United States
Environmental Protection
Agency
Great Lakes National
Program Office
536 South Clark Street
Chicago. Illinois 60605
EPA-905/4-80-003-B
Lake Michigan Intensive
Survey 1976-1977 -
Management Report
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LAKE MICHIGAN
BATHYMETRIC CHART
MORPHOMETRIC PARAMETERS
KEY FOR CONTOUR LINE IDENTIFICATION
LAKE MICHIGAN MORPHOMETRIC PARAMETERS
FT I J N D
IX
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LAKE MICHIGAN INTENSIVE SURVEY
1976-1977
MANAGEMENT REPORT
By
Robert
James
David S.
David
Madonna
Marvin
David C
J. Bowden
R. Clark
DeVault III
M. Lueck
F. McGrath
F. Palmer
Rockwel1
Great Lakes National Program Office
United States Environmental Protection Agency
536 S. Clark Street Room 932
Chicago, Illinois 60605
AUGUST 1981
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DISCLAIMER
This report has been reviewed by the Great Lakes National Program Office,
U.S. Environmental Protection Agency, and approved for publication. Approval
does not signify that the contents necessarily reflect the views and policies
of the U.S. Environmental Protection Agency, nor does mention of trade names
or commercial products constitute endorsement or recommendation for use.
iii
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FORWARD
The Great Lakes National Program Office (GLNPO) of the United States
Environmental Protection Agency was established in Region V, Chicago to
focus attention on the significant and complex natural resource represented
by the Great Lakes.
GLNPO implements a multi-media environmental management program drawing
on a wide range of expertise represented by Universities, private firms. State,
Federal, and Canadian Governmental Agencies and the International Joint
Commission. The goal of the GLNPO program is to develop programs, practices
and technology necessary for a better understanding of the Great Lakes Basin
Ecosystem and to el imlnate or reduce to the maximum extent practicable the
discharge of pollutants into the Great Lakes system. The Office also coordi-
nates U.S. action in fulfillment of the Great Lakes Water Quality Agreement
of 1978 between Canada and the United States of America.
IV
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TABLE OF CONTENTS PAGE
INTRODUCTION 1
CONCLUSIONS 3
ANNUAL VARIABILITY 3
PHOSPHORUS 4
WINTER EFFECTS 6
ACCUMULATION OF TOTAL DISSOLVED SOLIDS 9
CHLORIDES 9
SULFATES 12
SODIUM 13
BLUE GREEN ALGAE - FOOD CHAIN CONCERNS 13
TOXIC ORGANIC SUBSTANCES 15
HEAVY METALS 18
ATMOSPHERIC DEPOSITION 18
LONG TERM NEARSHORE IMPROVEMENTS - Illinois - Indiana 18
TROPHIC STATUS 18
U.S.E.P.A. RESPONSES 23
SPECIFIC RESPONSES 23
TECHNICAL ASSESSMENT TEAMS 23
PROGRAM DESIGN EVALUATION 25
MONITORING RESPONSES 25
ANNUAL LAKE ERIE PROGRAM 25
TRIBUTARY - HIGH FLOW LOADS 26
ATMOSPHERIC DEPOSITION 26
INVESTIGATION OF NEW POTENTIAL PROBLEMS 26
HARBOR SEDIMENT PROGRAM 27
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(contd.) TABLE OF CONTENTS PAGE
FISH FLESH CONTAMINANT PROGRAM 27
INTENSIVE GREAT LAKE SURVEILLANCE 27
STATES MONITORING GRANTS 27
WATER INTAKE PROGRAMS 29
RECOMMENDATIONS 29
ACKNOWLEDGEMENTS 32
REFERENCES 33
APPENDIX A - DESCRIPTION OF SURVEY A-l
APPENDIX B - QUALITY ASSURANCE USED BY GLNPO B-l
APPENDIX C - ORGANIZATIONS INVOLVED C-l
APPENDIX D - MICROFICHE 1976-1977 LAKE MICHIGAN D-l
INTENSIVE SURVEY DATA
MICROFICHE attached to back cover
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FIGURES PAGE
1. Total phosphorus open lake area between Milwaukee and Ludington 5
2. South Water Filtration Plant Chicago Water Purification Division
total phosphorus (ug/1) 1966-1980 8
3. Lake Michigan - Chloride trends 1860-1977 10
4. Lake Michigan - Sulfate trends 1878-1976 11
5. Distribution of sulfate (mg/1) 1976 Annual average, Spring 1976,
Summer 1976 14
6. Mean concentration of chlorinated hydrocarbons
in fish from Eastern Lake Michigan 16
7. Total coliform - south shore and north shore Chicago area lake
surveys 20
8. Chicago Water Purification Division South Water Filtration
Plant Chlorine and Carbon Dosage (pounds/million gallons/
year) 21
9. Lake Michigan estimated trophic states 22
Al. Lake Michigan survey cruise stations A-2
A2. Lake Michigan near shore survey cruise stations A-3
A3. Schematic representation of sampling depths in Lake Michigan A-4
A4. Flow chart illustrating sample processing on EPA monitoring
vessel. A-9
A5. Flow chart illustrating sample processing for study of
northern Lake Michigan A-10
vii
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TABLES
1. Averages of the southern basin cruises 1976-1977
Page
2. Lake Michigan July-August 1977 summary of metals
data from water samples 19
3. Enrichment problem relationships applied on Lake Michigan
data 24
4. Chemicals monitored In fish flesh 28
A-l. Parameters measured by GLNPO A-5
A-2. Selected cruise parameters measured by GLNPO A-6
A-3. System of parameters used to index the trophic state
of Lake Michigan A-7
B-l. Difference between split sample analyses
Southern Lake Michigan B-2
B-2. Shipboard check standard and reagent blank summary B-4
B-3. Upper Lake Reference Group performance
standards run during 1977 cruises B-7
B-4. Station L. Michigan 06 24-Hour Surveys 1977 B-9
viii
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INTRODUCTION
During 1976 and 1977, the Great Lakes National Program Office (GLNPO)
of the United States Environmental Protection Agency (USEPA) conducted
an intensive survey of the Lake Michigan in order to determine the
trophic status of the lake, changes or trends in water quality since
previous surveys and to establish a data base to support the developme .t
of predictive mathematical simulations which can be used to predict
the effects of remedial programs, particularly phosphorus removal.
A complete description of this study and the results of the study
including methodology is available in EPA document No. 905/4-80-003A
LAKE MICHIGAN INTENSIVE SURfEY 1976-1977 (Rockwell _et al 1980b). A
microfiche copy of the intensive survey data base available in STORET is
attached inside the back cover of the report.
The purpose of this executive summary is to summarize and discuss
the major findings of the study and to update those findings in light
of additional data that became available during or after the report
writing process.
The appendices to this report contain abbreviated descriptions
of the survey including station locations, parameters, analytical methods,
quality control and the roles of other organizations which participated
in or contributed to the study. Table 1 gives a brief summary of survey
results for the southern basin in 1976 and 1977.
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TABLE
Averages of the Southern Basin Cruises
1976-1977
(Means of two layer volume weighted cruise values)
Southern Basin
1976 1977
Water Temp. °C 8.9 7.4
Secchi (m) 4.4 5.4
Conductivity 25°C (umhos/cm) 274 276
Total Kjeldahl Nitrogen .164 .158
Total Alkalinity 107 107
Turbidity (TU) 1.8 0.9
Ammonia (ug/l) 7.2 5.2
Nitrite + Nitrate .226 .243
Total Phosphorus (ug/l) 8.0 5.6
Primary Productivity mg C/mVhr 4.9 3.9
CaIc i urn 35.5
Magnesium I 1.0
Sodium 4.7
Potass!urn I.07
Chloride 8.09 8.19
Sulfate 21.1 22.3*
Fluoride 0.10
Dissolved Reactive Silica 1.13 0.94
ChlorophylI "a" I.69 1.45
Units are mg/l unless otherwise noted. These are gross averages used to
characterize the lake in simple terms. They include substantial variance
in both time and space. For more precise information the reader is referred
to the full technical report Rockwell et. a I. (I980b) and Bartone and
Schelske (1979) who reported on 1976 data separately.
* Arithmetic average of selected sampling sites in Indiana Nearshore Study.
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CONCLUSIONS
ANNUAL VARIABILITY
Phosphorus is considered the principal limiting nutrient in Lake
Michigan. Phosphorus concentrations were dramatically deceased over
the winter between 1976 and 1977 throughout the entire southern basin
resulting in an improved trophic conditions evaluation in 1977.
* Total phosphorus concentration decreased from 8 ug/1
during 1976 to 5.6 ug/1 during 1977 in the open waters of
the southern basin. Substantial reductions also occurred at
nearshore stations.
* Turbidity decreased from an average of 1.8 HTU during
1976 to 0.9 HTU in 1977.
* Transparency, as measured by secchi disk, increased
from 4.4 meters during 1976 to 5.4 meters in 1977.
* Seasonal surface water nitrate depletion decreased
from 0.17 mg/1 during 1976 to 0.11 rag/I during 1977.
* Nitrate + Nitrite concentration averages increased
from .226 mg/1 in 1976 to .243 mg/1 in 1977.
" Epilimnetic phytoplankton populations decreased
from 4300 organisms/ml during 1976 to 3400 organisms/ml
during 1977.
Chlorophyll "a" concentrations decreased from 1.69
ug/1 during 1976 to 1.45 ug/1 during 1977.
* Primary productivity at the 5 meter depth decreased
from 4.9 mg/C/m3/hr during 1976 to 3.9 ing C/m3/hr during
1977.
Seasonal measurements of average dissolved reactive
silica (DRS) concentrations in the surface water were
higher throughout 1977 than during 1976. This can imply
less utilization by diatoms in the nearshore surface water.
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* Hypolimnetic dissolved reactive silica concentrations
were lower during 1977 than during 1976 at deep water
stations (depth greater than 80m). Volume weighted re-
active silica decreased in the summary averages (Table 1)
from 1.13 to .94 mg/1 which indicated a loss of frustules
to the sediments or bottom most layers of water.
All of these changes are consistent with an improvement in the trophic
status of the lake.
An indication of trophic status which is not consistent with these
improvements is that some species of green and blue-algae usually associated
with deteriorating systems appear to have increased throughout the southern
basin since 1962-63. However, their numbers were fewer in 1977 than in
1976 probably in response to the phosphorus reduction. There is also an
apparent increase in phytoflagellates during the 1962-63 to 1976-77
period. The phytoplankton population in the southern basin indicate
that the system suffers from cultural nutrient enrichment. This is
illustrated by the marked shift from diatoms to blue-green algae which
accompanied severe dissolved reactive silica concentration depletion in
the surface waters at open lake stations sites (>80 meters deep) in both
years and the marked increase of blue-green algae in the eastern zone
of transect one.
PHOSPHORUS
Phosphorus concentrations in Lake Michigan can vary sharply from
year to year. Fish and Wildlife Service data in an area between Milwaukee
and Ludington averaged 16 ug/1 during 1961 and the 1962-63 FWPCA study
found 6-7 ug/1 in the same area. During the early seventies the University
of Wisconsin found concentrations of 8 to 9 ug/1 along a transect between
Milwaukee and Lundington. Our study found levels of around 7 ug/1 in
1976 with a sharp decline to around 5 ug/1 in 1977. In the entire southern
basin total phosphorus concentrations declined from 8.0 _+ 0.8 in 1976 to
5.6 +_ 0.8 in 1977 (Figure 1). Eighty-five percent of the southern basin
stations showed a reduction in total phosphorus concentrations between
1976 and 1977. Total dissolved phosphorus also decreased at 92 percent
of the stations from a median of 3 ug/1 in 1976 to below detectable limits
in 1977.
Only a small portion of the southern basin lake-wide phosphorus decrease
can be attributed to load reductions. Phosphorus loadings to Lake Michigan
from industrial, municipal, atomospheric and tributary sources were 6566
-4-
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1950 1955 1960 1965 1970 1975 1980
Time
Figure 1
Total Phosphorous
Open Lake Area
Between Milwaukee and Ludington
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REFERENCES
Aekerman, W.C., R.H. Harmeson, and R.A. Sinclair. 1970. Some long
trends in water quality of lakes and rivers, American Geophysical Union
15: p515-522.
Allen, M.B. 1952. The Cultivation of Myxophyceae. Arch. Mikrobiol.
17: p34-53.
Allen, M.B. and D.I. Arnon, 1955. Studies on nitrogen-fixing
blue-green algae, growth and nitrogen fixation by Anabaena cylindrica.
Plant. Physio!. 30:366-372.
