.n
0.09
0.04
0.30
0.08
0.08
0.06
0.05
0.43
0.05
continued
-117-
-------
Table A-3 (continued)
Chlorophyll a^ (yg/1)
Lake Superior
Black River
Ontonagon
Upper Portage Entry
Lower Portage Entry
Eagle Harbor
Isle Royale
Big Bay
Presque Isle (Marquette)
Carp River (Marquette)
Munising
Grand Marais
Whitefish Point
Lake Huron
Detour
Cheboygan
Presque Isle
Alpena
Harrisville
Tawas
Saginaw Bay
Harbor Beach
Lexington
Lake Superior
Black River
Ontonagon
Upper Portage Entry
Lower Portage Entry
Eagle Karoor
Isle Rcyale
Big Bay
Presque Isle (Marquette)
Carp River (Marquette)
Muaising
Grand Marais
Whitefish Point
Lake Huron
Detour
Cheboygan
Presque Isle
Alpena
Harrisville
Tawas
Saginaw Bay
Harbor Beach
Lexington
n
2
6
3
3
1
3
2
6
3
6
2
2
2
6
2
7
1
6
2
4
2
n
12
12
6
6
6
6
12
12
12
12
12
12
12
12
12
12
12
12
6
12
12
SPRING
X
2.6
1.6
2.8
1.4
1.9
0.8
1.6
1.9
1.4
1.8
1.4
1.5
1.7
1.5
1.4
10. P
3.1
3.6
6.1
4.5
5.3
SPRING
X
5*
4
3
14*
10 *
4
8*
6*
3
3
3
7*
5*
5*
2
2
4
13*
2
2
1
SD
0.7
0.7
0.2
0.2
0.0
0.1
0.2
0.8
0.1
0.3
0.0
0.1
0.2
0.3
0.1
4.?
_
1.7
4.9
0.3
0.2
Copper
SD
5
3
2
s
4
4
4
3
5
3
1
4
3
1
2
3
2
9
2
1
1
n
2
6
3
3
1
2
2
5
6
6
2
2
2
6
2
6
2
6
3
6
2
(V9/1 )
n
12
12
6
6
6
4
12
12
12
12
12
12
12
12
12
12
12
12
6
12
12
FALL
X
2.0
1.6
0.9
l.o
2.4
2.4
0.6
1.2
1.1
1.3
1.1
0.7
1.8
2.6
2.0
6.5
3.1
3.3
5.7
6.2
2.6
FALL
Ic
2
2
4
2
2
4
3
3
2
3
2
2
2
1
8*
3
3
4
4
2
2
SD
0.0
0.4
0.1
0.6
6.0
n.«
0.3
0.4
0.4
0.3
0.3
0.1
0.6
1.7
0.2
2.2
0.2
0.7
6.6
0.6
0.2
SD
1
1
2
1
1
1
3
1
0
1
1
1
1
1
20
2
3
5
1
1
1
n
4
12
6
6
2
5
4
11
9
12
4
4
4
12
4
13
3
12
5
10
4
n
24
24
12
12
12
10
24
24
24
24
24
24
24
24
24
24
24
24
12
24
24
ANNUAL
X
2.3
1.5
1.9
1.7
2.1
1.*
1.1
1.6
1.2
1.5
1.2
1.1
1.8
2.1
1.3
8.7
3.1
3.5
5.9
5.4
3.T
ANNUAL
X
3
3
3
8*
6*-
4
6*-
4
3
3
3
4
3
3
5
3
3
8
3
i
2
SD
0.6
0.5
0.9
0.5
0.2
0.9
0.6
0.7
0.4
0.4
0.2
0.5
0.5
1.4
0.3
4.0
0.2
1.3
Q.3
1.2
1.4
SD
4
3
2
7
b
3
4
3
3
1
1
4
3
2
14
3
2
8
2
1
1
continued
-118-
-------
Table A-3 (continued)
Iron (ug/1)
Lake Superior
Black River
Ontonagon
Upper Portage Entry
Lower Portage Entry
Eagle Harbor
Isle Royale
Big Bay
Presque Isle (Marquette)
Carp River (Marquette)
Munising
Grand Marais
Whitefish Point
Lake Huron
Detour
Cheboygan
Presque Isle
Alpena
Harrisville
Taw as
Saginaw Bay
Harbor Beach
Lexington
Lake Superior
Black River
Ontonagon
Upper Portage Entry
Lower Portage Entry
Eagle Harbor
Isle Royale
Big Bay
Presque Isle (Marquette)
Carp River (Marquette)
Munising
Grand Marais
Whitefish Point
Lake Huron
Detour
Chsboygan
Presque Isle
Alpena
Harrisville
Tauas
Saginaw Bay
Harbor Beach
Lexington
n
12
12
6
6
6
6
12
12
12
12
12
12
12
12
12
12
12
12
6
12
12
n
12
12
6
6
6
6
12
12
12
12
12
12
12
12
12
12
12
12
6
12
12
SPRING
X
86
58
40
37
48
23
n
37
25
56
17
17
34
26
168
82
12
20
61
228
59
SPRING
X
3
2
2
3
2
1
<1
2
4
3
1
1
2
2
8
15
2
2
6
9
3
SD
49
27
13
49
13
24
7
35
12
55
14
6
17
16
261
262
5
5
33
138
34
Manganese
SD
2
1
1
2
1
0
-
3
2
3
0
0.
1
0
13
16
1
1
2
5
1
n
12
12
6
6
6
4
12
12
12
12
12
12
12
12
12
12
12
12
6
12
12
(wg/i)
n
12
12
6
6
6
4
12
12
12
12
12
12
12
12
12
12
12
12
6
12
12
FALL
X
42
64
62
27
18
11
55
22
19
54
14
23
66
22
21
84
25
16
84
184
34
FALL
X
2
4
2
1
1
1
2
2
2
2
<1
2
3
2
2
7
2
2
6
6
2
SD
33
50
70-
26
6
2
89
13
9
86
4
28
24
5
19
28
20
4
66
271
12
SD
2
3
2
1
0
0
3
2
2
3
2
1
0
1
2
1
1
4
5
1
n
24
24
12
12
12
10
24
24
24
24
24
24
24
24
24
24
24
24
12
24
24
n
24
24
12
12
12
10
24
24
24
24
24
24
24
24
24
24
24
24
12
24
24
ANNUAL
X
64
61
51
32
33
18
31
30
22
55
16
20
50
24
95
133
18
18
73
206
47
ANNUAL
X
3
3
2
2
2
1
2
i
3
3
<1
1
3
2
5
11
2
2
6
8
3
SD
47
39
49
38
18
19
67
27
11
70
10
20
26
12
196
189
16
5
51
211
28
SD
2
2
1
2
1
0
2
2
2
3
-
1
1
0
10
12
8
1
3
5
1
continued
-119-
-------
Table A-3 (continued)
Lead (ug/l)
Lake Superior
Black River
Ontonagon
Upper Portage Entry
Lower Portage Entry
Eagle Harbor
Isle Royale
Big Bay
Presque Isle (Marquette)
Carp River (Marquette)
Munising
Grand Marais
Whitefish Point
Lake Huron
Uetour
Cheboygan
Presque Isle
Alpena
Harrisville
Tawas
Saginaw Bay
Harbor Beach
Lexington
Lake Superior
Black River
Ontonagon
Upper Portage Entry
Lover Portage Entry
Eagle Harbor
Isle Royale
Big Bay
Presque Isle (Marquette)
Carp River (Marquette)
Munising
Grand Marais
Whitefish Point
Lake Huron
Detour
Cheboygan
Presque Isle
Alpena
Harrisville
Tawas
Saginaw Bay
Harbor Beach
Lexington
n
12
12
6
6
6
6
12
12
12
12
12
12
12
12
12
12
12
12
6
12
12
n
12
12
6
6
6
6
12
12
12
12
12
12
12
12
12
12
12
12
6
12
12
SPRING
3c
<5
<5
<5
<5
<5
<5
<5
<5
<5
<5
<5
<5
<5
7
4
7
6
-------
Table A-3 (continued)
Chemical Oxygen Demand
Lake Superior
Black River
Ontonagon
Upper Portage Entry
Lower Portage Entry
Eagle Harbor
Isle Royale
Big Bay
Presque Isle (Marquette)
Carp River (Marquette)
Munising
Grand Marais
Whitefish Point
Lake Huron
Detour
Cheboygan
Presque Isle
Alpena
Harrisville
Tawas
Saginaw Bay
Harbor Beach
Lexington
n
4
8
6
5
1
6
4
11
12
15
4
4
4
12
4
12
-
12
5
12
4
SPRING
X
5.3
4.8
5.4
3.3
4.5
5.1
4.3
4.4
2.7
5.4
6.8
4.6
5.5
5.8
5.8
15.2
--
6.0
12.2
3.7
4.5
SD
1.6
1.0
0.7
0.8
0.0
0.4
0.9
1.2
1.0
1.3
3.2
2.0
1.2
1.2
2.2
7.6
--
1.3
2.6
1.9
2.6
n
4
13
6
6
2
4
4
12
12
12
6
4
4
11
4
12
4
12
6
12
4
FALL
X
4.3
5.9
4.5
7.7
5.2
10.6
10.0
6.6
7.9
4.0
7.1
3.7
3.7
5.6
5.4
7.0
4.9
5.3
10.7
6.5
6.0
SD
0.3
1.8
0.5
0.1
1.1
2.5
2.9
1.9
2.3
1.4
6.2
0.3
0.6
0.9
0.2
0.3
0.2
0.8
4.0
0.8
1 .2
n
8
21
12
11
3
10
8
23
24
27
10
8
8
23
8
24
4
24
11
24
8
ANNUAL
X"
4.8
5.4
5.0
5.5
4.9
7.8
7.1
5.5
5.2
4.7
6.9
4.1
4.6
5.7
5.6
11.1
4.9
5.6
11.5
5.1
5.3
SD
0.7
0.8
0.7
3.1
0.5
3.9
4.1
1.5
3.7
1.0
0.3
0.7
1.3
0.2
0.3
5.8
0.2
0.5
1.1
2.0
1 .1
-121-
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4-> W «» -Mi r-
-127-
-------
Table A-6a.
