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LAKE MICHIGAN INTENSIVE SURVEY
1976-1977
By
David C. Rockwell
David S. DeVault III
Marvin F. Palmer
Clyde V. Marion
Robert J. Bowden
For
Great Lakes National Program Office
United States Environmental Protection Agency
536 S. Clark Street Room 932
Chicago, Illinois 60605
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LAKE MICHIGAN
BATHYMETRIC CHART
AND
MORPHOMETRIC PARAMETERS
1980
11
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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.
111
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FOREWORD
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 eliminate or reduce to the maximum extent
practicable the discharge of pollutants into the Great Lakes system. The
Office also coordinates U.S. actions in fulfillment of the Agreement between
Canada and the United States of America on Great Lakes Water Quality of 1978.
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TABLE OF CONTENTS
Page
INTRODUCTION 1
METHODS 3
RESULTS 36
Temperature 36
Secchi Disk and Turbidity 41
Phosphorus 46
Silica 49
Nitrate-Nitrite 52
Ammonia 57
Total Kjeldahl Nitrogen 61
Chlorophyll "a" 61
Primary Productivity 65
Phytoplankton 70
Microbiology 78
Chloride 78
Sulfate 81
pH • 81
Specific Conductivity 86
Trace Metals 86
Alkaline-Earth and Alkali Metals 119
DISCUSSION 120
Phosphorus 120
Silica 125
Nitrate - Nitrogen 128
Chlorophyll "a" 128
Phytoplankton 129
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(contd.) TABLE OF CONTENTS
Page
Conservative Ions 132
pH 133
Specific Conductivity 140
Transparency 140
Microbiology 140
Trophic Status 141
Metals . 143
Recommendations 143
Acknowledgments 146
References 147
Appendix A- Standards, Criteria, and Objectives for the Protection of Aquatic
Li^e in Lake Michigan
Appendix B- Microfiche- 1976-1977 Lake Michigan Intensive Survey Data
Appendix C- Vertical Chemical Variation at Open Lake Stations 1976-1977 by Basin
Appendix D- Biological Data
vi
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FIGURES
Page
1. Survey Cruise stations 5
2. Flow chart illustrating samples processing on EPA 18
monitoring vessel
3. Flow chart illustrating samples processing for study 25
of northern Lake Michigan
4. 1976-1977 Lake Michigan water temperatures by basin 38
5. Temperature °C 5 meter depth August 3-19, 1976, 40
April 19-24, 1977 and August 20-25, 1977
6. Station 6 24 hour survey EBT traces 42
7. Distribution of transparency - Secchi depth in meters 43
Spring 1976 and Annual Averages 1976-1977
8. 1976-1977 Southern Lake Michigan - Two layer volume 45
weighted average (TLVWA) turbidity (NTU) by cruise
epilimnetic mean (EM) and hypolimnetic mean (HM)
9. 1976-1977 Lake Michigan - TLVWA Total phosphorus (ug/1) by 47
cruise both basins EM and HM
10. 1976 Norhtern Lake Mcihgian - TLVWA - Total dissolved 48
phosphorus (ug/1) and dissolved orthophosphate EM and MM
11. Upper twenty meter distribution of total phosphorus (ug/1) 50
May 25-June 8, 1976, June 11-16, 1977, August 3-19, 1976
and August 20-25, 1977
12. Lake Michigan 18 water temperature (°C) and dissolved 51
reactive silica (mg/1) by cruise 1976-1977
13. Upper twenty meter distribution of dissolved reactive 53
silica (mg/1) May 25-June B, 1976, June 11-16, 1977,
August 3-19, 1976 and August 20-25, 1977
14. 1976-1977 Southern Lake Michigan - TLVWA Dissolved reactive 54
silica (mg/1) by cruise EM-HM
15. 1976 Northern Lake Michigan TLVWA Dissolved reactive and 56
suspended silica (mg/1) by cruise both basins EM and HM
16. 1976-1977 Lake Michigan TLVWA Nitrate + Nitrite (mg/1) 55
by cruise both basins EM and HM
17. Lake Michigan 18 Total ammonia (ug/1) and total nitrate + 58
nitrite (ug/1) by cruise 1976-1977
Vll
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Page
18. Upper twenty meter distribution of total and dissolved 59
nitrate and nitrite (mg/1) May 25-June 8, 1976, June 11-16,
1977, August 3-10, 1976 and August 20-25, 1977
19. 1976-1977 Lake Michigan TLVWA Total dissolved ammonia- 60
nitrogen (ug/1) by cruise both basins EM and MM
20. Upper twentv meter distribution of total ammonia (ug/1) 62
June 11-16, 1977 and August 20-25, 1977
21. Upper twenty meter distribution of total kjeldahl nitrogen 63
(ug/1) June 11-16, 1977 and August 20-25, 1977
22. Lake Michigan 18- Total phosphorus (ug/1) and chlorophyll 64
"a" (ug/1)'1976-1977 crusie results
23. 1976-1977 Lake Michigan TLVWA chlorophyll "a" (ug/1) by 66
cruise both basins EM and HM
24. Upper twenty meter distribution of chlorophyll "a" (ug/1) 67
May 25- June 8, 1976 and August 20-25, 197/
25. Southern Lake Michigan total phytoplankton and relative 71
abundance of major groups 1976
26. Southern Lake Michigan total phytoplankton and relative 72
abundance of major groups 1977-
27. Total phytoplankton June, August, September Mean and 74
individual cruise results (April, June, August,
September) 5 meter samples 1977
28. Total phytoplankton and the relative contribution of 77
major groups at a deep water station 23 in 1977
29. Annual geometric mean values distribution of aerobic 79
heterotrophs (organiams/ml) 1976-1977
30. 1976-1977 Lake Michigan TLVWA chloride (mg/1) by 80
cruise both basins EM and HM
31. Chloride concentration (mg/1) annual average 1976-1977 82
32. 1976 Southern Lake Michigan TLVWA'Sulfate (mg/1) 83
by cruise southern "basin EM and HM
33. Distribution of sulfate (mg/1) 1976 annual average, 84
May 25-June 2, 1976, August 3-10, 1976
34. 1976-1977 Lake Michigan TLVWA pH (S.U.) by cruise both 85
basins EM and HM
vi n
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Page
35. Upper twenty meter distribution of conductivity 87
in umhos May 25-June 3, 1976, June 11-16, 1977,
August 3-19, 1976 and August 20-25, 1977
36. 1976-1977 Lake Michigan TLVWA Specific conductivity 88
at 25°C (uinhos/cm) by cruise both basins EM and MM
37. Lake Michigan 1977 Metals survey distribution of 118
total potassium and total sodium (mg/1)
33. South water filtration plant Chicago Water Purification
Division. Total Phosphorus (ug/1) 1966-1979 124
39. Dissolved reactive silica in southern Lake Michigan 325
surface water 1954, 1963, 1976, 1977
40. Chloride time series at nearshore water intakes- 135
Grand Rapids, Milwaukee Linwood Ave. and Chicago
South Water Filtration Plants
41. Chloride (mg/1) open lake areas T37
42. Sulfate time series at nearshore water intakes-
Grand Rapids, Milwaukee Linwood Ave and Chicago
south Water Filtration Plants
43. Lake Michigan estimated trophic status 1976-1977
IX
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TABLES
Page
1 EPA sponsored Lake Michigan surveys 6
2A Stations sponsored by the USEPA in the southern basin
of Lake Michigan 7
28 Stations sampled by U. of Michigan and U.S. EPA in the
northern basin of Lake Michigan in 1976 and 1977 9
2C Milwaukee area nearshore stations 10
20 Indiana area nearshore stations 11
2E Chicago-Calumet area nearshore stations 12
2F Green Bay stations sampled by USEPA 12
2G Green Bay stations sampled by Michigan DNR 13
3A Parameters measured by GLNPO in 1976-1977 15
3B Selected cruise parameters measured by GLNPO in 1976-1977 16
4 Northern Lake Michigan station sampling depths and
number of samples 26
5 GLNPO shipboard check standard and reagent blank
summary 1976-1977 31
6 GLNPO differences between split sample analyses southern
Lake Michigan 1976-1977 33
7 Upper Lake Reference Group performance standards run
during USEPA 1977 cruises 35
3 Station L. MICH 06 24-hour surveys 1977 37
9 Lake Michigan transparency Seechi disc depth 44
10 Primary productivity, chlorophyll "a" and assimilation
coefficient 1976-1977 cruises 68
11 Lake Michigan July-August 1977 summary of metals data
from water samples 39
12 Total and dissolved aluminium (ug/1) 90
13 Total and dissolved arsenic (ug/1) 91
14 Total and dissolved barium (ug/1) 93
15 Total and dissolved boron (ug/1) 9£
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Page
16 Total and dissolved cadi urn (ug/1.) 95
17 Total and dissolved chromium (ug/1) 98
18 Total and dissolved copper (ug/1) 101
19 Total and dissolved iron (ug/1) 102
20 Total and dissolved lead (ug/1) 104
21 Total and dissolved manganese (ug/1) 106
22 Total and dissolved mercury (ug/1) 109
23 Total and dissolved molybdenum (ug/1) 110
24 Total and dissolved, nickel (ug/1) 113
25 Total and dissolved selenium (ug/1) 113 .
26 Total and dissolved silver (ug/1) 114
27 Total and dissolved vanadium (ug/1) 115
28 Total and dissolved zinc (ug/1) 116
29 Enrichment problem relationships applied to Lake
Michigan data 136
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INTRODUCTION
Monitoring and surveillance of the water quality of the lakes and
of connecting waterways are vital if we are to determine the most practical
means for protecting these irreplaceable freshwater supplies from physical,
chemical, and bacteriological health hazards. The lakes are large and
complex both individually and as a system. The Great Lakes water surface
areas are approximately equal to the surface areas of some states:
Maine (Lake Superior), West Virginia (Lake Huron or Lake Michigan), New
Jersey (Lake Ontario), and New Hampshire (Lake Erie). The water they
contain is estimated at 6000 trillion gallons. If this water was spread
evenly, all the conterminous states2 would be under 10 feet of water.
The International Joint Commission's Great Lakes Water Quality Board
has designed a long-term monitoring plan for the Great Lakes Basin providing
for a 9-year repeating cycle of intensive studies on each lake. This
plan is based, in part, on the assumption that the open waters of each
lake are changing slowly in response to cultural and environmental impacts.
The need for"skilled .personnel, large lake-going vessels, and demanding
laboratory analytical precision and accuracy are constraining requirements
in Great Lakes''surveillance. Consequently, intensive studies are confined
to one lake at a time. In cooperation with remedial programs, this program
will ensure to ;the fullest extent possible that meaningful action can be
taken for the prevention, reduction, and eventual control of pollution
in the entire Great Lakes Basin.
During 1976 and 1977, the U.S EPA undertook, in cooperation with the
University of Michigan, an intensive study of Lake Michigan. This two-year
study is the basis for this report.
OBJECTIVES OF SURVEILLANCE PROGRAM
The Water Quality Board has established surveillance goals (International
Joint Commission, GLWQB, 1976, p. VII) for the Great Lakes. One of these
goals requires surveillance and monitoring of the Great Lakes:
"To provide sufficient data to permit valid interpretation of
water quality conditions in order to distinguish the impact of
remedial programs from natural changes, both near to and remote
from sources. This goal entails documentation of the loadings
not under control of present remedial programs as well as moni-
toring ambient water quality or impacted biota in the system in
order to distinguish the impact of controlled loadings from the
impact from other causes."
^U.S. Lake Survey estimates 5457 cubic miles of water in the Great Lakes.
^Continental U.S. contains 2,975,000 square miles- Rand McNally, Popular
World Atlas, 1976.
1
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The first general conclusion and recommendation (International Joint
Commission, GLWQB 1976, p.3) is: „
"Monitoring and surveillance of the Great Lakes and connecting
waterways are necessary to evaluate the degree to which the
objectives, including non-degradation criteria, of the Canada-
United States 1972 Great Lakes Water Quality Agreement are
being achieved. As part of the above, monitoring and sur-
veillance are needed to assess the effectiveness of pollution
abatement measures. A surveillance program is required to
ascertain the nature and degree of changes in Great Lakes
water quality, particularly as a consequence of pollution
from existing or new direct and indirect human activities.
The program can also identify previously undetected con-
taminants before they have an adverse affect on the Great
Lakes environment. Surveillance provides valuable inputs
for establishing and revising limits and criteria for
both loading and aquatic contaminants."
The surveillance program for Lake Michigan was designed with four objectives
in mind:
1. To determine the status of the open and nearshore waters of Lake
Michigan in 1976-77 and to compare with the standards, criteria, and
objectives for the protection of aquatic life in Lake Michigan (Appendix A),
2. To provide data to characterize the chemical, physical, microbiological,
and biological aspects of the environment against which future changes
may be evaluated.
3. To compare present data with data collected in the past in order to
determine if Lake Michigan is changing and how these changes may be
occurring.
4. To determine how these changes are related to waste reduction and
pollution abatement programs.
AUTHORITY FOR STUDY
The Federal Water Pollution Control Act as amended in 1972 by Public
Law 92-500, Section 108 (a), authorized the EPA to enter into agreements
and to carry out projects to control and eliminate pollution in the
Great Lakes Basin. Section 104 (f) of the law provides the authority to
conduct research, technical development, and studies with respect to the
quality of the waters of the Great Lakes. Section 104 (h) grants authority
to develop and to demonstrate new or improved methods for the prevention,
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removal, reduction, and elimination of pollution in the lakes. The
Boundary Water Treaty between the United States of America and Canada in
Annex 2, paragraph 10, of the Great Lakes Water Quality Agreement required
both countries to monitor the extent of eutrophication in the Great
Lakes system and to develop measures to control phosphorus and other
nutrients. Article V (f) requires consideration of measures for the
abatement and control of pollution from dredging activities. The agreement,
signed in 1972, was reaffirmed in 1978.
PARTICIPANTS AND ROLES
The Great Lakes monitoring program is a cooperative effort involving
several government agencies and universities, with the U.S. EPA's Great
Lakes National Program Office (GLNPO), Chicago, providing overall coordi-
nation. Each organization whose data are reported on follows:
Great Lakes National Program 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 five areas, Chicago-Calumet,
Indiana, Milwaukee, and Green Bay areas. Station locations are illustrated
in Figure 1.
University of Michigan, Great Lakes Research Division (GLRD)
GLRD conducted five open lake cruises during 1976 in the northern half
of Lake Michigan and provided phytoplankton and zooplankton analyses for
nearshore studies uder grants fron the U.S. EPA. Station locations are
illustrated (Figure 1) in the northern basin of Lake Michigan. Separate
reports are in press for the northern basin and the zooplankton analysis
of Green Bay and Indiana nearshore studies. Stoermer and Stevenson (1979)
and Stoermer and Tuckman (1979) have completed reports on phytoplankton
for Green Bay and the Indiana nearshore study respectively.
Michigan Department of Natural 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
R00514601. David Kenage, William Crcal , and Robert Bash. In Press USEPA
Grosse lie, Michigan 48138.
METHODS
Methods Used by GLNPO
Vessel
In the Southern basin and nearshore cruises (Table 1) the R/V Simons
was used. The R/V Roger Simons is an ex-Coast Guard vessel build in
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Duluth, Minnesota by the Marine Iron and Shipbuilding Company as a light-
house tender. The vessel was built in 1939. The vessel is of the WAGL-
type, 122' overall length; beam-extreme 27'; draft maximum 7'; displacement,
full load 342 tons; hull material, steel; twin screw, 460 SHP propulsion
diesel.
Station Selection. The locations of the stations in the southern basin
(Table 2.) were the result of recommendations by the Monitoring Committee
for the Conference on the Matter of Pollution of Lake Michigan and Tri-
butary Basins (FWPCA 1968) and of the Great Lakes Water Quality Board (Inter-
nation Joint Commission, GLWQB 1976). All locations and data are available
in the USEPA data management system called STORET (Appendix B). The locations
of the open lake stations were influenced by the fact that they had
previously been sampled by the Federal Water Pollution Control Administration
in 1963 and 1970, the U.S. EPA in 1974 (STORET, 1975), or the U.S. Fish
and Wildlife Service in 1954-55, (Beeton and Moffett, 1964). Stations
were added to give greater coverage to the nearshore waters. Several
special stations around the Manitowoc and South Haven water intakes were
designated to evaluate water intake data in 1976.
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 thermocline,
5M above and 5M below mid thermocline. Any of the fixed depths above
that were within 3M of the thermocline depths were deleted.
Sampling. Tables 3a and 3b give, an overview of the parameters measured
during each cruises in 1976-77. In the southern basin samples were col-
lected by means of a hydrographic winch with 5/32 in. 5X7 stranded stain-
less steel aircraft cable, terminated with a 50 Ib. steel weight. General
Oceanics 8 liter and 5 liter rigid PVC Model 1010 Niskin water sampling
bottles were closed at the designated depths by General Oceanics bronze
messengers Model M1000MG. The bottles and messengers are designed so that
a messenger released from the deck can simultaneously close the first bottle
it encounters and cause this bottle to release a second messenger to close
a subsequent bottle. This sequence continues until the lowest sampling
bottle is encountered. A retractable overboard platform v/as used to
hold the person loading the Niskin bottles onto and subsequently re-
trieving the bottles from the cable. Sterile pre-evacuated 250 ml. ZoBell
bottles (APHA, 1975) were used for microbiology sample collection. A re-
tractable boom, a metering wheel (Kahlsico 5/32 in. wire block) for deter-
mining sampling depths and the necessary cable blocks for configuring the
cable completes the list of depth sampling equipment.
Water samples were processed as illustrated in the flow chart (Figure 2).
Each Niskin sampling bottle was emptied into the sample bottles as soon
as possible, normally within one minute and never later than 10 minutes,
after collection. All chemistry sample bottles were rinsed once with
sample before filling. New polyethylene containers (PEC), one gallon or
two and one half gallon, were used to hold the samples for the onboard
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Northern GrMn Bay
figure 1
• I.. Mirn 02
Survey Cruise Stations
Lake Michigan
1 , , TRANSECT 7
.-' « . . AM..,s
^* • "On '
'• I • • M. »\
ra Trantact S • YOH»IOH>VIN
I * SOUTHERN BASIN \
\ u '
Transect 4
«iun T • •» • •
»»wcto««J • Transact 3
LMtCFOH»Tl ,
Indiana Nearshore
Chicago Calumet Nearshore
0123
IN'
MHwMikM NMrahore
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TABLE 1
EPA SPONSORED LAKE,MICHIGAN SURVEYS
1976-1977
Cruise
Code
Northern Basin Open Lake Surveys (U. of Mich.) 1976
#1 Apr 22/Apr 28 1
#2 Jun 02/Jun 08 2
#3 Jul 10/Jul 17 3
#4 Aug 10/Aug 19 4
#5 Oct 07/Oct 13 5
Southern Basin Open Lake Surveys 1976
/H May 01/May 03 1
#2 May 25/Jun 02 2
#3 Jun 15/Jun 21 3
#4 Jul 07/Jul 13 4
#5 Aug 03/Aug 10 5
fi6 Aug 24/Sep 02 6
#7 Sep 14/Sep 20 7
#fi Oct 07/Oct 08 8
Whole Lake Two Day Surveys 1976
Jul 16/Jul 18 South to North (West-side) E
Jul 16/Jul 17 North to South (East-side) I), of Mich. M
Southern Basin Open Lake Surveys 1977
#1 Apr 19/Apr 24 1
#2 Jun 11/Jun 16 2
#3 Aug 20/Aug 25 3
#4 Sep 17/Sep 24 4
Trace Metal Surveys 1977
Southern Basin Jul 06/Jul 10 S
Northern Basin Jul 26/Aug 01 N
Milwaukee Nearshore Surveys 1977
#1 May 10/May 15
#2 Jul 13/Jul 18
Chicago-Calumet Nearshore Surveys 1977
#1 May 23/May 2R
#2 Aug 30/Sep n3
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(contd.) TABLE 1
Indiana Nearshore Surveys 1977
#1 Jim 11
#2 Aug 20
#3 Sep 24
Green Bay Surveys 1977
#1 May 03/May 19 (Mich. DNR)
#2 Aug 10/Aug 11
#3 Oct 05/Oct 08
TABLE 2A
Stations Sampled By the U.S. EPA In the Southern Basin of Lake Michigan
in 1976 and 1977
L. MICH
STATION
& DEPTH
# (m)
LATITUDE LONGITUDE
PREVIOUS*
SAMPLING
F P 74
OPEN LAKE CRUISES SAMPLED
(See Table 1 for Cruise Codes)
1976 1977
1 2 3 4~5~6' 7 8 E M1 1 2~T~4~ S
01
02
03
04
05
05a
05b
06
06a
06b
07
09
09a
10
11
12
13
13a
15
16
16b
17
18
15
22
18
16
35
6
13
66
27
14
4
11
31
97
128
62
17
30
37
22
79
100
161
41°46'00"
41 46 00
41 46 00
41 48 00
42 00 00
42 00 00
42 00 00
42 00 00
42 00 00
42 00 00
42 12 00
42 24 00
42 23 30
42 23 00
42 23 00
42 23 00
42 23 00
42 23 00
42 37 00
42 47 00
42 44 25
42 44 00
42 44 00
87°20'00"
87 13 00
87 00 00
86 53 00
87 25 00
87 37 00
87 33 20
87 00 00
86 39 00
86 35 40
87 43 00
87 47 00
87 42 30
87 25 00
87 00 00
86 35 00
86 20 00
86 23 20
86 18 00
87 41 00
87 31 40
87 25 00
87 00 00
X X
X X
X X
X X
X X
X X
X X
X X
X X
X X
X X
X X
X X
X X
X X
X X
XXX
XXX
XXX
XXX
XXX
XXX
XXX
XXX
XXX
XXX
XXX
XXX
XXX
XXX
XXX
XXX
XXX
XXX
XXX
XXX
X X X
XXX
XXX
XXX
XXX
XXX
XXX
XXX
XXX
XXX
XXX
XXX
XXX
XXX
XXX
XXX
XXX
XXX
XXX
XXX
XXX
XXX
XXX
XXX
XXX
XXX
X X X X
X X X X
X X X X
X X X X
X X X X
X X X X
X X X X
X X X X
X X X X
X X X X
X X X X
X X X X
X X X X
X X X X X
X X X X
X X X X X
X X X X
X X X X
X X X X
X X X X
X X X X X
X X X X
X X X X
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(contd.) TABLE 2A
L. MICH
STATION
& DEPTH
* (m)
19 92
20 22
20a 46
21 10
21a 44
21b 73
22 78
23 88
24 16
24a 80
25 20
25a 55
26 133
27 112
28 14
28a 77
29 17
29b 73
13c 18
13d 6
13e 6
13w 2
29c 6
29d 9
29e 11
29f 6
29g 10
29h 6
29j 6
29w 2
LATITUDE
42 44 00
42 44 00
42 44 00
43 08 00
43 08 00
43 01 50
43 08 00
43 08 00
43 08 00
43 06 00
43 36 00
43 36 00
43 36 00
43 36 00
43 36 00
43 36 00
44 36 00
44 36 10
42 24 35
42 24 00
42 22 55
42 24 00
44 08 20
44 07 00
44 06 05
44 07 07
44 04 55
44 05 25
44 03 35
44 06 00
LONGITUD:
86 35 00
86 15 00
86 18 00
87 53 00
87 47 45
87 37 15
87 25 00
87 00 00
86 19 00
86 28 00
87 44 00
87 39 20
87 22 00
86 55 00
86 33 00
86 47 00
87 34 00
87 27 00
86 19 20
86 17 30
86 17 50
86 17 00
87 33 30
87 33 35
87 35 10
87 36 25
87 37 05
87 38 25
87 30 30
87 40 00
PREVIOUS
SAMPLING
F P 74
X X
X X
X X
X
X
X X
OPEN LAKE CRUISES Sampled
(See Table 1 for Cruise Code)
1976 1977
12345678EM 1234SN
X
X X
X
X
X X
X X
X X
X X
X X
X X
X X
X X
X X
X X
X X
X X
XXX
XXX
XXX
XXX
XXX
XXX
XXX
XXX
X X
X X
X X
X
X
X
XXX
X
XXX
XXX
XXX
X X X X
X X X X
X X X X
X X X X
X X X X
X X X X
X X X X X
X X X X X
X X X X
X X X X
X X X X X
X X X X X
X X X X X X
X X X X X X
X X X X X
X X X X X
X X X X X
X X X X X
X X X X
X X X X
X X X X
X X X X
X X X X X
X X X X X
X X X X X
X X X X X
X X X X
X X X X
X X X X
X X X X
X X X X
X X X X
X X X X
X X X X
X X X X
X X X X
X X X X X
X X X X
X X X X
X X X X
X X X X
X X X X
X X X X
X X X X
X X X X
*Previous Sampling
F= U.S. Fish & Wildlife Service 1954/5, 1970/71
P= Federal Water Pollution Control Administration 1962/63
74= U.S. Environmental Protection Agency 1974
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TABLE 2B
Stations Sampled by U. of Michigan and U.S. EPA in the Northern Basin of
Lake Michigan in 1976 and 1977.