Andern, A. W., S. Eisenreich, F. Elder, T. Murphy, M. Sanderson, and
R.J. Vet. 1977. Atmospheric loading to the Great Lakes. University
of Windsor. 15p
Arnold, D.E. 1971. Ingestion, assimilation, survival and reproduction
by Daphnia pulex fed seven species of blue-green algae. Limnology and
Oceanography 16: p 906-920.
Assel, R.A., D.E. Boyce, B.H. DeWitt, J. Martha, and F.A. Keys. 1979.
Summary of Great Lakes Weather and Ice Conditions, Winter 1977-78. NOAA
Technical Memorandum ERL-GLERL 26. 123p
Bartone, Carl R., and C.L. Schelske. 1979. Limnological Conditions in
Lake Michigan Based on Analysis of 1976 Surveillance Data Large Lakes
Laboratory Grosse Ille, Michigan submitted for pub. J. of Great Lakes Research.
Beeton, A.M. 1965. Eutrophication of the St. Lawrence Great Lakes,
Limnol. Oceangr. 10: p240-254.
Beeton, A.M. 1969. Changes in the environment and biota of the Great
Lakes, p. 150-187. In: Euthrophication: Causes, Consequences, Correctives.
National Academy of Sciences, Washington, D.C. 661 p.
Beeton, A.M. and J.W. Moffet. 1964. Lake Michigan chemical data, 1954-
1955; 1960-61. U.S. Dept. Interior, Fish and Wildlife Service Data Report
No. 6. 102p
Brooks, J,L. 1969, Euthrophication and changes in the composition of the
zooplankton pp. 236-255 In: Eutrophication: Causes, Consequences, Correctives.
National Academy of Sciences. Washington, D.C. 661 p.
Chapra, S.C. and William C. Sonzogni. 1979. Great Lakes total phosphorus
budget for the mid 1970's. Journal WPCF Vol 51, No. 10. p2524-2532.
Ditoro, Dominic M. 1980. Personal Communication Manhattan College,
Environmental Engineering & Science Division. Bronx, New York 10471.
-33-
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metric tons in 1976 and 4666 metric tons during 1977 (IJC, GLWQB, I978a)
a difference of 1900 metric tons. A !.0 ug/I annual decrease In total
phosphorus corresponds to a annual loss of 5000 metric tons loading
(Chapra and Sonzogni, 1979). Assuming the southern basin reduction of
2.4 ug/I in one year is representative of the entire lake, a reduction of
12,000 metric tons would be required to produce this annual decline for
the lake. Thus, 15 percent or less of the change in phosphorus can be
attributed to reduction in loading.
WINTER EFFECTS
One explanation of this large and apparently natural decrease in
total phosphorus may be the severity of the intervening winter. An
abnormally large amount and duration of ice cover occurred during the
winter of 1976-77. The onset of freezing conditions was 30 days earlier
than normal. The maximum ice extent was 58 days longer than normal. The
beginning of early ice decay started 4 days later than normal {Quinn et
a I 1978). Quinn summarized the weather and ice condition for the winter
of 1976-1977.
"The winter of 1976-77 was the fifth coldest In the past
200 years. Record-breaking low temperatures from mid-October
to mid-February, associated with an upper air pressure pattern
consisting of a strong ridge in the westerly flow over North
America, resulted in extraordinary ice cover on the Great Lakes.
Ice was produced almost simultaneously in various shallow protected
areas of the Great Lakes in early December. The progression of
early winter, mid-winter, and maximum ice extent was from 4 to
5 weeks earlier than normal. At the time of maximum ice extent
in early February, Lake Superior was approximately 89 percent,
Lake Erie 100 percent, and Lake Ontario approximately 38 percent.
Spring breakup started In late February In the southern part of
the Great Lakes region and in early March in the northen part.
The bulk of ice cover was gone by the fourth week of April."
There are three mechanisms by which abnormal ice cover could affect
the trophic status of the lake.
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a. It could delay the thermal cycle of the lake. Thermal stratification
with a discernible epilimnion, thermocline, and hypolimnion appears to have
been delayed by the cold winter in 1977. The extent of thermal stratification
on the May 25-June 2, 1976 cruises was about the same as observed on the June
15-21, 1977 cruise. The epilimnetic waters in 1977 were about 3-4°C cooler
than in 1976 throughout the stratified season.
b. The ice cover would insulate the water mass from prevailing winds
which are responsible for mixing. This would increase sedimentation
in the lake. Resuspension of sediments would also be curtailed during
ice cover in areas that are normally stirred up by winds (Rodgers I960). That
increased sedimentation of suspended material occurred between 1976 and
1977 is suggested by mean turbidity values which decreased from 1.8 +_
.3 HTU in 1976 to 0.9 +_ .1 HTU in 1977. This change occurred during the
period between cruises ending in 1976 and starting in 1977.
c. Ice, particularly snow covered ice, would reduce the amount of
light reaching the lake. This would inhibit biological productivity under
the ice.
The loss of phosphorus between 1976 and 1977, should not be necessarily
considered permanent. Such a comparatively large phosphorus deposition in
the southern basin (up to 7.345 ICP metric tons) would result in upper
sediment layers being more highly enriched. This phosphorus is nearly
twice the estimated 1976 loadings of total phosphorus to the southern basin
(3.797 10^ MTs). Presumably this phosphorus could become a loading source
when then is subsequent resuspension during trubulent periods or via chemical
or biological recycling (Rodgers I960).
The winters of 1976-77 and 1978-79 were also more severe than normal.
Data from Chicago's South Water Filtration Plant indicate that total phosphorus
concentration was even lower during 1978 and 1979 averaging 12.1 +_ 1.4 ug/I
and 13.6 +_ I.I ug/l respectively versus an average of 18.3 +_ 1.0 ug/l during
1977 (Figure 2). During 1976, before the first severe winter, phosphorus
concentration at this intake averaged 22.4 +_ 1.6 ug/l (Figure 2). This plant's
water intake is influenced by nearshore conditions. However, since one intake
is 3 km offshore and is used when nearshore waters deteriorate, the plant's
water seems to also reflect lake conditions. The decrease in nearshore
total phosphorus in 1976-1978 noted at the plant was also found by the City
of Chicago and Illinois EPA (Lake Michigan Water Quality Report 1979,
I960) at sampling points located 10 km to 30 km offshore near Chicago. If
cold winters with extensive ice cover depress phosphorus levels during
the following year, then mild winters with little ice cover may result
in relatively higher concentrations during the following year. This
appears to be the case after the relatively mild winter of 1979-80.
Phosphorus concentrations at the Chicago water intake increased from an
annual average of 13.6 +.1.1 ug/l during 1979 to 16.7 +_ 1.2 ug/l during
I960 (Jan-Oct).
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00
1
50
40
30
20
10
196B
1967 1968 1969 1970 1971 1972 1973 1974 1975 1976 1977 1978 1979 1980
1981
11
Annual Mean + One Standard
Deviation Of Annual Mean
South Water Filtration Plant
Chicago Water Purification Division
From Seasonal And Comprehensive Chemical Analysis
Total Phosphorus In parts Per Billion
figure 2
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There is evidence that similar changes have occurred in the past. Phos-
phorus values in the entire southern basin averaged 13 ug/1 (Beeton 1969)
in 1960 and 1961. The winter of 1962-63 was severe, having an 80% maximum
ice cover which was the most extensive recorded at that time (Assel, et
al, 1979). Risley and Fuller (1965) reported total phosphorus values of
6-7 ug/1 during 1963. Some of the 6-7 ug/1 total phosphorus reduction may
be due to winter effects in addition to differences related to station
network, analytical methods and sampling strategies (Rousar and Beeton, 1973).
The apparent year-to-year variability of the Great Lakes phosphorus
levels complicates any attempt to evaluate or predict the effectiveness
of phosphorus control programs. Mathematical simulations of the bio-
logical cycles within the lakes have been very successful in predicting
responses given initial spring conditions (Ditoro 1980) but do not
predict the year-to-year variations very well. If this year-to-year
variability can be explained by annual ice cover it will be possible
to overcome this deficiency. If the annual variability of phosphorus
can be related to an observable variable such as ice cover, the effects
of meterological conditions may be separable from the effects of remedial
programs. Thus, the effects of remedial programs can be predicted and
measured with improved confidence.
ACCUMULATION OF TOTAL DISSOLVED SOLIDS
Conservative ions, primarily chloride, sulfate and sodium are accumulating
in Lake Michigan. Of these, chloride is accumulating at an increasing
rate. During 1976 the mean concentration of chloride in the open waters of
the southern basin was 8.09 mg/1 and during 1977 it was 8.19 mg/1 resulting in
an annual increase of 0.10 mg/1 (Table 1, and Figure 3). Sulfate concentration
has increased to 21.1 and is accumulating at a rate between 0.11 to 0.17
mg/1 per year. The sulfate concentration in Lake Michigan has risen 15
mg/1, the most of any conservative ion since 1877 (Figure 4).
CHLORIDES
Increases in conservative ion concentrations have been noted in
Lake Michigan water going back to the 1800's (Beeton, 1965). Concentration
increases of chloride, sodium plus potassium, sulfate, and total dissolved
solids have increased steadily over the years. As potassium concentrations
seem to be in equilibrium around 1 mg/1 (Torrey, 1976; Dobson, 1976),
the increase in sodium plus potassium must be due to sodium.
Before the extensive growth of population and industrial development
of the Lake Michigan drainage basin, chloride concentration in the 1860's
was around 1.2 + .3 mg/1 (Ackerman _e_t jil, 1970). The level may have repre-
sented an equilibrium concentration, however, the data are limited and
sampling locations not identified. By the turn of the century, chloride
concentrations had increased to 3.0 mg/1 (Ackerman ^t jl, 1970) in the
southern basin near Chicago. FWPCA (1968) observed mean chloride
-9-
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O
I
10-
8-
6 -
4 -
2 -
N.
O!
_0
£
O
Ackermann et al ( 1970 } earliest data
O Pre 1960 data After Beelon < 1969 )
Post 1960 data n is large
OGLNPO Rockwell et al ( 1980 )
* USDOI FWPCA { 1968 )
^ GLRD Great Lakes Research Division University of Michigan
O
O
O
O
O
O
O
p
Slope 01 3 ing- I yr
n 607 USDOI
1860
1870
1880
1890
I
1900
1910
I 1
1920 1930
1940
I
1950
I
1960
I
1970
1980
Lake Michigan
Chloride Trends
Figure 3
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25'
20
15
10-
O Pre 1960 after Beeton ( 1969 }
* Post 1960 data after Torrey ( 1976
OUSDOI FWPCA ( 1968 )
+ GLNPO Rockwell et al ( 1980 )
USDOi n=501
GLNPO 1976
n= 144
*** ^
o
o
1870
1880
I
1890
1900
1910
I
1920
I
1930
Lake Michigan
Sulfate Trends
I
1940
I
1950
I
1960
I
1970
I
1980
Figure 4
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concentration of 6.5 mg/1 at deep water stations in 1962-63. Chloride
concentrations during 1976 and 1977 were 8.1 and 8.2 mg/1 respectively.
The rate of increase between 1962 and 1977 averaged 0.13 mg/l/yr (Figure 3).
The rate of increase appears to be accelerating from 0.05 mg/l/yr (1860-1960),
using Beeton (1969) data, to a current rate between 0.10 mg/l/yr to 0.13
mg/l/yr (Figure 3).
The rate of chloride accumulation in the open lake between 1962 and
1976 would correspond to loadings between 8.3 x 10^ and 10.2 x 10 5 metric
tons/yr. The volume of Lake Michigan's annual discharge is about 1% of the
total volume of the lake ( 4900 km-*) (Torrey, 1976), and discharge con-
centrations ranged between 7 to 8 mg/1. The annual load of chloride discharged
is between 3.4 x 10^ and 3.9 x iQ metric tons. The increased annual chloride
burden for Lake Michigan would be about 5.5 x
The total tributary chloride load to Lake Michigan's basin was 7.1 x
metric tons during 1976 (IJC GLBC, 1978a). Point-source estimates for chloride
discharged directly to the lake was 2.0 x 105 metric tons in 1976 (IJC, GLBC, 1978a),
Atmospheric loading of chloride is estimated at 0.83 x 10^ metric tons per year
(Andern _e_t ad, 1977). The sum of these estimates (9.9 x 10-" metric tons) falls
within the limits of observed increases in ambient concentrations of chloride.
In 1972-73, salts used for road deicing throughout Lake Michigan's
drainage basin amounted to 4.45 x 10^ metric tons as chloride (Doneth, 1975).
Assuming that this load level has not decreased, that it represents a stable
proportion of the total load, and that most of this chloride eventually reaches
the lake; deicing compounds could account for 40 to 45 percent of the annual
load. ( Municipal and industrial treatment processes used to reduce phosphorus
and industrial wastes frequently produce chloride salts and also contribute to
increase loadings of chloride.)