Descriptive statistics for chemical and physical constituents
in the nearshore waters of Lakes Huron and Superior, 1975
"'TEMPERATURE
Lake Superior
Black River
Ontonagon
Upper Portage Entry
Lower Portage Entry
Eagle Harbor
Isle Royal e
Big Bay
Presque Isle
Carp River
Marquette Harbor
Munising
Grand Marais
Tahquamanon
Lake Huron
Detour
Cheboygan
Calcite
Presque Isle
Alpena
Harrisville
Tawas
Saginaw Bay
Harbor Beach
Lexington
Lake Superior
Black River
Ontonagon
Upper Portage Entry
Lower Portage Entry
Eagle Harbor
Isle Royale
Big Bay
Presque Isle
Carp River
Marquette Harbor
Munising
Grand Marais
Tahquamanon
Lake Huron
Detour
Cheboygan
Calcite
Presque Isle
Alpena
Harrisville
Tawas
Saginaw Bay
Harbor Beach
Lexington
N
3
10
3
3
-
18
6
10
10
10
10
10
3
10
10
10
10
14
10
_
9
10
10
N
-
8
-
-
8
12
-
8
8
8
8
8
8
8
8
8
12
8
_
8
8
8
X
8.6
9.8
6.5
7.6
-
4.5
7.5
8.3
8.3
9.6
10.9
11.3
14.0
8.8
12.2
10.7
10.2
12.9
8.8
-
21.2
10.0
11.1
TURBlblYV
(O.T.U.)
X
-
9.1
-
-
0.5
0.5
-
1.3
0.5
0.4
0.9
0.1
0.4
1.3
1.1
0.9
1.3
0.7
_
2.4
1.0
0.7
SD
4.0
1.5
2.6
0.5
-
0.9
2.9
3.8
2.8
4.1
4.4
1.4
0.8
1.4
2.4
0.5
0.5
2.5
1.1
_
5.7
2.6
2.0
SD
-
13.6
-
-
0.0
0.1
-
0.9
0.3
0.1
0.5
0.0
0.1
0.5
0.4
0.4
0.5
0.1
2.4
0.4
0.3
DISSOLVED OXYGEN pH
N
3
10
3
3
-
18
6
10
10
10
10
10
3
10
10
10
10
14
10
1
9
10
10
N
.
8
-
-
8
12
-
8
8
8
8
8
-
8
8
8
8
12
8
-
8
8
8
X
11.9
11.2
12.8
12.5
-
12.3
11.7
12.7
13.1
12.7
12.4
12.6
11.7
12.3
11.0
11.5
11.8
11.1
13.3
8.7
10.7
12.6
13.0
CHLORIDE
(mg/1 )
X"
.
2
-
-
1
1
-
1
2
1
1
1
-
4
6
6
6
6
6
-
SD N X SD
1 .2
1.0
0.9
0.1
-
0.2 12 7.6
0.6
0.8
0.7 8 7.7
0.7 6 7.8
0.8
0.4 8 7.6
0.2
0.7
0.6
0.6 8 7.9
0.4
1.1
0.4
0
2.5
0.8
1.0
sWi
SU. N X" SD
.
1 852
_ - -
- - -
0 830
0 12 3 1
_
0 841
1 832
0 831
0 830
0 831
-
1 8 11 1
1 8 14 2
1 8 14 1
1 8 14 1
2 12 16 1
0 8 1
- - -
16 12 8 22 6
6
5
0 8 15 1
0 8 15 1
-128-
-------
Table A-6a. (continued)
CONDUCTIVITY
Lake Superior
Black River
Ontonagon
Upper Portage Entry
Lower Portage Entry
Eagle Harbor
Isle Royal e
Big Bay
Presque Isle
Carp River
Marquette Harbor
Munising
Grand Marais
Tahquamanon
Lake Huron
Detour
Cheboygan
Calcite
Presque Isle
Alpena
Harrisville
Tawas
Saginaw Bay
Harbor Beach
Lexington
N
3
10
3
3
-
18
6
10
10
10
10
10
3
10
10
10
10
14
10
_
9
10
10
(ym ho/cm)
X
87
90
88
85
-
85
85
85
101
88
88
85
85
137
222
188
190
208
183
_ .
242
197
190
TOTAL UISSULVEU bUUUS
SD
2
9
4
1
-
1
1
3
27
3
2
1
1
21
28
10
5
14
3
57
5
4
TOTAL ORTHO-PHOSPHATE
(mg/1)
Lake Superior
Black River
Ontonagon
Upper Portage Entry
Lower Portage Entry
Eagle Harbor
Isle Royale
Big Bay
Presque Isle
Carp River
Marquette Harbor
Munising
Grand Marais
Tahquamanon
Lake Huron
Detour
Cheboygan
Calcite
Presque Isle
Alpena
Harrisville
Tawas
Saginaw Bay
Harbor Beach
Lexington
N
2
8
2
2
8
12
O
8
e
8
a
8
2
8
8
8
8
12
8
-
8
8
8
X
0.001
0.006
0.002
0.001
0.002
0.000
0.000
0.001
0.037
O.OOl
0.002
0.001
0.001
0.002
0.002
0.002
0.001
0.003
0.001
-
0.004
0.000
0.000
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
0
SD
.001
.008
.001
.001
.001
.000
.000
.001
.068
.001
.003
.001
.001
.001
.001
.001
.001
.001
.001
-
.007
.001
.001
N
2
8
2
2
12
2
8
6
8
8
8
8
8
8
8
12
8
4
8
8
TOTAL
N
2
8
2
2
8
12
2
8
6
8
8
8
2
8
8
8
8
12
8
-
8
8
8
(mg/1)
X"
57
60
57
56
55
55
56
59
59
59
56
85
152
126
124
139
119
146
128
126
ALKALNITY
(mq/1)
SD
1
4
1
0
1
1
0
3
1
1
1
-
9
14
5
3
5
1
_
26
2
1
PHOSPHORUS
(mg/1)
X
0.004
0.015
0.003
0.002
0.004
0.003
0.005
0.004
0.059
0.006
0.005
0.006
0.002
0.003
0.005
0.003
0.005
0.018
0.005
-
0.032
0.008
0.006
SD
_
0.021
0.001
-
0.002
0.004
0.001
0.006
0.109
0.003
0.002
0.002
0.001
0.001
0.001
0.001
0.001
0.009
0.001
-
0.044
0.003
0.003
N
8
8
12
-
8
8
8
8
8
-
8
8
8
8
12
8
-
8
8
8
X
41
40
44
-
40
46
44
41
41
-
59
100
79
81
91
72
-
91
82
81
SD
1
1
1
-
2
4
1
1
1
~
8.4
19.3
3.3
,2
7.1
1.0
~
11.1
1 .3
1.3
SILICON DIOXIDE
(mg/1)
N
-
8
-
-
8
12
-
8
8
8
8
8
-
8
8
8
8
12
8
-
8
8
8
X
-
2.
-
-
2.
2.
-
2.
2.
2.
2.
2.
-
1.
2.
1.
1.
1.
1.
-
0.
0.
0.