OPEN LAKE CRUISES Sampled
(See Table 1 For Cruise Codes)
STATION DEPTH (m) LATITUDE
LONGITUDE
1976
1 2 3 4 5 E M
NCM001
NCM002
NCM004
NCM006
NCM008
NCM009
NCM010
NCM011
NCM012
NCM013
NCM014
NCM015
NCM016
NCM017
NCM018
NCM019
NCM020
NCM021
NCM022
NCM023
NCM025
NCM027
NCM029
NCM030
NCM031
NCM032
NCM033
NCM034
NCM035
NCM036
NCM038
NCM039
NCM040
NCM041
NCM042
NCM043
NCM044
NCM045
NCM046
NCM047
NCM048
NCM049
7
31
159
171
160
137
42
7
7
28
111
160
243
250
241
419
157
247
227
75
186
120
28
32
7
34
66
82
91
85
11
50
7
14
25
28
31
26
75
137
101
75
44°10'30"
44 10 18
44 08 24
44 06 54
44 05 24
44 04 30
44 03 36
44 03 33
44 47 30
44 47 00
44 46 18
44 45 36
44 44 54
44 44 12
44 43 30
44 42 48
44 42 00
44 41 30
45 07 12
45 07 42
45 10 42
45 13 24
45 16 12
45 17 36
45 36 24
45 36 42
45 37 06
45 37 30
45 38 12
45 38 42
45 39 00
45 39 24
45 39 48
45 53 18
45 57 00
45 52 42
45 51 24
45 48 36
45 51 12
45 53 42
45 56 00
45 58 54
87°30'24"
87 28 24
87 14 00
86 59 44
86 46 00
86 39 00
86 32 00
86 31 18
87 17 48
87 12 42
87 05 24
86 58 00
86 50 42
86 43 18
86 35 54
86 28 30
86 21 06
86 15 48
86 04 24
86 08 00
86 22 30
86 36 48
86 51 24
86 57 42
86 35 48
86 32 42
86 25 30
86 18 00
86 03 30
85 54 00
85 48 18
85 42 36
85 37 06
85 35 12
85 35 12
85 28 30
85 22 00
85 15 00
85 15 00
85 15 00
85 15 00
85 15 00
X X X X X
X X X X X
X X X X X X
X X X X X
X X X X X X
X
X X X X
X X X X
X X X X X
X X X X
X
X X X X X X
X
X X X X X
X
X X X X X X
X X X X X
X X X X X
X X X X X
X X X X X
X X X X X X
X X X X X X
X X X X X
X X X X X
X X X X X
X X X X X
X
X X X X X
X X X X X
X
X X X X X
X X X X X
X X X X X
XX XX
XX X
X X
X X X X X
X X X X X
X X X X X
X X X X X
X X X X X
X X X X X
1977
N
X
-------
(contd.) TABLE 2B
STATION DEPTH (m) LATITUDE
NCM050
NCM051
NCM052
NCM053
NCM054
NCM055
NCM056
NCM057
NCM058
NCM059
NCM060
NCM061
NCM062
NCM063
NCM064
NCM065
NCM066
NCM067
NCM068
NCM069
NCM070
26
7
18
22
23
40
7
7
22
34
23
7
7
21
21
7
7
119
77
34
7
45001-24"
45 59 24
45 57 30
45 55 00
45 52 30
45 50 00
45 47 06
45 51 24
45 50 06
45 48 48
45 47 24
45 46 12
45 49 48
45 49 06
45 48 30
45 47 42
45 34 48
45 29 00
45 21 48
45 15 00
45 13 00
LONGITUDE
85°15'00"
85 00 00
85 00 00
85 00 00
85 00 00
85 00 00
85 00 00
84 49 24
84 49 24
84 49 24
84 49 24
84 49 24
84 45 00
84 45 00
84 45 00
84 45 00
85 33 30
85 33 24
85 33 12
85 33 06
85 33 00
OPEN LAKE CRUISES Sampled
1976 1977
1 2 3 4 5 E M
X X X X X
X X X X X
X X X X X
X X X X
X X X X X
X X X X X
X X X X X
X X X X X
X X X X X
X X X X X
X X X X X
X X X X X
X X X X X
X X X X X
X X X X X
X X X X X
X X X X
X X X X
X X X X
X X X X
X X X X
N
TABLE 2C
LAKE MICHIGAN
Milwaukee Area Nearshore stations each sampled three times
during each of the two 1977 surveys (See Table 1 for Cruise Codes)
STATION
MIL 01
MIL 02
MIL 03
MIL 04
MIL 05
MIL 06
MIL 07
MIL 08
MIL 09
MIL 10
DEPTH (m)
24
10
6
11
15
12
15
12
10
10
LATITUDE
42°59'00"
42 59 12
42 59 38
42 59 46
42 59 48
43 00 29
43 00 31
43 00 31
43 01 32
43 01 33
LONGITUDE
87047'00"
87 51 22
87 52 28
87 51 55
87 51 10
87 52 36
87 51 52
87 53 01
87 53 38
87 53 20
10
-------
(contd.) TABLE 2C
STATION DEPTH (m)
LATITUDE
LONGITUDE
MIL 11
MIL 12
MIL 13
MIL 14
MIL 15
MIL 16
MIL 17
MIL 18
MIL 19
MIL 20
12
47
17
7
10
12
5
15
45
15
43 01 34
43 01 39
43 01 41
43 02 22
43 02 39
43 02 43
43 03 35
43 03 55
43 04 00
43 04 17
87 52 55
87 46 00
87 51 08
87 53 22
87 52 48
87 52 03
87 52 00
87 51 13
87 47 00
87 51 18
TABLE 2D
Indiana area Nearsore stations each sampled once during
the 1977 open lake surveys #2, 3 and 4. (See Table 1 for Cruise Codes)
STATION
DEPTH (rn) LATITUDE
LONGITUDE
IND.
IND.
IND.
IND.
IND.
IND.
IND.
IND.
IND.
IND.
IND.
IND.
IND.
IND.
IND.
30
31
32
33
34
35
36
37
38
39
40
41
42
43
44
16
16
13
14
12
16
17
19
20
18
17
12
10
17
19
41042'
41 39
41 38
41 38
41 38
41 38
41 39
41 42
41 44
41 42
41 41
41 41
41 42
41 43
41 44
'10"
20
30
00
20
40
40
10
40
20
30
00
40
10
00
87°19'55"
87
87
87
87
87
87
87
87
87
87
87
86
86
86
19 47
19 45
19 42
10 40
10 50
11 10
12 00
03 40
02 30
02 00
01 50
57 00
57 20
58 00
11
-------
TABLE 2E
LAKE MICHIGAN
Chicago-Calumet area Nearshore stations each sampled three times during each
of the two Chicago-Calumet nearshore surveys. (See Table 1 for Cruise Codes)
STATION
DEPTH (m)
LATITUDE
LONGITUDE
CAL 06
CAL 11
CAL 13
CAL 20
CAL 21
CAL 22
CAL 23
CAL 24
CAL 25
CAL 26
CAL 27
CAL 28
CAL 29
CAL 30
CAL 31
CAL 32
CAL 33
CAL 34
CAL 35
10
11
11
12
11
13
16
11
12
12
12
11
18
13
15
13
10
8
13
41°40'10"
41 44 01
41 44 06
41 41 08
41 41 50
41 43 58
41 44 00
41 41 45
41 43 12
41 39 35
41 42 00
41 44 20
41 45 42
41 45 45
41 45 42
41 46 50
41 46 50
41 46 48
41 48 18
87026'20"
87 31 41
87 31 16
87 26 42
87 24 45
87 24 30
87 21 00
87 28 20
87 28 30
87 23 32
87 25 55
87 29 55
87 20 00
87 29 35
87 25 00
87 30 00
87 31 45
87 33 30
87 31 45
TABLE 2F
LAKE MICHIGAN
Green Bay stations sampled once during each Green Bay survey #2 and 3.
Green Bay survey #1 conducted by Michigan's Dept. of Natural
Resources. (See Table 1 For Cruise Codes)
STATION
GBAY 01
GBAY 02
GBAY 03
GBAY 04
GBAY 05
GBAY 06
GBAY 07
GBAY 08
GBAY 09
GBAY 10
DEPTH (m)
11
15
13
16
13
17
31
11
34
26
LATITUDE
LONGITUDE
45<>54 '00"
45 49 00
45 47 00
45 43 00
45 43 00
45 33 00
45 27 00
45 30 00
45 20 00
45 12 00
86°57'00"
87 03 00
87 04 00
87 04 00
87 02 00
87 07 00
87 08 00
87 17 00
87 15 00
87 28 00
12
-------
(contd.) TABLE 2F
STATION
GBAY
GBAY
GBAY
GBAY
GBAY
GBAY
GBAY
GRAY
GBAY
GBAY
GBAY
GBAY
GBAY
GBAY
GBAY
11
12
13
14
15
16
17
18
19
20
21
22
23
24
25
DEPTH (m)
15
12
20
21
26
18
9
21
35
38
22
12
24
18
LATITUDE
LONGITUDE
45°08'00"
45 05 00
45 04 00
45 02 00
44 57 00
44 51 00
44 53 00
45 08 00
45 18 00
45 27 00
45 29 00
45 31 00
45 32 00
45 43 00
45 47 00
87°33'00"
87 33 00
87 31 00
87 33 00
87 33 00
87 41 00
87 25 00
87 21 00
86 58 00
86 48 00
86 44 00
86 42 00
86 53 00
86 46 00
86 39 00
TABLE
2G
GREEN BAY STATIONS SAMPLED DURING GREEN BAY SURVEY #1
(Michigan DNR Green Bay Stations - A= 21 MICH)
STATION
550092
550093
550094
550095
550096
550097
210130
210131
210132
210133
210134
210135
210136
210138
210139
210140
210141
210142
860010
860011
860012
860013
860014
860015
860016
DEPTH (m)
15
34
15
15
15
26
9
9
11
17
12
30
30
30
30
30
15
12
15
16
15
15
i/!
30
46
LATITUDE
LONGITUDE
45029'30"
45 19 57
45 14 59
45 06 50
45 05 37
45 05 14
45 52 27
45 48 27
45 46 49
45 42 19
45 41 44
45 34 49
45 26 56
45 30 26
45 30 25
45 32 22
45 41 39
45 47 07
45 03 18
44 57 16
44 50 30
44 53 56
45 08 05
45 17 50
45 25 36
87°15'16"
87 16 41
87 27 28
87 33 22
87 33 29
87 30 00
86 57 48
87 01 25
87 03 03
87 02 59
86 59 41
87 01 53
87 08 12
86 44 12
86 41 01
86 51 38
86 45 08
86 38 18
87 34 02
87 34 32
87 43 43
87 24 47
87 16 13
86 58 30
86 48 38
13
-------
analyses and preparations. The temperature measurements were made on
the sample in the Niskin bottle or the phytoplankton sample. The primary
productivity samples were taken directly from the Niskin bottle.
Samples for Crustacean zooplankton were collected by vetical tow
from 1 meter above the bottom to the surface. At stations over 26 meters
in depth a second tow was made from 25 meters to the surface. A number
6 mesh net with a .5 meter mouth was used. Net efficiency was determined
by mounting a flow meter in the net mouth. This reading was then compared
to the reading obtained by raising the meter alone from the same depth as
the tow.
Samples for rotifer analysis were collected by Niskin bottle at the
same depths as chemical samples. The contents of each Niskin was filtered
through a 53 micron mesh net and a single composite sample preserved for
each station.
Dissolved nutrient samples were prepared by vacuum filtration of
an aliquot from the PEC for onboard analyses within an hour of sample
collection. Most samples were filtered within 30 minutes of collection.
A 47mm diameter n.45 urn membrane filter (HAWP 04700} held in a polycar-
bonate filter holder (Millipore XX 11 04710) with a polypropylene filter
flask was prewashed with 100 to 200 ml of demineralized water or sample
water. New 125 ml polyethylene sample bottles with linerless closures
were rinsed once with filtered sample prior to filling.
An aliquot was removed for the dissolved orthophosphate and the
dissolved silica determinations after which the remainder was preserved
with 1 ml/1 concentrated sulfuric acid to be subsequently analyzed for
total dissolved phosphorus.
Microbiological analyses described later were processed on-board
the R/V Roger Simons. If analysis was not performed immediately, samples
were frigerated at 4°C until analysis could be performed.
Aesthetics. Reports of any unusual visual conditions that existed at
any station were made. Conditions such as floating algae, detritus,
dead fish, oil, unusual water color, or other abnormal conditions were
recorded in the field observations.
Air Temperature was determined by use of a dial scale bimetallic helix
thermometer such as Weston Model 4200. The thermometer was allowed to
stabilize in the shade in an open area of the deck prior to recording
the temperature to the nearest 0.5°C.
Wind Speed and Direction Readings from a permanently mounted Danforth
Marine type Wind Direction and Speed Indicator were taken and recorded
while the vessel was stopped to the nearest 1° (to the right of true
north). Wind direction is accurate to _+ 10°. The reading of speed
was estimated to the nearest nautical mile per hour and stored as
14
-------
TABLE 3A
PARAMETERS MEASURED BY GLNPO
in 1976-1977
Parameter
Air Temperature
Wind Speed
Wind Direction
Secchi Depth
'•lave Height
Water Temperature
Optical Transmittance
Turbidity
Specific Conductance
pH
Total Alkalinity
Suspended Solids
"'"ota1 .Ammonia Nitrogen
Total Kjeldahl Nitrogen
Total f^itrate + 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
Selected
All1
All"1
All1
All1
Selected
Selected
Selected
Selected
Selected
All'
Sed-77
Selected
Selected
Selected
Selected
Sel ected
Selected
Al 1 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
appl icahle
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)
ZoBel 1 Sampl er
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 CuMtainer, 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
concentrated sulfuric acid added as preservative
concentrated nitric acid added as preservative
Lugols
}- ]
= 5
ml/I
ml/I
ml/1
Nutrients 610, 630, 665, 666, 671 £ 955 not run on metal cruises
15
-------
TABLE 38
SELECTED CRUISE PARAMETERS MEASURED BY GLNPO
in 1976-1977
=w=
3?
to
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CCCOCECOJQJ cotocc: roro
S_S_S_-t->S_J_S_-i>i^OO S_s_rOroCQCQ
QJCUCJ QjC(flJ33O'O'*«CUfDC:C
r" _r- .£7 c~ j^ _r" ^i ro ro ro ro i_ S- -^ -E re ro C C7
+-> -i-> j_>4_>-t_>+J+-) S 2^ OCJ r~ -C 4-* -(-> *'— f|~ OJ CU
33333331— r— •"-•!- 33~O-C:CUCJ
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Suspended Solids
Total Kjeldahl Nitrogen
Total Cyanide
Metals*
Total Chloride
Total Sulfate
Total Fluoride
Total Arsenic*
Fecal Coliform
Total Plate Count
Chlorophyll "a" fluor.
Pheophytin "a" fluor.
Total Phenolics
Primary Productivity
*Sampled on the 1977 metal cruises.
16
-------
miles per hour. The reading of direction from v/hich the wind was blowing
(wind direction) was estimated to the nearest 10° (to the right of true
north).
Wave Height. Average Wave height (valley to crest distance) was estimated
at each station by the senior crew member on the bridge. Wave heights
were recorded to the nearest 0.5 ft. Wave direction was not recorded
separately since it almost always coincided with wind direction.
Turbidity. Turbidity was measured with a Hach model 2100 Turbidimeter
within two hours of sample collection. Calibration standards were obtained
from the instrument manufacturer prior to the sampling season in 1976
and found identical within the readability of the instrument to a set
that had likewise been obtained in early 1075. The turbidimeter was
calibrated before analysis of each set of samples using a standard within
the anticipated range of turbidity. Some turbidity samples were heated
to 25°C to avoid condensation on the sample cuvet. Readings on the 0-1
range were recorded to the nearest 0.1 unit and readings from 1 to 40 range
were recorded to the nearest unit.
Secchi Disc Depth was estimated at each station on all cruises by use of a
standard 30 cm, all-white, Secchi disc. Secchi disc depths were recorded to
the nearest 0.5 meters.
pH. pH analyses were made by electrornetric measurement within 15 minutes
of sample collection. pH meters were standardized against two buffers,
pH 7.0 and 9.0(each prepared from commercial concentrates), to bracket
the pH of lake water. In 1976, the readings were recorded to the nearest
0.1 pH unit from a Sargent Welch model PBX pH meter. Readings from a
bimetallic dial thermometer were used to set the pH meter to compensate
for temperature effects. In 1977, readings were recorded to the nearest
0.01 pH unit from an Orion model 701 pH meter equipped with an automatic
temperature compensation probe. A combination glass membrane with a
silver/silver chloride internal electrode elements was used both years.
Temperature was determined by use of a dial scale bimetallic helix thermometer
such as Weston Model 4200. The thermometer shaft was immersed in the
full Niskin bottle or in the 1000 ml plastic sample bottle for phytoplankton.
Readings were estimated to the nearest 0.25°C within one minute of sampling.
Prior to use each day the thermometer was checked at one temperature,
and adjusted if necessary to comply with a mercury thermometer readable
to 0.1°C (ASTM No. 90 C).
Temperature and Light Transmission Profiles. Vertical profiles were
determined at each station from surface to bottom with a Martek Flodel
EBT/XMS electronic bathythermograph/transmissometer with a 1 meter
folded light path. The Martek constant speed electric winch with 1000
^eet of cable had an extension and retraction rate of approximately 10
meters/minute. Profiles were recorded on a Hewlett Packard XYY1 plotter
model 7044A. The temperature-depth profile was recorded both on descent
and ascent of the sensors. Because experience showed that the transmission
depth profile was independent of speed or direction of travel of the
17
-------
Raw Water From
B-l Niskin bottle
All chemistry depth
samples filtered through
a 53u net for integrated
rotifer sample
Polyethylene cuhitainer
one gal Ion or two and
one half gallon
CO
•125 ml polyethylene bottle with 0.125 ml con
(for total phosphorus and total kjeldahl nitrogen)
•125 ml polyethylene bottle with 0.65 ml con HN03
(for metals)
• 500 ml or 960 ml polyethylene with 10 rnl/1 Lugols solution
(for phytoplankton and water temperature)
,3 X 300 ml BOD bottles (1 dark)
(for primary productivity)
.300 ml BOD bottle
(dissolved oxygen)
,250 ml polyethylene bottle with 2.5 ml 1 N NaOH
(for phenol and cyanide)
»125 ml polyethylene bottle
(for chloride and sulfate)
-^ 500 ml (specific conductance and turbidity)
-> 100 ml (total alkalinity)
-> 100 ml fpH)
-^ 20 ml (ammonia and nitrate plus nitrite)
Filter
Mi "Moore HAWP
400 ml
Filtrate 20 ml (dissolved reactive silica and dissolved orthophosphate)
125 ml polyethylene bottle with
125 ml con HgStty
(total dissolved phosphorus)
Filter discard
Gel man glass fiber
type AE 500 ml
Filtrate discard
Filter-store in 10 ml of 90% acetone (chlorophyll "a")
Figure 2
Flow chart illustrating sample processing on EPA monitoring vessel.
-------
sensors (within the capability of the winch), this profile was sometimes
made in only one direction. The relatively long time constant of the
temperature sensor precluded the use of the temperature profile for
accurate temperature records at depths at which the temperature gradient
was large. Discrete readings of temperature, after sensor stabilization,
were made at selected depths to better define the true temperature profile.
Dissolved Oxygen. Dissolved oxygen was measured on water samples from
selected stations on some cruises. Analyses were made by the azide
modification of the Winkler test(EPA, 1974), or by a YSI-5720 self-
stirring BOD bottle probe which was calibrated daily against the modified
Winkler test. The dissolved oxygen analyses were made as soon as possible
after the samples were collected but in no case more than 30 minutes
after collection. Dissolved oxygen analyses were performed immediately
after sample collection when the probe was used. The dissolved oxygen
sample aliquot was obtained by inserting an eight to ten inch length of
flexible plastic tubing connected to the Niskin bottle outlet plug to
the bottom of a 300 ml glass BOD bottle. Flow was regulated by the outlet
plug so as to minimize turbulence and admixture of the sample with air.
Thiosulfate titrant normality was 0.0375, with a sample volume of 300
ml, so that the ml of titrant was equal to the mg/1 dissolved oxygen.
Dissolved Orthophosphate. Samples were analyzed for orthophosphate
using a Technicon Autoanalyzer system II and Technicon's industrial
method 155-71W(Murphy and Riley, 1962). This is the single reagent
ascorbic acid reduction method in which a phosphomolybdenum blue complex
is measured photometrically at 880 mu. The procedure was modified to
eliminate the dilution water with a corresponding sample water increase.
Levor IV, which was originally added to the dilution water, was added to
the single reagent(2.5 ml/I). Analyses were performed on the filtered
sample within two hours of sample collection.
Total Phosphorus and Total Dissolved Phosphorus. Samples were preserved
with 1 ml/1 concentrated sulfuric acid and stored in 125 ml plastic
bottles for up to 90 days before analysis. Conversion of the various
forms of phosphorus to orthophosphate was by an adaption of the acid per-
sulfate digestion method (Gales et. aJL ,1966). Screw cap tubes containing
sample and digestion solution were heated in a forced air oven for 1/2
hour at 150°C. After cooling, the resulting orthophosphate was determined
by the Technicon Autoanalyzer system II and Technicons industrial method
155-71W (Murphy and Riley, 1962).
Dissolved (Reactive) Silica. A Technicon autoanalyzer system II was
used with Technicon s industrial method No. 186-72W/Tentative (Technicon,
1973). This method is based on the chemical reduction of a silico-molybdate
in acid solution to "molybdenum blue" by ascorbic acid. Oxalic acid is
added to eliminate interference from phosphorus. Analyses were performed
on the filtered sample within two hours of sampling using a working
concentration range of 0-5 mg/1 as Si02«
Specific Conductance. Specific conductance was determined within two
hours of sampling using a Barnstead model PM70CB conductivity bridge and
a conductivity cell (YSI 3401 or YSI 3403, K=1.0). An immersion heater(such
as is used for heating a cup of water for instant coffee), connected to
19
-------
a proportional electronic temperature controller with thermister sensor
was used to heat the sample in a 250 ml. polypropylene beaker to 25.0°C.
The temperature was monitored with a mercury thermometer(ASTM 90C) with
0.1°C divisions. Rapid stirring was accomplished with an immersion glass
paddle attached to a small electric motor. When the specific conductivity
of a sample differed by more than (10% + 1 umho/cm) from the previous
sample, a fresh aliquot was taken for the determination so as to minimize
carry over from sample to sample. The apparatus was standardized daily
against 0.15 gram per liter KC1 solution according to the equation of
Lind et al_ (1959).
Total Alkalinity as CaCO> Total alkalinity was determined within two
hours of sampling by titration of a 100 ml aliquot to pH 4.5 with 0.02 N
H2S04- The pH controller/meter(Cole Parmer model 5997 with combination
electrode) was standardized daily with pH buffers 4.0 and 7.0 (each
prepared from Fisher Scientific concentrates). The acid was standardized
against 20 ml(diluted to 100 ml) of 1.0600 gram/liter NaeCOa (dried 3 hrs
@ 180°C in a forced air oven).
Chloride. A Technicon autoanalyzer system II was used with Technicon's
industrial method No. 99-70W(Zall et al_, 1956; O'Brien, 1962) with dilu-
ent water and sample tubes changed to produce a working range of 0 to 20
mg/1. In this method chloride ion displaces mercury from mercuric thio-
cyanate forming un-ionized soluble mercuric chloride. The released
thiocyanate reacts with ferric ion to form intensely colored ferric
thiocyanate which is determined photometrically. Raw water samples,
stored non-refrigerated in 125 ml or 250 ml polyethylene bottles with
plastic closures were analyzed within 90 days of sample collection.
Seven standards with no more than 4 mg/1 spread between adjacent con-
centrations were run with each group of samples. A least squares re-
gression technique was used to define the three constants of a quadratic
equation used for reduction of chart readings to concentrations(Alder
and Roessler, 1962).
Sulfate. Samples were analyzed for sulfate with a Technicon auto-
analyzer using Technicon's industrial method 118-71W (Lazrus j^t a]_, 1965)
with 1 ml/min sample and diluent pump tubes to give a 0-30 mg/1 range.
In this procedure the sample is first passed through a cation-exchange
column to remove interfering cations. It is then mixed with an equimolar
solution of BaCl2 and methyl thymol blue (MTB). Sulfate reacts with a
Ba reducing the amount of Ba available to react with MTB. The free MTB
is then measured photometically. Raw water samples, stored non-refrigerated
in 125 ml or 250 ml polyethylene bottles with plastic closures were
anlayzed within 90 days of sample collection. Seven standards with 5
mg/1 spread between adjacent concentrations were run with each group of
samples. A least squares regression technique was used to define the
four constants of a cubic equation used for reduction of chart readings
to concentration (Alder and Roessler, 1962).
Total Nitrate & Nitrite Nitrogen. A Technicon autoanalyzer was used
with Technicons industrial method No. 158-71W (Armstrong et_ a]_, 1967;
Grasshoff, 1969; FWPCA, 1969). In this procedure nitrate is reduced to
nitrite in a copper cadmium column, which is then reacted with sulfamila-
mide and N-1-napthylethylenediamine dihydrochloride to form a reddish
20
-------
purple azo dye. Nitrate & nitrite analyses were performed within 2
hours of collection.
Total Kjeldahl Nitrogen. Total Kjeldahl nitrogen samples were preserved
for no longer than 90 days by the addition of 2 ml concentrated h^SC^
per liter and refrigeration at 4°C. Preservative was added to samples
within 30 minutes of sample collection. Analyses were made by an "ultra-
micro semi automated" method (Jirka et^ a]_, 1976), in which a 10 ml sample
is digested with a solution of K?S04, H?S04, and HgO in a thermostated
370°C block digestor. After cooling and dilution with water, the sample
neutralization and ammonia determination (Berthelot Reaction) are accomp-
lished on a Technicon Autoanalyzer system II.
Total Ammonia Nitrogen. Total Ammonia nitrogen analyses were performed
with a Technicon Autoanalyzer system II using a modification of Technicon's
industrial method 154-71W/Tentative (Van Slyke and Hi 11 en, 1933). The
pump tubes rates were as follows: sample 0.80 ml/min, complexing agent
0.42 ml/min, alkaline phenol 0.23 ml/min, hypochlorite 0.16 ml/min,
nitroprusside 0.23 ml/min, and flow cell 1.00 ml/min. The ammonia deter-
minations were performed onboard as soon as possible but always within
eight hours of sample collection. Samples were maintained at 4°C until
analyzed.
Phytoplankton
Phytoplankton sample were collected at all depths at all stations in
both years of the study. Unfortunately, due to lack of resources, many
of the samples collected in 1976 were not analyzed and the majority
of those that were, were not identified beyond major taxonomic categories
(total blue greens, total greens, total flagellates, total pennate diatoms,
total centric diatoms). In 1977 samples from all depths at all stations
were analyzed to these same taxonomic categories. In addition, samples
from the 5 meter depth were identified to genus and, where possible, species.
Phytoplankton samples were collected with a Niskin-type sampler, 960 mis
of sample were withdrawn and preserved with 5 mis of Lugols solution
and stored in a cool dark place to await analysis.
The sample was vigorously shaken and 10 ml subsamples were removed and
placed in settling chambers. This was allowed to settle for approximately
24 hours in a vibration free area prior to counting and identification
with the inverted microscope. Twenty fields were counted and identified
at 400X magnification.
Diatoms, flagellates, and unicellular greens and blue greens are reported
as cells/ml. Colonial and filamentus greens and blue greens are reported
as colonies/ml and filaments/ml.
All zooplankton samples were narcotized with club soda and preserved
with 5 percent formalin. The samples were analysed by the Sedwick-Rafter
Method (A.P.H.A. 1971).
The zooplankton data is not included in this report but is available
from the Great Lakes National Program Office, 536 South Clark Street,
Chicago, Illinois 60605.