SULFATES
Southern basin sulfate concentration averaged 21.1 mg/1 in 1976. This
value is 30 to 35 percent higher than the mean concentrations of 16 to 18 mg/1
(Beeton and Moffett, 1964) observed in 1954-55 in the southern and northern
basins and 5 percent higher than the mean concentration of 20 mg/1 (FWPCA, 1968)
observed in 1962-1963. Atmospheric dry input of sulfate could be as high as
50 percent of the total load (785 MT.) (Slevering _et _al_, 1979) and may be a
possible explanation for the slightly higher epilimnetic sulfate concentrations
observed. In the nearshore records of water filtration plants the accumulation
of sulfates appears to be accelerating (Rockwell et al, 1980b). Tributary as well
as atmospheric sources impact these zones. A recent source of additional sulfate
ions is from the use of low phosphate detergents. These detergents contain about
twice as much sulfate by weight in their builders as high phosphate detergents
(Fuchs 1978).
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The proximity of the urban-Industrie I area along the southern shore of
Lake Michgian appears to contribute to the slightly higher sulfate concen-
trations in the southern basin (Figure 53. Based upon cl imatological data,
emissions of a reactive pollutant such as 862 in the Chicago urban-industrial
area would be expected to oxidize to sulfates and impact north and east of
Chicago. Ozone, another reactive pollutant, has had maximum recorded values
near Waukegan, Illinois (Illinois Annual Air Quality Reports, 1976, 1977,
1978, 1979). The conversion of SC>2 to sul fates may be reflected in higher
sulfate water concentrations offshore from Waukegan and in the southern
basin nearshore zones. An increasing atmospheric sulfate level is expected
due to long range transport of SC>2 from higher stacks heights which were
put in place during the past decade and from slightly increasing total
$02 emission loads within the Ohio River Basin-11.5 million tons
in 1970 to 12.8 million tons in 1975 (Stukel and Keenan, 1980).
The increasing levels of chlorides and sulfates will not threaten
drinking water standards (at 250 mg/l) even during the next several centuries
unless current loadings are increased dramatically. The biological consequences
of increased dissolved solid levels are unknown. Higher levels create
ever expanding habitat for brackish algal forms. Some new marine algal
forms have adapted to lake conditions and are now frequently observed in
the nearshore zones of Lake Michigan e.g. Bang!a atropurpurea, a red
attached algae.
SOD IUM
There is evidence however that increased levels of sodium favor the
growth of blue-green algae. Sodium concentrations averaged 4.8 mg/l in
1976-1977. These values were about 20 to 40 percent higher than the averages
observed by FWPCA (3.9-4.0 mg/l) during in 1962-63 and by Beeton and Moffett
during 1954-55 (3.3 to 3.4 mg/l).
BLUE-GREEN ALGAE - FOOD CHAIN CONCERNS
Makarewicz and Baybutt (In Press) observed an increase in relative
abundance of blue-green algae. In their data base, blue-greens (principally
Gomphosphaer!a and OsciII atori a) appeared and Increased once annual
sodiurn concentrations averaged 4.6 ug/l.
Several species of blue-green algae require sodium, frequently at con-
centrations at 4 to 5 mg/l or higher (Allen, 1952; Kratz and Myers, 1955;
Allen and Arnon, 1955). There is a large body of circumstantial evidence
which suggests that increase monovatent ion concentrations (particularly
sodium and potassium) may favor the development of blue-greens (Provasoli,
1969). That sodium, potassium, and other ions can enhance the uptake of
phosphate by blue-greens has been demonstrated by Jensen _et _aj_ (1976).
Anticipated discharges of salt will ultimately increase chloride Ion con-
centrations from the current 8 mg/l to over 19 mg/l (Richardson, 1980).
If sodium increases proportionately, then ultimate sodium ions levels
could be greater than 10 mg/I throughout the lake.
-13-
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figure 5
Distribution Of Sulfate In mg/l
1976
Annual
Average
MILWAUKEE
ZION
WAUKEGAN
LAKE FOREST
CHICAGO
>0 S 0 10 20 10 40
»^ ^- 1 1 1_J MiifS
to 5 010 20 30 «o 50 eo ?o
" 1« 1 1 1 1 11 «IIOMT[»S
BENTON
21.8' HARBOR
MICHIGAN CITY
HAMMOND
Spring 1976
May 25-June 2
ZION
WAUKEGAN
LAKE FOREST
CHICAGO
MICHIGAN CITY
HAMMOND
Summer 1976
August 3-10"
CHICAGO
BENTON
HARBOR
MICHIGAN CITY
HAMMOND
-------
Blue-green algae constituted 19.5% of the phytoplankton in the samples
collected during 1976 compared to 14.2% of the phytoplankton in the 1977
samples. Furthermore, blue-green algae increased in absolute numbers and
in percentage of phytoplankton in the south eastern portion of the southern
basin. Eutrophication commonly enhances the growth and abundance of
filamentous green or blue-green algae. Blue-green algae in particular
can form mats of colonial single cells or rafts of filaments which become
too large to be efficiently retained by grazers. The extracellular
sheath associated with the blue-green algae may be toxic or noxious, further
reducing the acceptability of these phytoplankton food resources for grazers
(Brooks, 1969; Arnold, 1971).
Increased blue-green algae domination, possibly resulting from higher
sodium levels, will reduce the quality if not, the quantity of the food
supply available to support game fish. It is not known to what extent
this would affect game fish populations. If the food supply is a critical
controlling factor, then the effect could be very severe. If not the
effect could be minor. Lake Erie, which has a sodium concentration ranging
between 7-12 mg/1 and is heavily dominated by blue-green algae, has an
apparently thriving fish population. (Lake Erie, however, is far more
biologically productive than Lake Michigan with 3 to 6 times higher phos-
phorus concentrations so that the food supply is more abundant and therefore
capable of absorbing loss of quality caused by blue-green domination.)
The Lake Michigan sports fishery has been described as one of the
most exciting in the world and is valued at many million of dollars each
year. If, as a result of increased sodium concentrations and reduced
phosphorus concentrations, blue-green algae dominance of the phytoplankton
increases; it would decrease the quality of the food supply. This could
conceivably lead to reduction or even a collapse of the sports fishery.
TOXIC ORGANIC SUBSTANCES
The concentration of DDT found in Lake Michigan trout during 1970
was 19 mg/kg on a whole fish basis. During 1976 the concentration of
DDT in Lake Michigan trout was 6 mg/kg. In coho salmon the concentration
dropped from 10 mg/kg in 1970 to less than 1 mg/kg in 1976 (See Figure 6).
These figures represent significant progress toward the solution of the
environmental problem which has the most direct impact on man and on man's
use of the Great Lakes, i.e. contamination by synthetic organic compounds
or toxic substances.
Toxic organic substances such as DDT and PCB bioaccumulate through the
food chain and have been found to have severe effects on mammals and birds
which are at the top of the food chain. The effects of PCB on man are well
documented. The United States Food and Drug Admininstration has established
limits on the concentrations of these substances in fish for the protection
of public health. As a result the consumption of fish from Lake Michigan is
severely restricted and interstate sale of trout and coho salmon is forbidden.
-15-
-------
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The public has been advised not to consume more than one meal per week.
Children and pregnant women are advised to avoid these species altogether.
PCB is now found throughout the environment. It is in the air, the water,
the soil and has been found in all parts of the globe. [It has been found
that eating one meal of Lake Michigan trout is equivalent to breathing
the air and drinking the water for a period of more than five years of exposure
potential to PCB (Sonzogni and Swain 1980).]
It has been estimated that 80%-90% of the PCBs reaching the lake come
by way of atmospheric fallout (Murphy 1977). They get into the atmosphere
when materials containing PCBs are incinerated or escape from land fills
via gas vapor (Andren et_ _al, 1977). The problem of PCB contamination in Lake
Michigan fish should eventually dissipate, but, it could take longer than
the dissipation of DDT because PCB is far more widely distributed in the
environment and appears to be easily merged into the atmosphere.
PCB concentrations were slightly lower in 1976 than in previous years
for all three species tested; coho salmon, brown trout, and chub. In 1977
the Michigan Department of Natural Resources reported that coho salmon
showed a decrease in PCB concentration, as compared to 1976 data, with
values ranging between 2.4 to 5.04 for whole fish samples. (In 1978 the
Illinois Department of Conservation detected 2.68 ppm PCB concentrations
in lake trout fillets). This would appear to be the start of a down-
ward trend, however, the Indiana Stream Pollution Control Board in 1977 found
in 77 lake trout fillets an average of 16.75 ppm PCBs. Values ranged
from 5.55 to 45.3 ppm. Although the manufacture of PCBs in the United
States has ceased and their use has been restricted, the lack of quality
assurance in these above tests places in doubt the establishment of any
definite downward trends in PCB concentrations in fish. The incorporation
of effective quality control measures in these tests would help to rectify
this problem.
DDT levels in bloater chubs appear to have bottomed out at a low level
which represents a decrease of more than 90% since 1969 (Figure 6). Total
dieldrin in bloaters chubs appear to be increasing to levels (Figure 6) that
are about twice the FDA levels for fillets and the 1978 U.S.-Canada Water Quality
Agreement level (IJC-GLWQB, 1978b).
Monitoring for toxic substances has been severely restricted by a lack
of reliable laboratory analysis capability. Analysing for these compounds
in lake water is a "state of the art" undertaking because of the very low
concentrations in the water,and a reliable method was not developed until
1980. Concentrations of many compounds in fish and sediments, however,
are much higher so that detecting them is much easier.
-17-
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HEAVY_METAL_S
Concentrations of heavy metals in Lake Michigan are substantially below
water quality standards or International Agreement objectives. This
indicates that there is not a significant trace metal problem in Lake
Michigan as far as water concentrations are concerned, but there could
be through bioaccumulation. Of 1040 analyses of lake water concentrates
including quality assurance replicates, there were a total of 12 analyses
above the Great Lakes Water Quality Agreement of 1978 objectives. Table
2 summarizes the results and compares them with these International
Joint Commission objectives.
ATMOSPHERICDEPOSITION
Annual loading of twelve aerosol constituents to the southern basin were
estimated from one site (Station 6). A comparison of minimum dry deposition
loadings to estimates of wet atmospheric loading and surface runoff inputs
shows that the atmospheric inputs by dry loading are at least 60 percent of
the total lead input, 30 percent of the total zinc input, 20 percent of the total
iron input and probably well over half the total sulfate and nitrate input
(Sievering _et_ _al 1979). Phosphorus dry input is about equal to wet deposition.
Total phosphorus atmospheric loads were estimated at about 16% of the total
phosphorus loads in 1976 (Eisenreich et al 1980).
LONG TERM NEARSHOREIMPROVEMENTS ILLINOIS-INDIANA
There have been gradual improvements in nearshore conditions in the
Illinois and Indiana nearshore zone (Rockwell et al 1980a). These changes
appear to be linked to remedial programs which resulted in the diversion
of twelve municipal plants and one industry in Lake County, Illinois in
the years 1973 through 1978; Indiana's phosphate detergent ban in 1972
and 1973; and pollution abatement programs undertaken by northwest Indiana
industries and municipalities during the 1970"s. Gradually improving
water quality is reflected in the decline in total coliform counts along
the north shore (Figure 7) and in reduction of chemicals used for water
purification at the south water filtration plant (Figure 8).
TROPHIC STATUS
Figure 9 compares the trophic status of Lake Michigan during 1976 with
its trophic status during 1977. The improved trophic conditions are
reflected in the substantially narrower mesotrophic nearshore zones during 1977.
-18-
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TABLE 2
LAKE MICHIGAN JULY - AUGUST 1977
SUMMARY OF METALS DATA FROM WATER SAMPLES
(all values in ug/1)
PARAMETER
TOTAL NUMBER
OF SAMPLES
NO. SAMPLES
LESS THAN INSTRUMENT
RESPONSE LEVEL
INSTRUMENT LIMIT OF
DETECTABILITY LESS
THAN VALUES
MAX. MEAN*
MIN STAND.
DEVIATION
DETECTION IJC
LIMIT** OBJECTIVE
1978
Arsenic
Barium
Beryllium
Cadmium
Cobalt
Copper
, Lead
o Manganese
i Molybdenum
Nickel
Silver
Vanadium
Zinc
Calcium
Magnesium
Potassium
Sodium
Fluoride
11
102
102
103
102
102
102
103
106
102
104
101
38
549
550
794
550
258
11
0
102
101
99
15'
50
81
22
92
98
95
1
0
0
0
0
0
2
1
2
2
1
1
6
1
1
5
3
10
3
1976 & 1977 (all values
.1
.1
.01
.1
.1
<2
40
<2
4
2
9
19
8
4
13
7
25
20
in rng/1)
46.5
14.9
2.4
13.9
0.114
<2
12
<2
<2
<1
1.8
6.6
<1
2.4
<5
<3
<10
11
34.