5
1
1
4
4
0
2
0
3
0
3
2
1
0
7
6
8
SD
.
0.8
-
-
0.0
0.0
-
0.1
0.2
0.0
0.1
0.0
-
0.1
1.6
0.1
0.1
0.3
0.1
-
0.4
0.3
0.0
continued
-129-
-------
Table A-6a. (continued)
CHLOROPHYLL-a
Lake Superior
Black River
Ontonagon
Upper Portage Entry
Lower Portage Entry
Eagle Harbor
Isle Royale
Big Bay
Presque Isle
Carp River
Marquette Harbor
Munising
Grand Marais
Tahquamanon
Lake Huron
Detour
Cheboygan
Calcite
Presque Isle
Alpena
Harrisville
Tawas
Saginaw Bay
Harbor Beach
Lexington
N
4
-
-
4
6
-
4
4
4
4
4
-
4
4
4
4
6
4
.
3
4
4
(V9/D
X
3.06
-
-
1.78
1.48
-
2.94
4.63
3.68
2.40
1.60
-
1.80
6.62
1.98
1.91
11.34
4.74
-
60.50
4.18
3.38
SD
0.28
-
-
0.11
0.27
-
1.02
1.74
0.90
0.71
0.39
-
0.47
8.48
0.09
0.24
5.50
1.20
-
46.76
1.17
0.91
AMMONIA-NITROGEN
N
2
8
2
2
8
12
2
8
8
8
8
8
2
8
8
8
8
12
8
-
8
8
8
ORGANIC-NITROGEN
Lake Superior
Black River
Ontonagon
Upper Portage Entry
Lower Portage Entry
Eagle Harbor
Isle Royale
Big Bay
Presque Isle
Carp River
Marquette Harbor
Munising
Grand Marais
Tahquamanon
Lake Huron
Detour
Cheboygan
Calcite
Presque Isle
Alpena
Harrisville
Tawas
Saginaw Bay
Harbor Beach
Lexington
N
2
8
2
2
8
12
2
8
8
8
8
8
2
8
8
8
8
12
8
-
8
8
8
(mq/1)
x"
0.09
0.14
0.08
0.08
0.08
0.10
0.08
0.10
0.17
0.11
0.09
0.08
0.08
0.11
0.14
0.12
0.13
0.25
0.17
-
0.56
0.23
0.19
SD
0.01
0.09
0.00
0.00
0.02
0.02
0.02
0.03
0.20
0.02
0.01
0.01
0.03
0.02
0.03
0.02
0.01
0.07
0.02
-
0.51
0.04
0.03
N
2
8
2
2
8
12
2
8
8
8
8
8
2
8
8
8
8
12
8
-
8
8
8
(mq/1 )
jf
0.003
0.004
0.003
0.002
0.005
0.001
0.001
0.002
0.015
0.001
0.002
0.001
0.001
0.002
0.005
0.003
0.003
0.016
0.004
-
0.009
0.005
0.001
SD
0.002
0.003
0.001
0.001
0.002
0.002
0.001
0.002
0.021
0.002
0.002
0.001
0.001
0.001
0.002
0.001
0.001
0.011
0.001
-
0.005
0.004
0.001
NITRATE-NITROGEN
N
2
8
2
2
8
12
2
8
8
8
8
8
2
8
8
8
8
12
8
-
8
8
8
TOTAL -NITROGEN
(mg/1)
X"
0.37
0.40
0.39
0.38
0.39
0.40
0.35
0.36
0.4?
0.36
0.34
0.33
0.30
0.39
0.32
0.37
0.36
0.44
0.42
-
0.71
0.51
0.45
SD
0.04
0.06
0.00
0.01
0.02
0.02
0.00
0.04
0.20
0.02
0.02
0.02
0.03
0.02
0.02
0.02
0.02
0.06
0.03
-
0.43
0.07
0.03
N
.
8
.
_
8
12
-
8
8
8
8
8
-
8
8
8
8
12
8
_
8
8
8
(mq/1)
I
0.27
0.26
0.31
0.30
0.30
0.30
0.27
0.26
0.26
0.26
0.25
0.25
0.22
0.27
0.18
0.24
0.23
0.18
0.24
-
0.14
0.28
0.26
'COD
(mg/1)
Y
_
7.0
_
_
2.2
2.6
-
6.8
3.8
1.3
5.9
2.0
-
4.8
4.5
3.0
3.1
10.6
3.7
.
15.0
3.9
3.3
SD
0.03
0.04
0.01
0.01
O.Q1
0.01
0.01
0.04
0.02
0.01
0.01
0.01
0.00
0.01
0.05
0.01
0.01
0.03
0.01
-
0.11
0.06
0.01
SD
_
8.0
-
-
0.6
1.3
-
1.6
3.3
0.7
1.9
0.7
-
0.6
2.1
1.2
1.0
4.5
2.2
-
10.1
1.5
2.1
continued
-130-
-------
Table A-6a. (continued)
CADMIUM
CHROMIUM
ARSENIC
(uq/l )
so
SD
SD
Lake Superior
Black River
Ontonagon
Upper Portage Entry
Lower Portage Entry
Eagle Harbor
Isle Royale
Biq Bay
Presque Isle
Carp River
Marquette Harbor
Munising
Grand Marais
Tahquamanon
Lake Huron
Detour
Cheboygan
Calcite
Presque Isle
Aloena
Harrisville
Tawas
Saqinaw Bay
Harbor Beach
Lexington
0.9
0.8
0.8
0.9
0.9
0.7
0.7
0.7
0.8
0.7
0.8
0.8
0.9
0.9
0.8
0.8
0.8
0.9
0.8
0.7
0.7
0.3
0.1
0.2
0.1
0.1
0.2
0.2
0.1
0.0
0.2
0.1
0.1
0.0
0.1
0.09
0.15
0.04
0.11
0.16
0.04
0.23 t
0.05
0.06
0.06
0.06
0.48*t
0.08
0.07
0.13
0.01
0.02
0.00
0.00
0.13
0.03
0.03
0.05
0.04
0.31
0.03
3
3
3
3
3
3
3
5
3
3
< 0.04
< 0.03
< 0.04
< 0.04
0.12
0.15
0.14
0.10
0.10
0.04
0.01
0.01
0.01
-
0.16
0.04
0.07
0.05
0.07
0.01
t Exceeds EPA criteria
* Exceeds IJC objectives
0.5
0.4
0.3
0.3
0.3
0.3
1.3
0.3
0.3
0.3
0.5
0.4
0.4
0.3
0.3
0.8
0.4
0.5
0.4
0.10
0.04
0.00
0.10
0.10
0.00
0.10
0.10
0.04
0.10
0.10
0.05
0.90
0.04
0.10
0.02
COPPER
(yq/1)
IRON
(ug/1)
MERCURY
(ug/D
SD
SD
SD
Lake Superior
Black River 3 1.7
Ontonaqon 3 1.5
Upper Portage Entry 3 1.3
Lower Portage Entry 3 1.9
Eagle Harbor 3 1.4
Isle Royale 3 1.0
Big Bay 3 1.5
Presque Isle 3 0.9
Carp River 3 1.3
Marquette Harbor 3 1.3
Munising 3 1.7
Grand Marais 5 2.6
Tahquamanon 5 1.8
Lake Huron
Detour 3 0.9
Cheboygan 3 l.o
Calcite 3 2.5
Presque Isle 3 0.7
Alpena 3 1.4
Harrisville 3 3.4
Tawas 3 2.2
Saginaw Bay 5 1.7
Harbor Beach 3 1.4
Lexington 3 1.1
0.6
0.9
0,4
0.4
0.2
0.3
0.4
0.2
0.2
0.4
1.0
0.8
0.3
3.2
0.1
0.4
0.7
0.8
19
30
43
9
49
6
8
7
6
6
9
9
10
21
16
24
24
11
14
22
8
23
18
1.7
7.6
16.0
1.1
16.0
1.4
1.9
1.0
0.8
1.3
1.4
1.5
3.3
1.8
1.8
6.0
6.9
2.8
2.0
5.8
1.0
10.0
1.8
0.02
0.02
0.02
0.02
0.02
0.02
0.02
0.02
0.02
0.02
0.02
0.03
0.04
0.02
0.02
0.02
0.02
0.02
0.03
0.04
0.02
0.01
0.01
0.01
continued
-131-
-------
Table A-6a. (continued)
Lake Superior
Black River
Ontonagon
Upper Portage Entry
Lower Portage Entry
Eagle Harbor
Isle Royale
Big Bay
Presque Isle
Caro River
Marquette Harbor
Munising
Grand Marais
Tahquamanon
Lake Huron
Detour
Cheboyqan
Calcite
Presque Isle
Alpena
Harrisville
Tawas
Saqinaw Bay
Harbor Beach
Lexinqton
N
3
3
3
3
3
3
3
3
3
3
3
5
5
3
3
3
3
3
3
3
5
3
3
MANGANESE
(ug/1)
X"
0.6
0.6
0.6
0.6
0.8
0.3
0.4
0.3
0.6
0.6
0.7
0.3
0.5
1.3
1.1
1.2
1.3
1.3
1.0
1.9
1.2
1.5
1.3
SD
0.0
0.1
0.1
0.2
0.2
0.0
0.1