21
-------
Chlorophyll "a" and Pheophytin. Samples for chlorophyll (100 ml to 500
ml) were taken from the PEC and filtered at 7 psi vacuum along with 1 to
2 ml of MgCOs suspension (10 gm/1) usually within 30 minutes of sample
collection. In some instances filtration was delayed for as long as 2 hours.
The filters (Gelman type AE 47mm glass fiber) were retained in a capped
glass tube containing 10 ml of 90% spectro-grade acetone at -10°C in the
dark for up to 30 days prior to completion of the anlaysis. The tubes
were placed in an ultrasonic bath for 20 minutes and then allowed to
steep for 24 hours prior to fluorometric analysis using an Aminco dual
monochromator spectrofluorometer (Strickland and Parsons 1972).
Primary Productivity (Carbon 14 Method). Primary productivity was measured
at the 5-meter depth sample from all stations and from each sampled
depth at selected stations. The samples were collected in an opaque
Niskin bottle and transferred to one opaque and two transparent 300 ml
BOD bottles. Each bottle was innoculated with 2 microcuries NaH 003.
The samples were incubated in an on-board incubator. The incubator
consisted of a container of circulating lake water to maintain the
temperature at that of the lake's surface and was illuminated with
fluorescent light. The light intensity in the incubator was approxi-
mately 120u Ein/m2/S which is roughly equivalent to the light intensity
at 15m for an offshore station in Lake Michigan at noon on a clear
June day as measured by a lambda quantum light meter by the GLRD of the
University of Michigan. This light intensity is not high enough to
saturate photosynthesis (Strickland and Parsons 1972). After four
hours the productivity samples were immediately filtered through a 0.45
urn membrane filter (Mi Hi pore AAWP 04700), using a vacuum of 6 to 8
inches mercury. The damp filters were immediately transferred to counting
vials containing 20 ml of FilterSolv (Beckman). The vials were then
refrigerated at 4°C in the dark for 24 hours prior to liquid scintillation
counting. Radioactivity was counted on a Beckman model LS333 scintillation
counter with quenching corrected by external standards and channels
ratio techniques. The difference between the average of the transparent
bottles and the dark bottle, along with the values obtained for pH,
temperature, and total alkalinity, were used to calculate the primary
productivity in mgC/m^/hr.
Aerobic Heterotrophs. Aerobic heterotrophic bacterial densities were
determined at several depths at all stations on all cruises by the membrane
filtration technique, using Bacto Plate Count agar with aerobic incubation
at 20°C for 48 hours (APHA, 1971). Counts were made with the aid of a
10-power stereomicroscope. Counts were made in accordance with Standard
Methods, (APHA,1975) except that total plate count agar plates, presolidi-
fied in petri dishes, type 50 x 15 mm, were used in place of pour plates.
Fecal Coliforms. Fecal coliform densities were determined at selected
stations using the membrane filtration method with M-fc broth base incubated
at 44.5°C for 24 hours. Colony counts were made with the aid of a 10-power
stereomicroscope and were recorded as organisms per 100 ml of water (APHA,
1975).
22
-------
Metals Total (Aluminum, Barium, Beryllium, Boron, Cadmium, Calcium,
Chromium, Cobalt, Copper, Iron, Lead, Magnesium, Manganese, Molybdenum,
Nickel, Potassium, Silver, Sodium, Tin, Titanium, Vanadium, Zinc) were
measured on samples from all depths at all stations on the first four
cruises and the south-north cruise (Table 1) in 1976. During 1977, metal
samples were collected from all parts of the lake using 21 nearshore
transects and 20 selected open lake stations. Each nearshore transect
was sampled at the 9m, 18m, 36m, and 54m bottom depth contours. Sampling
depth was 5m at all locations. A teflon Niskin bottle was used, and no
metallic implements were used in collecting the samples. These analyses
were done by Inductively Coupled Argon Plasma Emission Spectroscopy (ICAP).
The samples were preserved immediately upon collection with 5 ml/1
nitric acid. Samples were analyzed within 90 days of collection.
In 1977, samples were concentrated 10 times by evaporation before analysis
in order to increase the sensitivity of the analyses. This procedure resulted
in increased concentration of alkaline earths which acted as an interference
in the measurement of the heavy metals. This factor limited the improvement
in level of detectability achievable by concentration. All analyses were made
on unfiltered samples.
Total Arsenic was determined by flameless atomic absorption spectrophotometry
using a Perkin Elmer Model 503 atomic absorption spectrophotometer equipped
with an HGA 2100 Graphite Furnace (EPA, 1974).
Total Fluoride was determined by the specific ion electrode method. The
procedure was automated using a Technicon ISE (ion selective electrode)
module (temperature controlled) with automated addition of buffer, chelating
agent and sodium chloride. One liter of aqueous reagent for one to one
mixing with sample was prepared with 57 ml. of glacial acetic acid, 59 gm.
of sodium chloride, 2 gm. of 1 , 2 cyclohexylene dinitrilo tetraacetic acid
and enough sodium hydroxide to make the pH of the reagent read between
5 and 5.5.
Cyanide. Cyanide was measured at selected stations on the first two
nearshore cruises in 1977. Cyanide samples were preserved with 2 ml of
ION sodium hydroxide per liter within 10 minutes of sample collection,
and stored at 4°C. Samples were analyzed within 48 hours of collection by
the Technicon Industrial Method 315-74W.
Phenol. Phenol was measured at selected stations during the first near-
shore cruises of 1977. Analyses were done by the 4-AAP method with
distillation (EPA, 1974). Phenol samples were preserved with 1 g/1
copper sulfate and acidification to a pH of less than 4.0 with phosphoric
acid and refrigerated at 4°C. Phenol analysis was within 24 hours of sample
collection.
23
-------
Methods Used By GIRD
Vessel
Figure 3 shows the sample processing on board the Univeristy of Michigan's
vessel Laurentian.
Station Selection
Stations for study in northern Lake Michigan were selected to address
several questions related to physical, chemical, and biological conditions
in the open lake, inshore-offshore differences, and influences of hydrologic
exchange with Lake Huron through the Straits of Mackinac. Four east-west
transects were selected so that distances between were approximately equal
and so the transects could be run between natural physiographic features,
either shoreline points or islands. A rather dense network of stations was
established in the area west of the Straits of Mackinac to define the inter-
action of Lakes Michigan and Huron.
A line of stations running south from Reaver Island was included to
represent that area of the Lake. One master station was selected on each
of the east-west transects. The purpose of including master stations was
to investigate the vertical structure in greater detail at a limited number
of stations than could be accomodated within the time available for sampling
at all stations. It would not have been possible to sample and analyze
samples at every station, if samples had been collected at this frequency at
every station.
Water samples were taken with 8-liter Mi skin bottles at predetermined
depths of 2 and 5 m or at 5, 10 and 20 m intervals to the bottom; deeper
depths were adjusted so that 17 was the maximum number of Niskin bottles
used per station. Specific depths are listed in Table 4 . Water trans-
parency was measured with a 30-cm white Secchi disc. Temperature was
measured with a mechanical bathythermograph, and in addition, surface water
temperature was measured with a bucket and a 0.1°C division mercury thermo-
meter.
All methods used on the northern Lake Michgan cruises are described
in a manual of field and laboratory procedures (Davis and Simmons, 1979).
Samples for soluble chemical analyses were filtered through 47-mm HA
Millipore filters that were previously soaked and rinsed at least 3 times
with distilled-deionized water. These samples were stored at 4°C until
chemical analyses were completed in Nalge conventional polyethlene bottles
that were rinsed at least once with excess sample before filling.
A Cornini pH meter, Model 110 equipped with a digital expanded scale
and an automatic temperature compensator, was used on shipboard to measure
pH immediately after the samples were taken.
Specific conductance was measured on shipboard with a Leeds and Northrup
Model 4866-60 conductivity bridge, corrected to 25°C.
Subsurface light penetration was measured using a Licor model LI-192S
underwater quantum sensor coupled with a Licor model LI-185 quantum meter.
These measurements were not conducted at every station because of the time
involved and the presumed predictability and constancy of the attenuation
characteristics of Lake Michigan water.
24
-------
Raw Water from
8-1 Mis kin
FILTER
ro
ui
UNFILTERED
HA Mlllipore
250 ml
HA Millipore
600 ml
Filtrate-Discard
Filter-store in amber vial containing 8 ml 90% acetone.
Freeze for chlorophyll 60 ml. unfrozen for
analyses. |chemical analyses
Filtrate
60 ml, freeze for chemical
analyses
Filter-store in flip-top vial for
particulate silica
Filtrate-Discard
Filter-store in amber vial for participate carbon and
nitrogen analyses
ze for
1 phos-
3on
Tei
PH
Sp.
AH
ml
iperature
:cific conductance
alinity
50-120
Phyto
Add f
(4%
ml
ilankton
utaral dehyde
hy volume)
2200
C-V
3 o»
ml 60 m
Fre
k -6 L & 2 D tot
P
FIG. 3. Flow chart illustrating sample processing for study of northern Lake Michigan.
-------
TABLE 4
NORTHERN LAKE MICHIGAN
Station # Sampling Depths No. of Samples
01 2, 5 2
02 5, 10, t, 1 m from bottom 4
04 5, 10, t, 50, 100, 1 m from bottom 6
06 5, 10, 20, 30, 40, 50, 70, 90, 110, 130, 150, 160
1 m from bottom 13
08 5, 10, t, 50, 100, 1 m from bottom (replicate station) 6
10 5, 10, t, 50, 1 m from bottom 5
11 2, 5 2
Transect Total 38
12 2, 5 2
13 5, 10, t, 50, 1 m from bottom 5
15 5, 10, t, 50, 100, 1 m from bottom 6
17 5, 10, 20, 30, 40, 50, 70, 90, 110, 130, 150, 170, 190
210, 230, 240, 1 m from bottom 17
19 5, 10, t, 50, 100, 1 m from bottom (replicate station) 6
20 5, 10, t, 50, 100, 1 m from bottom 6
21 2, 5 2
Transect Total 44
22 2,5 2
23 5, 10, t, 50, 1 m from bottom 5
25 5, 10, 20, 30, 40, 50, 70, 90, 110, 130, 150, 170, 180
1 m from bottom 14
27 5, 10, t, 50, 100, 1 m from bottom (replicate station) 6
29 5, 10, t, 50, 100, and/or 1 m from bottom 6
30 5, 10, t, 50, 100, 1 m from bottom 6
31 2, 5 2
Transect Total 41
32 2, 5 2
34 5, 10, t, 50, 100, 1 m from bottom (replicate station) 6
36 5, 10, 20, 30, 40, 50, 70, 80, and 1 m from bottom 9
38 5, 10, t, 1 m from bottom 4
39 5, 10, t, 50, 100, 1 m from bottom 6
40 2, 5 2
Transect Total 27
-------
(con't) TABLE 4
NORTHERN LAKE MICHIGAN
Station #
41
42
43
44
45
46
47
48
49
50
51
52
53
54
55
56
57
58
59
60
61
62
63
64
65
Sampling Depths
5, 10
5, 10, 20
5, 10, 15
5, 10, 20, 30
2, 5
5, 10, 20
5, 10, 20, 30
5, 10, 20
5, 10, 20
2, 5
2, 5
5, 10, 15
5, 10, 20
5, 10, 20
5, 10, 20, 30
2, 5
2, 5
5, 10, 20
5, 10, 20, 30
5, 10, 20
2, 5
2, 5
5, 10, 20
5, 10, 20
2, 5
No. of Samples
2
3
3
4
2
3
4
3
3
2
2
3
3
3
4
2
2
3
4
3
2
2
3
3
2
Straits Area Total
70
"t" denotes thermocline sample which was replaced with a 20 m sample
during homotherraous conditions.
27
-------
Samples for primary production were obtained at 5m at all stations.
Water samples (265 ml) were taken from the Niskin sampling bottles in
glass-stoppered Pyrex bottles, injected with a known quantity of KC
as sodium bicarbonate (ca 1.0 y Ci) and incubated in a shipboard incubator.
Surface lake water was pumped through the incubator to maintain temperature
and fluorescent lights were used as the light source. The light in the
incubator was approximately 120u Ein/mz/S. Two lights and one dark
bottle were incubated for 3 to 4 hours after which the entire contents
were filtered onto 47-mm HA Mi Hi pore filters, rinsed with distilled water,
and counted on a Nuclear Chicago liquid scintillation counter.
Alkalinity was determined from pH measurement on 20 ml samples which
....._ added to 4 ml of 0.01N HC1. Measuremen-
from 5m where ' C productivity was measured.
were added to 4 ml of 0.01N HC1. Measurements were made only on samples
T
Nutrient analysis was performed shortly after sample collecting using
a Technicon AutoAnalyzer II equipped to measure five nutrients—nitrate
plus nitrite nitrogen, ammonia nitrogen, soluble reactive silica, chloride,
and soluble reactive phosphates. Samples for total phosphorus were frozen
and returned to Ann Arbor for analyses. Methods used for these chemical
analyses are described by Davis and Simmons (1979) and specific information
is presented in the following paragraphs.
Nitrate was measured by reducing it to nitrite with a copper-cadmium
reduction column. The nitrite produced and the nitrite initially present
in the sample were then determined by a diazotization-coupling reaction
using sulfanilamide and N-1-naphthyl-ethylene diamine. The resulting
colored complex was measured at 550 nm. Nitrite was not analyzed separately,
as quantitatively insignificant values would be expected in non-polluted
oxygenated waters.
Ammonia and ammonium ions were measured by conversion of ammonium ions
to ammonia in a basic medium. Ammonia reacts with hypochloride and phenol to
produce an indolphenol blue color which was measured at 630 nm. The reaction
was catalyzed by nitro-prusside and EDTA v/as added to prevent precipitation of
alkali earth metals.
Silica was determined by reacting it with acidified molybdate to form
a silicomolybdate complex that is reduced by ascorbic acid to an intense
heteropoly blue which was measured at 660 nm. Oxalic acid was added to
destroy any phosphomolybdate.
Soluble reactive phosphorus was measured by formation of antimony-
phosphomolybdate complex in acid medium which was reduced by ascorbic acid
and measured at 880 nm.
Chloride was determined from its reaction with mercuric thiocyanate
that forms un-ionized but soluble mercuric chloride. The related thiocyanate
in the presence of a ferric ion reacts to form a red complex, Fe (SCNJ3.
The resulting color was measured at 480 nm.
Chemical analyses for total phosphorus and total soluble phosphorus
were performed in the laboratory on thawed samples. Samples were concen-
trated by evaporation and then digested with acid potassium persulfate
28
-------
for one and a half hours in an oven at 110°C, as modified from Menzel and
Corwin (1965). The samples were then analyzed for soluble reactive phosphorus
on an AutoAnalyzer I. The blue color produced was measured at 630 nm.
Samples for total particulate silica were collected on 47-nm HA
Millipore filters and placed in plastic flip-top vials. In the laboratory
participate silica was decomposed with HN03HF reagent. The excess hydro-
fluoric acid was complexed with boric acid^ Silica concentrations in the
decomposed samples were determined by atomic absorption spectrometry using
a nitrous oxid-acetylene flame (David and Simmons 1979).
Samples for chlorophyll "a" (250 nil) were filtered onto 47-nm HA
Millipore filters that v/ere then extracted in 90 percent acetone buffered
with magnesium carbonate. Samples v/ere stored in amber vials in the dark
at 0°C for a minimum of 12 hours. On the earlier cruises, some chlorophyll
determinations were made on ship. Otherwise, they v/ere done in our laboratory
in Ann Arbor. Samples were centrifuged, and then 5 ml were transferred to
sample cuvettes and read in a Turner Model 111 fluorometer. Samples were
subsequently acidified with two drops of 50 percent V/V HC1 and read in the
flurometer for phaeopigment determination (Strickland and Parsons 1968). All
results were corrected for phaeophytin. The phaeophytin fraction generally
represented a small proportion of the chlorophyll "a", so possible errors
resulting from the addition of excess amounts of hydrochloric acid (Riemann
1978) would probably be small.
Methods Used by MDNR
Details of methods can be found in Limnological Survey of Nearshore Waters
of Lake Michigan 1976. EPA Grant R005146-01 David Kenage, William Creal,
and Robert Bash In Press USEPA Grosse Ille, Michigan 48138.
Quality Assurance Used By GLNPO
Data quality assurance, evalation, 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
sample (one near the top of the analytical working range and one near the
bottom) and a reagent blank wer 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 for the true values was expresses as A+Bx where x is the
true value and A and B are constants determined from a representative
sampling. Exceeding this allowable deviation resulted in the deletion
of the data fro 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 analyses. The
differences between the four subsamples 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 duplication were
selected at random.
29
-------
Successive duplicate ZoBell samples for total aerobic heterotrophs were col-
lected 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 Rosolic acid used in m-FC media), date the media container was opened, and
pH checked. Col i form 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 incu-
bators, autoclave, and water bath were recorded. The pH meter and balance
were checked for accuracy on a regular basis.
Quality Assurance consisted of 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 5). These check standards were analytical
checks as apposed to sampling checks, i.e. they were not carried through the
sampling and preservation procedures,
Reagent water was prepared onboard with a Mi Hi pore Milli-Q reagent grade
water system. The system contained a carbon cartridge, demineralizer cartridges,
a 0.? u final membrane filter, and a 10 megohm-cm indicator light. Feed water
to the system was obtained from the onboard potable water supply and was de-
ionized with high capacity hose-nipple cartridges prior to feeding the Mill-Q
system.
Performance evaluation samples were provided as unknowns by EPA Region V
nua"!ity Assurance Office (Table 6).
Duplicate samples were obtained by lowering a second Niskin bottle to the
same depth from which the original sample was taken. Each Niskin bottle (the
original and the duplicate) was used to fill two sample bottles for each parameter,
One duplicate/split sampling was performed with each 10 to 20 regular samples
(Table 7).
Volume Weighting Calculation. The two-layer volume weighted average was
determined by the equation TLVWA= (MI V] + ^2 '^/(V^ +
MI= mean of all samples in the upper twenty meters.
M£= mean of all 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
Vo= volume of water below twenty meters
South Basin 1795.1 km3
North Basin 2003.6 km3
30
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TABLE 5
GLNPO Shipboard Check Standard & Reagent Blank* Summary
1976
Parameter
Total Alkalinity mg/1
Total Alkalinity mg/1
Specific Conductivity umho/cm
Specific Conductivity umho/cm
Specific Conductivity umho/cm
Ammonia N mg/1
Ammonia N mg/1
Ammonia N mg/1
Ortho Phosphate P mg/1
Ortho Phosphate P mg/1
Silica Si 02 mg/1
Silica Si 02 mg/1
Nitrate + Nitrite N mg/1
Nitrate + Nitrite N mg/1
Concentration
100
80
203.3
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/1, Ortho Phosphate - P. 0.002 mg/1, Si02 0.03 mg/1,
N03 + N02-N 0.01 mg/1.
1977
Turbidity JTU
pH SU.
pM SU.
pH SU.
reagent blank
9.18
7.01
reagent blank
137
117
124
122
0.184
9.06
6.99
5.41
0.085
0.096
0.041
0.549
31
-------
(contd.) TABLE 5
Shipboard Check Standard & Reagent Blank Summary
1977
Parameter
Total Alkalinity mg/1
Total Alkalinity mg/1
Total Alkalinity mg/1
Specific Conductivity umho/cm
Specific Conductivity uhmo/cm
Specific Conductivity uhmo/cm
Ammonia-N mg/1
Ammonia-N mg/1
Ammonia-N nig/1
Ortho Phosphate-P mg/1
Ortho Phosphate-P mg/1
Ortho Phosphate-P mg/1
Silica Si 02 mg/1
Silica SiO? mg/1
Silica Si 02 mg/1
Nitrate + Nitrite-N mg/1
Nitrate + Nitrite-N mg/1
Nitrate + Nitrite-N mg/1
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
Deviation
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
32
-------
TABLE 6
GLNPO
DIFFERENCES BETWEEN SPLIT SAMPLE ANALYSES
SOUTHERN LAKE MICHIGAN
Parameter
ma/i*
Number of
Splits
Mean Absolute
Value of Differences
Standard Deviation
Of Differences
1976
Turbidity (HTU)
Specific Conductance
(umhos/cm)
pH (SU)
Total Alkalinity
Suspended Solids
Total Ammonia (ug/1)
Total Nitrate
+ Nitrite
Total Phosphorus
(ug/1)
Calcium
Magnesium
Potassium
Sodium
Total Chloride
Total Sulfate
Total Fluoride
• 214
210
218
208
144
136
180
254
74
74
no
76
200
200
40
0.031
0.15
0.0096
0.29
0.038
1.323
0.0067
1.221
0.084
0. 01 8
0.0011
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
Dissolved Reactive
Silica
208
0.015
0.075
33
-------
(contd.^ TABLE 6
1977
Turbidity (HTU)
Specific Conductance
(umhos/cm)
pH (SU)
Total Alkalinity
Suspended Solids
Total Ammonia-N
Total Kjeldahl-N
Total Nitrate
+ Nitrite
Total Phosphorus
Total Chloride
Total Sulfate
Dissolved Reactive
Silica
Chlorophyll "a"
(ug/1)
Pheophytin (ug/1)
*Unless Otherwise noted.
222
224
224
224
30
202
222
214
200
206
34
224
136
134
0.019
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
0.17
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
34
-------
TABLE 7
Upper Lake Reference Group Performance
Standards Run During USEPA 1977 Cruises
Number of Analyses
Mean
Standard Deviation
True or Vali
Nitrate + Nitrite
Nitrogen mg/1
Standard #1
Standard #2
Ammonia
Nitrogen mg/1
Standard #1
Standard #2
Qrthophosphate
as P mg/1
Standard #1
Standard #2
Dissol ved
Reactive Silica
as SiO? mg/1
Standard #1
Standard #2
Standard #3
Standard #4
Standard #5
Standard #6
19 0.3232
19 0.4047
19 0.0117
19 0.0187
19 0.0031
19 0.0057
12 0.751
12 0.851
8 2.38
8 2.41
4 1.28
4 1.46
0.0067
0.0077
0.0016
0.0018
0.0006
0.0008
0.014
0.018
0.087
0.039
0.015
0.026
Accepted
0.32
0.40
0.011
0.018
0.004
0.007
0.76
0.86
2.47
2.52
1.35
1.52
35
-------
This comuputation was developed to estimate average lake concentrations.
Comparison of means and standard errors computed using TLVWA with computer
volume weighted calculations (Yiu, 1978) for the southern basin gave similar
statistic results for total phosporus and temperature. This comparison would
suggest that in the southern basin TLVWA results can be used for other para-
meters which are more uniformly distributed and that the station network and
sample depths were well chosen for characterization of lake water quality.
In the northern basin, TLVWA results are affected by the dense station network
in a relatively shallow basin of Lake Michigan near the Straits of Mackinac.
This influence is most noticeable for epilimnetic values of chloride and
conductance and can be seen by comparing figures 30 and 31; and 35 and 36
respectively.
The layering of the lake at 20 meters depth has been shown to
representative of the average depth of the epilimnetic layer for both
1076 and 1077 (Barton and Schelske 1970, Rodgers, 1980).
Twenty-Four Hour Surveillance
Three 24 hour surveys on June 9-10, August 18-19, and September 6-7,
1977 were conducted at an 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 8 contains
the results by depth for these visits. Except for the thermocline zone, the
standard errors of the mean values are very low.
The importance of the uniformity of the results within the epilimnion
and hypolimnion is the apparent insensitivity to actual time of sampling
at a station during a given twenty-four hour period. The relatively larger
standard errors of the mean concentrations in the thermocline region probably
result from the internal wave structure and mixing between the layers in this
region.
RESULTS
Temperature
Thermal stratification with a discernible epilimnion, thermocline, and
hypolimnion occurred both years. The lake warmed first in the southern
nearshore zones and exhibited a nearshore to offshore, south to north
warming pattern. Epilimnetic water temperatures averaged 3° to 4°C
warmer in 1976 than 1077 from June through September in the southern
basin (Figure 4). In the southern basin, waters warmed from the first
cruise in both years through August when the highest epilimnetic average
temperatures of 19.7°C and 16.3°C were observed in 1976 and 1977 respect-
ively. Northern basin waters followed the same warming pattern as described
earlier. Some northern basin cruise average temperatures were 1-2°C cooler
than southern basin even though the northern basin cruises usually followed
corresponding southern basin cruises by one week. (Figure 4) The northern basin
epilimnetic average temperature of 17.1°C occurred in the August 1976
cruise.
36
-------
TAfiLi: .".
Station I.. MICH 06 24-Hour Surveys 1977
(number of samples) mean + standard error of mean
Depth
M
2
5
12
20
30
40
55-64
2
5
10
17
22
27
40
00 65
""~J
2
5
10
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
(12) .65+. 04
(12) .67+.02
(12) .65+.02
(12) .66+. 02
(12) .75+.03
(12) .79+. 03
(12) .92+. 02
(12)1. 26+. 19
(12)1. 21+. 02
(12)1. 28+. 02
(12)1.32+.02
(15)l.29+.03
(12)1.25+.03
(9)1.27+.03
(12)0.77+.03
(12)0.72+.02
Water Temp
°C
(11)12.4+.!
(11)12.4+,!
(11)12.1+. 2
(11)11.8+.!
(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+.1
(12) 5.6+.1
(12)21.0+.!
(12)21. O+.O
(12)20. 9+.0
(14)20.2+. 3
(11)15. S+.4
(9) 9.4+. 7
(12) 6.1+.2
(12) 5.8+. 2
Micromhs/cn
at 25°C
(11)278+. 4
(ll)279+.3
(11)279+. 2
(11)278+. 2
(11)278+. 3
(ll)277+.2
(11)277+. 2
(11)278+.0
(12)271+. 3
(12)271+. 2
(12)271+. 2
(12)274+.4
(12)277+. 4
(ll)279+.3
(12)279+. 2
(12)279+.2
(12)268+. 3
(12)268+.!
(12)268+.!
(15)269+.4
(12)276+. 3
(9)279+. 3
(12)280+. 2
(12)280+. 2
PH
(11)8. 35+. 01
(11)8. 34+. 01
(11)8. 35+. 01
(11)8, 35+. 01
(11)8. 35+. 01
(11)8.327.01
(11)8. 15+. 01
(11)8.10+.01
(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
(9)8. 13+. 04
(12)7. 98+. 01
(12)7.97+.01
Tot
ALK
lr.K/1
(11)108+. 2
(11)108+. 2
(11)108+. 2
(11)108+. 2
(11)108+. 2
(11)108+. 2
(11)108+. 2
(ll)108+.2
(12)108+. 2
(12)108+.!
(12)108+.!
(12)109+. 3
(12)HO+.2
(11)111+.!
(12)111+.!