10.
1.
4.
0.
<2
8
<2
<2
<1
<1
<6
<1
<1
<5
<3
<10
<3
9 20.7
8 7.8
1 0.9
8 3.3
102 0.07
4.2
1.3
9.3
1.2
3.4
2.2
0.9
0.1
0.7
0.004
2
1
2
2
1
7.5
9
1
2.2
7.2
3
10
11
0.5
0.1
0.01
1.5
0.1
50
"~ " ~
0.2
5
25
___
25
30
30
1.20
*Values below the detection limit were arbitarily assigned a value of 1/2 the detection limit for purposes of
calculating the mean.
**Detection limit = mean of blanks + 2 standard deviations of mean.
-------
1500-
1000'
I
«
*
500.
400.
300-
200
E
o 100<
EC
o
cc
LJJ
m
40-
30-
20.
10-
5
4-
3-
0-
South Shore Lake Survey
North Shore Lake Survey
Adapted from Lake Michigan
Water Quality Report 1979
by the City of Chicago Department
of Water and Sewers
\
\
\
v
Open Water Survey
1969
1971
1973
1975
1977
1979
Total Coliform
Figure 7
-20-
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Figure 8
Chicago Water Purification Division
South Water Filtration Plant
Dosage Pounds/Millions Gallons/Year
C
o
_Q
i_
S3
O
0)
£
'Z
_o
O
6
5
4
3
2
1
0
16
15
14
13
1973
1974
1975
1976
1977
1978
1979
1980
-------
Figure 9
Lake Michigan
Estimated Trophic Status
MUSKEGON
GRAND HAVEN
B£NTON HARBOR
MICHIGAN CITY
Area Not
Studied In 1976
Study Area Involved Open Lake Monitoring
In Northern And Southern Basins.
1976
Eutrophic
Mesotrophic
MUSKEGON
| GRAND HAVEN
f Mesotrophic
WNTON HARBOR
MICHIGAN CITY
Eutrophic
HAMMOND Mesotrophic
Area Not
Studied In 1977
Study Areas Included Nearshore Zones At
Milwaukee, Chicago. Calumet And Green Bay,
Open Lake Monitoring In Southern Basin Only.
1977
-22-
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Many different systems have been developed for characterizing the trophic
status of lakes. Systems based on empirical observations from many
different water bodies have been derived. The systems most applicable to the
Great Lakes were developed by the IJC Upper Lake Reference Group (1976),
Dobson (1976) and Rast and Lee (1978). These systems were used to evaluate
Lake Michigan. Although these systems are an improvement over the purely
subjective judgment previously used to define the trophic state of the
lakes, they do not entirely agree with each other. Further, the processes
of eutrophication which these systems attempt to quantify are not linear
and not monotonic. Table 3 provides a summary of the trophic status
indicator values, which were developed for total phosphorus, chlorophyll
"a", and secchi depth by each observer. Table 3 also contains trophic
status indicator transition values for aerobic heterotrophs which have
been proposed by the Great Lakes Research and Surveillance staff and which
may be used together with each of the previous systems, to expand their
indicator categories to include microbiology (Rockwell et al 1980b).
The evaluation for Lake Michigan was developed by applying all three
systems to data for each station and applying the consensus or most
prevalent result for each year. Improved conditions during 1977 are
reflected by the narrow mesotrophic zones along the shore lines. Eutrophic
zones shown are Milwaukee and Indiana Harbor Canal in 1977 are the results
of near shore studies conducted during that year and undoubtedly existed
during 1976 also.
U.S.E.P.A. RESPONSES
The response of the Great Lakes National Program Office (GLNPO) to the 1976-
1977 intensive field year has been an on-going process. The GLNPO monitoring
program has moved to include a search for toxic chemicals which may be
bioaccumulating in fish and sediments. This programs seeks to pinpoint
sources of Great Lakes toxics via harbor and tributary monitoring. Programs
to compute actual loadings of pollutants to the Great Lakes have been a
part of the GLNPO program for several years. However, these loading
programs have recently expanded through high flow monitoring to more
accurately determine tributary loads and atmospheric inputs into the lakes.
SPECIFIC RESPONSES
TECHNICAL ASSESSMENT TEAMS (TAT)
The Great Lakes intensive survey on Lake Michigan in 1976-1977 collected
more data on this lake's water quality than ever before in history. Processing
that information and interpreting its significance required an extensive
dedication of time and agency personnel - two commodities in short supply
due to resource constraints and the necessity to have timely enough data
interpretation actually effect control programs.
-23-
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TABLE 3
ENRICHMENT PROBLEM RELATIONSHIPS APPLIED ON LAKE MICHIGAN DATA
01igotrophic Mesotrophic-Eutrophic
Mesotrophic Indicator Indicator
Transition Values Transition Values
H.H. Dobson Systems (1976)
Summer Total Phosphorus (ug/l) 8 19
ChlorophylI "a" (ug/i) 2 5
Seechi Depth (meters) 6 3
I JC
The Waters of Lake Huron & Lake Superior'
Upper Lakes Reference Group (1976) - Volume I
Total Phosphorus (ug/l5 6.5 14.1
Chlorophyll "a" (ug/l) 2.4 7.8
Seechi Depth (meters) 8.6 2.9
Rast and Lee (1978)
Annual Total Phosphorus (ug/l) 10 20
Summer Mean Epilimnetic Chlorophyll "a" (ug/l) 2 6
Seechi Depth (meters) 4.6 2.7
Surveillance & Research Staff
Aerobic Heterotrophs
Aerobic Heterotrophs - nearshore 120 2000
(15 meters and >3 kilometers)
'Estimates of the mid-range of each parameter were made from page 128 of the report
"The Waters of Lake Huron and Lake Superior".
-24-
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During 1980 and 1981, GLNPO assembled TAT's for Lake Erie and Lake Huron
to help prepare reports directed to the scientific community, governmental
decision makers, and the pub!ic-at-large based upon intensive field year
efforts. U.S. universities, particularly the sea-grant universities,
have developed research programs on the Great Lakes involving well recognized
scientists. During FY 1980, direct grants were made to Ohio State
University's Center for Lake Erie Area Research and to the University of
Michigan's Great Lakes Research Division to provide assistance in data evaluation,
coordination of reports, report writing and technical editing. These teams will be
teams will be responsible for data from the 1978-1979 intensive field
years on Lake Erie and the 1980 intensive field year on Lake Huron.
PROGRAM DESIGN EVALUATION
To date the selection of station networks and the frequency of cruises
necessary for an intensive year of monitoring on the Great Lakes has been
based on best judgment. Actual implementation may be less than required
due to weather conditions or financial resource constraints. However,
field work imposes a limitation on discovery of spacial variability and
meteorological variability. To better understand the sufficiency of
sampling networks and frequencies, open lake eutrophication simulations
were developed and are underway using Lake Michigan's 1976-1977 data
base. Lake Erie will be evaluated in a similar manner if the Lake Michigan
simulations meet expectations.
The open lake eutrophication simulations require a minimum number of
stations and sampling cruises to assure a sufficient data base for their
verification and operation. The verified model can be used to determine
the adequacy of the station network and cruise schedule. It can also be
used to project long term changes in chlorophyll "a" levels dependent on
various remedial program strategies such as phosphorus controls.
One unexpected finding of the intensive survey of Lake Michigan in 1976-
1977 was the rapid and large change in lake chemistry apparently brought
on by the extensive ice cover resulting from the severe winter. Lake
chemistry changes exceeded expectations, by far. Lake simulations will
be modified to include a capability to vary spring lake concentrations
based on winter meteorological conditions.
MONITORING RESPONSES
ANNUAL LAKE ERIE PROGRAM
One lake has been selected for annual programs by the GLNPO, Lake Erie,
since it is the most eutrophic as well as the smallest of the the Great Lakes.
Due to its relatively small size, lake conditions here could change more
rapidly than in the other lakes due to loading changes. Lake Erie has a
-25-
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filling time of 2.5 years for the entire lake, while the filling time for Lake
Michigan is estimated at 100 years. The first GLNPO annual program for
Lake Erie was funded in 1980. It includes a limited number of open lake
stations to provide an estimate of annual trophic conditions and to determine
the extent, severity, and duration of dissolved oxygen depletion in the
central basin. This annual program also monitors nearshore conditions by
quantative measurements of cladophora growth.
TRIBUTARY HIGH FLOW LOADS
To improve annual estimates of nutrients and metals loadings to the
Great Lakes, 12 high flow events on each major tributary are monitored in addition
to regular monthly surveys. This program provides more accurate estimates
of the annual tributary loads to the Great Lakes. Loading data is very
important in modeling simulations of eutrophication responses to
various phosphorus management strategies.
ATMOSPHERIC DEPOSITION
The atmosphere has been found to be a significant source of many
chemicals. In the southern basin of Lake Michigan atmospheric loads
of anthropogenically derived trace elements (lead, zinc, and iron),
nutrients (nitrate and phosphate), and a conservative ion (sulfate) are
found to be a large percentage of the individual total loads for these
substances (Sievering _et _al_ 1979). To improve estimates of atmospheric
contributions, GLNPO has instituted a network of 40 bulk and wet atmospheric
deposition sampling sites along the shorelines and on some islands within
the Great Lakes. In addition to their primarily function to provide
information on nutrients, metals and toxic substances, these sites will
collect information to support the requirements of the National Acid
Rain monitoring program.
INVESTIGATION OF NEW POTENTIAL PROBLEMS
The 1976-1977 Lake Michigan field work, as well as the report from a
grant to study the fifty year phytoplankton record from the City of
Chicago's water filtration intakes, focused attention on sodium inputs to the
the lake as a potential critical nutrient controlling the growth rates of some
blue-green algae in Lake Michigan waters.
New waste control processes and road salting programs contribute
sodium to the basin. The concentration of sodium in Lake Michigan varies
between 4 and 5 mg/1. Laboratory experiments with sodium concentrations
levels above 5 mg/1 have resulted in some species of blue-green algae
thriving. Concentration of 4 mg/1 to 5 mg/1 sodium may be a critical
threshold above which blue-green algae are found to have a competative
advantage over other forms of algae. Should this situation hold in the
waters of Lake Michigan, it would alter the composition of the food base
for zooplankton and, eventually fish. The nature and severity of this
potential shift to blue-green algae is not known. However, this preliminary
information would suggest a study of controls on the use of salt in road
deicing and industrial processes so as to protect the lake against deterioration
of its food chain at the most fundamental level.
-26-
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HARBOR SEDIMENT PROGRAM
Toxic substances are being introduced into the environment from many
sources. Secondary compounds from these toxicants are often formed in the
environment. Some of these secondary compounds are more hazardous than the
primary chemicals from which they came» River, harbor, and lake sediments
collect pollutants. Under some circumstances sediments may release the
pollutants they have collected. To identify "hot spots" where toxic substance
have accumulated, GLNPO has initiated a harbor sediment program. This
program will seek out contaminated sediments in 19 harbors in 1981, searching
for a wide range of toxic compounds in the sediments. With this information
harbor sediment dredging activities will then be reviewed to evaluate the
desirability of depositing any contaminated sediments found in the harbors
in the adjacent lake.
FISH FLESH CONTAMINANT PROGRAM
Bioaccumulation of toxic contaminants has been shown to present significant
health hazards to man, even though the contaminant levels are may be low in
the environment. Since fish are near the top of the aquatic food chain and
are consumed by man, GLNPO has undertaken an extensive program to search for
a wide range of chemicals in fish flesh (Table 4).
During the 1970*s, the use of DDT was banned and PCB's were greatly
restricted. The fish monitoring program has tracked the response to these
actions and is used to assess the effectiveness of the remedial programs
designed to limit the exposure of the biological and physical environment to
these chemicals.
The fish program is directed at both open lake game fish and at near-
shore areas. It is used in conjunction with findings from the sediment
program to identify areas where bioaccumulation of toxics substances is
occuring.
INTENSIVE GREAT LAKE SURVEILLANCE
The regular intensive surveys of the Great Lakes will continue in the
Lake Ontario basin in 1981-82. GLNPO will implement intensive nearshore
studies in the Niagara River area, Rochester embayment, and the Oswego area.
These areas have been identified as water quality problem areas. The
studies will determine compliance with state water quality standards and Inter-
national Agreement objectives. Canadian agencies will conduct the intensive
survey of Lake Ontario open waters.