0.0
0.2
0.2
0.1
0.3
0.2
0.1
0.1
0.0
0.1
0.2
0.1
0.1
0.1
0.1
0.3
N
3
3
3
3
3
3
3
3
3
3
3
5
5
3
3
3
3
3
3
3
5
3
3
NICKEL
(uq/1)
I SD
0.8
0.8
0.9 0.2
0.8
0.8
0.9
0.8
0.8
0.4
0.8
0.8
0.8
0.9
< 0.9 0.1
< 0.8
< 0.8
< 0.9 0.1
< 0.8
< 0.9 0.1
0.9 0.1
1.0 0.1
1.4 0.4
0.9 0.1
N
3
3
3
3
3
3
3
3
3
3
3
5
5
3
3
3
3
3
3
3
5
3
3
LEAD
(uq/1)
x"
0.5
0.4
0.2
0.3
0.2
0.2
0.5
0.3
0.4
0.4
0.4
0.8
0.4
0.4
0.4
0.4
0.4
0.7
1.0
0.8
0.5
0.7
0.7
SD
0.3
0.3
0.1
0.0
0.1
0.0
0.2
-
0.1
-
0.2
0.4
0.2
0.3
0.2
0.0
0.2
0.4
0.7
0.2
0.2
0.1
0.3
ZINC
(uq/1)
Lake Superior
Lake Superior
Black River
Ontonagon
UDDer Portage Entry
Lower Portage Entry
Eagle Harbor
Isle Royale
Big Bay
Presque Isle
Carp River
Marquette Harbor
Munising
Grand Marais
Tahquamanon
Lake Huron
Detour
Cheboygan
Calcite
Presque Isle
Alpena
Harrisville
Tawas
Sag in aw Bay
Harbor Beach
Lexinqton
N
3
3
3
3
3
3
3
3
3
3
3
5
5
3
3
3
3
3
3
3
5
3
3
X
2.3
1.6
1.7
4.4
1.5
1.5
2.6
1.1
1.0
1.0
2.1
2.7
2.4
< 2.5
< 1.9
< 2.3
< 1.6
< 3.0
4.9
2.4
< 1.3
2.5
2.2
SD
1.0
0.6
1.2
2.8
0.3
0.4
1.0
0.2
0.1
0.4
0.9
0.9
1 .3
0.4
0.6
0.8
0.4
1.3
3.7
0.9
0.5
0.4
0.6
-132-
-------
UD ^o co ro r-- < ro <^- roro
O O O O O r fOOOOO
iOcOCnO^i CT> CTi O CO CO
i OOOi OOi Oi
co co ai o cr» co «=* ico^c
OOOi O O i IOO
. LO
o r-
o en
J~ O OJ
OJ S- , rtS
> -U C
fO t/l -
r*~ o LO ro i «^r o o '
CNJ. c\jvoc\Jc\jr--r^.c
juni ODCT^cr^frCNJO
O i OOOi ^fi i
< i cocoooo^coroocococo
cocococooocoooocn
C\JrOi CO L
ii criroi OP--OCNJ
-
Q)
0
CD
tonagon
c:
M +->
QJ Q)
Q- 0
S- rtJ I i Q)
31 O >> O -i
Q-" iri n rv
QJ CD CT
uS^mct o
OJ S- C
iff 1
CT-i C O"
E J:o£
o
S-
13
n:
OJ
1
c
en
3 O
O -0
O C_J
IO rD
i i CQ
QJ S-
=J Q)
CTT3
to C
d. H;
« to
oj i-
-------
Table A-7.
Descriptive statistics for sediment constituents in the
nearshore waters of Lakes Superior and Huron, 1974.
Location
lake Superior
Slack River
C.itonagon
Upper Portage Entry
Lower Portage Entry
Eagle Harbor
Isle koyale
Big Bay
Presque Isle (Marquette)
Carp River (Marquette)
ionising
S'and Marais
W*i1tefi:h Point
Lake Huron
Os tour
Cheboygan
Presque Isle
Alpena
Harrisville
Tav»oS
Sagi.naw Bay
Harbor Beach
Lexington
Cases
Minimum
0.2
O.2
0.2
0.2
2.6
0.5
0.2
<0.2
<0.2
4.7
0 5
0.3
0.2
<0.2
0.5
0.3
0.4
0.2
<0.2
0.2
0.2
-- vu i at i te
(*)'
Maximum
0.2
2.2
0.6
0.2
2.6
0.5
0.2
0.5
0.4
32.0
0.5
0.4
0.2
0.7
0.5
0.8
0.4
0.6
0.3
0.9
0.2
OU 1 1 Gb--
t
Mean
0.2
0.8
0.4
0.2
2.6
0.5
0.2
0.3
0.3
13.0
0.5
0.4
0.2
0.4
0.5
0.5
0.4
0.4
0.2
0.5
0.2
Standard
Deviation
0.7
0.2
0.0
0.0
0.2
0.1
10.4
0.1
0.2
0.2
0.1
0.1
0.3
---
Minimum
6.4
7.2
7.4
6.1
7.3
7.2
6.7
6.7
6.5
5.4
7.5
6.2
7.6
7.1
7.5
7.2
7.2
7.6
7.4
6.8
8.0
y
Maximum
6.4
7.9
7.6
6.5
7.3
7.3
6.7
7.5
6.8
6.7
7.5
6.8
7.6
7.7
7.5
7.5
7.2
8.0
7.7
7.0
8.0
Mean
6.4
7.5
7.5
6.3
7,3
7.3
6.7
7.0
6.6
6.1
7.5
6.5
7.6
7.5
7.5
7.4
7.2
7.8
7.fi
6.9
8.0
Standard
Deviation
0.2
0.1
0.2
0.1
0.3
0.1
0.5
0.4
0.2
0.1
0.1
0.2
0.1
* EPA Criterion:
-Total Kjeldahl Nitrogen-
(mg/kg)*
-Total Solids-
Location Cases
lake Superior
Black River 1
Ontonagon 6
Upper Portage Entry 3
Lower Portage Entry 3
Eagle Harbor 1
Isle Royale 2
Big Cay 1
Presque Isle (Marquette) 6
Carp River (Marquette) 6
Munis ing 6
Grand Marais 1
Whitefish Point 2
Lake Huron
Detour i
Cheboygan 5
Presque Isle 1
Alpena 6
Harrisville 1
Tawas 6
Sagi.naw Bay 3
Harbor Beach 4
Lexington 1
* EPA Criterion: 1,000 mg/kg
Standard
Mini mum Maximum Mean Deviation
486
86
20
160
13
34
691
156
Minimum Maximum Mean
27
23
18
81
80
120
55
36
39
3,300
T4"
220
24
82
120
440
80
230
38
590
360
27
1.200
170
120
80
340
55
72
130
4,700
440
24
2,500
120"
1,700
80
500
240
4.100
360
27
394
71
98
80
116
55
54
62
3,766
I/I
i *f
330
24
356
120
1,033
80
330
110
2,573
360
87
70
80
81
86
60
81
80
81
20
84
75
87
73
66
56
90
74
84
43
85
87
90
85
82
86
73
81
89
84
38
84
81
87
86
66
81
90
84
91
78
85
87
83
83
81
86
67
81
83
83
27
84
78
87
82
66
72
90
81
88
56
85
Standard
Deviation
5
0
4
4
15
-134-
-------
Table A-7 (continued)
Chemical Oxygen Demand-
(mg/kg)*
-Total Phosphorus-
(mg/kg)*
Standard
Location
lake Superior
Black River
Ontonagon
Upper Portage Entry
Lower Portage Entry
Eagle Harbor
Isle Roy ale
Big Bay
Presque Isle (Marquette)
Carp River (Marquette)
Munis ing
Grand Marais
Whitefish Point
Lake Huron
Detour
C'neboygan
Presque Isle
Alpena
Harris vi lie
Taw as
Saginaw Bay
Harbor Beach
Lexington
* EPA Criterion: 50,000
Location
lake Superior
Black River
Ontonagon
Upper Portage Entry
Lower Portage Entry
Eagle Harbor
Isle Royale
Big Bay
Presque Isle (Marquette)
Carp River (Marquette)
i'5unising
Grand Marais
Whitefish Point
Lake Huron
Detour
Cheboygan
Presque Isle
Alpena
Harrisville
Taw as
Sagi.naw Bay
Harbor Beach
Lexington
Cases
1
6
3
3
1
2
1
6
6
6
2
1
5
1
6
1
6
3
4
1
mg/kg
Cases
1
6
3
3
1
2
1
6
6
6
1
2
5
i
1
3
A
4
i
Minimum
900
400
700
1,700
900
6,000
2,000
1,200
700
200,000
6,200
500
2,600
27,000
9,300
2,000
7,900
1,500
32,000
5,400
Minimum
0.8
0.4
0.5
0.7
0.6
1.2
1.4
o'.5
0.6
4*2.