(12)105+.3
(12)105+.!
(12J105+.2
(15)106+. 3
(12)108+.4
(9)1 10+. 3
(12)110+. 3
(12)110+.2
lOt 3 I
NH3-N
"8/1
(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+0. 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
TKN-N N02+N0 -N
Survey//! 6/9 - '0/77
(11)0.16+.0!1 (11)0.195+002
(11)0. 16+. 005 (11)0.195+ 001
(11)0. 16+. 006 (11)0.195+. 002
(11)0. 15+. 007 (11)0.195+. 002
(11)0.15+.008 (11)0.196+. 002
(11)0.16+.007 (11)0.200+. 002
(11)0. 14+. 007 (1D0.218+.002
(11)0. 15+. 008 (11)0.226+.002
Survey#2 8/18 -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 U2)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
Survej#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)O.I2+.010 (9)0.230+. 007
(12)0. 11+. 009 (12)0. 263+. 001
(12)0.11+.009 (12)0. 263+. 001
Total P
(11)4.4+0.4
(11)4.0+0.2
(11)4.8+0.3
(11)4.1+0.3
(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+0.2
(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+0.2
(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
(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
(U)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+.05
(12)8. 26+. 02
(12)8.25+.02
Diss. Reactive
Silica niR/1
(11)0. 50+. 010
(11)0.50+.009
(11)0. 51+. 013
(11)0.54+.010
(11)0.56+.009
(11)0.63+.013
(11)0.87+.016
(11)1. 03+. 009
(12)0. 22+. 002
(12)0.22+.002
(12)0.23+.003
(12)0.23+.002
(12)0.36+.028
(11)1.26+.007
(12)1.30+.007
(12)1. 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
Hecerocropha
(11)12+ 3
(6)12+ 1
(6)16+ 6
(6)23+ 4
(7)28+ 7
(6)24+ 1
(6)18+ 3
(6)14+ 3
(8) 1+0
(11) 8+ 3
(11) 26+11
(6) 3+1
(6) 4+1
(3) 15+5
(3) 27±12
(6) 4+1
Chlorophyll a
ug/1
(11)0. 83+. 04
(11)0. 91+. 06
(11)1. 03+. 04
(11)1.1 1+.02
(11)1. 12+. 07
(11)1.37+. 16
(10)1.92+.09
(11)1. 71+. 11
(12)0. 76+. 04
(12)0. 72+. 05
(11)0. 81+. 06
(11)0.94+.06
(10)0.85+.06
(11)0.90+.08
(11)0.73+.07
Secclii
Depth
mecera
(7)6.5+0.3
(7)5.7+0.3
(7)4.2+0.2
-------
»* • -*— tram;
remperaTures By Basin
00
oo
12 -
10 -
8 -
6-
4-
2 -
20
18 -
IB -
14-
12-
10 -
8 -
6-
4_
2 -
8 -
6-
4-
2-
Two Layer Volume
Weighted Average
By Basin
f
^
g
i
X
1
I
I
I
&
^
I
X
\
i
1
§
i
i i i i
Epilimnetic Mean
Samples Within
The Upper Twenty
Meters
1
i
a
I
3
I
-------
A thermal bar was observed in the southern basin during April 19-24 in 1977.
It was evident southward from 0-15 kilometers from shore along the eastern
shoreline between transects 2 through 5, following transect 2 across the
central portion of the southern basin and northward along the western shoreline
between transects 2 and 3 up to 12 kilometers from shore (Figure 5).
In 1976, thermal stratification had begun along shore (to 2-6 kilometers
offshore), in the southern portion (north to transect 2 and 3) during
May 25-June 2, 1976. The entire southern basin had warmed 5° to 15°C
above hypolimnetic water temperatures by June 15-21, 1976. Stratification
occurred later in 1977. During the June 11-16, 1977 cruise, thermal
stratification had begun and extended to 9-15 kilometers offshore, in the
southern basin south of transect 3, and along the eastern shorelines
between transects 3 and 5. Complete stratification had occurred by the
next survey on August 20-25, 1977 (Figure 5). The autumnal cooling period
began after the August cruises in both basins in 1976 and the southern basin
in 1977. The cooling period was similar to the spring warming with the
lake cooling first in the nearshore.
Extreme upwelling events in the southern basin with water temperatures
below 10°C were not observed in 1976 or 1977. The somewhat offshore location
(1 to 3 kilometer or greater distance from shore) of the nearest monitoring
stations may have contributed to the absence of observed upwellings.
However, there were indications of upwelling events in both years.
These events were sometimes confined to a single transect during a cruise.
Upwelling temperature patterns were observed at both eastern and western
ends of a transect during the same day due to the 12 to 14 hour transit
time to cross the lake.
The most noticeable of upwelling events were observed during August
3-19, 1976 and during August 20-25, 1977. The August 1976 event appears
to have been centered on transect 6 where an observed 5°C change (19.0°-14.0°C)
in 5-meter depth temperatures occurred along the eastern coast. The
August 1977 event occurred primarily near Milwaukee Wisconsin in the
southern basin (Figure 5) with lowest observed nearshore temperature at
transect 5. The greatest change in 5-meter temperatures in this event
occurred on the western shore, transect 4, with a 5.8°C change (14.2-20.0°C)
between stations 16 to 18, and on the eastern shore, transect 6, with a
4.7°C change (18.0-13.3°C) between stations 28a and 28 (Figure 5).
Appendix, Tables Cl thru C3 gives the vertical variation of some of
the parameters sampled at the deepwater stations on 1976 and 1977 in
both basins during the main lake cruises. The water column was remarkably
uniform during isothermal conditions. After stratification was established
the epilimnetic and hypolimnetic layers were also uniform. The metalimnetic
layer exhibited the greatest varability.
Figure 6 contains reproductions of temperature stratification traces
for the three twenty-four hour surveillance cruises. During the June
24-hour survey (Figure 6), the thermocline was most frequently at 25.5
meters and averaged 24.5 meters. The shallowest thermocline depth
estimate was 20.5 meters and the deepest estimate was 26.5 meters. The
thickness of the epilimnetic layer is estimated to be approximately 22
meters with minimum thickness of 18.5 and a maximum thickness of 23.5 meters.
39
-------
figure 6
Temperature°C
5 Meter Depth
Aug. 10-19,1976
Aug. 3-10, 1976
NTON HARBOR
HAMMOND
Ht MON HARBOR
April 19-24. 1977
MUSKEGON
GRAND HAVEN
ZION
WAUMGAN
LAKE FORES
BENTON HARBOR
August 20-25, 1977
40
-------
Maximum thickness occurred at 8 and 10 p.m. Temperature measured in the
epilimnetic layer during this 24-hour period ranged from greater than 11°
to 13.4QC. The metalimnetic layer, characterized by a IOC/meter temperature
gradient, is estimated at an average thickness of 8 meters with extreme values
of 6 to 10 meters. Temperatures monitored in this layer during 24-hour period
ranged from as low as 5.8°C to as high as 12.4°C. The temperature in the hypo-
limnetic layer averaged 5.4 ^ 0.6°C during the ten sampling periods. Hypolimnetic
waters began at a mean depth of 30 meters (range 26 to 33.5 meters). Hypolimnetic
temperatures ranged from less than 7.9°C to a minimum of 4.4°C. Internal wave
action on the metalimnetic interface is evident and reflected in the variations
of thickness of each layer.
In the August survey (Figure 6) epilimnetic waters had warmed to a maximum
of 22.2°C and were almost isothermal with a minimum temperature of 21.5°C. The
thermocline's average depth occurred at 19.5 meters. The shallowest depth was
at 25.5 meters. The thickness of the epilimnion averaged about 16.5 meters
(ranging from 15.5-19.5 meters). The metalimnion averaged about 14 meters
(ranging from 11 to 16.5 meters) thick. Metalimnion temperatures ranged
from less than 22°C to greater than 5.6°C. The average temperature change
in the metalimnetic layer on each sample run was 15. 5 +_ 0.4°C. Hypolimnetic
waters began (on average) around 30.5 meters (ranging from 28.5 to 32 meters)
deep. Hypolimnetic temperatures were less than 7.4°C to a minimum of 5.0°C.
The water column had begun to cool by September (Figure 6) and showed
the deepest average thermocline location of the three 24-hour surveys at
25.5 meters. This depth, 25.5 meters, v/as also the most frequent depth
estimate from the two-hour observations. The thermocline depth ranged in
a narrow band from 23.5 to 25.5 meters.
Secchi Disc and Turbidity
Secchi disc depth measurements were greater away from the nearshore
zone. Figure 7 shows areal patterns from spring 1976 (the May 25-June 8
cruises) as well as the means for the 1976 and 1977 study periods. Water
clarity was highest in the deep offshore waters of the northern basin
and lowest near Milwaukee in 1976.
Secchi disc depth measurements declined in both basins throughout the
summer until late August in both offshore and nearshore waters in 1976.
A similar pattern was also observed in the southern basin in 1977.
Secchi disc measurements in the northern basin averaged 1 to 3 meters
greater than those in the southern basin at similar calendar periods
throughout 1976. During July 1976 nearshore station measurements were 3
meters less than open lake stations in the southern basin. This difference
was reduced to less than 0.5 meters during August and September 1976. A
similar pattern occurred in the northern basin in 1976. Nearshore Secchi
depth measurements varied less in both basins in 1976 than offshore
station readings. Southern basin nearshore Secchi depths ranged from
2.9 to 4.9 meters and northern basin values ranged from 5.6 to 6.8 meters
(Table 9).
41
-------
figure 6
Station 6
24 Hour Survey EBT Traces
X
June 10. 1977 18
31, *, bC 60
Depth tn Meters
Aug 18
M
i
i
1
i
i
•: V-,,,
t
I
•
I
1
!
1
4
',
Aug 19
12
' i "1 :
1 ::
9 Aug 18 19 1977
1
I 3
1;
'u
, 9
i
\ ;
-i. • s
Depth In Meters
DepthJih
Meter*
, S«pt«.7. 1877 |e
70 10 20 30 40 so ec
-------
Figure 7
Distribution Of Transparency - Secchi Depth
In Meters
June 2-8
GO
May 25 - June 2
BENTON HARBOR
MICHIGAN CITY
Spring 1976
MUSKEGON
GRAND HAVEN
BENTON HARBOR
MICHIGAN CITY
Annual Average 1976
• LUDINGTON
1 / /
i:—' 7.0 I \ \
^J\\
"" >S f
GRAND HAVEN
ZION
WAUKEGAN
LAKE FOREST
BENTON HARBOR
MICHIGAN CITY
Annual Average 1977
-------
TABLE 9
LAKE MICHIGAN
Transparency-Secchi Disc Depth (m)
Number of Samples Arithmatic Mean _+ Standard Error
CRUISE DATES No. OPEN LAKE No. NEARSHORE No. Combined
SOUTHERN
May 1-3
May 25-June 2
June 15-21
July 7-23
Aug 3-10
Aug 24 -Sept 2
Sept 14-20
Oct 7-8
2
23
23
23
23
23
23
4
8.
5.
7.
6.
4.
2.
3.
5.
0
5
3
8
4
5
8
8
NORTHERN
April 21-29
June 2-8
July 10-19
Aug 10-19
Oct 5-15
42
48
47
40
30
10.
10.
7.
6.
6.
8
0
5
2
5
SOUTHERN
April 19-24
June 11-16
Aug 19-25
Sept. 17-24
23
10
23
23
6.
6.
6.
4.
7
8
1
4
BASIN
+
+
+
+
+
+
+
+
2.0
0.4
0.3
0.5
0.3
0.1
0.1
0.8
BASIN
+
+
±
+
±
0.6
0.5
0.1
0.3
0.1
BASIN
+
+
+
+
0.3
0.6
0.4
0.2
1976
1
16
16
16
15
16
16
2
1976
17
16
14
16
6
1977
16
9
16
15
1.5
3.4
5.1
3.7
3.7
2.9
3.7
5.0
5.9
6.8
6.8
6.1
5.6
4.8
5.5
4.6
3.8
+ 0.2
+_ 0.4
+ 0.2
+_ 0.2
+_ 0.2
_+ 0.2
+_ 0.0
+_ 0.4
+_ 0.3
_+ 0.3
± °-3
^0.5
+ 0.3
4- 0.8
+ 0.2
+, 0.3
3
39
39
39
38
39
39
6
59
64
61
56
36
39
19
39
38
5.8 +_
4.6 _+
6.4 +_
5.5 _+
4.1 +_
2.7 +
3.7 +_
5. 5 +_
9.4 +_
9.2 +_
7.3 1
6.1 +
6.4 _+
5.9 j-
6.2 +_
5.5 +_
4.2 jf
2.5
0.3
0.3
0.4
0.2
0.1
0.1
0.5
0.5
0.4
0.1
0.2
0.1
0.3
0.5
0.3
0.2
44
-------
figure 8
1976-1977 Southern Lake Michigan
Two Layer Volume Weighted Average (V)
Turbidity (NTU) By Cruise
Epilimnetic Mean (E)
Hypolimnetic Mean (H)
2.0
en
1.0 —
0.0 —
Cruise 76-1 * 76-2
* Transect 6 Only
76-3
s
76-4
76-5
T T
tl
76-6
I
76-7
Plus or minus one standard error
76-8*
_ 2.0
_ 1.0
NuifiMr
Of Samples
In Mean
_ 0.0
77-1
77-2
77-3
77-4
-------
Southern basin turbidity in 1976 and 1977 are plotted in Figure 8.
Turbidity in 1976 ranged from 1 to 2.3 HTU in the epilimnetic waters.
Exclusive of the first and last cruises where fewer samples were taken, tur-
bidity increased until the cruise in late August 1976. In 1977, epilimnetic
turbidity levels were observed around 0.8 HTU for most of the year with
an increase to 1.2 HTU in the last cruise in September. The 1977 values
were nearly constant and similar in both epilimnetic waters and hypolimnetic
waters from the April cruise through the August cruise. There is little
evidence that stratification had any affect on turbidity in the deep waters
(Appendix Table Cl and C3).
Phosphorus
Between 1976 and 1977 large decreases were observed in total phos-
phorus in the southern basin. Reductions in the depth weighted mean
total phosphorus concentrations occurred at ninty-two percent (36 of 39)
of the southern basin stations. Using data from the six complete 1976
cruises and the four cruises in 1977 the reduction in total phosphorus
in the southern basin was from 8.0j^ .8 ug/1 in 1976 to 5.2 +_ .2 ug/1 in
1977. The five 1976 Northern basin cruises averaged 7.4 +_ 1.0 ug/1.
Epilimnetic and hypolimnetic concentrations decreased an average of 2.2
=g/l and 3.1 ug/1 respectively. The distribution of total phosphorus in
the epilimnion and hypolimnion was almost constant in 1977 while there
was a greater variation in 1976 perhaps reflecting seasonal change in the
total phosphorus concentrations (Figure 9). The total phosphorus concen-
trations in the epilimnion at the deep water stations tended to be
lower but was not statistically different from the hypolimnion in both
years and both basins. This can also be seen in the vertical distribution
in Appendix Tables C1-C3.
The decrease in total phosphorus between 1976 and 1977 in the
southern basin was also observed in the total dissolved fraction, which
decreased from a median concentration of 3 ug/1 in 1976 to below detect-
able levels (<3 ug/1) in 1977. The Mann Whitney Test (Zar, 1974) indicates
that this difference is significant at the 95% confidence level. Median
values of total dissolved phosphorus were at 3 ug/1 or less than 3 ug/1
in the epilimnion throughout 1976 in the southern basin. Median values
of total dissolved phosphorus were at 4 ug/1 or less in the hypolimnion
throughout 1976 in the southern basin. In 1977 the median value was
less than 3 ug/1 throughout the entire basin. Lower detection limits
for total dissolved phosphorus permitted real values to be reported for
the northern basin in 1976 and appear to range between 2 to 5 ug/1
through the summer.
Dissolved ortho-phosphate concentrations were frequently below the
detection limits of the methodology (2 ug/1) in both 1976 and 1977 in
the southern basin. In the northern basin Figure 10 contains three
cruise results for detection limits at (1 ug/1).
46
-------
figure 9
1976-1977 Lake Michigan
Two Layer Volume-Weighted Average (V)
Total Phosphorous P (ug/l) By Cruise
Epilimnetic Mean (E)
Hypolimnetic Mean (H)
•
10.0 _
9.0 _
8.0 _
60
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_ 8.0
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Number
Of Sample.
In Mean
Crime 76-1* 76-2 76-3 76-4 76-5 76-6 76-7 76-8* 77-1 77-2 77-3 77-4 76-1 76-2 76-3 76-4 76-5
i -. _ — Cmi+Unvn D->»:.t 1 C s>i i+k> urn Rocin 1 4 IMrtrtharn Racin
-------
figure 10
1976 Northern Lake Michigan
Two Layer Volume-Weighted Average (V)
Epilimnetic Mean (E)
Hypolimnetic Mean (H)
I
i One standard error
00
^ 3
\
0>
3
ffi
76-1 76-2 76-3 76-4 76-5
Total Dissolved Phosphorus
Number
01 Samples
In Mean
76-2 76-3 76-4
Dissolved Orthophosphate
-------
Spacial variations in the upper twenty meter distribution of total
phosphorus in 1976 and 1977 spring and summer cruises are displayed in
Figure 11. Nearshore values are elevated due to nearshore processes
and land run off. Elevated values occur near major urban centers and
large tributaries. Water exchange from Green Bay increases the phosphorus
load in northern Lake Michigan. Low total phosphorus values were found
in the Straits of Mackinac. The reduction in total phosphorus between
1976 and 1977 in the southern basin in clearly evident when comparing the
August cruises.
Si 1 i ca
In both years in all areas of the lake, dissolved reactive silica
(DRS) showed a progressive decrease in the surface water through the
stratified period. Surface values away from shore declined from winter
values ranging from 1.20 to 1.30 mg/1 which were monitored at stations
on the 40-50 meter contours near Sturgeon Bay in February 1977 to an
observed average of 0.24 + .01 mg/1 in 1977 at the deep water stations
during August (Appendix Tables Cl and C3). The average concentration in
August 1976 at the deep water stations was 0.26 + 0.01 mg/1. These represent
reductions of up to 80% of the silica concentrations found during isothermal
conditions. Mean surface DRS concentrations were at an observed minima
during August cruise both years when surface temperature were at an observed
maxima. Hypolimnetic concentrations of DRS tended to increase during the
summer. DRS concentrations appeared to decrease rapidly after water
temperature had increased above 6°C.
Figure 12 shows the vertical distribution of DRS at station 18
(depth 60 meters) for the eight cruises starting May 29, 1976 and
ending April 21, 1977 which covers a complete annual cycle. During May
1976 before stratification the vertical DRS distribution was approxi-
mately uniform. Surface concentration was 1.32 mi/I and 1.54 ing/1 was
measured near the bottom. As wanning occurred, the surface concentration
of DRS decreased until it reached 0.20 mg/1 on August 7, 1976. Hypolimnetic
DRS concentrations increased with the bottom sample reaching a maximum
of 2.09 mg/1 on August 7, 1976. DRS concentrations returned to a
homogeneous distribution during the winter period. The homogeneous
isothermal spring distribution was approximated by the first 1977 cruise
in April when DRS values of 1.14 mg/1 (surface) and 1.10 mg/1 (bottom)
were monitored. The pattern of epilimnetic DRS decrease during the stratified
period also occurred in 1977. This seasonal cycle was typical of open
lake stations where inputs of silica via upwelling, sediment resuspension
and surface run off were not important (Appendix Tables C1-C3).
DRS minima in the metalimnion layer as seen most clearly in the June
18, 1976 and August 27, 1976 vertical profiles, was typical of open lake
stations in both 1976 and 1977. The DRS depletion began first in the
nearshore areas and southern latitudes and followed the warming patterns.
3y June 1976 and 1977 the concentrations of DRS at the surface of stations
(depth 80 meters or greater) was reduced to levels found at the nearshore
49
-------
Figure 11
Upper Twenty Meter
Distribution Of Total Phosphorous In ug/l
June 2-8. 1976
May 25 -
June 2. 1976
BENTON HARBOR
MICHIGAN CITY
HAMMOND
MILWAUKEE fJ /
WAUKEGAN
LAKE FOREST AV/ 5
GRAND HAVEN
BENTON HARBOR
MICHIGAN CITY
June 11-16. 1977
August 10-19, 1976
Vt GRAND HAVEN
August 3-10, 1976
IENTON HARBOR
ICHIGAN CITY
MUSKEGON
GRAND HAVEN
BENTON HARBOR
MICHIGAN CITY
August 20-25,1977
50
-------
figure 12
Lake Michigan 18
Water Temperature Centigrade (Dashed) top scale
Dissolved Reactive Silica mg/l (Solid) bottom scale
WATER TEMPERATURE CENTIGRADE IDASHEp)
\
MAY 29, 1976 JUNE 18. 1976 JULY 9,1976 JULY 17, 1976
AUGUST 7, 1976 AUGUST 27, 1976 SEPTEMBER 17, 1976 APRIL 21, 1977
JUNE 14, 1977 AUGUST 23. 1977 SEPTEMBER 21, 1977
51
-------
stations in both basins (around .6 mg/1) (Appendix Tables C1-C3). Open
lake epilimnetic water concentrations continued to decline to below .3
mg/1 in August 1976 and 1977 while noarshore waters remained around .6
mg/1 except for the Illinois and Indiana nearshore zone which declined
below .3 mg/1 in August 1976 (Figure 13).
Figure 14 compares the cruise results for both years, presenting
the epilimnetic, hypolimnetic, and two layer volume weighted average in
the southern basin. The southern basin epilimnetic DRS seasonal patterns
in 1976 and 1977 are similar with epilimnetic cruise means of 0.50 +_ .13
mg/1 in 1976 and 0.63 + .21 mg/1 in 1977 with mean epilimnetic 1977 cruise
values being higher than comparable calendar values in 1976. Total water
column and hypolimnetic concentrations were lower during 1977 cruises
than 1976 cruises in the southern basin. Open lake silica concentrations
were at lower levels in 1977 than 1976. The nearshore waters in the
western portion of basin, however were higher in 1977 leading to the
higher epilimnetic mean (Figure 13).
Figure 15 compares cruise results for the northern basin in 1976
for DRS and suspended silica. The seasonal decrease in DRS concentrations
was also apparent in the northern basin DRS. Suspended silica increased
in the water column thru July and returned to April levels by October.
DRS depth weighted means were computed at each station in the southern
basin of the lake between 1976 and 1977. The open water stations appear
to have lower DRS concentrations in 1977 than in 1976. The zone (about
10 km wide, along the Illinois and Indiana shoreline showed an increase
in ORS, (Rockwell e_t al 1980). This area had the lowest DRS concentration
levels in the southerTTTtasin in 1976 (Figure 13).
In comparing spring and summer 1976 northern basin to southern
basin DRS concentrations, the northern basin silica concentrations were
generally lower (Figure 13). Northern basin cruise were one week
later in the season than the southern basin cruises. While these differ-
ences may reflect, in part, differences due to ship laboratory analytical
processess, surface water temperature differences, and the additional
time available for silica uptake, a picture of lake wide seasonal depletions
of DRS concentrations is documented.
Nvtrajte-J^i trrte
Epilimnetic total nitrate + nitrite as nitrogen, (TNN), concentrations
decreased through the stratified period in both years (Figure 16), while
TNN remained essentially constant in the hypolimnetic waters throughout
the season. Changes in the vertical distribution of TNN concentrations
developed during the season. TNN showed lower concentrations in the
epilimnion when compared with hypolimnion which were statistically signi-
ficant (p >.95) in the latter half of the cruises in both 1976 and 1977,
A similar seasonal effect is seen in dissolved nitrate and nitrite,
(DNN), in the northern basin.
52
-------
figure 13
Upper Twenty Meter
Distribution Of Dissolved Reactive Silica In mg/l
8, 1976
May 25- June 2,
1976
LAKE FOREST
MICHIGAN CITV
Milwaukee
ZION
WAUKEGANI
LAKE FOREST
GRAND HAVEN
BENTON HARBOR
MICHIGAN CITY
June 11-16, 1977
August 10-19,
1976
August 3-10,
1976
ENTON HARBOR
MICHIGAN CITY
Milwaukee
ZION
WAUKEGAN
LAKE FOREST
MUSKEGON
I GRAND HAVEN
BENTON HARBOR
MICHIGAN CITV
August 20-25, 1977
53
-------
figure 14
2.0
— 1.8
1.6
— 1.4
1.2
1.0
.08
.06
— .04
.02
S
s
1976-1977 Southern Lake Michigan
Two Layer Volume-Weighted Average
Dissolved Reactive Silica (mg/l) by cruise
or Total Reactive Silica *°
Epilimnetic Mean (E)
Hypolimnetic Mean (H)
S
T
Cruise 76-1 '° 76-2 76-3 76-4 76-5
* Transect 6 only
I
One standard error
2.0 _
1.8
1.6 —
1.4 —
1.2 _
1.0
0.8 _
0.6 _
0.4
Number
Of Samples
In Mean
76-6
76-7 76-8"
77-1 77-2 77-3 77-4
-------
en
en
10 _
09 _
07
0.6 _
0.5 _
04 _
03 _
0.2 _
0.1 _
figure 15
1976 Northern Lake Michigan
Two Layer Volume Weighted Average (V)
Silica (mg/l) By Cruise
Epilmnetic Mean {E)
Hypolimnetic mean (H)
_ I
i
- - Plus or Minus One Standard Error
_ 10
0.9
_ fl-8
_ 07
_ 06
_ 05
04
03
_ 0.2
Number
Of Samples
In Mean
Cruise 76-1 76-2 76-3 76-4 76-5 76-1 76-2 76-3 76-4 76-5
I Dissolved Reactive 1 I Suspended 1
-------
figure 16
0.30.
0.25 _
0.20-
en
0.15 _
0.10 _
0.05-
1976-1977 Lake Michigan
Two Layer Volume-Weighted Average (V)
Nitrate + Nitrite N (mg/l) By Cruise
Epilimnetic Mean (E)
Hypolimnetic Mean (H)
0.00 76-1 • 76-2 76-3
Transect 6 only *
s
i
S
a
76-4 76-5 76-6
76-7*
Southern Basin-
Total
I
-j- OM Stindird Error
s
3
77-1 77-2 77-3 77-4
3
E
5
V
I
8
H
1
5
E
s
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I
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1
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f.
5
V
I
s
H
Of
Sunpks hi Mttn
76-1 76-2 76-3 76-4 76-5
| Northern Basin
Dissolved
-------
Figure 17 illustrates the seasonal variation in the vertical distri-
bution of TNN, at Station 18, a typical deep water site. TNN's homogeneous
distribution is evident during the isothermal regime in May 1976, and
April and June 1977. Depletion of TNN in the epilimnion occurs during
the other visits and is most severe in the August 1976 and September
1977 cruises.