STATE MONITORING GRANTS
Funds have been made available to monitor the Great Lakes bordering
the State of Michigan over a five year period. Work involves fish moni-
toring for toxic substances, tributary monitoring, water intake monitoring
and verification, and nearshore studies at selected problem areas.
-27-
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TABLE 4
CHEMICALS MONITORED IN FISH FLESH
Contaminants monitored (Lipid content determined on all samples)
(a) Al! samples:
Organics
DDT and Metabol ites
AId rin/D i eId ri n
PCBs
Mi rex (Lake Ontario only)
Chlordane ( o£ , ~y , oxy)
Heptachlor
Heptachlor Epoxlde
MetaIs
Arsen ic
Cadmi um
Copper
Lead
Chromi um
Mercury
Zinc
(b) Selected samples will be scanned for organics and metals
using best available methods. The organic scans involving
acid, base, and neutral extraction should include, but not
necessarily be I imited to:
Endr in
Kepone
Li ndane
Methoxychlor
Toxaphene
Dichlorobenzenes
Tr I chIorobenzene
(HCBD) Tetrachlorobenzene
PentachIorobenzene
Hexac hIoroben zene
p - Bromoan i so Ie
Chlorinated Naphthaline
MethyI naphtha I ene
Tr ichlorophenol
Pentac hIoropheno!
TetrachIorophenoI
Tetrac hIoroeth yI en e
Chlorinated Styrenes
(Octa & Poly)
HexachIorobutad i ene
B-BHC (Benezene Hexachloride)
(BHC I, 2, 3, 4, 5, 6-
Hexac hIorocycIohexane)
Polybrominated Biphenyls
Chlorinated Terphenyls
Polynuclear Aromatic Hydrocarbons
-28-
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WATER INTAKE PROGRAMS
Water intakes are in the nearshore zone and provide permanent monitoring
posts. Several sites have been selected on the Great Lakes to provide a
minimun amount of weekly data year round. These sites can link together the
intensive year efforts. They will provide some detection of major trends in
the nearshore areas where they are located.
RECOMMENDATIONS
Toxics in the environment have become the most significant threat to
man's enjoyment of available fishing resources in the Great Lakes. More
importantly, bioaccumulation of a wide range of known organic and inorganic
contaminants has been shown to be a significant health hazard to man
and predators at the top of the aquatic food chain. During the seventies pro-
duction bans were placed on DDT and PCB. A fish monitoring program is required
to track the effect that bans have on ambient levels of toxics in fish
flesh. The program should also attempt to identify additional compounds
that are bioaccumulating in Great Lakes's fishes.
Toxics also accumulate in sediments. Secondary compounds can form
in sediments from toxic introduced into the environment. To identify
geographical "hot spots" toxic substance accumulation, a harbor sediment
program is recommended. This program should be coordinated with the
fish flesh monitoring to enable remedial program resources to be directed
to curtail and to clean up hazardous substances which effect food resources
and the public health.
The fish and harbor sediment monitoring programs will provide
identification of potential industrial and municipal sources of hazardous
substances. This information can be used to modify National Pollutant
Discharge Elimination System (NPDES) permits to curtail or eliminate
sources of toxicants which may pass into the Great Lakes.
Nutrient loads to the Great Lakes have not been quantified adequately
by the previous tributary and atmospheric monitoring programs. Mathematical
simulations of lake responses to various phosphorus removal strategies
are based on mass balance equations and observed concentrations in the
lake. The mass balance equation is made up of terms involving inputs
from tributaries, atmospheric sources, point source discharges, and
sediments, as well as outputs from the lake. Accurate estimates of the inputs
are required for the models to successfully predict responses within the
required ranges so as to measure alternative remedial program effectiveness.
The annual variability of ambient phosphorus concentrations within the
lake has significance for the design of lake monitoring programs. The
present strategy, which calls for intensive surveys during two of every nine
years, is based on the assumption that significant changes occur slowly over
a period of years. The magnitude of the observed decrease in total phosphorus
which occurred during the 1976-77 winter raised the issue of what is an
appropriate long-term nutrient monitoring strategy. Since meterological
-29-
-------
conditions during the 1976-77 winter significantly altered this aspect
of Lake Michigan's chemistry and since total phosphorus concentrations
during the ice-out period determine in large part the annual 1imnological
response of the system, the current monitoring strategy is inadequate. There
appears to be sufficient evidence that this type of concentration change is
not unique to Lake Michigan and occurs in the other Great Lakes (Rockwell, 1981).
Thus, proper interpretation of long term trends requires annual determinations
of the ice-out conditions on each of the Great Lakes.
Within the intensive field year program observed changes occurring
between cruises indicate the need for biweekly or weekly monitoring at
selected sites. These stations should be monitored to characterize shorter
term phenomena, such as phytoplankton succession or nutrient cycling, and to
increase our knowledge of the biological processess essential to controlling
eutrophication responses of the ecosystem. Less frequent monitoring can
miss some aquatic species or short lived blooms. Knowledge of these events
are useful in characterization of the lakes biological status. However,
the intensive monitoring completed during 1977 at a single deep water
station showed that during a twenty-four hour period the hour-to-hour
variability was not statistically significant. Thus, the assumption that
a cross-lake transect completed within one day is synophic, is reasonable,
provided a storm does not occur.
Variable sedimentation rates during winter appear to be the most
probable mechanism for the rapid changes in total phosphorus concentrations
observed during the 1976-77 field years on Lake Michigan. Lake models
need to be enhanced to account for sediment transport, deposition, and
resuspension processes. To successfully incorporate these mechanisms and
their relationships to winter meterological conditions, studies of winter
sedimentation rates in deep lakes are required.
Increasing levels of chloride and sulfate concentrations will not
threaten drinking water standards during the next several centuries unless
loads are dramatically increased. However, increasing concentrations of
these conservative ions are making possible an ever expanding habitat for marine
algal forms. Some new marine algal forms have been observed in the
nearshore zones of Lake Michigan as well as in other more eutrophic Great
Lakes. Furthermore, increasing sodium concentrations in Lake Michigan may
permit certain blue-green algae species to grow more rapidly and selectively
replace more desirable zooplankton food sources during the summer. Studies
of sodium and other conservative ion effects on phytoplankton in the
southern basin of Lake Michigan need to be undertaken. Control options
to restrict chloride and sodium inputs from road de-icing and industrial
processes should be investigated.
-30-
-------
In summary our recommendations are:
(1) Toxic monitoring programs should continue to be implemented to
determine effectiveness of remedial activities. These
programs include
a) Fish flesh monitoring of game fish in the open lake and at river mouth
collection sites.
b) Harbor sediment monitoring at selected sites to detect high concen-
trations of toxic contaminants.
c) Toxics monitoring in the water column at selected sites to determine
existing background levels.
(2) The nutrient monitoring strategy should be modified to improve the ability
to predict long term effects of alternate phosphorus control remedial programs,
This modification should involve
a) High flow event monitoring twelve times per year at selected major
tributaries.
b) Improved and expanded atmospheric load monitoring at selected sites
along the shore lines and on islands within the Great Lakes.
c) Determining spring ice-out conditions at selected sites on each of
the Great Lakes each year.
d) Adding weekly to biweekly monitoring at selected intensive field
year sites.
e) Conducting limited mid-winter surveys after an intensive Great Lake
field year.
(3) Expansion of current knowledge in several significant new problem areas
is recommended:
a) Studies of sodium and conservative ion effects on phytoplankton in the
southern Lake Michigan Basin should be initiated.
b) Studies of winter sedimentation processes and incorporation of sedi-
ment transport, deposition and resuspension processes into new or
existing lake modes should be undertaken.
-31-
-------
ACKNOWLEDGMENTS
We wish to thank the other past and present members of the Great
Lake National Program Office including Mr. Terry Moan, Mr. Stanley
Witt, and Dr. Clyde Marion for their contribution to the scientific
report which was used as the basis for this management report.
The authors are also grateful for the significant contributions to this
study which were made by the scientific community. Although it is not
practical to reference each contribution, we want to thank Dr. Alfred Beeton
and Mr. Nelson Thomas for their support and advice during the entire
project effort.
We want to thank Ms. Melody Adams of Great Lakes National Program
Office secretarial staff and Ms. Iris Williams of MAR, INCORPORATED for
their dedicated efforts in typing and modifying the report.
We also wish to acknowledge the personal efforts of Mr. Phillip
Reed and Mr. Joseph Szawica in providing the South Chicago water
filtration plant data used in this report.
The bathymetric chart and morphometrie parameters were prepared by
Ratko Ristic and Jovanka Ristic and we thank them for their kind permission
to use their work.
-32-
-------
Dobson, H.F.H. 1976. Euthrophication status of the Great Lakes.
Unpublished manuscript, CCIW.
Doneth, J. and the Great Lakes Basin Commision. 1975. Material usage
in the U.S. Great Lakes Basin. Task 8 for PLUARG.
Eisenreich, S.J., P.J. Emm!ing, and A.M. Beeton 1980. Determination
of Atmospheric Phosphorus Addition to Lake Michigan. Environmental Research
Laboratory-Duluth OR&D USEPA EPA 600/3-80-063.
Federal Water Pollution Control Admin. 1968. Lake Michigan basin,
physical and chemical conditions. U.S. Govt, Printing Office Sip.
Fuchs, R.J., 1978. Trends in the use of inorganic compounds in home
laundry detergent in the United States. Chemical Times and Trends, p 36-41.
Illinois Annual Air Quality Reports 1976-1979. Illinois Environmental
Protection Agency, 2200 Churchill Road, Springfield, Illinois 62706.
International Joint Commission Great Lakes Water Quality Board. 1978a
Great Lakes Water Quality, Appendix B Surveillance Sub-Committee Report.
International Joint Commission Great Lakes Water Quality Board. 1978b.
Great Lakes Water Qualtiy, 1975 Annual Report.
International Joint Commission, Upper Lakes Reference Group. 1976.
The waters of Lake Huron and Lake Superior, Vol. I summary and recommendation.
Jensen, T.E. and L. Sicko-Goad. 1976. Aspects of Phosphate Utilization
By Blue-Green Algae. Corvallis Environmental Research Laboratory, Ecological
Research Series EPA-600/3-76-103.
Kratz, W.A. and J. Myers. 1955. Nutrition and growth of several
blue-green algae. Am. J. Bot 42:282-287.
Lake Michigan Water Quality Report 1978-1979. 1979-1980. The City
of Chicago Department of Water and Sewers and Illinois EPA Division of
Water Pollution Control.
Makarewicz, J.C. and R.I. Baybutt. In Press. Analysis of the Phyto-
plankton Community of Lake Michigan at Chicago. I. Longtenn Changes in the
Phytoplankton Community Structure. II. The Correlation of Increased Sodium
Levels with Blue-green Algae Growth. Torrey Botanical Bulletin.
Murphy, T.J. 1977. Polychlorinated Biphenyls in Precipitation in
the Lake Michigan Basin. Technical Report, Environmental Protection Agency.
Provasoli, L. 1969. Algal nutrition and eutrophications. p574-593. In;
Eutrophieation: Causes, Consequences, Correctives. National Academy of
Sciences, Washington. 661 p.
Quinn F.H., R.A. Assel , D.E. Boyce, G.A. Leshkevitch, C.R. Snider,
and D. Weisnet. 1978. Summary of Great Lakes Weather and Ice Conditions,
Winter 1976-77. Technical Memorandum ERL-GLERL 20. 141p
-34-
-------
Rast, W. and G.F. Lee. 1978. Summary analysis of the North American
OCED eutrophication project: Nutrients loading-Lake response relationships
and trophic state indices. EPA-600/3-78-008.
Richardson, W. 1980. Personal communication. EPA Large Lakes
Research Station Grossee lie, Michigan.
Risley, C., Jr. and F.D. Fuller. 1965. Chemical characteristics of
Lake Michigan. Proc. 8th Conf. Great Lakes Res., Great Lakes Res. Div.
Publ. No. 13, Univ. of Michigan, p. 168-174.
Rockwell, D.C., C.V. Marion, M.F. Palmer, D.S. DeVault, and R.J.
Bowden. 1980a. Environmental Trends in Lake Michigan p 91- 132 In: Phosphorus
Management Strategies for Lake S. RC Loehr, C.S. Martin, W. Rast.
Ann Arbor Science. 490 p.
Rockwell, D.C., C.V. Marion, M.F. Palmer, D.S. DeVault, and R.J.
Bowden. 1980b. Lake Michigan Intensive Survey 1976-1977 EPA-905/4-80-
003-A 185p
Rockwell, D.C., 1981. Maximum Percent Ice Cover as an Indicator
Mechanism for Changes in Large Lake Total Phosphorus Concentrations.