0.1
0.8
2.0
0.5
In
. d
1. 1
1.3
0.7
1.1
411
.4
40
Maximum
900
85,000
6,500
2,200
900
12,000
2,000
2,400
2,400
660,000
TiOTT
8,300
500
51.000
27,000
82.000
2,000
17,000
5,200
83,000
5,400
Total
Mean
900
18,950
2,633
1,866
900
9,000
2,000
1,917
1,600
380,000
7,250
500
27,180
27,000
33,883
2,000
11,283
2,766
62.000
5,400
(mg/kg) *
Maximum Mean
0.8
7.4
0.7
0.9
0.6
i fi
1 . D
1 4
i.'o
1.1
0. 1
o.'g
2.0
1.1
1.2
H
1.3
1.1
5.6
7.3
0.8
0.8
0.6
0.8
0.6
I/i
. 4
1 A
\ . 4
0.7
0 7
fr
" . i
0.9
2.0
1.0
1.2
2.9
1.3
0.9
2.9
5.2
TTT
Deviation
33,213
3,348
288
4,242
462
551
192,561
1,484
29,711
26,608
3,757
2,107
22,315
Standard
Deviation
0.4
0.1
0.1
0.3
0.2
Oo
. £
1.8
0.1
0.4
1.9
0.1
2.4
1.4
Standard
Minimum Maximum Mean Deviation
21
49
28
60
154
62
28
42
44
13
16
24
* EPA Criterion: 420.0 mg/kg
60
71
40
85
110
21
320
56
110
150
57
80
63
19
55
50
22
30
9
15
66
60
130
130
140
110
28
320
220
5ZO
310
57
120
63
77
55
160
22
64
38
65
66
60
91
97
112
110
25
320
137
302
235
57
100
63
56
55
78
22
49
20
50
66
-Total Cadmium---
(mg/kg)*
Minimum Maximum Mean
Standard
Deviatiot
<0.4
<0.4
<0.4
<0.4
<0.4
O.4
<0.4
<0.4
<0.4
<0.4
<0."
<0.4
<0.4
O.4
<0.4
<0.4
<0.4
<0.4
<0.4
<0.4
<0.4
<0.4
<0.4
<0.4
<0.4
<0.4
<0.4
<0.4
<0.4
<0.4
<0.4
<0 6
<0."4
<0.4
^0.4
<0.4
<0.4
-------
Table A-/ (.continued)
Location
Black River
Ontonagon
Upper Portage Entry
Lower Portage Entry
Eagle Harbor
Isle Royale
Big Cay
Prssque Isle (Marquette)
farp River (Marquette)
Munising
Grand Marais
Whitefish Point
Lake Huron
Detour
C^eboygan
Presque Isle
A i pen A
Harnsville
Tawas
Sagi.naw Bay
Harbor Beach
Lexington
* EPA Criterion 25 mg/kg
Cases
(mg/kq)*
Minimum
0.4
3.2
4.8
1.8
1.4
12 0
2.6
3.8
2.0
2.4
0.2
<0.2
-------
Table A-7 (continued)
Location Cases
lake Superior
Black River 1
Ontonagon 6
Upper Portage Entry 3
Lower Portage Entry 3
Eagle Harbor 1
Isle Royale 2
Big Bay 1
Presque Isle (Marquette) 6
Carp River (Marquette) 6
Munis ing 6
Erand Marais 1
Whitefish Point 2
Lake Huron
Colour 1
Cheboygan 5
Proxue Isle 1
Alpena 6
Herrisvilie 1
IcWaS 6
Sagi.naw Bay 3
Harbor Beach 4
Lexington 1
(mg/kg)*
Minimum
56
48
50
24
82
300
64
48
36
100
17
28
130
17
120
42
38
42
20
190
110
Maximum
56
160
240
36
82
640
64
310
76
220
17
58
130
110
120
110
38
240
100
280
110
Mean
56
87
125
31
82
470
64
108
54
172
17
43
130
53
120
70
38
121
63
243
110
Standard
Deviation
44
101
6
240
99
16
40
21
36
23
76
40
45
-Total Mercury-
(mg/kg)*
Minimum Maximum Mean
<0.1
<0.1
<0.1
<0.1
<0.
0.2
<0 1
0.1
0.5
.1
<0.1
O.I
O.I
0.1
0.3
O.'l
1 0.1
1 O.I
1 O.I
1 O.I
1 O.I
1 0.1
1 O.I
1 0.1
1 <0.1
<0.1
<0.1
<0.1
<0.1
<0.1
<0.1
<0.1
<0. 1
<0. 1
Standard
Deviation
0.1
* EPA Criterion: 300.0 mg/kg
Location Cases
lake Superior
Black River 1
Ontonagon 6
Upper Portage Entry 3
Lower Portage Entry 3
Eagle Harbor i
Isle Royale 2
Big Bay 1
Presque Isle (Marquette) 6
Carp River (Marquette) 6
Muni sing 6
Grand Marais ")
Whitefish Point 2
Lake Huron
Detour 1
Cheboygan 5
Presque Isle l
Alpena 6
Harrisville l
Tawas 6
Sagi.naw Bay 3
Harbor Beach 4
Lexington 1
* L?n Criterion 20.0 rag/kg
(mg/kg)*
Minimum
4
5
10
2
13
38
T
6
<]
16
2
4
2
<1
20
6
5
7
2
24
TO
Maximum
4
20
38
2
13
78
~3~
140
5
38
"2
6
2
12
20
15
5
20
8
38
To
Mean
4
10
22
2
13
58
~S
1
28
2
5
2
5
20
10
5
13
6
31
10
Standard
Deviation
6
15
0
__
28
52
2
9
1
4
3
__
6
3
6
-Total Selem'um-
(mg/kg)
Minimum Maximum Mean
<0.1 <0.1
<0.1 <0.1
<0.1 <0.1
<0.1 <0.1
<0.1 <0.1
<0.1 <0.1
<0.1 <0.1
<0.1 <0.1
<0.1 <0.1
<0.1 <0.1
<0.1
Standard
Deviation
continued
-137-
-------
Table A-7 (continued)
Location
Lake Superior
Black River
Ontonagon
Upper Portage Entry
Lower Portage Entry
Eagle Harbor
Isle Royale
Big Bay
Presque Isle (Marquette)
Carp River (Marquette}
Muni sing
Grand Marais
Whitefish Point
Lake Huron
Detour
Cheboygan
Presque Isle
Alpena
Harrisville
Tawas
Saginaw Bay
Harbor Beach
Lexington
Cases
1
6
3
3
1
2
1
6
6
6
1
2
1
5
1
6
1
6
3
4
1
Minimum
8.8
6.4
10.0
6.8
14.0
44.0
22.0
10.0
6.6
87.0
16.0
14.0
5.4
5.6
34.0
24.0
26.0
12.0
3.4
44.0
70.0
I U Ld I L- 1
(mg/kg]
Maximum
8.8
22.0
30.0
9.0
14.0
84.0
22.0
48.0
17.0
190.0
16.0
19.0
5.4
140.0
34
44
26
26
12
170
"TO
1*
Mean
8.8
13.0
19.0
8.1
14.0
64.0
22.0
21.8
11.1
134.0
160
ie'.5
5.4
40.7
34.0
31.0
26.0
19.6
8.3
126.0
70.0
Standard
Deviation
6.2
10.1
1.2
28.2
13.9
3.4
42.5
3.5
55.8
7.3
5.5
4.4
57.2
(mq/kn)*
Cases
1
3
2
2
1
2
2
3
3
5
3
1
3
1
3
1
3
4
2
1
Minimum
310
230
5400
<35
300
95
<35
<35
<35
1500
290
350
250
430
440
240
210
140
1300
330
Maximum
310
540
5400
<35
300
460
70
940
90
61,000
6000
350
3900
430
2000
240
400
230
1400
330
Mean
310
370
5400
^35
300
278
44
325
91
16,840
3997
350
1817
430
1180
240
330
195
1350
330
Standard
Deviation
157.2
0.0
0.0
258.1
36.8
532.3
88.9
24,867.3
3213.6
1879.1
783.1
104.4
40.4
70.7
...