In the northern basin (Figure 18), DNN did not appear to have statis-
tically significant (p >.95) nearshore to offshore gradients over the
season. In Figure 18 the northern basin data is DNN and the southern
basin is TNN. The principal form of nitrate + nitrite is the soluble
fraction since no significant differences were found in comparing TNN
and DNN in the southern basin. Further comparison of TNN in the southern
basin with DNN in the northern basin indicated no statistically significant
differences (p >.95) in the epilirnnion or hypolimnion.
Comparisons between the nearshore and open lake zones, showed
relatively lower values for both TNN and DNN in the early cruises
(June 1976-1977) in the nearshore epilimnetic waters, while the later
cruises (August 1976-1977) showed relatively higher values in the
nearshore epilimnetic waters (Figure 18). These patterns are
illustrated with the depletion of DNN in the shallow nearshore zones in
the northern basin near Green Bay and along the western shore into the
southern basin in Figure 18. In the August cruises in areas where upwelling
was noted, near Muskegan in 1976 and near Milwaukee in 1977, higher
values of TNN are noted along shore when compared to deeper waters
(Figure 18).
TNN was homogeneous (.256-.260 mg/1) throughout the water column
during isothermal conditions in the deep water stations in both years
(Appendix Tables Cl and C3). Depletion during the summer to levels around
.088 jf .003 mg/1 occurred in the open lake surface waters. This represented
a 66% reduction in TNN concentrations in 1976. In 1977 observed depletion
effects were not as severe with surface water TNN concentration lows at
.134+_ .005 rng/1 which represented a 50% reduction from isothermal condition
concentrations. This depletion is widespread across the entire epilimnetic
layer in the southern basin both in 1976 and 1977 (Appendix Table Cl and
C3) in the deep waters of the lake. Depletion is also evident in the surface
water DNN concentrations which declined from .230 +_ .006 mg/1 to .121 +_
.003 mg/1 in the northern basin in 1976 (Appendix Table C2).
Ammonia
Ammonia levels encountered in Lake Michigan during 1976-1977 ranged
from less than 1 ug/1 to 30 ug/1 with TLVWA of cruise data ranging from
2.7 ug/1 to 8.6 ug/1. These levels are at least two orders of magnitude
lower than those found in the harbor areas surveyed (Appendix B).
Figure 19 shows means for the epilimnion, hypolimnion, and volume
weighted mean for 1976 and 1977 cruises. Total ammonia concentrations
declined at 87% of the southern basin stations between 1976 and 1977.
57
-------
figure 17 Lake Michigan 181976-1977 Cruise Results
Total Ammonia NH3-N ug/l (Dashed) Top Scale
Total NO2 + NO3 mg/l (Solid) Bottom Scale
MA t 39 1976
10 70 30
03 09 16 23
AUGUST 27 1976
10 ?0 30 40
ug/l
09 16 33 30
AUGUST 7 1976
U> 30 , 3U 40
mg/l
ug/l
ifc ?3 3d 0? 09 16 ?3 30
mg/l
ug/l
AUGUST 23 1977
TOTAL NO2 * N03 MG/L (SOLID)
16 73 30
mg/l
SEPTEMBER 21 1977
58
-------
figure 18
Upper Twenty Meter
Distribution Of Nitrate And Nitrite
In mg/l
Dissolved
June 2-8,
1976
GRAND HAVEN
.22
ZION
WAUKEGAN
LAKE FOREST
Total
May 25 - June 2,
1976
BENTON HARBOR
MICHIGAN CITY
LUDINGTON
MUSKEGON
GRAND HAVEN
Total
BENTON HARBOR
HAMMOND
June 11-16, 1977
59
Dissolved
August 10-19,
1976
HF NTON HARBOR
.14
MICHIGAN CITY
Total
August 3-10,
LUDINGTON
MUSKEGON
GRAND HAVEN
Total
ZION
WAUKEGAN
LAKE FOREST
.18
1ENTON HARBOR
MICHIGAN CITY
August 20-25, 1977
-------
ngure fa
11.0
10.0
9.0
8.0
7.0
6.0
01
o
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4.0
3.0
2.0
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1976-1977 Lake Michigan
Two-Layer Volume-Weighted Average (V)
Ammonia - Nitrogen (ug/l) by Cruise
Epilimnetic Mean (E)
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Northern Basin
Total
Dissolved
-------
This is reflected in southern basin total ammonia TLVWA of cruise data which
ranged between 4.0.+_ .2 to 8.6 +_ .9 ug/1 in 1976 as compared with 1977
values which ranged between 2.7 +_ .1 to 6.2 _+ .3 ug/1. Northern basin
dissolved ammonia TLVWA of cruise data ranged between 5.2 + .2 to 10.0
+_ .4 ug/1 in 1976.
Ammonia concentrations are highly variable in the lake and nearshore.
During June 11-16, 1977 concentrations were below the cruise detection level
(<3 ug/1) for most of the western portion of the southern basin. The following
cruise during August 20-25, 1977 concentrations were above 18 ug/1 in the
same area (Figure 20).
Vertical variations in ammonia distribution were observed following
stratification. The typical sequence observed was an increase in ammonia
near and just below the thermocline of deep-water stations around the 20
to 30 meter depth. Figure 17 shows this development in both 1976 and
1977. This pattern was observed both years at deep water stations
(Appendix Tables C1-C3) and suggests that this development is characteristic
of the lake in both basins.
Total Kjeldahl Nitrogen (TKN)
In the first three^cruises in 1976 and in all cruises in 1977 in the
southern basin total kjeldahl nitrogen concentrations were consistently
higher in the epilimnetic waters than in the hypolimnetic waters. TKN .
showed a tendency to increase in the metalimnion and developed a local
maximum in the deep water stations (greater than 80 meters in depth)
in the southern basin during the stratified period in 1976 (Appendix
Table Cl). The layer differences were statistically significant
(p >.95) after the first cruise each year. Nearshore TKN values were
greater than offshore values in the upper layer in 1976 during all three
cruises. Figure 21 illustrate these spatial distribution of TKN during
third and fourth cruise of 1977.
Chlorophyll "a"
The seasonal vertical chlorophyll "a" pattern is displayed in Figure 22
for cruises in 1976 and 1977 at station 18. The temperature distribution
for these cruises can be found in Figure 12. The vertical distribution
of chlorophyll "a" at this deep water station (Figure 22) was similar
to that reported by Brooks and Torke (1971). The vertical distribution
was homogeneous during the early isothermal cruises. With the onset of
thermal stratification, higher concentrations occurred in the epilimnion
with a maxima in the lower thermocline in June and July. This maxima
disintegrated in September.
61
-------
Upper Twenty Meter Distribution
Of Total Ammonia In ug/l
June 11-16, 1977
ro
MILWAUKEE
LAKE FOREST
CHICAGO
3.5 MUSKEGON
^^
GRAND HAVEN
BENTON HARBOR
MICHIGAN CITY
HAMMOND
Aug. 20-25, 1977
MILWAUKEE
MUSKEGON
GRAND HAVEN
BENTON HARBOR
MICHIGAN CITY
HAMMOND
10 5 0 10 20 30 4O
' ' ' | ' ' ' MILES
105 O 10 20 30 40 50 60 70
| I ill I I i I I KILOMETERS
-------
figure 21
Upper Twenty Meter Distribution
Of Total Kjeldahl Nitrogen In ug/l
June 11 -16, 1977
240
MILWAUKEE
ZION
WAUKEGAN
LAKE FOREST
CHICAGO
MUSKEGON
GRAND HAVEN
BENTON HARBOR
MICHIGAN
CITY
Aug. 20-25, 1977
MILWAUKEE
ZION
WAUKEGAN
LAKE FOREST
CHICAGO
MUSKEGON
GRAND HAVEN
BENTON HARBOR
MICHIGAN
CITY
HAMMOND
10 5 0 10 20 30 40
' ' ' | 111 MILES
105 010 2O 30 40 50 60 70
| ' i i I I I i I I KILOMETERS
-------
Lake Michigan 18 - 1976-1977 Cruise Results
. Total Phosphorous ug/l (Dashed) Top Scale
Chlorophyll- a ug/l (Solid) Bottom Scale
JUIV 11 1976
AUGUST 23 IftTT
Figure 22
64
-------
Higher average values were monitored in the epilimnetic layer when
compared to the hypolimnetic layer in the southern basin (Figure 23).
This pattern is also observed in the 1976 data in the northern basin.
Epilimnetic values observed in the southern basin were lower throughout
1977 than those observed in 1976. In 1976 Northern basin chlorophyll
"a" concentrations were similar to those in the southern basin.
Figure 24 illustrates the area! distribution of chlorophyll "a"
during June and August 1976 and 1977. The pattern is fairly uniform in
the open waters with concentrations ranging from 1 to 2 ug/1 . Higher
concentration occur in the nearshore zones and near tributaries and
urban areas. In 1977 chlorophyll "a" values can be seen to be somewhat
lower on the August cruise than in August 1976.
Primary Productivity
Mean incubated primary productivity for the eastern and western
nearshore and openlake regions is illustrated in Table 10. Although
productivity estimates can not be considered representative of in situ
rates, the use of the on-deck incubator allows for comparison among
all samples. The results of the '^C uptake experiments indicate the
amount of carbon the phytoplankton will fix given a uniform amount of
light. Thus phytoplankton obtained from 5 meter stations where the
water is clear and low in nutrients will yield low levels of '^C uptake.
On the other hand, phytoplankton collected where nutrients are plentiful
but light is limiting are likely to respond with high levels of '^C
uptake. The high levels of uptake being a consequence of the higher
light levels in the on-deck incubator compared to low in situ levels.
The results for 1976 (Appendix Table Cl) showed a fairly high level
of ^C uptake from southern Lake Michigan. In the open lake uptake
rates were highest in June and slightly lower in the midsummer and fall.
These results imply sufficient nutrients for primary production, but
with some reduction in photosynthesis by July and August. Both nearshore
regions showed somewhat higher '^C uptake than the open lake. These
results, which were not unusual, indicate that higher nutrient levels
induced higher levels of primary productivity. Most likely the nutrient
levels nearshore were more than adequate for primary production and the
phytoplankton were responding well to the high light intensities in the
incubator.
The 1977 primary production results (Table 10) show a dramatic
change from 1976. Levels of productivity were somewhat lower in 1977
especially in the eastern nearshore. Another difference between 1976 and
1977 was the relatively uniform level of '4C uptake on a spatial basis in
1977. The difference between the eastern nearshore and openlake stations
was markedly reduced in 1977.
65
-------
3.0 _
2.0 _
cr>
1.0—
Cruise
•i -I f gure 23
-i-
J-
S
E
* 1
M
01
V H
1976-77 Lake Michigan
•L Two Layer Volume - Weighted Average (V)
Chlorophyll (ug/l) By Cruise
Epilimnetic Mean (E)
Hypolimnetic Mean (H)
*
:
__
"T*
4
i '
•Jb
9
1 H
•
4
•
U
E
k
,
•
i ii
v »
•
?
\
-L
9
E 1
4 *")
-4 k
!•••
9
1 H
"T"
-4 i-
(0
E
I
V
-4 h
$
H
ft
9
E
3
V
J
H
I
a
E
I
V
I
-------
figure 24
Upper Twenty Meter
Distribution Of Chlorophyll a In ug/l
June 2-8. 1976
MUSKEGON
GRAND HAVEN
May 25-June 2,
1976
BENTON HARBOR
MICHIGAN CITY
WAUKEGAN
LAKE FOREST •'
MUSKEGON
GRAND HAVEN
BENTON HARBOR
June 11-16. 1977
MICHIGAN CITY
"67
10
-19,
976
Aug. 3-10, 1976
BENTON HARBOR
MICHIGAN CITY
ZtON
WAUKEGAN
LAKE FOREST
MUSKEGON
GRAND HAVEN
ENTON HARBOR
Aug. 20-25, 1977
MICHIGAN CITY
-------
TABLE 10
Primary Productivity, Chlorophyll "a",
and Assimilation Coefficient
Crusies Date
Eastern Nearshore
Western Nearshore
Openlake
June 15-21, 1976
Primary Production
(mg c/m^/hr)
Chlorophyll "a"
(mg/m#)
Assimilation coefficient.
13.9 ± 9.0
3.0 ± 1.2
4.2 ± 1.7
5.3 ± 1.7
2.9 ± 1.5
2.0 ± 0.7
5.3 ± 2.0
1.7 ± 0.9
3.6 ± 1.8
July 7-13, 1976
Primary Production
(mg c/n//hr)
Chlorophyll "a"
(mg/rrr)
Assimilation coefficient
15.9 ± 11.2
4.5 * 3.6
3.8 ± 1.8
5.8 ± 5.7
2.5 -t 2.7
5.0 ± 2.5
4.6 ± 2.2
1.4 ± 0.6
3.8 ± 2.1
August 24-Septemebr 2, 1976
Primary Production
(mg c/nv'/hr)
Chlorophyll "a"
(mg/n/)
Assimilation coefficient
September 14-20, 1976
Primary Production
(mg c/rrr/hr)
Chlorophyll "a"
(mg/m3)
Assimilation coefficient
5.7 ±
1.5 ±
3.9 ±
6.2 ±
1.9 ±
3.6 ±
2.1
1.0
1.4
1.6
0.6
1.6
8.8 ±
2.4 ±
3.7 ±
5.3 ±
1.8 ±
3.7 ±
6.4
1.1
1.4
2.1
1.0
1.9
4.7 ±
1.6 ±
3.5 i
4.9 ±
1.6 ±
3.2 ±
3.1
0.7
3.2
1.8
0.4
1.3
68
-------
(contd.) TABLE 10
Crusies Date
Eastern Nearshore Western Nearshore Openlake
April 19-24, 1977
Primary Production
(mg c/m/hr)
Chlorophyll "a"
(mg/m3)
Assimilation Coefficient
June 11-16, 1977
Primary Production
(mg c/m3/hr)
Chlorophyll "a"
(mg/m3)
Assimilation Coefficeint
August 20-25, 1977
Primary Production
(mg c/m3/hr)
Chlorophyll "a"
(mg/m3)
Assimilation Coefficient
September 17-24, 1977
Primary Production
(mg c/nrVhr)
Chlorophyll "a"
(mg/m3)
Assimilation Coefficient
4.5 ± 0.8 5.6
2.8 ± 0.7 3.5
1.7 ± 0.6 1.6
Only stations
6.2 ± 3.4 4.3
2.9 ± 1.3 1.8
2.1 ± 0.8 2.5
4.8 ± 1.3 7.3
1.3 ± 0.6 2.5
3.9 ± 1.1 3.0
4.55 ± 0.7 5.3
1.4 ± 0.4 2.0
3.6 ± 1.4 3.5
± 1.3
± 0.3
± 0.5
5a and 9
i 2.2
•* 0.8
± 1.1
± 3.4
1 1.2
± 0.5
± .5
± .9
± 2.8
4.2 ± 1.1
1.6 ± 0.7
2.8 ± 1.0
3.1 ± 1.3
2.2 ± 1.0
1.5 ± 0.6
3.7 i 1.4
0.9 ± 0.3
4.6 ± 1.5
4.6 t 1.0
1.2 ± 0.5
4.3 ± 1.5
-------
Phytoplankton
Figures 25 and 26 illustrate the mean total phytoplankton (pannel A)
and the precentage contribution (pannel B) of major groups in the nearshore,
offshore, and open lakeU) in 1976 and 1977. In 1977 samples from both the
2 and 5 meter depth were analysed. These were averaged for Figure 26.
In 1976 the majority of the samples were from the 5 meter depth in the
early portion of the study (May 25-June 21). In the later portion of the
1976 study, many stations were represented by 2 meter samples only.
Thus Figure 25 is based on the average of 2 and 5 meter samples or a
single 2 or 5 meter sample from each station. This undoubtedly introduces
some error as bluegreen algae were frequently more abundant in the 5 meter
samples during stratified periods. We, however, feel a reasonable description
of the size and gross composition of the phytoplankton population in the
upper epilimnion is presented.
Phytoplankton populations were typically highest nearshore and
decreased toward the open lake. Relative abundance of diatoms was usually
more abundant on the early cruises and decreased through the stratified
period. The greatest diatom populations were observed in the nearshore
in May, 1976 and April, 1977. Diatom populations in the open lake increased
through June. The Cyanophyta increased from a numerically minor component
on the early cruises to the second most abundant group in midsummer
(August or September) of each year. The period of greatest blue green
abundance corresponds to the greatest epilimnetic water temperatures
(Figure 5) and lowest epilimnetic silica concentrations (Figure 15).
The most (numerically) abundant component of the phytoplankton identi-
fied throughout both years of the study were the phytoflagellates which
comprised between 45 and 67 percent of the total population. This
composite group is comprised primarily of unidentified forms (called mis-
cellaneous flagellates in this report), Cryptomonas spp. and Dinobryon
spp. Also included, usually in small numbers, are Ceratium, Chlamydomonas,
Euglena, Phacus, Mallomonas, Periddinium, Trachelomonas.
The results of this study may be affected by the low (400x) magnification
used throughout the study. It is possible than smaller forms including
small centric diatoms may be underestimated at magnifications below
lOOOx (Holland, 1979). The cruise interval was to long to detect seasonal
flucuation. Holland (1979) recommends a minimum interval of 2 weeks between
samples. The annual phytoplankton maxima were also possibly missed.
Makarewicz and Baybutt (1980) report that this occurs as early as March
in the Chicago nearshore.
^Nearshore (0 to 3 km from shore)
Offshore (3 to 8 km from shore)
Open lake (greater than 8 km from shore)
70
-------
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li stribut ion
Figure 27 illustrates the mean horizontal distribution of total phyto-
plankton at the 5 meter depth in the southern basin in 1977. As the
thermal bar was located nearshore and appeared to be enhancing the inshore-
offshore difference in populations in the south-western and central
eastern portions of the basin in April, the annual mean represents the
June, August and September cruises only. The individual cruises are
also illustrated in Figure 27. The highest populations occurred near-
shore throughout the study; however, some nearshore stations routinely
exhibited relatively higher populations than others. These include
station 5a off Chicago, stations 21 and 21a off Milwaukee, station 20
and 20a north of the Kalamazoo River and stations 16 and 16b south of
Milwaukee.
During the April 1977 Cruise ( Appendix Table 01) diatoms or
flagellates dominated at all stations with green and blue green algae a
very minor component. There was a striking difference in both size and
composition at the generic and species level inshore and offshore. This
was apparently related to the thermal bar (Figure 5) accentuating the
difference between nearshore and open lake phytoplankton populations
through warmer water temperatures and nutrient entrapment. The wanner
(greater than approximately 6°C) water stations typically exhibited
total phytoplankton populations 2 to 5 times those of the cold water
stations. At most stations throughout the study, miscellaneous flagellates
typically were dominant. When this dominance is ignored, a difference .
in composition of the plankton inshore and offshore of the thermal bar
becomes evident. With the exclusion of miscellaneous flagellates,
the warm (_>6°C) water stations were dominated by large populations of
Fragilaria crontonensis with Dinobryon spp and Cryptomonas spp., occasion-
ally occurring as codominates. Subdominates included Dinobryon spp.,
Crytomonas spp. Cryptomonas ovata, Melosira spp., Synedra spp., and
Ankistrodesmus falcatus. Other species (Appenidx Table Dl) including
Tabellaria fenestrata which were not among the dominates or Subdominates
were more abundant at the warm water stations than lakeward of the thermal
bar. The colder stations beyond (lakeward of) the 6°C isotherm were
dominated by Melosira spp., Cyclotella spp., and Cryptomonas spp. Subdomi-
nates at these stations included Melosira spp., Cyclotella spp., Oscillatoria
1imnetica, Ankistrodesmus falcatus, Asterionella formosa, and Crytomonas
erpsa. The eutrophic indicator Diatoma tenue var. elongatum (Stoermer
andTang, 1970) occurred at several nearshore, offsTiore ancTopen lake
stations. Greatest concentrations of this species were found at stations
5a, 6b, 20, 20a, 16b, with 60 cells/ml and station 24a with 140 cells/ml.
The only blue green of any significance was Oscillatoria 1imnetica,
which occurred at most stations in concentrations between 20 and 140
filaments/ml, and Schizothrix calcicola, found at several near and
offshore stations (20 to 80 filaments/ml).
Cell counts of £. crotonensis and J. fenestrata were positively
correlated with water temperature and negatively correlated with dissolved
silica over ranges of 1.2 to 9.0°C and .35 to 1.24 mg/1 respectively.
These correlations were significant at the 99 percent confidence level and
indicate that these species were probably responding to increased water
temperature and were at least partially responsible for the decrease in
silica observed above ^ 6°C (See Silica Results).
73
-------
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-------
By the June 1977 cruise (Appendix Table D2) the population densities
at those nearshore stations which had been within the thermal bar in
April had decreased while those lakeward of the thermal bar had increased.
Flagellates dominated at all stations with exception of 10, 17, and 18,
comprising between 23 and 83 percent of the total population. Diatoms
were the second most abundant group comprising between 10.7 and 49.8
percent of the populations at individual stations. The blue green algal
component of the total population had increased to between 1.2 and 6.3
percent of the population.
All near and offshore stations with the exception of 21a and 25a
were dominated by miscellanous flagellates in concentrations between 460
(21.9%) and 1820 (54.5%) cells/ml. Stations 21a and 25a were dominated
by Dinobryon spp. (3240 cells/ml, 65.6%) and Cryptomonas spp. (1160 cells,
24.6%) respectively. Subdominates at the near and offshore stations in-
cluded Cryptomonas spp, Fragilaria crotonensis. Rhizosolem'a longiseta,
Dinobryon spp, NfeTosira jp_p_, SynedVa ulna, FragiTaria intermedTa, and
Ankistrodesmus falcutus.
The open lake stations were dominated by either Dinobryon spp, f^lelosira
spp. or miscellaneous flagellates. Subdominates were essentially those
found in the near and offshore with the exception of the Cyanophyte
Oscillator! a limnetica, which occurred among the subdorninates at stations
5 (120 filaments/ml) and 12 (120 filaments/ml). Stations 10, 17, and 18
were dominated by Melosira spp. These stations also had lower 5 meter
water temperatures ranging from 4.5 to 6.0°C as opposed to 6.0 to
15.5°C for the rest of the basin.
0_. limnetica was common in the plankton, occurring in small (30 to 140
filaments/ml) concentrations at nearly all stations. Other relatively
common bluegreens include Microcoleus lyngbyaccus which was found in
nearshore samples in small (30 to 90 organisms/ml) numbers and Schizothrix
calico!a which was found in all areas of the basin in small numbers.
The eutrophic indicator Diatoma tenue var. elongatum (Stoermer
and Yang, 1970) occurred at all of the nearshore stations with the greatest
abundance (170 cells/ml) being observed at stations 5a and 13. JD. tenue
also occurred in lessor abundances at stations 5b (30 cells/ml), 5 (30
cells/ml), 25a (90 cells/ml), 16b (120 cells/ml), 18 (30 cells/ml), 24a
(60 cells/ml) and 27 (30 cells/ml).
In August 1977 ( Appendix Table D3) total phytoplankton densities
had decreased from June levels at most stations. 31ue green algae had
increased dramatically and replaced the diatoms as the second most abundant
group at most stations. Diatoms remained important at several nearshore
stations where (Figure 13) silica concentrations higher than those in
the open lake were observed.
Cell counts of A^. formosa, J_. fenestrata, and £. crotonensis were
negatively correlated with water temperature and positively correlated
with dissolved silica. These correlations were significant at the 95
percent confidence level for ^. formosa and the 99 percent level for
both J_. fenestrata and £. crotonensis. In addition, J. fenestrata was
positively correlated with nitrate-nitrite (p>.99). Temperature, silica,
75
-------
and nitrate-nitrite ranged from 11.0 to 21.5°C, .18 to 1.12 mg/1, and
.13 to .23 mg/1 respectively at the 5 meter depth in August. The lowest
water temperature and highest nutrient concentrations were observed in
the nearshore as a result of upwelling {See Figure 5, 13, and 18).
Miscellaneous flagellates were dominant at all near and offshore
stations with the exception of station 13 where Fragilaria crontonensis
dominated. Subdominants in the near and offshore areas included Cryptomonas
spp. , Anacystis spp., Aphanothece spp., F_. crontonensis, Melosira spp. and
^\. formosa.
The open lake was dominated by miscellaneous flagellates, Cryptomonas
spp. , Anacystis spp. and at stations 23 and 27, £. crontonensis. Aphanothece
spp. and Gomphosphaeria lacustris were common components of the offshore
and open lake plankton. ^. limnetica, while still common, had decreased
from April and June levels particularly in the nearshore. Filamentous
bluegreens were relatively unimportant with the exception of stations 16
and 19 where Anabaena spp. constituted 21.6% (580 filaments/ml) and 9.9%
(230 filaments/ml) respectively.
Piatoma tenue var. elongatum occurred sporadically in small numbers
(30-170 cells/ml) in all areas but was primarily confined to the south-
western portion of the basin. _D. tenue reached its greatest abundance
at station 5a off Chicago, 170 eel Is/ml.
Blue green algae and flagellates continued to dominate during the
September 1977 cruise (Appendix Table D4). Total phytoplankton densities
increased somewhat in the more northerly portions of the basin and decreased
in the southerly portions (Figure 27) when compared to August. Diatoms
were somewhat more abundant than during August along the lower 3 transects
but had decreased in the more northerly portion of the southern basin.
They also were more abundant in the nearshore.
Miscellaneous flagellates, Crytomonas spp. , or Anacystis spp. were
dominant at most stations. ^. formosa, F. crotonensis, R. eriensis, and
.?_• limnetica were negatively correlated Tp>.95) with water temperature
and positively (p>.95) correlated with nitrate-nitrite concentrations.
These species appeared to be responding favorably to the decrease in
temperature and possibly epilimnetic nutrient increases associated with
autumnal cooling in the nearshore.
Vertical Distribution
Figure 28 illustrates the vertical distribution of total phyto-
plankton and the percentage contribution of the major phytoplankton
groups at station 23 on the June, August, and September, 1977 cruises.
This station was typical of the open lake stations in 1976 and 1977.