Abstract Twenty Fourth Conference on Great Lakes Research. International
Association for Great Lakes Research. The Ohio State University Columbus,
Ohio April 28-30, 1981. p 38.
Rodgers, P. 1980. Personal communication. DePaul University
Large Lakes Research Station Grosse IIle, Michigan 48138.
Rousar, D.C. and A.M. Beeton. 1973. Distribution of phosphorus,
silica, chlorophyll "a", and conductivity in Lake Michigan and Green Bay,
Wise. Academy of Science, Arts, and Letters. Vol. 61, p 117-141.
Si evering, H., D. Mehul, D.A. Dolske, R.L. Hughes, and P. McCoy.
1979. An Experimental Study of Lake Loading by Aerosol Transport
and Dry Deposition in the Southern Lake Michigan Basin. USEPA-GLNPO.
EPA-905/4-79-016.
Sonzogni W.C. and W.R. Swain. 1980. Perspectives on U.S. Great Lakes
Chemical Toxic Substances Research. J. Great Lakes Research Vol. 6 Number 4
p 265-274.
STORET is a computerized data base system maintained by the U.S. EPA
for the storage and retrieval of data relating to the quality of the water-
ways within and contiguous to the United States.
Stukel, J. and B.R. Keenan, 1980. Ohio River Basin Energy Study-University
of Illinois, Champaign, Illinois.
Torrey, M.S. 1976. Environmental Status of the Lake Michigan Region. Volume
3. Chemistry of Lake Michigan. Argonne National Laboratory, Argonne, Illinois.
418p.
-35-
-------
APPENDIX A
DESCRIPTION OF SURVEY
Figure A-l shows the station locations and schedules for cruise conducted
on the main lake. The station were selected to provide complete coverage of
the main lake and representative coverage of nearshore zones which were not in
problem areas. Figure A2 shows locations of stations used in nearshore studies
in problem areas which were conducted during 1977. Separate reports on these
nearshore studies are being prepared. The actual location of many of the stations
was selected because data from these points are available from older studies
primarily the 1962-63 study of Lake Michigan conducted by the U.S. Public Health
Service.
Depth Selection. During the first four cruises of 1976, each station was
sampled when possible, at 2, 5, 10, 20, 50, 100 meters, and 1 meter above
the bottom. Throughout the rest of 1976 and during 1977 additional samples
were taken from thermally stratified stations at mid thermoeline, 5M above
and 5M below mid thermoeline. Any of the fixed depths above that were within
3M of the thermoeline depths were deleted (Figure A-3).
Table A-l, A-2 and A-3 list the analyses performed on each cruise.
and the rationale for the parameters used to index the trophic state of
Lake Michigan.
Figure A-4 illustrates the sample processing performed on the USEPA
monitoring vessel Roger R. Simons and Figure A-5 shows the sampling pro-
cessing on board the University of Michigan vessel Laurentian.
A-l
-------
Fiffiire A 1
Lake Michigan
Survey Cruise Stations
NORTHERN BASIN
Transect 6
MILWAUKEE
/
/
/
n IIA
218
\
Transect B
SOUTHERN BASIN
it
\ffi GRAND HAVEN
«i
*
19 20* 20
Transect 4
* « 10 11 12 13«- 13j
ZIONy» S* * * *,
WAUKEGAN-J Transect 3
LAKE FOREST
CHICAGO
8 »A «8 -^fe BENTON HARBOR
. /
Transect 2
SCAIE
Ob 0 10 2O 30 40 50
1 I 1
1 2 3
^xik
Trans0ct 1 MtcHtGANciiY
^ ***
L_l 1 I I | I I
10 S 0 10 20 30 40 SO 60 70 80 KILO
I I I I I I I I I I I
METERS
HAMMOND
A-2
-------
Hgure A-2
Northern Greenbay
Nearshore Study
Milwaukee Nearshore / *M
, 5
9
Chicago Calumet Nearshore
s -
SCALE MILES I
' \ 1 ' P
Indiana Nearshore
Lake Michigan
Nearshore Survey
Cruise Stations
A-3
-------
>
jr-
Temperature °C
5°
20°
0
I 20--
Q.
03
o
50--
100--
150--
Upper Epilimnion
(Surface)
Lower Epilimnion
Surface
Mid-
Water
Bottom
Surface
Bottom
Nearshore
Station
Upper
Hypolimnion
Unstratified
Shallow Lake
200'-
(Bottom)
Lower
Hypolimnion
Figure A-3
SCHEMATIC REPRESENTATION OF
SAMPLING DEPTHS IN LAKE MICHIGAN
Statified Deep Lake
-------
TABLE A-l
PARAMETERS MEASURED BY GLNPO
in 1976-1977
Parameter
Air Temperature
Wind Speed
Wind Direction
Seechi Depth
Wave Height
Water Temperature
Optical Transmittance
Turbidity
Specific Conductance
PH
Total Alkalinity
Suspended Solids
Total Ammonia Nitrogen
Total Kjeldahl Nitrogen
Total Nitrate + Nitrite
Total Phosphorus
Total Dissolved Phosphorus
Dissolved Orthophosphate
Total Cyanide
Metals
Total Chloride
Total Sulfate
Total Fluoride
Dissolved Reactive Silica
Total Arsenic
Fecal Coliform
Total Plate Count
Chlorophyll "a" fluor.
Pheophytin "a" fluor.
Total Phenolics
Primary Productivity
Aesthetics
Phytoplankton
Zooplankton
STORET
Cruises
Stations
Depths
Sample
00020
00035
00040
00078
70222
00010
00074
00076
00095
00400
00410
00530
00610
00625
00630
00665
00666
00671
00720
00940
00945
00951
00955
01002
31616
31749
32209
32213
32730
70990
All
All
All
All
All
All
All
All
All
All
All
Selected
All1
Se lee ted
Alll
All1
All1
All1
Se lee ted
Selected
Selected
Selected
Selected
All1
Sed-77
Selected
Selected
Selected
Selected
Selected
Selected
All where
Selected
Open lake
All
All
All
All
All
All
All
All
All
All
All
All
All
All
All
All
All
All
Select
All
All
All
Select
All
Select
All
All
All
All
All
All
applicable
All
All
__
All
cont.
All
All
All
All
All
All
All
All
All
All
All
All
5M
All
All
All
All
5M
Selected
Selected
All
All
All
5M
All
Integrated
Shaded from Sun
Onsite meas.
Onsite meas.
Onsite observ.
Onsite observ.
Niskin, EBT
EBT
Niskin-PEC
Niskin-PEC
Niskin-PEC
Niskin-PEC
Niskin-PEC-petri di
Niskin-PEC
Niskin-125 PE(S)
Niskin-PEC
Niskin-125 PE(S)
Niskin-PEC-125 PE(S
Niskin-PEC-125 PE
Niskin-250 PE (A)
Niskin-PE (N)
Niskin-125 PE
Niskin-125 PE
Niskin-125 PE
Niskin-PEC-125 PE
Niskin-PE (N)
ZoBell Sampler
ZoBell Sampler
Niskin-PEC
Niskin-PEC
Niskin-250 PE (A)
Niskin-BOD bottles
Niskin PE 960
Net #6 PE 960
EBT= Electric bathythermograph/transmissometer
PEC= Polyethylene Cubitainer, one gallon or 2 1/2 gallon
PE = Polyethylene, preceding number indicates volume in mis.
(A)= 10 ml/1 NaOH (l.ON) added as preservative
(S)= 1 ml/1 concentrated sulfuric acid added as preservative
(N)= 5 ml/1 concentrated nitric acid added as preservative
(L)= 5 ml/1 Lugols
^Nutrients 610, 630, 665, 666, 671 & 955 not run on metal cruises
A-5
-------
TABLE A-2
SELECTED CRUISE PARAMETERS MEASURED BY GLNPO
in 1976-1977
c
(D
Q.
o
vD vD vD C vQ vQ vQ
r- r- r- i_ r- r- r-
CTv CTv CTv CD CTv CTv ON
r-
r-
«x3
CN
O in co r-
CN
CD CD CD
> > >
in m in
CD CD CD
ID ID ID
C C C
0) 0) 0)
Q. Q. Q.
000
c c c
CD CD CD
C CD
(D >
1_
>- U
CD m
I- CD
:: ^.
in ro
o
>- CD CD
CD > >
> 1- 1-
u in m
in
CD CD
CD l_ 1-
^ o o
ID -C -C
in in
C (D ID
0) 0) CD
Q. c C
CN
c
1-
0)
+- 4- +-
C CD CD
CD =3 =3
(D (D
O O O
O O
CO CO
o
CO
>- >- CN
CD CD =»fc
> >
1- 1_ «3
in in
CD CD
i_ i_ vo
o O
in in o
ID (D -H
CD CD (D
C C 4-
m
O O
en en
(D ID I.
u u -c
JC -C <*
CJ CJ CN
CN
^ ^
CD CD
> >
1_ l_
^ ^
in m
CD CD
vO fO fO
C
O c c
CD CD
+- Q. Q.
(D O O
in c c
CD CD
l_ -C -C
CN
>- >-
CD CD
1- l_
3 ^
in m
CD 0)
i_ i_
q o
in in
ID ID
CD CD
C C
(D ID
C C
fO ID
CN
(D 0)
in in
"fr O O
CN CO CO
(D (D
CD CD
C C
0) 0)
0) CD
Suspended Sol ids
Total Kjel da hi Nitrogen
Total Cyanide
MetaIs*
Total Chloride
Total Sulfate
Total Fluoride
Total Arsenic*
FecaI Coli form
Total Plate Count
ChlorophylI "a" fluor.
Pheophytin "a" fluor.
Total Phenol ics
Primary Productivity
'Sampled on the 1977 metal cruises.
A-6
-------
TABLE A-3
SYSTEM OF PARAMETERS USED TO INDEX THE TROPHIC
STATE OF LAKE MICHIGAN
Physical Measurements
Temperature: ... exerts control on biological activities; identifies location
of thermocl ine
pH: ... affects biological activity; may reflect rate of photosynthesis
Conduct!v ity: ... a meausre of dissolved material that will conduct an
electrical current
Transmi ssi biI ity: ... an indicator of concentration of suspended solids
Wind Direction & Velocity, Estimate of Wave Height and Period: ... important
factors in mixing lake water
Water Chemistry
Dissolved Oxygen: ... depletion of oxygen, particularly in the hypolimnion
beneath the thermocl ine, limits higher life forms
AIkaIi n i ty: ... buffer to control pH; a measure of calcium bicarbonate in
lake (an alternative nutrient for algae)
Soluble Reactive Phosphorus: phosphorus is currently considered to be primary
cause of eutrophication as a nutrient of phytoplankton - form of phosphorus
instantly (most readily) available to phytoplankton
Total Dissolved Phophorus: form of phosphorus available to phytoplankton
over a period of time ( twenty days).
Total Phosphorus: form of phosphorus used in trophic evaluation system to
measure all the phosphorus in the environment
Ammon ia: ... indicator of nitrogen concentration, breaks down to nitrate/
nitrite, indicator of relatively recent pollution
Nitrate + N itr ite: ... nitrogen is a primary nutrient of phytoplankton
A-7
-------
A-3 (Cont.)
Biological Parameters
Plankton: ... species of phyto- and zooplankton present, and their relative
abundance may also indicate state of eutrophication
P r i mary Produ cti v i ty: water sample (containing phytoplankton) obtained on
station, NaCOs tagged with radioactive carbon added, sample incubated and
cells filtered on shipboard, '^C in cells counted on mainland ... primary
productivity is rate of incorporation of inorganic carbon into molecules
of living cells (increase of biomass); another indicator of state of
eutrophication
Aerobic Heterotrophs & Coliforms: heterotrophic bacteria require complex
organic compoundsof nitrogen and carbon for their metabolic synthesis and
thus are very sensitive to minute changes of fluctuations in nutrient
concentrations. Coliform are indicators of organic loadings especially
nearshore. Both are indicators of the nutrition status of lakes
Chlorophyll "a": ... measurement of these pigments can provide insight into
relative amount of standing crop of algae, results to be correlated with
primary productivity study and phytoplankton study
A-8
-------
Raw Water From
8-1 Niskin bottle
AlI chemistry depth
samples filtered through
a 53u net for integrated
roti fer sample
Polyethylene cubitainer
one gallon or two and
one half gal Ion
>I25 ml polyethylene bottle with
(for total phosphorus and total
0.125 ml con
kjel da hi nitrogen)
0.65 ml con HNC>3
>I25 ml polyethylene bottle with
(for metaIs)
^500 ml or 960 ml polyethylene with 10 ml/1 Lugols solution
(for phytoplankton and water temperature)
43 X 300 ml BOD bottles (I dark)
(for primary productivity)
4 300 ml BOD bottle
(dissolved oxygen)
£250 ml polyethylene bottle with 2.5 ml I N NaOH
(for phenol and cyanide)
^ 125 ml polyethylene bottle
(for chloride and sulfate)
-^500 ml
-> 100 ml
-» 100 ml
-) 20 ml
(specific conductance and turbidity)
(total alkalinity)
(pH)
(ammonia and nitrate plus nitrite)
^Filtrate 20 ml (dissolved reactive silica and dissolved orthophosphate)
FiIter
Mil I pore HAWP
400 ml
125 ml polyethylene bottle with
125 ml con H2S04
(total dissolved phosphorus)
I ten d iscard
4Fi I trate discard
Gel man glass fiber
type AE 500 ml
.^Filter-store in 10 ml of 90$ acetone (chlorophyll "a")
Figure A-4
Flow chart illustrating sample processing on EPA monitoring vessel.