*EPA Criterion 90 mg/kg
*EPA Criterion 1000 mg/kg
Location
Lake Superior
Black River
Ontonagon
Upper Portage Entry
Lower Portage Entry
Eagle Harbor
Isle Royal e
Big Bay
Presque Isle (Marquette)
Carp River (Marquette)
Munising
Grand Marais
Whitefish Point
Diethyhexelphthalate-
(yg/kg)
Cases Minimum Maximum
SD
<90
300
<90
330
390
<90
230
<90
250
270
<90
500
310
370
390
<90
600
390
350
17,000
<90
396
178
350
390
<90
315
272
290
4994
100
187
28
-
-
120
196
53
6855
(vg/kg)
Cases
1
3
2
2
1
2
2
3
3
5
Minimum
100
no
210
110
280
<60
<60
<60
<35
<60
Maximum
100
220
260
120
280
<60
150
160
190
540
X
100
163
235
115
280
<60
105
103
92
330
SD
0
55
35
7
0
.
64
67
88
274
240
370
316
68
11
260
330
287
38
Lake Huron
Detour
Cheboygan
Presque Isle
Alpena
Harrisville
Tawas
Saginaw Bay
Harbor Beach
Lexington
350
<90
<90
<90
<90
<90
<90
<90
410
350
290
<90
350
<90
<90
<90
<90
410
350
126
<90
147
<90
<90
<90
<90
410
-
141
-
176
_
0
0
0
0
1
2
1
3
1
4
2
1
150
350
260
<200
180
<60
<200
<60
520
150
390
260
210
180
370
290
<60
520
150
370
260
137
180
143
173
<60
520
_
28
.
64
.
196
91
0
-
continued
-138-
-------
Table A-7 (continued)
U.S. EPA guidelines for the pollutional classification
of Great Lakes Harbor sediments, 1977.
PARAMETERS
Non
Polluted
Moderately
Polluted
Heavily
Polluted
Volatile Solids (%)
Oil and Grease
COD
Total Phosphorus
Ammonia
TKN
Cyanide
Iron
Manganese
Barium
Lead
Mercury
Nickel
Arsenic
Cadmium
Chromium
Copper
Zinc
<5
<1 ,000
<40,000
<420
<75
<1,000
<0.10
<17,000
<300
<20
<40
<1.0
<20
<3
*
<25
<25
<90
5-8
1,000-2,000
40,000-80,000
420-650
75-200
1,000-2,000
0.10-0.25
17,000-25,000
300-500
20-60
40-60
N.A.
20-50
3-8
*
25-75
25-50
90-200
>8
>2,000
>80,000
>650
>200
>2,000
>0.25
>25,000
>500
>60
>60
>1.0
>50
>8
>6
>75
>50
>200
* Lower limits not established
-139-
-------
Table A-8.
Descriptive statistics for sediment constituents in the
nearshore waters of Lakes Superior and Huron, 1975.
Location Cases
Lake Superior
Marquette Harbor 4
Lake Huron
Calcite 4
Saginaw Bay t 2
Location Cases
Lake Superior
Marquette Harbor 4
Lake Huron
Calcite 4
Saginaw Bay t 2
* EPA Criterion: 420 mg/kg
Location Cases
Lake Superior
Marquette Harbor 4
Lake Huron
Calcite 4
Saginaw Bay t 2
(mg/kg)
Minimum Maximum i'can
0.5 0.7 0.7
0.2 0.6 0.3
0.7 1.3 1.0
(mg/kg)*
Minimum Maximum Mean
32 62 47
8 23 16
21 29 25
Minimum Maximum Mean
80 85 83
64 91 72
83 83 83
Standard
Deviation
0.1
0.2
0.4
Standard
Devi at ion
15
6
6
Standard
Deviation
2
13
0.0
(mg/kg)
Minimum Maximum
58 280
78 710
80 130
* EPA Criterion :
*
Mean
156
465
105
Standard
Deviation
107
271
85
1000 mg/kg
(mg/kp)*
Minimum t'aximum Mean
0.2 1.1
0.2 15.0
0.4 o 4
* EPA Criterion:
Vo"
Mini-r.um Maximum
0.4 0.4
0.2 0.5
0.4 0 4
1.0
5.9
0.4
75 mg/kg
latile So'
(%)*
Mean
0.4
0.3
0.4
Standard
Deviation
OB
6.2
0.0
lids
Standard
Deviation
0
0.2
0,0-
* EPA Criterion: 5% dry weight
t Saginaw Bay data was calculated without river stations
-140-
-------
Table A~8 (continued)
Location Cases
Lake Superior
Marqjette Harbor 4
Lake Huron
Calcite 4
Saginaw Bay ^ 2
* EPA Criterion: 50,000 mg/kg
Location Cases
Lake Superior
Marquette Harbor 4
Lake Huron
Calcite 4
Saginaw Bay + ?
* EPA Criterion: 6.0 mg/kg
Location Cases
Lake Superior
Marquette Harbor 4
Lake Huron
Calcite 4
Saginaw Bay u 2
Chemical Oxygen Demand
(mg/kg}*
Standard
Minimum Maximum Mean Deviation
920 8800 4880 4358
1300 30,000 2500 949
1300 2,800 2050 1%0
(mg/kg)*
Standard
Minimum Maximum Mean Deviation
0.2 0.2 0.2 0
0.2 0.2 0.2 0
0.4 0.4 0-4 0-0
(mg/kg)*
Standard
Minirum Mximum Mean Deviation
2.2 5.2 3.3 1.4
0.6 6.0 4.0 2.5
0.2 0.4 03 01
(mg/kg)*
Minumum Maximum Mean
0.5 1.0 0.7
0.4 1.8 0.9
0.8 1.8 1.3
*EPA Criterion: 3.0 mg/kg
(mg/kg)*
Minimum Maximum Mean
2.0 4.0 3.1
3.4 26.0 16.1
2.0 ? 6 23
* "PA Criterion: 25.0 mg/kg
(mg/kg)*
Minimum Maximum Mean
2000 2800 2200
1700 3800 2500
1600 2600 2100
Standard
Deviation
0.3
0.6
0.7
Standard
Deviation
0.8
9.4
0 4
Standard
Deviation
516.4
948.7
707
EPA Criterion: 25 mg/kg
* EPA Criterion: 17,000 mg/kg
t Saginaw Bay data was calculated without river stations
continued
-141-
-------
Table n-o (continued)
Total Lead
(mg/kg)*
Standard
-Total Manganese-
(mg/kg)*
Standard
Location
Lake Superior
Marquette Harbor
Lake Huron
Calcite
Saginaw Bay t
OLailQarU .juanuaiu
CasejL Minimum Maximum He an Deviation Hi "i mum Maximum Mean Deviation
2.0 8
4.0 12
0.5 2
4.5
1 .3
2.7
3.6
1 .1
24
56
19
70 53
88 74
36 28
22
13
12
* EPA Criterion: 40.0 rag/kg
Location
Lake Superior
Marquette Harbor
Lake Huron
Calcite
Saginaw Bay )
-Total Mercury-
(mg/kg)*
* EPA Criterion: 300.0 mg/kg
-Total Nickel-
(mg/kg)*
Standard
Standard
Cases, Minirum Maximum Mean Deviation Minimum Maximum Mean Deviation
0.01
0.01
C.02
o,02
0.07 0.05
0.02 0.02
0.02.
0.03
0.00
3.8
5.5
0.1
2.4
2.4
* EPA Criterion: 1.0 mg/kg
EPA Criterion: 20.0 mg/kg
Location
Lake Superior
Marquette Harbor
Lake Huro-i
Calcite
Saginaw Bay t
-Total Splenium-
(mg/kg)
Cases Minimum Maximum Mean
0.1
0.1
0.1 0.1
0.2 0.4
=.0.1 <0.1
Total Zinc
(mg/kg)*
Standard Standard
Deviation Minimum Maximum Mean Deviation
0.4
0.0
7.0 17.0 11.5
9.4
6.0
26.0 19.4
10.0 9, 0
4.1
7.1
2,8
t Saginaw Bay data was calculated without river stations
* EPA Criterion: 90.0 mg/kg
-142-
-------
Table A-9. List of ohytoplankton species found in nearshore
Lake Superior, spring and fall, 1974.