Throughout the season the number of total phytoplankton was re-
markably uniform even in the deeper areas of the southern basin. The
blue green algae were most abundant during August and September, with
76
-------
figure 28
I 10
o
M
W
43
20
25
50
75
Total Phytoplankton And The Relative
Contribution Of Major Groups At A Deep Water
Station 23 In 1977
6/15/77
2(75)
5(68}
10(6 0)
50(5 0)
75(48)
8/24/77
2(19 0)
5(18 2)
12(18 5)
17(16 0)
22 (9 0)
82 (5 0)
9/19/77
2 (18 0)
5 (18 0)
15 (17 5)
20 (18 0)
25 (15 0)
86 (5.5)
Circles represent size of the total phytoplankton
population at a given depth.Sections represent
the percent contribution of major groups.
Numbers at lower right are sample depth and in
parenthesis, sample temperature.
Flagellates
Cyanophytes
Diatomae f" ~j
Chlorophyta I
-------
their greatest relative contribution frequently occurring in lower
epilimnetic or metalimnetic samples. Diatoms were typically a major
component at all depths in June. However, in August and September they
were usually a minor component of epilimnetic assemblages. Diatoms were
numerically important components in the metalimnetic and bottom samples
throughout the 1976 and 1977 cruise periods. The phytoflagellates
dominated the phytoplankton at all depths on all cruises in both years.
The chlorophyll "a" maximum in the lower thermocline, previously discussed
(See chlorophyll "a" results), corresponds to the diatom maximum.
Microbiology
In 1976 and 1977, heterotrophic bacterial densities in the open lake
were found to be 9/ml (range 2-33) and 8/ml (range 2-35) respectively. In
the nearshore zone in 1976 the geometric mean value for aerobic hetero-
trophs was 21/ml (range 5-87), and in 1977, was 30/ml (range 8-110) (Figure 29),
Bacteria were generally more numerous near the shoreline where conditions
exist such as immediate, more concentrated nutrient rich drainage water,
and warmer temperatures which promote or maintain higher concentrations
of bacteria, including transitory organisms than would be found farther
out in the open lake (Taylor, 1940).
No fecal coliform bacteria were detected in samples taken from the
open lake stations during the 1976 study. Nearshore counts were almost
invariably 1/100 ml except for an occasional higher result not exceeding
12/100 ml. No fecal coliform determinations were performed on any open
lake samples in 1977.
Chloride
Chloride concentrations are similar in values in vertical distribution
(Appendix Table Cl and C3) and exhibit little if any seasonal trend (Figure
30). Epilimnetic chloride concentrations were higher than hypo!imnetic
values in both basins. Even though individual chloride measurements were
almost the same between the epilimnion and hypolimnion there is a small but
statistically significant (p >.95) increase in chloride concentrations in
the upper layer (0-20 meter) when compared to the lower layer (20 to bottom).
Chloride concentration in the southern basin in 1976 were 8.30^ .06 mg/1
and 8.02 _+ .07 mg/1 for the upper and lower layers respectively. In 1977
these concentrations were 8.32 +_ .04 mg/1 and 8.17 _+ .03 mg/1. In 1976,
northern basin concentrations were lower than those in the southern basin
Figure 31. The average of TLVWA values for the five northern basin cruises
was 7.7 _+ 0.1 mg/1 as compared to 8.0 +^ 0.1 mg/1 for the six complete cruises
in the southern basin Figure 30. The dense stations network near the Straits
of Mackinac biases the epilimnetic TLVUA values in the northern basin. With
these stations removed, the five northern basin cruises epilimnetic chloride
values ranged between 7.8 to 8.0 mg/1. The average of TLVWA values is esti-
mated to be 0.1 mg/1 low due to the dense station network near the Straits
of Macki nac.
78
-------
Figure 29
Annual Geometric Mean Values
Distribution Of Aerobic Heterotrophs
In Organisms/ml.
12ft * MUSKEGON
\\ • 6RAMD HAVEN
2,ON
WAUKEGAN
LAKE FOREST
BENTON HARBOR
MICHIGAN CITY
1976
GRAND HAVEN
ZION •
WAUKEGAN •
LAKE FOREST 1
BENTON HARBOR
MICHIGAN CITY
(1 10 /O
_1 I Mill s
H) 5 I) H>
(() 4O SO h(> /()
I I I I 1 KUOMtTlHS
1977
-------
1976-77 Lake Michigan
Two Layer Volume-Weighted Average (V)
Chloride (mg/l) by cruise
Epilimnetic Mean (E)
Hypolimnetic Mean (H)
— 8.4
— 8.3 .
— 8.2
8.1
— 8.0
o
7.8
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7.6
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Whole water column mean concentrations averaged for each cruise
period in 1976 and 1977 and are displayed in Figure 31. In the southern
basin, chloride concentrations were greatest in the eastern and south-
eastern nearshore in both years. Lowest individual southern basin con-
centrations (7.8 mg/1) were found in the deep water stations. This
pattern was also evident in 1977. The lowest concentrations 7.0 mg/1 in
the entire lake were found in the Straits of Mackinac. Greatest concentrations
were observed at nearshore stations near Manistee and Ludington where an
annual mean of 9.0 mg/1 was observed in 1976.
Chloride concentrations exhibited a concentration gradient in the
1976 annual distribution (Figure 31) where values in the southern most
portion of the southern basin were around 8.7 mg/1 and decreased north-
ward to the Straits of Mackinac (7.0 mg/1).
SuVfate
Sulfate levels found in the southern basin of Lake Michigan in 1976
varied in a narrow range seasonally, specially and vertically. TLVWA cruise
means averaged 21.1 + .4 mg/1 in 1976. The epilimnion had a slightly
higher annual mean (71.3 +_ .4 mg/1) than the hypolimnion (21.1 + .4
mg/1) in 1976 (Figure 32). There may be a slight south to nortTT gradient
in the southern basin concentration of sulfate as seen in the 1976 annual
distribution (Figure 33) and in spring (Cruise 2) and summer (Cruise 5)
cruises. These contours represent entire water column average concentrations
at each station. The annual distribution is an average over all cruises.
Sulfate was not measured in 1977.
In 1976, nearshore pH ranged from 7.5 to 8.6 in the southern basin and
8.0 to 9.0 in the northern basin. The open lake pH ranged from 7.6
to 8.8 in the southern basin and from 7.8 to 8.8 in the northern basin.
In 1977 southern basin nearshore and open lake station pH ranged from
7.8 to 8.7 (Appendix B).
The open waters exhibited a seasonal change in pH in the epilimnetic
waters. For stations with depths greater that 80 meters pH was uniform
during isothermal conditions throughout the water column and had values
from 7.9 to 8.0. (Appendix Table Cl and C3) By August each year epilimnetic
pH values had increased to 8.4 tp 8.5 at these sites while hypolimnetic waters
remained between 7.9 to 8.0. During the stratified period pH ranged 0.3
to 0.5 pH units greater in the epilimnetic waters of the offshore stations
in the southern basin than in corresponding hypolimnetic water (Figure 34).
Spacial variations in pH in the southern basin in the epilimnetic waters
of the open lake did not vary more that 0.1 units during an individual
cruise. Lower pH values were occasionally found at the stations nearest
shore.
81
-------
figure 31
Chloride Concentration In mg/l
Annual Average
• Benton Harbor
Michigan City
1976
Milwaukee
Zion
Waukegan
Lake Forest •
Benton Harbor
Michigan City
10 S 0 10 20 30 40
»—J -i 1 1 ' ' MILES
10 S 0 10 20 30 40 SO 60 70
1977
82
-------
figure 32
co
oo
22.2 —
22.0 —
1976 Southern Lake Michigan
Two Layer Volume Weighted Average (V)
Sulfate (mg/l) By Cruise
Epilimnetic Mean (E)
Hypolimnetic Mean (H)
figure
_ 22.2
22.0
21.8 —
21.6 —
21.4 —
21.2 —
21.0—
20.8— '
20.6—
20.4 —
20.2 _
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I
Plus or minus one standard error
Cruise 76-1 * 76-2 76-3
•Transect 6 only
76-4
76-5
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76-7 76-8 ,*
-------
Figure 33
Distribution Of Sulfate In mg/l
1976
Annual
Average
cc
4=
CHICAGO
BENTON
21.4'/ 21.8' HARBOR
MICHIGAN CITY
Spring 1976
May 25-June 2
ZION
WAUKEGAN
LAKE FOREST •
CHICAGO
MICHIGAN CITY
Summer 1976
August 3-10*
CHICAGO
BENTON
HARBOR
MICHIGAN CITY
HAMMOND
-------
figure 34
1976-1977 Lake Michigan
Two Layer Volume Weighted Average (V)
pH (S.U.) By Cruise
Epilimnetic Mean (E)
Hypolimnetic Mean (H)
— 8.6
_ 8.5
8.4
— 8.3
co
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Specific Conductivity
The spacial distribution of specific conductivity in Figure 35
illustrates conductivity values plotted from the upper twenty meters
at each station. Conductivity was higher nearshore and decreases
lakeward. Uniform values for conductivity in transects 7-9 in the
northern has in result in a random contour line. Lowest conductivity
values (240-250 umhos/cm) are observed in the Straits of Mackinac. This
spacial pattern appears to be representative of conductivity's distribution
in the lake.
Conductivity in the epilimnetic waters exhibited a seasonal effect
in the southern basin (Figure 36) with lower values occurring in August
and September in both basins. Conductivity values during the early
spring isothermal period appear to be uniform at the deep water stations
(80 meters or greater) and had maximum levels between 274 and 276 umhos/cm
throughout the water column in both basins (Figure 35 and Appendix Table
C1-C3). For the northern basin the TLVWA epilimnetic values for con-
ductivity are biased low (Figure 36) due to the dense station network
in the shallow waters near the Straits of Mackinac. With these stations
removed, epilimnetic values for conductivity ranged from 266 to 274
umhos/cm for the last four cruises.
TRACE METALS
Table 11 presents summary results for arsenic, barium, beryllium,
cadmium, cobalt, copper, lead, manganese, molybdenium, nickel, silver,
vanadium, zinc, calcium, magnesium, potassium, sodium and fluoride
concentration in water samples. Some or all data for iron, chromium,
tin, aluminum, boron, titanium, and zinc have not been presented because
quality assurance tests indicate they were not reliable.
Results indicate that higher metal values in water samples were
found more frequently in the transects north of Frankfort toward the
mouth of Grand Traverse Bay. The source of these metals is unknown.
There have been several recent surveys of Lake Michigan water by
other investigators for metals using atomic absorption spectroscopy
(AAS), either by flanneless graphite furnace (FGF), or by direct aspiration
either without preconcentration (DA) or by solvent extraction of a metalo-
organic complex (SE). Other methods used include neutron activation
analysis of freeze dried samples (NAA), spark source mass spectroscopy
of freeze dried samples (SSMS), and direct reading spectrography (DRS).
This study used an Inductively Coupled Argon Plasma Emission Spectroscopy
(ICAP) as a source for DRS. All of these surveys lacked thorough documented
quality assurance procedures so that the role of contamination, positive
and negative interferences and other sources of error is unknown.
A parameter by parameter discussion of our results and those available
in other recent surveys follows.
86
-------
Figure 35
Upper Twenty Meter
Distribution Of Conductivity In umhos
June 2-8, 1976
May25-June2.
IENTON HARBOR
MICHIGAN CITY
, BON
WAUKEGAN .
LAKE FOREST
CHICAGO L_
June 11-16,
1977
BENTON HARBOR
MICHIGAN CITY
Aug. 10-19,
1976
Aug. 3-10,
1976
WAUKE
LAKE FOI
276 '
273((^ MUSKEGON
I
GRAND HAVEN
August 20-25,
1977
WAUKEGAN 276
LAKE FOREST
CHICAGO
BENTON HARBOR
MICHIGAN CITY
87
-------
300
Figure 36
1976-77 Lake Michigan
Two Layer Volume-Weighted Average (V)
Specific Conductivity at 25°C (umhos/cm) by cruise
Epilimnetic Mean (E)
Hypolimnetic Mean (H)
— 290
• -f- One Standard Error
CO
CO
— 280
270
_ 260
250
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-------
TABLE 11
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
CO
Arseni c
Barium
Beryllium
Cadmium
Cobalt
Copper
Lead
Manganese
Molybdenum
Nickel
Silver
Vanadium
Zinc
Calcium
Magnesium
Potassium
Sodi urn
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
.1
.1
.01
.1
.1
<2
40
<2
4
2
9
19
8
4
13
7
25
20
values in mg/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.
-------
Al umi num
There are no applicable water quality or drinking water standards
for aluminium nor is there an objective stated by the Great Lakes Water
Quality agreement of 1980 (Appendix A). According to data from Cope!and
and Ayers (1972) on dissolved aluminium and aluminium in sediment, it
appears that any determination of total aluminium in the water would be
highly dependent upon the amount of suspended sediment in the water.
Table 12 shows mean values of total aluminium an order of magnitude
higher than the values for dissolved aluminium in Lake Michigan water.
TABLE 12
Total Aluminium (ug/1)
Sample Description
Lake County Illinois
Water Plant Intake
Weekly determination
Monthly diurnal
Date/Number
Jan-Dec 1972
48 samples
Jan-Dec 1972
40 samples
Monthly replicate deter- Jun-Dec 1972
mination in Southwestern 209 samples
Lake Michigan Illinois-
Wisconsin State!ine
to Waukegan
Monthly intake samples
of Zion Nuclear generat-
ing Plant
Monthly duplicates of two
stations. 2.3 mi. North
ft 3.2 mi. South of Pt.
Beach Nuclear Power Plant.
3 depths each
July 73-Jun 77
178 samples
Sept 72-Nov 73
144 samples
Nov 73-Oct 74
144 samples
Nov 74-Oct 75
138 samples
Nov 75-Oct 76
142 samples
Mean Range Source
200 <100-600 Industrial Biotest
(1972b)
AAS/DA
300 <100-600 p. 172
100 <100-500 Industrial Biotest
(1972a)
Table A-22
p.277
AAS/DA
110 10-700 Nalco (1977)
AAS/DA
AAS/FGF
500 100-6000 Wisconsin Electric
(1972-76)
Table 5.5-4 p.5.0-
300 100-1200 Table 2.3-60/82
p. 2.0-74/96
120 100-5000 Table 2.25/35
p. 2.0-49/59
250 100-800 Table 2-25/356
p. 2-57/68
AAS/DA
90
-------
Dissolved Aluminium (ug/1)
Sample Description
Three lakewide surveys
surface samples
Seventeen kilometer
offshore near Grand
Date/Number Mean
Aug 69-Jun 1970 27
54 samples
1971 11
1 sample
Ranje Source
4.9-150 Cope!and 8 Ayers
(1972)
NAA
Wahlgren, Edgington,
Rawlings (1972)
SSMS
Arsenic
The 1977 lakewide survey for total arsenic consisted of 11 samples
analyzed hy AAS/FGF analysis. All values were below the 2 ug/1 detection
limit. The Great Lakes Water Quality agreement specifies that total
arsenic in an unfiltered water sample from the boundary waters should
not exceed 50 ug/1 (Appendix A).
Data in Table 13 is near the detection limit in all cases. Al-
though three different analytical methods are represented, the results
are all in the same range. The dissolved arsenic appears to be in the
same range as total arsenic though none of the total arsenic means
represent lakewide surveys.
TABLE 13
Total Arsenic (ug/1)
Sample Description
Replicate monthly deter-
minations Southwestern
Lake Michigan
Lake County Water Intake
Kensoha Water Intake
North Chicago Water
Intake
Monthly duplicates of
two stations. 2.3 mi.
North mi. South of Pt.
Beach Nuclear Power
Plant. 3 depths
each
Sampled Dec, Apr, May
Jul , Aug, Oct.
Date/Number Mean
Jan 1970-
Apr 1971
44 samples " 1.4
44 samples 1.1
44 samples 1.2
Sep 72-Nov 73
144 samples 1
Nov 73-Oct 74
144 samples <1
Nov 75-Oct 76
70 samples <1
Dec 76-Oct 77
72 samples 1
AAS/FGF
Range Source
Industrial Biotest
(1972a)
<.5-3.1 Table X
<.5-3.2 p II A-20
0.5-2.7 Arsine/Col orimetric
Wisconsin Electric
-------
TABLE 13 (contd.)
Total Arsenic (ug/1)
Sample Description
Monthly survey within
three mile of Kewaunee
Nuclear Power Plant
12 samples per survey
Quarterly analyses of
intakes at Pullian
Power plant of Lower
Green Bay
Monthly replicates near
Hammond Indiana Bailly
Metals survey Figure 37
Date/Number Mean
1973 1
1974 <1
1975 1
1976, 96 samples 1
Jan-Dec 1973
8 samples <50
May-Nov 1974
290 samples <,8
July-August 1977 <2
11 samples
<50-<50
<2
Source
Nalco (1976)
AAS/FGF
Univ. of Wise. (1974)
Texas Instruments
(1975)
This study
I CAP
Dissolved Arsenic (ug/1)
Three lakewide surveys
surface samples
Barium
Aug 1969-Jun 1970
54 samples 1
0.16-2.6
Cope!and & Ayers (1972
NAA
The 1977 survey data showed a mean of 12 ug/1, and a range of 8
to 40 ug/1 with 102 samples. With the exception of three values 25, 30 and
40 ug/1, all values were between 3 and 21 ug/1. The 25, 30, and 40 ug/1
values were associated respectively with the samples from the fifty-
four meter contour of transect XIV off Pt. Detour, the nine meter contour
of transect XVII north of Charlevoix MI, and station 29 off Manitowoc, WI.
This survey could be biased as much as 8 ug/1 low because of an over-
compensation for an interference. Even so, the mean value would be only
about half the mean value found by Copeland and Ayers (1972).
Worst case examples of duplicates from the same Niskin bottle for
this survey were 10, 15, and 14, 18 even though the resolution of the
procedure is a small fraction of a microgram per liter.
Applicable water quality and drinking water standards for total
barium in Lake Michigan are all 1 mg/1 (Appendix A). The Great Lakes
Water Quality agreement contains no objective for barium.
Table 14 reveals a rather broad range of values by each author
both temporally and spacially. The means and ranges of Copeland and
Ayers (1972) and Rossman (1980) are very similar, though the former
reports a lakewide survey using neutron activation analysis of freeze
dried water while the later surveyed a small area near Cook Power
plant by atomic absorption spectroscopy. The values given by Kopp
and Kroner (1968) are three month composites of weekly samples from
92
-------
a single point. Though one might expect minimal variation in such a
survey, their samples showed nearly a three fold variation in magnitude.
The limited solubility of barium sulfate could create problems in a pre-
concentration procedure such as used by Kopp and Kroner (1968), Copeland
and Ayers (1972), and the present survey, though Rossman (1980) indicated
no such pre-concentration step.
TABLE 14
Total Barium (ug/1)
Sample Description
Metals Survey Figure 37
Date/Number Mean
July-Aug 77 12
102 samples
Source
This Study
I CAP
Dissolved Barium (ug/1)
Three month composites of
weekly samples from pub-
1ic water intakes at
Milwaukee, Wisconsin and
Gary, Indiana
Three lakewide surveys,
surface samples
1962/
1967
10 samples
9 samples
Aug. 1969/
June 1970
54 samples
18
21
37
10-26
14-41
6.1-110
Kopp & Kroner (1968)
DRS
P H-6
P H-7
Copeland & Ayers
(1972)
NAA
Seventeen kilometer offshore 1971
near Grand River 1 sample
Nearshore samples
near Cook Nuclear
Power Plant
1974/1975
88 samples
24
44
14-69
Wahlgren, Edgington,
Rawling. (1972)
SSMS
Rossman (1980)
AAS
Beryllium
All 136 samples from the 1977 Lake Michigan survey were below the 2
ug/1 detection limit. Water Quality criteria and drinking water standards
are not available for beryllium (Appendix A) though the metal is toxic
enough to man that special precautions are necessary when working with
the metal or its salts. (Handbook of Chemistry and Physics 1970-1971)
Kopp and Kroner (1968) reported no dissolved beryllium in composites
from Gary Indiana and Milwaukee Wisconsin water plant intakes 1962/67 at
a detection limit of 0.1 ug/1.
93
-------
Boron
The results for boron on the 1977 survey were unuseable because
of negative quality assurance data. Applicable drinking water and water
quality standards for boron are 1.0 mg/1. The Great Lakes Water Quality
agreement does not specify an objective for boron. (Appendix A)
Table 15 shows a median value of means for total boron to be 50
ug/1 in Lake Michigan proper while the one sample for dissolved boron
is 33 ug/1.
Samp1e Descriptiion
Replicate monthly deter-
minations Southwestern
Lake Michigan
Lake County Water Intake
Kenosha Water Intake
North Chicago Water Intake
Lake County Illinois
Water Plant Intake
Weekly determination
Monthly diurnal
TABLE 15
Total Boron (ug/1)
Date/Number Mean
Jan 1970/Apr 1971
44 samples
44 samples
44 samples
Jan-Dec 1972
52 samples
Jan-Dec 1972
40 samples
100
100
100
50
60
50-160
50-200
50-140
20-220
20-220
Source
Industrial Biotest
(1972a)
Table X
p II A-21
Colorimetric
Industrial Biotest
(1972b) p. 172
Industrial Biotest
(1972b) p. 172
Monthly replicate deter-
minations in Southwestern
Lake Michigan Illinois-
Wisconsin Stateline to
Waukegan
Monthly intake samples of
Zion Nuclear generating
plant
Monthly duplicates of two
station. 2.3 mi. North
& 3.2 mi. South of Pt.
Beach Nuclear Power Plant.
3 depths each
Jun-Dec 1972
207 samples
July 73-Jun 77
178 samples
Sep 72-Nov 73
144 samples
Nov 73-Oct 74
144 samples
68
30
<100
<10-160
10-110
<100-<100
<200
<200-<200
Industrial Biotest
(1972b)
Table A-23 p. 278
Colorimetric
Nalco (1977)
Colorimetric
Wise. Electric
(1972-76)
Table 5.5-4
p 5.0-424/6
Table 2.3-60/82
p 2.0-74/96
94
-------
Sample Descri pti on
Monthly survey within
three miles of Kewaunee
Nuclear Power Plant
12 samples per survey
Quarterly analyses
of intakes at Pullian
Power Plant Lower
Green Bay
TABLE 15 (contd.)
Total Boron (ug/1)
Date/Number Mean Range
Nov 74-Oct 75 <200 <200-<200
138 samples
Nov 75-Oct 76 <200 <200-<200
142 samples
1973 30 10-120
1974 30 <10-150
1975 30 <10-170
1976, 96 samples 30 <10-80
Jan-Dec 1973 6.5 4.6-8.5
8 samples
Dissolved Boron (ug/1)
Source
Table 2.0-25/35
p 2.0-49/59
Table 2-25/35b
p 2-57/68
Nalco (1976)
Col orimetric
Univ. of Wise.
(1974)
Seventeen kilometer 1971
offshore near Grand River 1 sample
33
Wahlgren, Edgingti
Rawling (1972)
SSMS
Cadmium
In the 1977 lakewide survey, 101 of 103 samples were below the 2 ug/1
detection limit of the ICAP procedure. Maximum value detected was 4 ug/1.
Applicable water quality and drinking water standards specify a maximum
of 10 ug/1. (Appendix A) The Great Lakes Water Quality agreement of
1978 specifies an objective of 0.2 ug/1 on an unfiltered water sample.
Most of the data in the Table 16 tend to indicate that the actual values
are in the low tenths of a ug/1. Nalco 1977 (Zion intake), Texas Instruments
(1975) (lake samples in the vicinity of the Bailly plant) and the University
of Wisconsin (1974) (Lower Green Bay) indicate mean values over 1 ug/1.
TABLE 16
Total Cadmium (ug/1)
Sample Description
Replicate monthly deter-
minations Southwestern Lake
Michigan
Date/Number
Jan 1970/Apr 1971
Mean
Source
Industrial Biotes
(1972a)
Table X
95
-------
TABLE 16 (contd.)
Total Cadmium (ug/1)
Sample Description
Lake County Water Intake
Kenosha Water Intake
Six hour composites at
the Waukegan Generating
Station during a 24 hr.
period (Replicates
implied)
Date/Number Mean Range
44 samples <1
-------
TABLE 16 (contd.)
Total Cadmium (ug/1)
Sample Description
Monthly replicates
snear Hammond Indiana
Bially nuclear plant
Metals Survey Figure 37
Date/Number Mean
May-Nov 1974 2.0
290 samples
July-August 77 <2
103 samples
<2-4
Source
Texas Instrument
(1975)
AAS
This Study
ICAP
Dissolved Cadmium (ug/1)
Seventeen kilometer
offshore near Grand
River
1971
1 sample
0.1
Wahlgren, Edgington
Raw!ing (1972)
SSMS
*Replicate was 2, next highest value 11.
Chromium
Applicable drinking water and water quality standards and the
Great Lakes Water Quality Agreement of 1978 specify 50 ug/1 Chromium as
a maximum value (Appendix A).
Table 17 shows a median mean of 2 ug/1 with 75% of the means within
the range 1 to 3 ug/1. The values obtained on the 1977 survey were
between 3 and 13 ug/1 with a median value of 7. It is not obvious how
an interference could produce such a range of data, however it seems
likely in view of the data from Table 15 that these values are biased
high.
TABLE 17
Total Chromium (ug/1)
Sample Description
Replicate monthly deter-
minations Southwestern
Lake Michigan
Date/Number
Jan 1970/Apr71
Mean
Source
Industrial Biotest
(1972a)
Table X
97
-------
TABLE 17(contd.)
Total Chromium (ug/1)
Sample Description
Lake County Water Intake
Kenosha Water Intake
.North Chicago Water Intake
Six hour composites at
the Waukegan Generating
Station during a 24 hr.
period (Replicates implied)
Lake County Illinois
Water Plant Intake
Weekly determination
Monthly diurnal
Monthly replicate deter-
minations in Southwestern
Lake Michigan
Illinois-Wisconsin State-
line to Waukegan
Monthly intake samples
of Zion Nuclear generating
plant
Monthly duplicates of
two stations. 2.3mi.
North & 3.2mi. South
of Pt.Beach Nuclear Power
Plant 3 depths each
Date/Number
Mean
Monthly survey within
three mile of Kewaunee
Nuclear Power Plant
12 samples per survey
Quarterly analyses of
intakes at Pullian Power
Plant on Lower Green Bay
44 samples
44 samples
44 samples
20 Sep 1972
8 samples
6 Dec 1972
8 samples
2
2
2
5
9
Jan-Dec 1972
48 samples 2
Jan-Dec 1972
40 samples 3
Jun-Dec 1972
209 samples 2
Jul 73-Jun 77 12
82 samples
Sep 72-Nov 73 3
144 samples
Nov 73-Oct 74 <5
144 samples
Nov 74-Oct 75
138 samples 1.6
Nov 75-Oct 76
142 samples 2.4
1973 2
1974 1
1975 0.8
1976, 96 samples 1.0
Jan-Dec 1973
8 samples <10
3-7
6-10
1-8
-------
TABLE 17 (contd.)