-------
>
i
Raw Water from
8-1 Niskin
bottle
FILTER
UNFILTERED
HA Mi I Ii pore
250 ml
HA Mi I Iipore
600 ml
GFC
300 ml
Temperature
pH
Specific conductance
AI ka I i n i ty
50-120 ml
Phytoplankton
Add flutaral dehyde
(4/5 by vol ume)
FiItrate-Di scard
Filter-store in amber vial containing 8 ml 90% acetone.
^ Freeze for chlorophylI _ 60 ml. unfrozen for
analyses.
FiItrate
chemical analyses
60 ml. freeze for chemical
analyses
v FiI ten-store in flip-top vial for
' participate si I ica
FiItrate-Di scard
Filter-store in amber vial for particulate carbon and
nitrogen analyses
2200 ml
C-14
3 or 6 L & 2 D
60 ml
Freeze for
tota I phos-
phor us
FIG. A-5 Flow chart illustrating sample processing for study of northern Lake Michigan.
-------
APPENDIX B
QUALITY ASSURANCE USED BY GLNPO
Data quality assurance, evaluation , and control were achieved by the
following techniques. A maximum permissible shelf life was indicated for
each analysis, and no data were taken from samples whose shelf life exceeded
this value. New bottles, rinsed once with sample, were used for all chemical
samples. With every 20 samples or less, a pair of known stable reference
samples (one near the top of the analytical working range and one near the
bottom) and a reagent blank were analyzed. The reagent blanks were collected
in the sample bottles from the reagent water source and treated thereafter
like the other samples. Allowable deviation of the reference samples and
reagent blanks from the true values was expressed as A+Bx where x is the
true value and A and B are constants determined from a representative samp I ing.
Exceeding this allowable deviation resulted in the deletion of the data for
samples associated with these reference samples. With every 20 samples or
less, duplicate samples were collected. Each of these two samplings (Niskin
bottles) were split into separate sample bottles to give a total of four
subsamples for the chemistry ana lyes. The differences between the four sub-
samples were then used to establish the variability arising from small changes
in time or location in Lake Michigan and in laboratory analyses. The samples
for dupl ication were selected at random (Table B-l).
The Quality Assurance program included check standards, reagent blanks,
duplicate samples, split samples and performance evaluation samples (unknowns).
Two check standards prepared from reagent materials were normally analyzed
with every 10 to 20 samples (Table B-2). These check standards were analytical
checks as apposed to sampling checks, i.e. they were not carried through the
sampl ing and preservation procedures.
B-1
-------
TABLE B-l
GLNPO
DIFFERENCES BETWEEN SPLIT SAMPLE ANALYSES
SOUTHERN LAKE MICHIGAN
Parameter
mg/1*
Number of
Splits
Mean Absolute
Value of Differences
1976
Standard Deviation
Of Differences
Turbidity (HTU)
Specific Conductance
(umhos/cm)
pH (SU)
TotaI AIkaIi n i ty
Suspended Sol ids
Total Ammonia (ug/I)
Total Nitrate
+ Nitrite
Total Phosphorus
(ug/l)
CaIc t um
Magneslum
Potassi um
Sod i um
Total Chi or ide
Total Sulfate
Total Fluoride
Dissolved Reactive
Si Iica
214
210
218
208
144
136
180
254
74
74
1 10
76
200
200
40
0.031
0.15
0.0096
0.29
0.038
1.323
0.0067
1.221
0.084
0.018
0.001 1
0.022
0.020
0.016
0.00028
0.59
1.12
0.089
1.20
1.39
0.138
0.054
0.095
0.88
0,19
0.058
0.18
0.29
0.64
0.0014
208
0.015
0.075
3-2
-------
(contd.) TABLE B-I
1977
Turbidity (HTU)
Specific Conductance
( urn ho s/cm)
pH (SU)
TotaI AIkaIi n i ty
Suspended Sol ids
Total Ammonia-N
Total Kjeldahl-N
Total Nitrate
+ Nitrite
Total Phosphorus
Total Chloride
Total Sulfate
Dissolved Reactive
Si I ica
ChlorophylI "a"
(ug/ I)
Pheophytin (ug/l)
*Unless Otherwise noted.
222
0.019
0.17
224
224
224
30
202
222
214
200
206
34
224
136
134
0.094
0.0067
0.076
0.043
0.00012
0.0038
0.0014
0.00040
0.035
0.044
0.00094
0.016
0. 12
0.76
0.044
0.84
0.30
0.0013
0.055
0.0078
0.0034
0.26
0.67
0.028
0.71
0.14
B-3
-------
TABLE B-2
GLNPO Shipboard Check Standard & Reagent Blank* Summary
1976
Parameter Concentration
Total Al ka 1 in ity mg/l
Total Al kal in ity mg/ 1
Specific Conductivity umho/cm
Specific Conductivity umho/cm
Specific Conductivity umho/cm
Ammon i a N mg/ 1
Ammonia N mg/l
Ammon ia N mg/l
Ortho Phosphate P mg/l
Ortho Phosphate P mg/l
Si 1 ica Si02 mg/l
Si 1 ica Si02 mg/l
Nitrate + Nitrite N mg/l
Nitrate + Nitrite N mg/l
100
80
293.3
245.0
196.5
0.044
0.02940
0.01470
0.0079
0.0021
2.14
1 .07
0.72
0.21
Number
13
14
26
22
4
217
217
5
239
240
186
186
166
165
Mean Found
98.2
80.14
291 .73
244.77
196.50
0.04430
0.03003
0.01580
0.00792
0.0021
2.215
1.120
73.0169
22.0715
Standard
Deviation
1.240
1 .724
2.017
0.712
0.577
0.00161
0.00222
0.00045
0.00095
0.00082
0.0276
0.0288
0.0313
0.0092
*all reagents blanks in 1976 were less than or equal to the following values.
Ammonia - N 0.003 mg/l, Ortho Phosphate - P. 0.002 mg/l, Si02 0.03 mg/l,
N03 + N02-N 0.01 mg/l.
1977
Turbidity JTU
pH SU.
pH SU.
pH SU.
reagent blank
9.18
7.01
reagent blank
137
1 17
124
122
0.184
9.06
6.99
5.41
0.085
0.096
0.041
0.549
B-4
-------
(contd.) TABLE B-2
Shipboard Check Standard & Reagent Blank Summary
1977
Parameter
Total Alkalinity mg/l
Total Al kal inity mg/l
Tota ! A 1 ka ! i n i ty mg/ 1
Specific Conductivity umho/cm
Specific Conductivity uhmo/cm
Specific Conductivity uhmo/cm
Ammonia-N mg/l
Ammon ia-N mg/l
Ammonia-N mg/l
Ortho Phosphate-P mg/l
Ortho Phosphate-P mg/l
Ortho Phosphate-P mg/l
Si i ica Si 02 mg/l
Si 1 ica Si02 mg/l
Si 1 ica Si 02 mg/l
Nitrate + Nitrite-N mg/l
Nitrate + Nitrite-N mg/l
Nitrate + Nitrite-N mg/l
Concentration
100
80
reagent blank
293.3
196.5
reagent blank
0.044
0.0147
reagent blank
0.0393
0.0210
reagent blank
4.28
2.14
reagent blank
0.72
0.21
reagent blank
Number
135
135
136
131
133
136
253
248
250
256
252
256
258
260
262
254
252
242
Mean Found
100.22
80.40
1.06
291.7
196.4
1.2
0.0444
0.0152
0.00029
0.0388
0.0207
0.0004
4.259
2.139
0.0052
0.721
0.209
0.0000
Standard
Dev i at Ion
0.87
0.87
0.46
1 .48
1 .69
0.53
0.00218
0.00203
0.00075
0.00189
0.00140
0.00056
0.078
0.051
0.015
0.0159
0.0083
0.0019
B-5
-------
Reagent water was prepared onboard with a Millipore Mi I ! i-Q reagent
grade water system. The system contained a carbon cartridge, demineral Izer
cartridges, a 0.2 u final membrane filter, and a 10 megohm-cm indicator light.
Feed water to the system was obtained from the onboard portable water supply
and was deionized with a high capacity hose-nipple cartridges prior to feeding
the Mi I I i-Q system.
Performance evaluation samples were provided as unknowns by EPA Region
V Quality Assurance Office (Table B-3).
Sucessive duplicate ZoBel t samples for total aerobic heterotrophs were
collected at the same locations as the chemistry duplicates. A distilled
water suitability and detergent toxicity test for microbiology was determined
on the shipboard de- ionized water and distilled water used in this study.
Media used were recorded as to date of reception, lot number (including lot
number of Rosol ic acid used in m-FC media), date the media container was
opened, and pH checked. Coliform colony verification (on at least 10 percent
of samples), sterility and air controls on the media, and sterility controls
on the filter funnels and buffered dilution water were performed and recorded.
Lot numbers also kept on the membrane filters. Daily temperature readings
on the incubators, autoclave, and water bath were recorded. The pH meter and
balance were checked for accuracy on a regular basis.
Volume Weighting Calculation. The two- I ayer volume weighted average was
determined by the equation TLVWA= (M| V| + M2 V2)/(V| + V2)
M|= mean of all samples In the upper twenty meters.
of a I 1 samples in the below twenty meters.
V|= volume of water in the upper twenty meters.
South Basin 574.3 km3
North Basin 423.4 km3
₯2= volume of water below twenty meters
South Basin 1795. I km3
North Basin 2003.6 km3
B-6
-------
TABLE B-3
Upper Lake Reference Group Performance
Standards Run During USEPA 1977 Cruises
Number of Analyses Mean
Standard Deviation
True or VaIue
Nitrate + Nitrite
Nitrogen mg/l
Standard #1
Standard #2
Ammon la
Nitrogen mg/l
Standard #1
Standard #2
Orthophosphate
as P mg/l
Standard #1
Standard #2
Dissol ved
React ive Si 1 ica
as Si 02 mg/l
Standard #1
Standard #2
Standard #3
Standard #4
Standard #5
Standard #6
19 0.3232 0.0067
19 0.4047 0.0077
19 0.0117 0.0016
19 0.0187 0.0018
19 0.0031 0.0006
19 0.0057 0.0008
12 0.751 0.014
12 0.851 0.018
8 2.38 0.087
8 2.41 0.039
4 1.28 0.015
4 1.46 0.026
Accejjted
0.32
0.40
O.Oi 1
0.018
0.004
0.007
0.76
0.86
2.47
2.52
1.35
1.52
B-7
-------
The computation was developed to estimate average lake concentrations.
With the exclusion of the dense station network in the Straits of Mackinac
comparison of means and standard errors computed using TLVWA with computer
volume weighted calculations (Yiu, 1978) gave similar statistic results
for total phosphorus and temperature. This comparison would suggest that
TLVWA results can be used for other parameters which are more uniformly
distributed and that the station network and sample depth were well
chosen for characterization of lake water quality. The layering of the
lake at 20 meters has been shown to be representative of the epilimnetic
layer (Bartone & Schelske, 1979 and Rodgers, 1980) for both 1976 and 1977.
Twenty-Four Hour Survei11 anee
Three 24-hour surveys were conducted on June 9-10, August 18-19, and
September 6-7, 1977 at a open lake station (L. Mich. 6) in the southern basin.
The unique aspect of these monitoring efforts was regular two-hour sampling
at one lake position for approximately 24 hours. Table B-4 contains the results
by depth for these visits.
Note that the variability over a 24 hour period for all parameters was
very low compared to the variability with depth and the variability between
24 hour periods. This is particularly true in the epllimnion and the hypolimm'on.