Chlorophyta
Ankistrodesmus
convolutus
AL falcatus
A^_ spiral is
Cer astern as
irregular is
Chlamydomonas
globosa ~
£._ polypyrenoideum
C^ snow ii
C. sp
C7|£ 1
IL l£l
Chlorella
ellipsoidea
Closteriopsis
longissima
Closterium gracile
C_. parvulum
Coelastrum dubium
C. kuetzingianum
C^_ microporum
reticulatum
sphaericum
Cosmarium contractual
£^_ formulosum
C^ psuedoprotuberans
C_^ subtumidum
C^ sp.
Crucigenia
apiculata
C^_ quadrata
£._ tetrapedia
Dactylococcus
infusionum
D._ sp.
Dictyosphaerium
ehrenbergianum
ID^ pulchellum
Dispora
crucigenioides
Elakatothrix
gelatinosa
£_._ v i r i d i s
£L SP-
frajiceia droescheri
F. ovalis
CToecystis amp 1 a
G^_ gigas
&. major
G^ sp.
Golenkinia
paucispina
G. radiata
G:
Tiyalotheca mucosa
Kirchneriella
cgntorta
K. lunar is
K^ obesa
Lagerheimia
ciliata
LL ci triform is
L_._ longiseta
].._ subsalsa
L^ sp.
Micractinium
pusillum
Mougeotia americana
VL_ elegantula
M^ sp.
^ocystis borgei
(L_ elliptica
Q^ pusilla
0^ submarina
Pediastrum
biradiatum
£_._ boryanum
P_._ duplex
£^_ duplex var.
gracilimum
P_._ tetras
Penium sp.
Scenedesmus abundans
S_._ acuminatus
S_^ acutiformis
S^_ arm at us
S^ bijuga
S^_ dimorphus
S^ longus
$._ obliquus
^ opoliensis
-143-
^ quadricauda
Schroederia setigera
Sphaerocystis
schoeteri
Staurastrum
chaetocercus
$._ dejectum
S^_ furcigerum
^ paradoxum
S_^ polymorphum
_S^_ sebaldi
Stipitococcus
vasiformis
S. sp.
Tetraedron
arthrodesmiforme
J_^ caudatum
J_._ minimum
!_._ pentaedricum
J_._ prescottii
T_^ trigonum
.
Tetrastrum glabrum
X^ heteracanthum
J._ regulare
Ulothrix
subconstricta
U^ subtil issima
U. sp.
Unknown Chlorophyta
Bacillariophyta
Achnanthes aff inis
A_^ clevei
A. flexella
A_^ hungarica
A^_ lanceolata
A^_ minutissima
AJ. sp.
Amphora ovalis
A_._ ovalis var.
lybica
A^ perpusilla
A^ sp.
Amphipleura
pellucida
continued
-------
Table A-9 (continued)
Amp hi pr or a ornata
AnomoeneiT vitrea
Astrionella formosa
A._ gracillima
Attheya zachariasi
Cocconeis diminuta
£._ pediculus
iL placentula
£._ sp.
Coscinodiscus rothii
Cyclotella antiqua
C._ atomus
£_._ caspia
C^_ comensis
C_._ comta
C_._ glomerata
C^_ kutzingiana
C_._ meneghiniana
£._ michiganiana
C_._ ocellata
C^ pseudostelligera
£_._ stelligera
C^ striata
F_,._ crotonensis
£_._ gracile.
F. harrissonii
.
C. sp. 1
Cymatopleura solea
Cymbel 1 a aff inis
£._ cesatii
C. cuspidata
£7 inaequaVTs
£_._ mirocephala
C^ postata'
C_._ sinuata
C_._ tumida
C_._ tumidula
C^ turgida
C_._ ventricosa
C^ sp.
Denticula elegans
JL_ tenuis
Diatoma elongatum
D_._ tenue
D^_ vulgare
Diploneis elliptica
CL_ marginestriata
2^ oculata
D^_ puella
Epithemia sp.
Eunotia pectinalis
Fragilaria capucina
F. construens
intermedia
lapponica
leptostauron
pinnata
vaucheriae
__
£_._
F_._
F_._
f_._
F.
Gomphonema
angustatum
^_ olivaceum
G.. SB..
Gyrosigma sp.
Melosira granulata
M._ islandica
VL_ varians
Meridion circulare
Navicula cryptocephala
IL_ cryptocephala
var. veneta
N_._ decussis
NL_ elginensis
IL_ exigua
_N^_ gregaria
H._ hustedii
N^ lanceolata
N_._ menisculus
N_._ placentula
N^ pupula
Nk_ radios a
N_._ reinhardtii
^L_ subtilissima
N_^ tripunctata
hL_ tuscula
N_^ viridula
Neidium affine
N_._ iridis
Nitzschia acicularis
N^_ bacata
N_._ filiform is
N^ fonticola
H._ gracilis
N_._ kutzingiana
N. linearis
Rhoicosphenia
curvata
Stephanodiscus astraea
S^ astraea var.
minutula
^._ dubius
_S^_ hantzschii
S_._ invisitatus
Surirella oval is
S^ ovata
S. robusta
Synedra acus
S^ amphicephala
S^ cyclopum
S_._ delictissima
$_._ radians
$_._ rumpens
$_._ tenera
$_._ ulna
S^_ vaucheriae
S^_ sp.
Tabellaria fenestrata
J_._ flocculosa
Unknown
Bacillariophyta
Cyanophyta
Anabaena
felissii
N^
N.
palea
sinuata
Opephora martyi
Rhizosolenia eriensis
R. longiseta
A. flos-aquae
A_._ planctonica
A_._ subcylindrica
A_._ wisconsinense
A^ sp.
Aphanocapsa
delicatissima
A_._ elachista
Aphanothece
clathrata
A_._ microspora
A_._ nidulans
A^ sp_^
Chamaasiphon
confervicola
Chroococcus
dispersus
C^_ kuetzingianum
C. limneticus
C_._ microspora
C_._ minor
C^ minutus
(continued)
-144-
-------
Table A-9 (continued)
C._ prescottii Cryptophyta
Coelosphaericum Chroomonas nordstedtll
naegelianum Cryptomonas erosa
Cyanarcus hamlformis ^ ovata
Dactylococcopsis
acicularis Rhodomonas minuta
2^_ fascicularis --
D.. smith 11 Pyrrophyta
JL. IPr. . Ceratium hirundinella
Gompnosphaena --
aponina Euglenophyta
^- lacustns Euglena sp.
Lyngbya contorta Phacus spT~
Merlsmopedia convoluta --
M^ punctata Chloromonadophyta
Micrpcystis Gonyostomum semen
aeruginosa Unknown flageTTites
M. flos-aquae
K incerta
Oscillatoria
acutissima
_0^ angusta
0_^ angustisslma
0._ prolifica
0^_ splendida
Q_._ subbrevis
0^ tenuis
Q._ sp.
Phormidium mucicola
£_._ tejiue
Unknown blue-green
Chrysophyta
Chrysosphaerella
longispina
Dinobryon bavaricum
Jh_ caudata
D._ divergens
D^ sertularia
D^_ sociale
D^ stipitatum
D^ tabellarTae
Mallomonas acaroides
!L caudata
Ophiocytlum
capitatum
Stjpltococcus
vasiformis
Synura ulvella
S\_ sp7
-145-
-------
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-160-
-------
Table A-15. List of phytoplankton species found in nearshore Lake Huron
spring and fall, 1974.
Chlorophyta
Ankistrodesmus
convolutus
A^ falcatus
A^ spiralis
Cerasterias
irregularis
Chlamydomonas
globosa
C_^ polypyrenoideum
C snowii
£1. ££
C. sp 1
C. sp 2
Chlorella
ellipsoidea
Closteriopsis
longissima
Closterium gracile
C^ parvulum
Coelastrum dub ium
C. kuetzingianum
C. microporum
C^ reticulatum
C. sphaericum
Cosmarium contractum
C._ formulosum
C. psuedoprotuberans
C. subtumidum
C^ sp.
Crucigenia
apiculata
C. quadrata
C. tetrapedia
Dactylococcus
infusionum
D. sp.
Dictyosphaerium
ehrenbergianum
D_^ pulchellum
Dispora
crucigenioides
Elakatothrix
gelatinosa
E. viridis
E . sp.
Franceia droescheri
F. ovalis
Gloecystis ampla
G. gigas
G. major
£1 IP-
Golenkinia
paucispina
G. radiata
G. sp.
Hyalotheca mucosa
Kirchneriella
contorta
K. lunaris
K._ obesa
Lagerheimia
ciliata
L_._ citriformis
L. guadriseta
L._ longiseta
L. subsalsa
Micractinium
pusilium
Mougeotia americana
M^ elegantula
M^ sp.