Total Chromium (ug/1)
Sample Description
Monthly replicates near
Hammond Indiana Bially
Nuclear Plant
Date/Number
May-Nov 1974
40 samples
Source
Texas Instruments
(1975)
AAS
Dissolved Chromium (ug/1)
Three lakewide surveys
surface samples
Nearshore samples near
Cook Nuclear power plant
Seventeen kilometer off-
shore near Grand River
Aug 69-Jun 1970 1.7
Apr, May, Jul 1974 1.6
& Apr &Jul 1975
88 samples
1971
1 sample 7.2
0.5-4.0 Copeland & Ayers
(1972)
NAA
0.7-4.1 Rossman (1980)
AAS/FGF
Wahlgren, Edgington,
Rawling (1972)
SSMS
Cobalt
Cobalt levels found in 1977 were below the level of detection (1 ug/1)
in 131 samples out of 136 analyzed. Of the remaining five samples, a
value of 3 ug/1 was found at the 54 meter contour of transect XIV and
the other 4 samples, one at 2 ug/1, and three at 1 ug/1 were measured in
an area north of Frankfort to Grand Traverse Bay. Bowen (1966) gives
0.9 ug/1 Co as a typical level in fresh water. Copeland and Ayers found
values ranging from 0.033 to 0.57 ug/1 soluble cobalt. Rossman (1978)
reported 0.1-3.0 ug/1 soluble cobalt in the epilirnnetic and hypolimnetic
waters of nearshore Lake Michigan between St. Joseph Michigan and Michigan
Citys Indiana.
Copper
The Great Lakes Water Quality agreement specifies a maximum of
5 ug/1 copper for the protection of aquatic life (Appendix A). The
drinking water standards are 1 mg/1 for USPHS, and 1 mg/1 for EPA and
Illinois has a water quality standard of 20 ug/1 (Appendix A).
Table 18 shows an overall range of 0.1 to 143 ug/1 with a median mean
of 3 ug/1. Total and dissolved copper appear to be of the same order
of magnitude. Rossman (1980) presented a figure of 0.64 ug/1 contamination
from sample handling.
99
-------
The ICAP detection limit for the 1976 samples was 4 ug/1. Of 581
samples, 16 exceeded that limit (3%), however 3 out of 16 (18%) of the
quality control blanks exceeded that same limit. For the 1977 survey,
using a ten-fold concentrate on the ICAP, the detection limit was 1 ug/1
Of 130 samples, 24 were less than 1 ug/1, while 6 out of 21 quality
control blanks were less than 1 ug/1. Nine samples were 4 ug/1 or more
(7% compared to 3% in 1976), while one quality control blank was 4 ug/1
(5%). Mean sample concentration was 1.75 ug/1, calculated by arbitrarily
assigning a value of 0.5 ug/1 to those samples below the 1 ug/1 detection
limt. Mean collection contamination was 1.05 ug/1 compared to Rossman's
0.64 ug/1. This does not include any contamination that may have occurred
in or before the Niskin bottle in either the Rossman or the EPA survey.
TABLE 18
Total Copper (ug/1)
SampJ_e Description
Replicate monthly deter-
minations Southwestern
Lake Michigan
Lake County Water Intake
Kenosha Water Intake
North Chicago Hater Intake
Six hour composites at
the Waukegan Generating
Station during a 24 hr.
period (Replicated im-
plied)
Lake County Illinois
Water Plant Intake
Monthly diurnal
Monthly replicate deter-
minations in Southwestern
Lake Michigan Illinois-
Wisconsin State!ine to
Waukegan
Monthly intake samples
of Zion Nuclear generating
plant
Date/Number Mean
Jan 1970/Apr 1971
44 samples
44 samples
44 samples
30-31 May 1972
4 samples
29-30Jun 1972
8 samples
20 Sep 1972
8 samples
6 Dec 1972
8 samples
Jan-Dec 1972
60 samples
Jun-Dec 1972
3
77
2
18
Jul, 73-Jun77
82 samples
5.4
1-7
44-120
8.4-24
23
8
30
2
5
0
.6-83
.7-11
19-72
.9-12
0.7-35
0.0-32
Source
Industrial Biotest
(1972a)
Table X
p II A-
AAS/SE
Industrial Biotest
(1972b)
Table 26, p 128
Table 27, p 122
Table 28, p 139
Table 29, p 142
AAS/SE
Table 5 p 172
Industrial Biotest
(1972b)
Table A-3 p 28/6
Nalco (1977)
AAS/SE
AAS/FGF
ICO
-------
TABLE 18 (contd.)
Total Copper (ug/1)
Sample Description
Monthly duplicates of
two stations. 2.3 mi.
North ft 3.2 mi. South
of Pt. Beach Nuclear
Power Plant. 3 depths
each
Sampled Dec, Apr,May,
Jul, Aug, Oct.
Monthly survey within
three mile of Kewaunee
Nuclear Power Plant
12 samples
Quarterly analyses of
intakes at PullianPower
plant on LowerGreenBay
Monthly replicates near
Hammond Indiana Bially
Nuclear plant
Metals Survey figure 37
Date/Number
Sep 72-Nov 73
144 samples
Nov 73-Oct 74
144 samples
Nov 74-Oct 75
138 samples
Nov 75-Oct 76
142 samples
Dec 76-Oct 77
72 samples
Mean
3
3
2
1
Jan-Dec 1973
8 samples
May-Nov 1974
40 samples
July-Aug 77
6.9
<5-10
1.7-5
1973
1974
1975
1976, 96 samples
1.4
1.9
0.9
1.7
0.1-4.9
0.8-9.2
<0.1-5.8
0.5-12
6.0-8.1
1.8
Source
Wise. Electric
(1972-77)
Table 5.5-4
p 5.0-424/6
Table 2.3-60/82
p 2.0-74/96
Table 2.0-25/35
p 2.0-49/59
Table 2-25/35b
p 2-57/68
Table 2-2
p 2-33/37
AAS/SE
AAS/FGF
Nalco (1976)
AAS/SF
AAS/FGF
Univ. of Wise.
(1974)
Texas Instruments
(1975)
This Study
I CAP
Dissolved Copper (ug/1)
Three lakewide surveys
surface samples
*next highest value 17
Nearshore samples near
Cook Nuclear Power Plant
88 samples
Seventeen kilometer off-
shore near Grand River
Aug 69-Jun 1970 5 <7-14.2*
54 samples
Apr, May, Jul 1974
& Apr & Jul 1975 2.5 0.8-8.0
1971
1 sample
9.3
Cope!and & Ayers
Rossman (1980)
AAS/FGF
Wahlgren, Edgington
Rawlings (1972)
SSMS
101
-------
Iron
Applicable water quality and drinking water standards and the Great
Lakes Water Quality Agreement specify a maximum iron concentration of
300 ug/1 (Appendix A). Table 19 provides a range of means for total
iron from nearshore areas of 38 to 1200 ug/1. The range of means for
dissolved iron is 7 to 39 ug/1.
Values from the 1976 survey averaged 34 ug/1 with a standard deviation
of 57 ug/1 and a detection limit of 20 ug/1. Two of the ten quality
control blanks exceeded the 20 ug/1 detection limit (i.e. 21 and 40
ug/1). For the 1977 survey the concentration technique provided a
detection limit of 2 ug/1. The 1977 mean of 23 ug/1 with a standard
deviation of 22 ug/1 for 134 samples was accompanied by 21 quality
control blanks with a mean of 19 ug/1 and standard deviation of 13 ug/1.
It would appear from this that the actual mean value for the entire lake
may be less than 10 ug/1.
TABLE 19
Total Iron (ug/1)
Sample Description
Replicate monthly deter-
minations Southwestern
Lake Michigan
Lake County Water Intake
Kenosha Water Intake
North Chicago Water Intake
Six hour composites at
the Waukegan Generating
Station during a 25 hr.
period (Replicated im-
plied)
Lake County Illinois
Water Plant Intake
Monthly diurnal
60 samples
Date/Number
Jan 1970/Apr 1971
44 samples
44 samples
44 samples
30-31 May 1972
4 samples
29-30 Jun 1972
8 samples
20 Sep 1972
8 samples
6 Dec 1972
8 samples
Mean Range Source
Industrial Biotest
(1972a)
Table X
9-450 p II A-21
9-460 AAS/SE
7-490
Industrial Biotest
(1972b)
730-940 Table 26, p 128
200-350 Table 27, p 132
330-800 Table 28, p 139
940-1200 Table 29, p 142
AAS/SE
240
210
170
840
260
470
1100
Jan-Dec 1972
350
10-1100
p 173, 186
AAS/SE
102
-------
TABLE 19 (contd.)
Total Iron (ug/1)
Sample Description
Monthly replicate deter-
minations in Southwestern
Lake Michigan
Illinois-Wisconsin State-
line to Waukegan
Date/Number
Jun-Dec 1972
209 samples
Mean
138 14-630
Source
Industrial Biotest
(1972b)
Table A-Z4
p 289
AAS/SE
Monthly intake samples
of Zion Nuclear generating
plant
Monthly duplicates of
two stations. 2.3 mi.
North & 3.2 mi. South
of Pt. Beach Nuclear
Power Plant. 3 depths
each
Jul 73-Jun 77
Sampled Dec, Apr, May
Jul, Aug, Oct.
Monthly survey within
three mile of Kewaunee
Nuclear Power Plant
12 samples per survey
Quarterly analyses
of intakes at Pullian
Power plant on Lower
Green Bay
Monthly replicates
near Hammond Indiana
Bially nuclear plant
Sep 72-Nov73
144 samples
Nov 73-Oct 74
144 samples
Nov 74-Oct 75
138 samples
Nov 75-Oct 76
142 samples
Dec 76-Oct 77
72 samples
1973
1974
1975
1976, 96 samples
Jan-Dec 1973
20 samples
May-Mov 1974
290 samples
1200 13-940 Nalco (1977)
AAS/SE
AAS/FGF
Wisconsin Electric
(1974)
260
200
110
220
<100
93
140
38
79
50-1400
<100-600
<1 00-500
<100-500
100-350
2-950
5-1600
2-300
2-710
Table 5.5-4 p 5
Table 2.3-60/82
p 2.0-74/96
Table 2.0-25/35
p 2.0-49/59
Table 2-25/35b
p 2-57/68
Table 2-2
p 2-33/37
AAS
Nalco (1976)
AAS/SE
AAS/FGF
700 300-1900
44
1-200
Univ. of Wise.
(1974)
Texas Instruments
(1975)
AAS
Dissolved Iron (ug/1)
Three lakewide surveys
surface samples
Aug 69-Jun 1970
54 samples
19 5-56 Copeland & Ayers
(1972)
NAA
103
-------
TABLE 19 (contd.)
Total Iron (ug/1)
Samples Description
Nearshore samples near
Cook Nuclear Power Plant
Monthly replicates near
Hammond Indiana Bially
nuclear plant
Date/Number Mean
Apr, May, Jul 1974 7
& Apr & Jul 1975
88 samples
May-Nov 1974 39
290 samples
2-186
Source
Rossman (1980)
AAS/FGF
Texas Instruments
(1975)
AAS
Lead
Public water supply sources are limited to 50 ug/1 lead. The
recommended IOC objective for lead is 25 ug/1 (Appendix A). This objective
was not violated in any of the samples from our 1977 survey.
The maximum value found was 19 ug/1 at one station near the mouth
of Indiana Harbor while fifty of the 102 samples were below the 6 ug/1
detection limit. An overall mean concentration of 6.6 ug/1 was calculated
by arbitrarily assigning a value of 3 ug/1 lead to all <6 results.
In Table 20 the median of the means is 3 ug/1 and the maximum value
found was 170 ug/1.
TABLE 20
Total Lead (ug/1)
Sampl_e Description
Replicate monthly deter-
minations Southwestern
Lake Michigan
Lake County Water Intake
Kenosha Water Intake
North Chicago Water
Intake
Six hour composites at
the Waukegan Generating
Station during a 24 hr.
period. (Replicates
implied by eight samples
Date/Number Mean
Jan 1970/Apr 1971
44 samples 3 2-6
44 samples 2 1-5
44 samples 2 1-5
30-31 May 1972
4 samples 4 3-5
29-30 Jun 1972
8 samples 3 2-4
Source
Industrial Biotest
(1972a)
Table X
p II A-23
AAS/SE
Industrial Biotest
(1972b)
Table 26p 128
Table 27 p 133
104
-------
TABLE 20 (contd.)
Total Lead (ug/1)
Sample Description
Date/Number
Mean
Lake County Illinois
Water Plant Intake
Monthly diurnal
Monthly replicate deter-
minations in Southwestern
Monthly intake samples
of Zion Nuclear Gene-
rating Plant
Monthly duplicates of
two stations. 2.3 mi.
North ?i 3.2 mi. South
of Pt. Beach Nuclear
Power Plant. 3 depths
each
Sampled Dec, Apr, May.
Jul, Aug, Oct.
Monthly survey within
three mile of Kewaunee
Nuclear Power Plant
12 samples per survey
Quarterly analyses
of intakes at Pullian
Power Plant on Lower
Green Bay
20 Sep 1972
8 samples
6 Dec 1972
8 samples
10
8
5-19
5-18
Jan-Dec 1972
46 samples
Jun-Dec 1972
209 samples
Jul 73-Jun 77
82 samples
Sep 72-Nov 73
144 samples
Nov 73-Oct 74
144 samples
Nov 74-Oct 75
138 samples
Nov 75-Oct 76
138 samples
Dec 76-Oct 77
67 samples
1973
1974
1975
1976 96samples
Jan-Dec 1973
8 samples
5.5
<1-30
2
1
1
14
10
5
1
1
3
10
<1-70
<1-
all
26
<10
Source
Table 28 p 140
Table 29 p 143
AAS/SE
Industrial Biotest
(1972b)
Table 5 p 173
Industrial Biotest
(1972b)
Table A-35 p 290
AAS/SE
Nalco (1977)
AAS/SE
AAS/FGF
Wisconsin Electric
(1972-77)
Table 5.5-4
p 5.0-424/6
Table 2.3-60/82
p 2.0-74/96
Table 2.0-25/35
p 2.0-49/59
Table 2-25/35b
p 2-57/68
Table 2-2
p 2-33/37
AAS/FGF
Nalco (1976)
p 2-32
AAS/SE
AAS/FGF
Univ of Wise.
(1974)
105
-------
TABLE 20 (contd.)
Total Lead (ug/1)
Sample Description
Monthly replicates
near Hammond Indiana
Date/Number
May-Nov 1974
40 samples
Metals Survey Figure 37 July-Aug 77
102 samples
Mean Range
7
-------
TABLE 21 (contd.)
Total Manganese (ug/1)
Sample Description
Six hour composites at
the Waukegan Generating
Station during a 24 hr.
period. (Replicates
implied by eight samples)
Lake County Illinois
Water Plant Intake
Monthly diurnal
Monthly replicate deter-
minations in Southwestern
Monthly intake samples
of Zion Nuclear Gene-
rating Plant
Monthly duplicates of
two stations. 2.3 mi.
North & 3.2 mi. South
of Pt. Beach Nuclear
Power Plant. 3 depths
each
Sampled Dec, Apr, May,
Jul, Aug, Oct.
Monthly survey within
three mile of Kewaunee
Nuclear Power Plant
12 samples per survey
Quarterly analyses
of intakes at Pullian
Date/Number
30-31 May 1972
4 samples
29-30 Jun 1972
8 samples
Jan-Dec 1972
46 samples
Jun-Dec 1972
209 samples
Jul 73-Jun 77
82 samples
Sep 72-Nov 73
144 samples
Nov 73-Oct 74
144 samples
Nov 74-Oct 75
138 samples
Nov 75-Oct 76
142 samples
Dec 76-Oct 77
72 samples
1973
1974
1975
1976, 96 samples
Jan-Dec 1973
8 samples
Mean Range
16 14-17
4 2-6
2
-------
TABLE 21 (contd.)
Total Manganese (ug/1)
Sample Description
Monthly replicates
near Hammond Indiana
Metals Survey Figure
37
Date/Number
May-Nov 1974
287 samples
July-Aug 77
103 samples
Mean Range
Source
Texas Instruments
7
-------
TABLE 22
Total Mercury (ug/1)
Sample Description
Date/Number
Replicate monthly deter- Jan 1970/Apr 1971
mi nations Southwestern
Lake Michigan
Lake County Water Intake 44 samples
Kenosha Water Intake 44 samples
North Chicago Water 44 samples
Intake
Weekly data obtained
Weekly data obtained
at the Waukegan Gene-
rating Station
Six hour composites at
the Waukegan Generating
Station during a 24 hr.
period (replicates
implied)
Lake County Illinois
Water Plant Intake
Monthly diurnal
Jan 72-Dec 72
46 samples
30-31 May 1972
4 samples
29-30 Jun 1972
8 samples
20 Sep 1972
8 samples
6 Dec 1972
8 samples
Jan-Dec 1972
58 samples
Monthly replicate deter-
minations in Southwestern Aug-Dec 1972
149 samples
Monthly intake samples
of Zion Nuclear Gene-
rating Pal nt
Monthly duplicates of
two stations. 2.3 mi.
North ft 3.2 mi. south
of Pt. Beach Nuclear
Power Plant. 3 depths
each
Jul 73-Jun 77
82 samples
Sep 72-Nov 73
144 samples
Nov 73-Oct 74
144 samples
Nov 74-Oct 75
138 samples
Nov 75-Oct 76
142 samples
Mean Range Source
Industrial Biotest
(1972a)
0.75 0.05-2.6 Table X
0.22 0.11-0.51 p II A-23
0.56 0.07-3.0 AAS/Flameless
Industrial Biotest
0.63 <0.05-11.0 (1972b)
Table 21, p 113
AAS/Flameless
Industrial Biotest
(1972b)
0.21 <0.05-0.55 Table 26, p 129
0.05 <0.05-0.13 Table 27, p 133
0.15 <0.05-0.49 Table 28, p 140
0.13 <0.05-0.18 Table 29, p 143
Industrial Biotest
(1972b)
AAS/Flameless
0.12 <0.05-0.46 Table 5, p 173
Industrial Biotest
(1972b)
0.36 <0.05-3.4 Table A-38 p 293
Nalco (1977)
0.67 <0.05-10 AAS/Flameless
Wisconsin Electric
(1972-77)
Table 5.5-4 p 5.0
p 5.0-424/6
Table 2.3-60/82
p 2.0-74/96
Table 2.0-25/35
p 2.0-49/59
Table 2-25/35b
p 2-57/68
0.8
1
0.2
<0.2-20
<0.2-2.3
<0.2-2.2
<0.2-2.2
109
-------
TABLE 22 (contd.)
Total Mercury (ug/1)
iMEl?- Description
Date/Number
Mean
Ranqe
Source
Sampled Dec, Apr,May,
Jul, Aug, Oct.
Monthly survey within
three, mile of Kewaunee
Nuclear Power Plant
12 samples per survey
Quarterly analyses
of intakes at Pullian
Power Plant on Lower
Green Bay
Monthly replicates
snear Hammond Indiana
daily nuclear plant
Dec 76-Oct 77
72 samples
1973
1974
1975
1976, 96 samples
Jan-Dec 1973
8 samples
May-Nov 1974
248 samples
<0.2 <0.2-0.7
0.09 <0.05-2.9
0.08 <0.05-0.89
0.12 <0.05-0.32
0.21 <0.05-8.9
0.19 0.13-0.21
0.3 <0.2-3.4
Table 2-2
p 2-33/37
AAS/Flameless
Nalco (1976)
Table 2.12
p 2-32
Univ. of Wise.
(1974)
Texas Instrument
(1975)
AAS/Flameless
Dissolved Mercury (ug/1)
Three lakewide surveys
surface samples
Aug 69-Jun 70
54 samples
Copeland & Ayers
0.03 0.011-0.057 (1972)
NAA
Molybdenum
There are no water quality or drinking water standards for Molybdenum.
Values from the 136 samples in 1977 resulted in a mean of 2.4 and a
standard deviation of 1.1 The quality control blanks indicated a detection
limit of 2.2 ug/1. Eighty-eight of the 136 samples exceeded this conservative
detection limit. Our values for total molybdenum agree well with the
lakewide survey (Copeland and Ayers 1972) for dissolved molybdenum (Table 23).
TABLE 23
Total Molybdenum (ug/1)
Samp!e Description
Metals Survey Figure 37
Date/Number
July-Aug 77
106 samples
Mean
2.4
Range
Source
This Study
ICAP
110
-------
TABLE 23 (contd.)
Total Molybdenum (ug/1)
Sample Description
Three month composites
of weekly samples from
public water intakes
at Milwaukee, Wise.
and Gary, Indiana
Three lakewide surveys
surface samples
Nearshore samples
near Cook Nuclear
Power Plant
Date/Number
Mean
Dissolved Molybdenum (ug/1)
1962/1967
10 samples
9 samples
Aug 1969/Jun 1970
54 samples
Apr,May, Jul 1974
Apr 8 Jul 1975
54*
13*
2*
12.1
Source
Kopp & Kroner
(1968)
DRS
<11-129 p H6
<13-73 p H7
0.1-4.8 Copeland £ Ayers
(1972)
NAA
2.4-38 Rossman (1980)
AAS/FGF
*Mean of samples above detection limit.
Nickel
The U.S. Canada Great Lakes Water Quality agreements specifies a
maximum Nickel concentration of 25 ug/1 in the boundary waters (Appendix A)
The data from Table 24 show a range of means from <1 to 7.4 ug/1
with a range of values from <1 to 29 ug/1.
From the 1977 survey, only 13 out of 102 samples exceeded the 5
ug/1 instrument detection limit. Eleven of these were from the same
general area of the lake, but since the samples were run in the same
sequence as they were collected, and since one of the 23 quality control
blanks had a value of 11 ug/1 compared to highest sample value of 13
ug/1 the significance of these positive values is questionable.
TABLE 24
Total Nickel (ug/1)
Sample Description
Replicate monthly deter-
mination Southwestern
Lake Michigan
Lake County Water Intake
Kenosha Water Intake
North Chicago Water
Intake
Date/Number
Jan 1970/Apr 1971
44 samples
44 samples
44 samples
Mean
2
2
2
1-5
1-3
Source
Industrial Biotest
(1972a)
Table X
p II A-
AAS/SE
111
-------
TABLE 24 (contd.)
Total Nickel (ug/1)
Sample Description
Six hour composites at
the Waukegan Generating
Station during a 24 hr.
period, (replicates
implied)
Lake County Illinois
Water Plant Intake
Monthly diurnal
Date/Number
20 Sep 1972
8 samples
6 Dec 1972
8 samples
Jan-Dec 1972
40 samples
Monthly replicate deter- Jun-Dec 1972
minations in Southwestern 209 samples
Lake Michigan Illinois-
Wisconsin state line
to Waukegan
Monthly intake samples
of Zion Nuclear gene-
rating plant
Monthly duplicates of
two stations. 2.3 mi.
North 5 3.2 mi. South
of Pt. Beach Nuclear
Power Plant 3 depths
each
Monthly survey within
three mile of Kewaunee
Nuclear Power Plant
12 samples per survey
Quarterly analyses
of intakes at Pullian
Power Plant on Lower
Green Bay
Monthly replicates near
Hammond Indiana Bailly
Nuclear Plant
Jul 73-Jun 77
82 samples
Sep 72-Nov 73
144 samples
Nov 73-Oct 74
132 samples
Nov 74-Oct 75
138 samples
Nov 75-Oct 76
142 samples
1973
1974
1975
1976, 96 samples
Jan-Dec 1973
8 samples
May-Nov 1974
40 samples
Mean
4
3
<5
<5
<5
1
2
Source
Industrial Biotest
(1972b)
2-6 Table 28 p 140
3-3 Table 29 p 143
AAS/SE
Industrial Biotest
(1972b)
-------
TABLE 24 (contd.)
Total Nickel (ug/1)
Sample Description
Metals Survey Figure 37
Date/Number
July-Aug 77
102 samples
Mean
<5
<5-12
Source
This Study
I CAP
Dissolved Nickel (ug/1)
Nearshore samples
near Cook Nuclear
Power Plant
Seventeen kilometer
offshore near Grand
River
Apr, May, Jul ,1974
" Apr ft Jun 1975
88 samples
1971
1 sample
7.4 2.3-18.6
7.7
Rossman (1980)
AAS/Flameless
Wahlgren, Edgington,
Rawlings (1972)
SSMS
Selenium
The Great Lakes water quality agreement specifies 10 ug/1 as a
maximum for selenium to protect raw water for public water supplies.
Applicable water quality and drinking water standards are all 10 ug/1
(Appendix A). The values in Table 25 are below 1 ug/1 except for the
one determination performed with spark source mass spectroscopy (1.3
ug/1). Selenium was not determined on the 1976/77 surveys.
Sample Description
Monthly replicates
near Hammond, Indiana
Bailly Nuclear Plant
TABLE 25
Total Selenium (ug/1)
Date/Number Mean
May-Nov 1974
40 samples
0.8
Source
Texas Instruments
(1975)
AAS/FGF
Dissolved Selenium (ug/1)
Three lakewide surveys
surface samples
Seventeen kilometer
offshore near Grand
River
Aug.69-June70
54 samples
1971
1 sample
Copeland & Ayers
0.08 .03-0.17 (1972)
NAA
Wahlgren, Edgington
1.3 Rawlings (1972)
SSMS
113
-------
Silver
Applicable drinking water standards for silver are 50 ug/1. Illinois
has a water quality standard of 5 ug/1. The IJC has no objective for
silver (Appendix A).
The literature on silver determinations in Lake Michigan is sparse
and appears limited to dissolved silver (Table 26). The lakewide survey
by Copeland and Ayers (1972) found all samples to be within the range of
0.06 to 1.2 ug/1. At the same time they found average sediment values
of 0.67 mg/kg. If this value is representative of the suspended sediment,
then there is roughly 100 to 1000 times as much silver in the water as
there is in the suspended sediment (based on suspended sediment values
of 0.5 to 5 mg/1). Regarding the 1977 survey, 98 of the 104 samples and
all of the quality control blanks were less than the 3 ug/1 detection
limit. Seven ug/1 was the highest value and it was from the 18 meter
contour near the Wisconsin, Illinois state line. Concentrations of 3
ug/1 and 5 ug/1 were recorded off Racine Wisconsin. Values of 3 ug/1
were recorded north of Frankfurt, Michigan. These total silver values are
somewhat higher than the dissolved silver values found by others. Also
they are very near the detection limit, i.e. only one is more than twice
the detection limit.