The somewhat higher variability in the thermocline and near bottom layers can
be attributed to the internal wave structure of the thermocline and to small
errors in the depth of the samples respectively. This low hour-to-hour vari-
ability is significant because it indicates that diurnal variability is not
important in the open waters of Lake Michigan for the parameters measured.
Stations collected over a 24 hour period therefore, can be considered to
be reasonably synoptic for these parameters. This conclusion would not
apply if a storm or major weather change occurred during the period.
B-8
-------
TABLE B-4
Station L. MICH 06 24-Hour Surveys 1977
Depth
M
2
S
12
20
25
30
40
55-64
2
9
10
17
22
27
40
65
7 2
1 5
JO
15-20
25
30
55
64
Turbidity
TU
(11) .58+.03
(11) .67+, 04
(11) .59+.03
(11) .56+. 02
(11) .61+.03
(11) .60+.03
(11) .79+.03
(11)1. 10+. 05
(12) .65+.04
(12) .67+.02
(12) .65+.02
(12) .66+. 02
(12) .75+.03
(12) .79+.03
UJ) .92+..02
(12)1.26+.19
(12H.21+.02
(12)1.28+.02
(I2)l.32+.02
(15)1.29+.03
(12)l.25+,03
(9)1.2?+.Q3
(12)0.77+.03
(12)0.72+,02
Water Temp
°c
(11)12. 4+.1
(H)l2,4+".l
(11)12. 1+.2
(11)11. 8+.1
(11)11. 2+.2
(11) 8.6+. 4
(11) 4.9+.1
(11) 4.6+.1
(12)21.2+.!
(12)21. O+.O
(12) 21. O+.O
(12)17. 8+.3
(12)13. 4+.S
(11) 6.0+.1
(12) 5,6+. I
(12) 5.6+.1
(12)21.0+.!
(12)21. O+.O
(12)20. 9+.0
(14)20.2+. 3
(11)15. 8+.4
(9) 9.4+.7
(12) 6.1+.2
(12) 5.S+.2
Conductivity
Microaiha/siB
at 25°C
(1D278+.4
(11)279+. 3
(ll)279+.2
(ll)278+.2
(11J278+.3
(ll)277+.2
(1D277+.J
(11)278+.0
(12)271+.3
(12)271+.2
(12)271+.2
(12)274+.4
(12J277+.4
(11)279+. 3
(12J279+.2
(12)279+,2
(12)268+. 3
(12)268+.!
(12)268+.!
(15) 269+. 4
(12)276+. 3
(9)279+.3
(123280+.2
(12)280+. 2
fa
(11)8.35+.01
(ll)8.34+.01
(11)8. 35+. 01
(11)8. 35+. 01
(11)8. 35+. 01
(11)8.327.01
(1D8.15+.01
(ll)8.10+.0l
(12)8. 59+. 02
(12)8.56+.01
(12)8.57+.01
(12)8.52+.01
(12)8.38+.01
( 11)8. 04+. 01
(12)8.03+.01
(12)8.02+.01
(12)8.46+.01
(12)8.46+.01
(12)8, 46+. 01
(15)8. 43+. 01
(12)8. 32+. 02
(9J8.13+.04
(12) 7, 98+. 01
(12)7,97+.01
fot
ALK
nx/1
(11)108+. 2
(11)108+. 2
(H)108+.2
(ll)108+.2
(ll)108+.2
(H)l08+.2
(11)108+. 2
(11)108+. 2
(12)108+. 2
(12)108+.!
(12)108+.!
(12)109+.3
(12)110+. 2
(11)111+.!
(12)111+.!
(12)111+. 2
(12)105+. 3
(12)105+.!
(12)105+. 2
(15)106+. 3
(l2)108+.4
(9)110+. 3
(12)110+. 3
(12)110+. 2
Total
HHj-H
»R/1
(11)2.1+0.1
(11)2.3+0.2
(11)2.0+0.0
(11)2.0+0.0
(11)2.0+0.0
(11)2.2+0.1
(11)4.9+0.4
(11)6.6+0.3
(12)2.3+0.2
(12)2.3+0.1
(12)2.3+0.1
(12)5.9+0.6
(12)12.5+0.5
(11)2.5+13.2
(12)2.7+0.2
(12)3.0+0.2
(12)2.6+0.2
(12)2.2+0.1
(12)2.3+0.2
(15)5.5+0.8
(12)13.2+0.6
(9)5.7+1.1
(12)2.2+0.1
(12)2.1+0.1
Tot
TKH-H NO +HO -N
mg/1 nq/I
Survey*! 6/9 - '0/77
(11)0.16+.011 UD0.195+.002
(11)0.16+.005 (1D0.195+.001
(11)0.16+.006 (11)0.195+.002
(11)0.15+.007 (11)0,195+.002
(11)0.15+.008 (ll)0.196+.002
(11)0.16+.007 (11)0.200+.002
(11)0.14+.007 (11)0.218+.002
(11)0.15+.008 (H)0,226+.002
Survey#2 fl7l8 -19/77
(12)0.18+0.01 (12)0.140+. 002
(12)0.19+0.01 (12)0.139+.001
(12)0.18+0.01 (12)0.141+.00'
(12)0.17+0.01 (12)0.157+.001
(12)0.18+0.01 (12)0.189+. 003
(11)0.14+0.02 (11)0. 265+. 002
(12)0.16+0.01 (12)0. 264+. 001
(12)0.19+0.02 (12)0.266+.001
Survey#3 9/6 - 7/77
(12)0.14+.007 (12)0.114+.001
(12)0.15+.005 (12)0.114+.001
(12)0. 16+. 014 (12)0.114+.001
(15)0.14+.005 (15)0.120+.002
(12)0. 14+. 005 (12)0.158+. 005
(9)0.12+.010 (9J0.230+.007
(12)0. 11+. 009 (12)0. 263+. 001
(12)0. 11+. 009 (12)0. 263+. 001
total f
ug/1
(11)4.4+0.4
(11)4.0+0.2
(11)4.8+6.3
(11)4.1+6.3
(11)4.3+0.3
(11)4.3+0.4
(11)4.5+0.3
(11)5.9+0.7
(12)3.2+0.2
(12>3.5+0,2
(12)3. 9«. 2
(12)4.2+0.3
(12)4.4+0.2
(11)4.5+0.2
(12)5.1+0.3
(12)9.3+2,2
(12)3.0+0.0
(12)3.4+6.2
(12)3,4+0,3
(15)3,2+0.1
(12)4.7+0.9
(9)4.0+0.3
(12)4.4+0.4
(12)4.2+0.2
Chloride
04/1
<6)8.50+.03
(8)8. 55+. 02
(7)8,53+.03
(7)8. 50+. 04
(5)8. 42+. 02
(8)8.40+,03
(9)8.23+,05
(6)8.26+,01
((1)8.27+,02
(12)8.28+._02
(12)8.29+.02
(12)8. 28+. 01
(12)8.30+.02
(11)8. 21+. 01
(12)8. 23+. 02
(12)8.20+.02
(12)8.35+.03
(12)8. 37+. 03
(12)8. 36+. 02
(15)8.41+.02
(12)8.51+,04
(9)8. 30^f,05
(12)8. 26+. 02
(12)8.25+,02
Diss. Reactive
Silica rnx/l
(ll)0.50+.010
(11)0.50+,009
(ll)0,5l+,013
(Il)0,54+.0l0
(lt)0.56+,009
(11)0,63+,013
(11)0,87+,016
(11)1.03+,009
(12)0,22+,002
(12I0.22+.002
(12)0.23+,003
(12)0.23+,002
(12)0. 36+, 028
(11)1. 26+. 007
(12)1.30+,007
(12)l.31+,005
(12)0.21+.002
(12)0. 21+. 003
(12)0. 21+. 003
(15)0. 23+. 008
(12)0.46+.030
(9)0.94+.080
(12)1. 38+. 007
(12)1. 40+. 006
Aerobic
Heterotropha
(11)12+ 3
(6)12+ 1
(6)16+ 6
(6)23+ 4
(7)28+ 7
(6)24+ 1
(6)18+ 3
(6V14+ 3
(8) 1+ 0
(11) 8+ 3
(11) 26+11
(6) 3+1
(6) 4+1
(3) 15+5
(3) 27±I2
(6) 4+1
Chlorophyll i
ug/1
(ll)0.83+,04
(ll)0.9l+.06
(H)1.03+.04
(ll)l.ll+,02
(H)1.12+.07
(11)1. 37+. 16
(10)1.92+.09
(U)1.71+.ll
(12)0.76+,04
(12)0.72+.05
(11)0.81+.06
(ll)0.94+.06
(11)1. 00+. 07
(10)0.85+,06
(11)0.90+.08
(11)0.73+.07
Secchi
Depth
meters
(7)6.5+0.3
(7)5.7+0.3
(7)4,2+0.2
NOTE: (number of samples at depth
mean value ± standard error of mean
-------
APPENDIX C
ORGANIZATIONS INVOLVED
A number of organizations, other than Great Lakes National Program
Office (GLNPO), participated or made significant contributions to the
1976-1977 survey of Lake Michigan. The authors wish to acknowledge the
roles of these agencies in the study.
Great Lakes NationalProgram Office (GLNPO)
The GLNPO conducted 12 open lake cruises during 1976 and 1977 on the
southern basin of Lake Michigan. A special study was made to determine locations
of heavy metal concentrations in the entire Lake during 1976 and 1977 by GLNPO.
Nearshore studies were conducted in four areas; Chicago-Calumet, Indiana, Mil-
waukee, and Green Bay.
University ofMichigan, Great Lakes Research Division (GLRD)
GLRD conducted five open lake cruises during 1976 in the northern half
of Lake Michigan and nearshore studies in 1977. In addition staff of GLRD
provided phytoplankton and zooplankton analyses for nearshore studies
under grants from the U.S. EPA. Separate reports are in press for the
northern basin and the plankton analysis of Green Bay and Indiana nearshore
studies. Stoermer and Stevenson (1979) and Stoermer and Tuckman (1979)
are available phytoplankton reports for Green Bay and the Indiana near-
shore study respectively.
Michigan DepartmentofNaturaI Resources (MDNR)
The MDNR conducted the first of the three nearshore surveys in Green
Bay during 1977 under a grant from the U.S. EPA. Results can be found in
Limnological Survey of Nearshore Waters of Lake Michigan 1976. EPA Grant
R005I460I. David Kenage, William Creal, and Robert Bash. In Press USEPA
Grosse lie, Michigan 48138.
C-l
-------
Nat ionaIOcean ic and Atmpspher i c Adm i n i strat Ion (NOAA) t= U.S. Department of
Commerce - Great Lakes Environmental Research Laboratory (GLERL) conducted
current metering studies in the southern basin, in the transition zone between
Green Bay and Lake Michigan. U.S. EPA provided ship support to deploy and
recover the current meters.
Governors State U nIversi_ty_(GS U) - Conducted a study of atmospheric loading to
the lake from the Chicago metropolitan area, with grants and ship support from
U.S. EPA. Sievering _et aj_ (1979) is a report on this work.
University of Wisconsin(U.W.) - Conducted studies of dry atmospheric fallout
to the southern basin during regular GLNPO cruises.
NationaI Atmospheric and Space Admi nistration (NASA) - Made several remote
sensing overflights of the southern basin to demonstrate and develop remote
sensing applications to water quality monitoring. Water samples were collected
by GLNPO to calibrate remote sensing outputs with actual in-lake conditions
(ground truth).
ArgonneNationalLaboratory (AND, U.S.Department of Energy - Studied
sedimentation rates In the southern basin with ship support from GLNPO.
WisconsinDepartment of Natural Resources (DNR) - Compiled biological and
chemical monitoring data applicable to the southern half of Green Bay,
under a grant from GLNPO.
Cities ofMilwaukee, Chicago, Grand Rapids, Manitowoc and South Haven - located
on Lake Michigan provided data or sent samples frorn their public water filtration
pi ants.
Fish and WlId I ife Service - Great Lakes Laboratory, Ann Arbor, Michigan
and Columbia National Fish Laboratory, Columbia, Missouri provided toxic
contaminate data in fish flesh from eastern Lake Michigan.
State University of New York at Brockport - Analyzed long term phytoplankton
and chemical data from the Chicago Water Filtration system under a grant
from GLNPO. Makarewicz and Baybutt (in press Torrey Botanical Bulletin)
are two reports on this work.
C-2
-------
APPENDIX D
MICROFICHE - LAKE MICHIGAN
INTENSIVE SURVEY DATA 1976-1977
MICROFICHE ATTACHED TO INSIDE BACK COVER
Errata Units for nearshore primary productivity are
mi I I igrams /rtP/hr
D-l
------- |