Oocystis borgei
0^ elliptica
0. pusilla
0. submarina
Fedlastrum
biradiatum
P. boryanum
P. duplex
_?_._ duplex var.
gracilimum
P_^ tetras
Scenedesmus abundans
S. acuminatus
S_._ acutiformis
S± armatus
S^ bijuga
S. dimorphus
S. longus
S. obliquus
S^ opoliensis
S^ quadricauda
Schroederia setigera
Sphaerocystis
sehoeteri
Staurastrum
chaetocercus
S^ dejectum
S^ furcigerum
S_^ paradoxum
S. polymorphum
S_._ sebaldi
Stipitococcus
vasiformis
S_^ sp.
Tetraedron
ar throde smi forme
T^ caudatum
T. minimum
T. pentaedricum
T^ prescottii
T. trigonum
T^ sp.
Tetrastrum glabrum
T^ heteracanthum
T. regulare
Ulothrix
subconstricta
U. subtilissima
U. sp.
Unknown Chlorophyta
Bacillariophyta
Achnanthes affinis
A. clevei
A. flexella
A. hungarica
A. lanceolata
A. minutissima
A. sp.
Amphora ovalis
A. ovalis var.
lybica
A. perpusilla
A. veneta
-161-
-------
Table A-15 (continued)
A. sp.
Amphipleura
pellucida
Amphiprora ornata
Anomoeneis vitrea
Astrionella formosa
Attheya zachariasi
Cocconeis diminuta
C. pediculus
C. placentula
C. sp.
Coscinodiscus rothii
Cyclotella antLqua
C. caspia
C. comensis
C_^ comta
C_^ glomerata
C_^ kutzingiana
C^ meneghiniana
C_^ michiganiana
C_^ ocellata
C. pseudostelligera
C_^ stelligera
C. striata
C. sp.
C_^ sp. 1^
Cymatopleura solea
Cymbella affinis
C_^ cesatii
C. cuspidata
C. inaequalis
C. mirocephala
C. postata
C. tumida
C. tumidula
C_._ turgida
C. ventricosa
C. sp.
Denticula elegans
D. tenuis
Diatoma elongatum
EK_ tenue
D_._ vulgare
Diploneis elliptica
D_._ marginestriata
D. oculata
D. puella
Epithemia sp.
Fragilaria capucina
F. construens
F. crotonensis
F. harrissonii
F. intermedia
F. lapponica
F. leptostauron
F. pinnata
F. vaucheriae
F. sp.
Gomphonema
angustatum
G. olivaceum
G. sp.
Gyrosigma sp.
Melosira granulata
M. islandica
M. varians
Meridion circulare
Navicula cryptocephala
N. cryptocephala
var. veneta
N. decussis
N. elginensis
N. exigua
N. gregaria
N. hustedii
N. lanceolata
N. menisculus
N. placentula
N. pupula
N. radiosa
N. reinhardtii
N. subtilissima
N. tripunctata
N. tuscula
N. viridula
Neidium affine
N. iridis
Nitzschia acicularis
N. bacata
N. filiformis
N. fonticola
N. gracilis
N. kutzingiana
N. linearis
N. palea
N. sinuata
Opephora martyi
Rhizosolenia longiseta
R. longiseta
Rhoicosphenia
curvata
S. astraea var.
minutula
S. dubius
S. hantzschii
S. invisitatus
Surirella ovata
S. ovata
S. robusta
S. sp.
Synedra acus
S. amphicephala
S. cyclopum
S. delictissima
S. radians
S . rumpens
S. tenera
S. ulna
S. vaucheriae
S. sp.
Tabellaria fenestrata
T. flocculosa
Unknown
Bacillariophyta
Cyanophyta
Anabaena flos-aquae
A. planctonica
A. subcylindrica
A. wisconsinense
A. sp.
Aphanocapsa
delicatissima
A. elachista
Aphanothece
clathrata
A. microspora
A. nidulans
A. prasina
A. sp.
Chamae siphon
confervicola
Chroococcus
dispersus
C. kuetzingianum
C. limneticus
C. minor
C. minutus
C. prescottii
Coelosphaericum
naegelianum
Stephanodiscus astraea
-162-
-------
Ta.hle 4^15 (continued)
Cyanarcus hamiformis
Dactylococcopsis
acicularis
£._ fascicularis
EL smith ii
__
Gomphosphaeria
aponina
G. lacustris
Lyngbya contorta
Merismopedia convoluta
M^ punctata
Microcystis
aeruginosa
M^ f los-aquae
M. incerta
Oscillatoria
acutissima
0. angusta
0. angustissima
0^ prolif ica
0. splendida
0^ tenuis
0. sp.
Phormidium mucicola
P._ tenue
Unknown blue-green
Chrysophyta
Chrysosphaerella
longispina
Dinobryon bavaricum
D. caudata
P. divergens
D. sertularia
D. sociale
D. stipitatum
D. tabellariae
Mallomonas acaroides
M. alpina
M. caudata
Ophiocytium
capitatum
Stipitococcus
vasiformis
Synura ulvella
Cryptophyta
Chroomonas nordstedtii
Cryptomonas erosa
C^ ovata
C. sp.
Rhodomonas minuta
Pyrrophyta
Ceratium hirundinella
Euglenophyta
Euglena sp.
Phacus si
ChLoromonadophyta
Gonyostomum semen
Unknown flagellates
-163-
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TECHNICAL REPORT DATA
(Please read Instructions on the reverse before completing)
1. REPORT NO.
EPA-600/3-80-059
3. RECIPIENT'S ACCESSION-NO.
4. TITLE AND SUBTITLE
Limnology of Michigan's Nearshore Waters
of Lakes Superior and Huron
5. REPORT DATF
JULY 1980
ISSUING DATE
6. PERFORMING ORGANIZATION CODE
7. AUTHOR(S)
R.E. Basch, C.H. Pecor, R.C. Waybrant, D.E. Kenaga
8. PERFORMING ORGANIZATION REPORT NO.
9. PERFORMING ORGANIZATION NAME AND ADDRESS
Environmental Protection Bureau
Michigan Department of Natural Resources
Lansing, Michigan 48909
10. PROGRAM ELEMENT NO.
1BA769
11. CONTRACT/GRANT NO.
R005146-01
12. SPONSORING AGENCY NAME AND ADDRESS
Environmental Research Laboratory
Office of Research and Development
U.S. Environmental Protection Agency
Duluth, Minnesota 55804
13. TYPE OF REPORT AND PERIOD COVERED
Final 1974-1976
14. SPONSORING AGENCY CODE
EPA/600/03
15. SUPPLEMENTARY NOTES
Great Lakes National Program Office, Region V, U.S.
Chicago, Illinois, 60605
Environmental Protection Agency,
16. ABSTRACT
Limnological assessments, including water and sediment chemistry, bacterial
densities, zoo- and phyto-plankton and benthic macroinvertebrate community structure,
and fish contaminants, were performed at 24 locations in Michigan'g nearshore waters
of Lakes Superior and Huron in 1974 and 1975. The nearshore waters of Lake Superior
were all oligotrophic with generally high water quality as reflected by consistently
high dissolved oxygen, reactive silica and nitrate, and low phosphorus, total
dissolved solids (TDS), chlorophyll a and bacterial densities. A statistical trend
analysis based on 1974 through 1976 T~GLECS) data indicated significant increases
in the concentrations of dieldrin, DDT and mercury in Lake Superior lake trout.
These same data show no statistical changes in PCB concentrations from 1974 to 1976.
The nearshore waters of Lake Huron were oligotrophic in the northern section
and became mesotrophic at the southern end of the lake. Eutrophic conditions were
found at Alpena harbor and Saginaw Bay. Areas of severe water quality degradation
occured at Alpena and Saginaw Bay as a result of large inputs of phosphorus and
TDS. A statistical analysis based on 1975 through 1978 GLECS data suggested a peak
in 1976 for dieldrin, DDT and mercury in Lake Huron lake trout. The same data showed
no statistical changes in PCB concentrations from 1975 through 1978.
17.
KEY WORDS AND DOCUMENT ANALYSIS
DESCRIPTORS
b.IDENTIFIERS/OPEN ENDED TERMS C. COS AT I Field/Group
Algae, Fishes, Lakes, Nutrients,
Contaminants
Lake Superior
Lake Huron
06/F
13. DISTRIBUTION STATEMENT
Release Unlimited
19. SECURITY CLASS (This Report)
Unclassified
21. NO. OF PAGES
189
20. SECURITY CLASS (Thispage)
Unclassified
22. PRICE
EPA Form 2220-1 (9-73)
it U.S. GOVERNMENT PRINTING OFFICE: ]980--657-165/0066
-175-
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