TABLE 26
Total Silver (ug/1)
Sample Description
Metals Survey Figure 37
Date/Number Mean
July-Aug 1977
104 samples <3
<3-7
Source
This Study
I CAP
Three month composites
of weekly samples from
public water intakes at
Milwaukee Wise, and
Gary, Indiana
Dissolved Silver (ug/1)
1962/
1967
10 samples
9 samples
1.6*
Kopp & Kroner (1968)
DRS
P-H-7
P-H-7
Three lakewide surveys,
surface samples
Seventeen kilometer
offshore near Grand
River
Aug 1969-
June 1970
54 samples
1971
1 sample
0.3 0.06-1.2
1.5
Copeland & Ayers
(1972)
NAA
Wahlgren, Edgington,
Raw!ing (1972)
SSMS
*0ne composite from Milwaukee was 1.6 ug/1 no silver was detected in the other
18 composites.
114
-------
Vanadium
There are no water quality or drinking water standards for Vanadium
(Appendix A).
Of 101 observation and 23 quality control blanks, 6 observations
and 1 quality control blank exceeded the detection limit of 10 ug/1.
All these positive values were found between transects XVI and XIX.
Other investigators found (Table 27) less than 3 ug/1, but this is
the first lakewide survey for total vanadium.
Table 27
Total Vanadium (ug/1)
Sample Description Date/Number Mean Range Source
Monthly replicates May-Nov 1974 <3 all <3 Texas Instruments
near Hammond Indiana 290 samples (1975)
Bailly Nuclear Plant
Metals Survey Figure 37 July-Aug 77 <10 <10-25 This Study
101 samples ICAP
Dissolved Vanadium (ug/1)
Three lakewide surveys Aug 69-June 70 0.2 <.15-0.42 Copeland & Ayers
surface samples 54 samples (1971)
NAA
Zinc
The Great Lakes '^later Quality agreement of 1978 specifies an objective
for total zinc of less than 30 ug/1 for protection of aquatic life (Appendix
A).
Table 28 shows a median mean of 12 ug/1 with an overall range of
0.1 to 370 ug/1. The 1977 survey resulted in 136 samples and 20 quality
control blanks with mean values respectively of 13.6 (S.D = 8.6) and
11.7 (S.D. = 5.0) excluding one outlying blank of 41 ug/1 and two outlying
samples (<1000 & 236).
Most of the references contain no information on quality control
blanks or contamination. Copeland and Ayers (1972) used an all plastic
sampling apparatus and tested their procedure for recovery, but make no
mention of any contamination checks. Rossrnan (1980) used acid washed
sample bottles and carried a filtered distilled water blank from the
storage sample bottle through the analysis, similiar to our quality
control blank. He found an average contamination of 1.4 ug/1 zinc.
115
-------
There are several differences between his procedures and ours so
that it is impossible to state at this time why our blanks were higher
than his or where the contamination in either case was introduced. It
seems likely that much of the zinc in Table 28 is the result of contamination.
TABLE 28
Total Zinc (ug/1)
Sample Description
Replicate Monthly deter-
minations Southwestern
Lake Michigan
Lake County Water Intake
Kenosha Water Intake
North Chicago Water
Intake
Weekly data obtained
at the Waukegan Gene-
rating Station
Six hour composites at
the Waukegan Generating
Station during a 24 hr.
period, (replicates
implied).
Lake County Illinois
Water Plant Intake
Weekly determination
Date/Number
Jan 1970/Apr 1971
44 samples
44 samples
44 samples
Jul-Dec 1972
47 samples
30-31 May 1972
4 samples
29-30Jun 1972
8 samples
20 Sep 1972
8 samples
6 Dec 1972
8 samples
Jan-Dec 1972
58 samples
Jan-Dec 1972
60 samples
Monthly replicate deter-
minations in Southwestern Jun-Dec 1972
Lake Michigan 203 samples
Illinois-Wisconsin state
line to Waukegan
Monthly intake samples
of Zion Nuclear gener-
ating plant
Jul 73-Jun 77
81 samples
Mean Range Source
Industrial Biotest
(1972a)
41 10-100 Table X
160 62-370 p II A-22
8 5-13 AAS/SE
Industrial Biotest
(1972b)
18
-------
TABLE 28 (contd.)
Total Zinc (ug/1)
Sample Description
Monthly duplicates of
two stations. 2.3 mi.
North & 3.2 mi. south
of Pt. Beach Nu clear
Power Plant. 3 depths
each
Sampled Dec, Apr, May,
Jul, Aug, Oct.
Monthly survey within
three mile of Kewaunee
Nuclear Power Plant
12 samples per survey
Quarterly analyses of
Power Plant on Lower
Green Bay
Date/Number
Sep 72-Nov 73
144 samples
Nov 73-Oct 74
144 samples
Nov 74-Oct 75
138 samples
Nov 75-Oct 76
142 samples
Dec 76-Oct 77
72 samples
1973
1974
1975
1976, 96 samples
Jan-Dec 1973
8 samples
Mean Range Source
Wisconsin Electric
(1972-77)
4 <0.5-30 Table 5.5-4
p 5.0-424/6
Table 2.3-60/82
5 2-10 p 2.0-74/96
Table 2.0-25/35
4.7 3-8 p 2.0-49/59
Table 2-25/35b
7 <1-19 p 2-57/68
10
13
10
8.5
8.0
-------
Lake Michigan - 1977
Metals Survey
XVI
XV
STURGEON BAY AF/ '•"
, /*»:/.
t.l • '0
IISTEE
GREEN BAY '
xi
/'•' 1.0
XX
LUDINGTON
XXI
IX
MILWAUKEE
VIII
ZION
WAUKEGAN
LAKE FOREST
CHICAGO
Vllj
vi, V-
MUSKEGON
• GRAND HAVEN
HI
BENTON HARBOR
! • -•
\ • .- i1
\
^ • ,., , «
_,"' / ^S MICHIGAN CITY
HAMMOND
Total Potasium in mg/l
Transect locations are schematic
only. Actual samples were collected
along axis at 9m, 18m, 36m,
and 54m contours.
XVI
> LUDtNGTON
4.3 4.1 4.0 6.0
XXI
t.>
MILWAUKEE
* ,»
>• MUSKEGON
o s.o
• * ^ GRAND HAVEN
4.» 5.1 1.1 |
4.1 4.2 4.5 4.5
III
VI
WAUKEGAN «.«•' ,.»
LAKE FOREST
CHICAGO
..
*-,, /
"•^VP
BENTON HARBOR
•> *•*
»• •
MICHIGAN CITY
HAMMOND
Total Sodium in mg/l
10 5 0 10 20 30 40
10 5 0 10 20 30 40 50 6O 70
figure 37
118
-------
Alkaline-Earth and Alkali Metals
Calcium
There are no recommendations for calcium in the water quality or
drinking water standards although it is cosidered under hardness (Appendix
A). Our 1976 data suggests a seasonal variation in calcium concentrations
in the southern basin. Using the TLVWA calculations and data from Appendix
B spring levels of 35.1 +_ 0.2 mg/1 result for both the partial cruise 1
(transect 6) and for cruise 2. Epilimnetic levels increased from 34.9 +_
.2 mg/1 (Cruise 1) and 35.4 +_ 0.1 mg/1 (Cruise 2) to 37.0 + .3 mg/1 in
June (Cruise 3) and decreased to 36.2 _+ 0.1 mg/1 (Cruise 47 and 33.7 _+
.1 mg/1 in late August 1976 (Cruise 6). Lower calcium values occur only
in the northern most transects near the Straits of Mackinac. Except for
two observations of above 40 mg/1 calcium ranged between 31.9-38.4 mg/1
in the southern basin in 1976 with mean concentrations of 35.5 mg/1.
Higher values tended to be monitored near shore for most of the transects
in the 1977 surveys. The spacial variation of calcium in the 1977 survey
showed variations of less than 2 mg/1 for most transects where samples were
collected at 9, 18, 36, and 54 meter depth contours with higher results
occurring at the 9 meter depth contour. A typical transect in this area
near Holland, Michigan, had values of 36, 34.6, 34.8, and 34.2 mg/1 at the
four depth contours given earlier. There is a suggestion that calcium
values are higher than average in the southern most and southeastern
sections of the southern basin. For the two year period calcium averaged
34.9 +_ 0.1 mg/1 for all samples taken throughout the lake (Table 11).
Magnesium
There are no recommendations for magnesium in the water quality or
drinking water standards although it is considered under hardness (Appendix
A). Using the TLVWA calculations and data from Appendix B, spring concen-
trations in 1976 of 10.7 + 0.05 ug/1 for 32 samples and 11.0 +_ 0.02 mg/1
for 150 samples occurred (Turing the partial cruise 1 (transect 6) and
for cruise 2 respectively. Cruise 3, 4 and 6 with about 60 samples each
resulted in values of 11.1 _+ .04, 11.2 _+ .04 and 11.0 _+ .03 mg/1 in 1976
respectively. Lower magnesium values ( ~ 8 mg/1) occurred in the northern
most transects in 1977. Higher values tended to be monitored nearshore
for many of the transects in the 1977 surveys. Combining 1976-1977
monitoring results gave a mean of 10.8 +_ .9 mg/1.
Potassium
There are no recommendations for potassium in the water quality or
drinking water standards (Appendix A). Using the TLVWA calculations and
data from Appendix B, concentration levels in 1976 of 1.11 _+ .01 mg/1
for 32 samples and 1.06 _+ .004 mg/1 for 205 samples were monitored in
the partial cruise 1 (transect 6) and for cruise 2 respectively. Cruises
3, 4 and 6 showed approximately the same values of 1.01 +_ .01, 1.08 +_
.01, and 1.07 + .01 mg/1 respectively. These levels were characteristic
throughout the Take and in the water column. Figure 37 shows the spacial
consistency throughout the lake including the region near the Mackinaw
Straits in 1977. Combining 1976-1977 monitoring results gave a mean of
1.1 +_ .01 mg/1 (Table 11).
119
-------
Sodi urn
There are no recommendations for sodium in the water quality or drinking
water standards (Appendix A). Using the TLVWA calculations and data from
Appendix B, concentration levels for cruises 1,2, 3, 4, and 6 resulted in a
narrow range of values 4.57 +_ .03, 4.84 +_ .03, 4.87 + .04, 4.73 _+ .03, and 4.59
_+ .02 mg/1 for 32, 149, 58, 61, and 59 samples respectively. Figure 37 shows
the spacial spacial distribution in 1977. Lower sodium values were monitored
in the Straits of Mackinaw and in transect VII between Milwaukee and Chicago.
Occassional high values appear nearshore and in the southern basin. Combining
1976-1977 monitoring results gave a mean of 4.8 _+ 0.7 mg/1 (Table 11).
Fluoride
Fluoride concentrations allowable in drinking water vary depending on
temperature Torrey (1976). Water quality standards permit 1.2 mg/1 to 1.4
mg/1 (Appendix A). Using the TLVWA calculations and data from Appendix B,
concentration levels for cruises 1,3, 5, and 7 in 1976 resulted in a narrow
range of values 0.102, 0.101, 0.103 and 0.099 mg/1 for 33, 57, 61 and 45
samples respectively. Combining 1976-1977 monitoring results gave a
mean of 0.102 _+ .004 mg/1 (Table 11). Maximum level observed was .114 mg/1
which is less than 1/10 of the standards.
Discussion
In examining the 1976 and 1977 Lake Michigan intensive survey data,
a logical interpretation is to link the results of the latter survey to the
earlier one. In doing this, a large and apparently natural removal of phosphorus
occurred between the two surveys.
The discussion will begin with the observed decrease of phosphorus and
suggest that the severe winter and extensive ice cover of 1976-1977 was the
apparent principal causative agent. Subsequent discussion will generally
follow the pattern established by the results section.
Phosphorus
Extensive phosphorus data in the Lake Michigan open waters is quite
infrequent with substantial time gaps between studies. One open lake area
where data has been taken over several year intervals, with five to seven
year gaps intervening between studies, is between Milwaukee and Ludington.
Beeton and Moffett (1964) gave 13 total phosphorus concentration values
for three stations (8, 9, and 11) in this area for 1954 with a mean of 12.7
+_ 2.1 ug/1. The same authors gave data of 15.7 _+ 4.0 ug/1 (n=7) for two
stations (12d, 13a) in 1960 which were east and south of Milwaukee. The
overall average of all stations exclusive of the extreme southern end
was 13 ug/1 for the 1954-55 and 1960-61 period Beeton (1969). It should
he noted that the winter of 1962-63 had 80% maximum percent ice cover,
120
-------
the most extensive on record at that time (Assel et_ al_ 1979), may
account in part for the lower P concentration of the latter studies
assuming a natural cleansing occurred during the 1962-63 winter. Rousar
and Beeton (1973) concluded in reviewing total P data from 1954 through
1971 that the lack of a suitable lakewide water quality monitoring program
and analytical differences prevented drawing conclusions regarding total
P changes. Risley and Fuller (1965) give total phosphate concentrations
as P04 of 20 ug/1 (6-7 ug/1 as P) in this area in 1962-63 with most
of their samples in this area being from 1963. Rousar (1973) reports on
total phosphorus concentration (as P) at three open lake stations at the
4 meter depth between 27 May 1970 and 20 October 1971. His averages
ranged from 8.0 to 8.9 ug/1 for 40 cruises in these two years. Our
results from stations 22, 26 and 27 in the same area of the southern
basin indicate mean surface concentrations at 1 meter depths of total
phosphorus (as P) of 6.7 +_ 0.9 ug/1 (n=26) in 1976 and 5.0 _+ 1.1 ug/1
(n=12) in 1977.
Prior to 1962-63, phosphorus concentrations in Lake Michigan between
Milwaukee and Ludington were higher than current levels with some decrease
occurring between 1961 and the FWPCA study in 1962-63. The pattern in
the area between Milwaukee and Ludington after 1961 is an increase from
1962-63 levels of around 6 or 7 ug/1 to concentrations of 8 to 9 ug/1 in
the early seventies. This declined to 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 +_ .8 in 1976 to
5.2 +_ .2 in 1977. 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. The lake-wide decrease from 1976 to 1977 in both total and total
dissolved phosphorus were significant at greater than 95% confidence
level using Students T Test and the Mann Whitney Test (Zar, 1974) respec-
tively.
The change in phosphorus concentrations between 1976 and 1977 are
of interest due to the unexpected size of the decrease. For the entire
basin the estimated total phosphorus load, from industrial, municipal,
atmospheric, and tributary sources were 6566 and 4666 metric tons in
1976 and 1977 respectively, a decrease of about 2000 metric tons (IJC
GLWQB, 1978). A 1.0 ug/1 annual decrease in total phosphorus corresponds
to a loss of 5000 metric tons from Lake Michigan (Chapra and Sonzogni, 1979).
The 2 to 3 ug/1 decrease in phosphorus concentration observed in the
southern basin between 1976 and 1977, if characteristic of the entire
lake, would suggest a load decrease of between 10,000 and 15,000 metric
tons for the entire lake. Thus, natural causes within the lake appear
responsible for 80 to 85 percent of the decrease in total phosphorus
between 1976 and 1977.
One explanation of this large and apparently natural decrease in
total phosphorus may be the severity of the intervening winter. The
abnormally large amount and duration of the ice cover was unusual for
121
-------
for the 1976-77 winter. 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 ot^ _al_ (1978). Quinn et a]_ (1978), p.l, summarized the
weather and ice condition for the wTTTter 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, assoc-
ated 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 83 percent ice covered,
Lake Michigan over 90 percent, Lake Huron 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 northern part. The bulk of ice cover
was gone by the fourth week of April".
The severe winter appears to have caused some differences in the
lake thermal regime between the two years of this study. Thermal strati-
fication with a discernible epilimnion, thermocline, and cold hypolimnion
appears to have been delayed by the cold winter in 1977. The extent of
thermal stratification on the May 25-June 2, 1976 cruise 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.
If the deposition of particulate matter during the 1976-1977 winter
was enhanced due to the ice cover then many of the observed physical,
biological and chemical changes may have a common and interacting cause.
The ice cover would insulate the water mass from prevailing winds
which are responsible for mixing. Resuspension of sediments may also be
curtailed during ice cover in areas that are normally wind driven (Rodgers
1980). 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 decrease was significant
at tFe 99% confidence level. This change occurred during the period between
cruises ending in 1976 and starting in 1977.
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 • 103 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 • 103 MTs). Presumably this phosphorus could become a loading source
when there is subsequent resuspension during turbulent periods or via chemical
or biological recycling (Rodgers 1980).
122
-------
To look at possible relationships between the effects of severe winters
contributing to the reduction of total phosphorus concentrations in deep
Great Lakes basins, available total phosphorus data were regressed using
annual freezing degree days and maximum percent ice cover for Lake Michigan
and Lake Ontario. Spring total phosphorus concentrations from offshore
cold-core water in Lake Ontario was used from Dobson (1980). An average of
March and April monthly average total phosphate data from the South Chicago
Water Filtration Plant was used with permission (see credits). Annual
freezing degree days (Chicago and Toronto) and maximum percent ice cover
for the period 1968-1979 is used from Assel (1980). Values for the winters
1977-79 were preliminary estimates provided by R. Assel. Maximum percent
ice cover and annual freezing degree days are highly correlated at .86
between Lake Michigan and Chicago, but are correlated only at .63 between
Lake Ontario and Toronto.
The best fit using Lake Michigan information cited earlier showed
that increasing values of the parameter, annual Chicago freezing degree
days was correlated (p>.995) with decreasing total phosphate (as P) concen-
trations at Chicago.
Total P (ug/1) =39.0 - 0.019 (Chicago Annual Freezing Degree Days)
(2.5)1 (0.0029)1
The best fit using Lake Ontario data cited earlier showed that increasing
values of the parameter, maximum percent ice cover, was correlated (p>.995)
with decreasing spring total phosphorus concentrations in offshore cold-core
water in Lake Ontario.
Total P (ug/1) =22.9 - 0.074 (Maximum percent ice cover)
(0.44)1 (0.011)'
These regressions suggest that severe winters help explain a part
of the decrease in total phosphorus concentrations. During the cold
winters in 1976 thru 1979 total phosphorus concentrations have been
observed to decline. An increase in total phosphorus would be predicted
after a mild winter. Increases in total phosphorus concentrations, after
mild winter, from the previous year spring levels have also been observed
in Lake Michigan. (Lake Michigan Water Quality Report 1979, 1980) Snow
(1974) suggests that observed phosphorus concentrations in the near-shore
waters are determined largely by stirring up of bottom sediments which con-
tain phosphorus.
The water sampled by the City of Chicago are more representive of near-
shore conditions than those of open lake waters. However, open lake
decreases found between 1976-1977 in phosphorus concentrations by this
study were also found by the City of Chicago and Illinois EPA (Lake
Michigan Water Quality Report 1979, 1980) in their ten year survey of
south and north shore surveys as well as their open lake survey which
One standard error of the coefficient.
123
-------
ro
SO
40
30
20
10
_L
1966
1967
1968 1969
1970
1971
1972
1973
1974
1975
1976
1977
1978 1979 1980
South Water Filtration Plant
Chicago Water Purification Division
From Seasonal And Comprehensive Chemical Analysis
Total Phosphorus In parts Per Billion
figure 38
-------
consists of 14 sampling points located 10 to 30 kilometers offshore between
Evanston, Illinois and Burns Harbor, Indiana. Chicago's south water
filtration plant record illustrates nearshore decreases in total phosphorus
(Figure 38) which began in the mid seventies. Contributing to the observed
changes in phosphorus concentrations in the Chicago nearshore area over
this decade were phosphate detergent bans implemented by Indiana in
1972-73 and curtailment of municipal and industrial discharges in northeastern
Illinois and northwestern Indiana from 1974-1978 (Lake Michigan Water Quality
Report 1978, 1980).
Silica
The annual silica cycle in the southern basin surface waters of Lake
Michigan shows an apparent decrease in dissolved reactive silica (DRS) in
Lake Michigan over the last three decades (Figure 39). Schelske and Stoermer
(1971) suggest that silica declined over 4 mg/1 from 1926 through 1970 due
to phosphorus enrichment which stimulated high levels of diatom pro-
ductivity depleting available supplies of silica. Edgington et _al_ (1980)
question the validity of the earlier data since there does not appear to
be sufficient amorphous Si02 in the sediments to account for the decrease
of soluble Si02 in the water. If the earlier silica data were accurately
determined, this annual rate of DRS depletion of about 0.1 mg SiOo/yr.
would require phosphorus loads which may not be physically possible
(Johnson and Eisenreich, 1979) unless there are some other silica sinks
which have not been identified such as crystalline forms or increased
standing crops of diatoms.
Seasonal epilimnetic DRS concentration reductions were evident in
the open lake in 1976 and 1977 (Figure 13) reflecting biological activity.
DRS concentrations were reduced to concentrations around 0.2 mg/1 in
1976 and between 0.1 and 0.2 mg/1 Si02 in 1977 in the open lake. Nearshore
DRS levels were reduced to these very low levels along the western shore
in 1976 but not along the eastern shore. In 1977 DRS levels in both
eastern and western nearshore zones were around 0.5 to 0.6 mg/1.
Almost all the deep lake stations, which are least influence by up-
welling effects and cultural impacts, showed declining silica mass between
1976 and 1977 (Rockwell et al_ 1980). The apparent loss of silica in the
deep water stations may Toe" a temporary effect caused by the extensive
ice cover which hindered the normal resuspension and remineralization
of diatom frustules.
The nearshore stations along the western nearshore showed increasing
silica concentrations in 1977 over 1976, while eastern nearshore zones
showed a mixed pattern. Both east and west nearshore zones are influenced
by upwelling. Cruise data show temperature patterns characteristic of
upwelling at various times in both years (Figure 5). To look at possible
relationships between water temperature and DRS, DRS data were regressed
using sample water temperature and water temperature gradients to charac-
terize the effect upwelling may have had on DRS concentrations for all
the cruises in a given year. Water temperature gradients were based on
comparing sample water temperatures at the same or equivalent depths
125
-------
ro
O)
E
Dissolved Reactive Silica
In Southern Lake Michigan
Surface Water
1954-1963-1976-1977
Standard
Error
Mean Value
• 1976
A 1977
Jan Feb Mar Apr May June July Aug Sept Oct Nov Dec
-------
from the nearshore station and a deep water station of the same transect.
The regression equation is of the form DRS = K-j + l<2 • TEMP + l<3 •
A TEMP. If l<3 is significant in the regression equation it would imply
that upwelling helps explain DRS concentration changes.
The station pairs used to determine water temperature gradients and
thus to characterize upwelling along each transect and the zones in
which they were grouped were as follows:
Group 1) (5a, 5) (9, 10) (16, 17) Southern portion western shore
Group 2) (21, 22) (25, 26) Northern portion western shore
Group 3) (6B 6) (13, 12) Southern portion eastern shore
Group 4), (20, 19) (24, 23) (28, 27) Northern portion eastern shore
Regressions for 1976 and 1977 gave results as follows:
Group 1- 1976 DRS = 0.81 - 0.0029 • TEMP - 0.0063 • A Temp
(0.054)1 (0.0031)1 (0.0067)1
Group 1- 1977 DRS = 1.28 - 0.051 • TEMP + 0.00050 • A TEMP
(0.10)1 (0.008)1 (0.011)1
Group 2- 1976 DRS = 0.76 - 0.028 • TEMP - 0.063 • A TEMP
(0.050)1 (0.0033)1 (0.0046)1
Group 2- 1977 DRS = 1.59 - 0.083 • TEMP + 0.0011 • A TEMP
(0.18)1 (0.016)1 (0.0011)1
Group 3- 1976 DRS = 0.39 - 0.015 • TEMP - 0.034 • A TEMP
(0.15)1 (0.0085)1 (0.013)1
Group 3- 1977 DRS =0.78-0.019 • TEMP - 0.055 • A TEMP
(0.20)1 (0.012)1 (0.018)1
Group 4- 1976 DRS =1.31 - 0.045 • TEMP - 0.039 • A TEMP
(0.13)1 (0.0072)1 (0.0096)1
Group 4- 1977 DRS = 1.25 - 0.048 • TEMP - 0.061 • A TEMP
(0.04)1 (0.0032)1 (0.0048)1
The '<3 coefficients for the A TEMP term were characterized as follow
at the 95%' confidence level for the entire cruise seasons in 1976 and 1977:
Groups 1976 1977
1 Not Significant Not Significant
2 Significant Not Significant
3 Significant Significant
4 Significant Significant
The results of the individual regressions by area and year showed
that upwelling had a statistically significant impact, as expressed by
significant A TEMP coefficients, on DRS concentrations in the southern
basin along the eastern shore for both years. Along the western shore
in the southern basin, upwelling had a statistically significant impact
on DRS concentrations only along the northern portion of the western
nearshore in 1976. The multiple regression showed upwelling did not
significantly influence DRS concentration levels in 1976 or 1977 along
standard error of the coefficient.
127
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the southern portion of the western nearshore. This is the nearshore
zone bordering the greater Chicagoland urban complex. The elimination
of the municipal discharges in Lake County Illinois and Northern suburbs
of Chicago would be expected to reduce nutrient loads in the nearshore
zone. These reductions may have resulted in less DRS utilization in 1977.
The analysis presented suggest that the increase of DRS along the western
shore of the southern basin may not be attributed solely to upwelling
leaving open the possibility of other potential factors such as the
elimination of municipal discharges and severe winter impacts.
Nitrate-Nitrogen
Schelske and Roth (1973) show the magnitude of nitrate depletion in
the epilimnion may be proportional to an increasing degree of eutrophication.
To gauge this depletion in the area between Milwaukee and Ludington we have
taken the difference between the epilimnetic winter (or earliest cruise data)
high and summer epilimnetic low nitrate concentration for the years 1962-63
(F.W.P.C.A., 1968), 1970-71 (Rousar, 1973), and 1976-1977 (this study).
These differences ranged from .10-.14 mg/1 in 1977. (Note the overlap
of the 1962-63 and 1977 results which occured after severe winters and
extensive ice cover). Comparisons of the vertical variation within
the deep water stations (Appendix Table C1-C3) show a maxium difference
of .21 mg/1 in 1976 in Southern Basin, .10 mg/1 in 1976 Northern Basin, and
.14 mg/1 in 1977 in Southern Basin. Schelske and Roth (1973) observed a
0.06 mg/1 vertical variation at several deep water stations in the northern
basin. These results would suggest an impacted lake with a gradual worsening
of eutrophication from 1962-63 through 1976 and a return to 1962-63 levels
in 1977. By comparison, Lake Superior, an oligotrophic lake (Beeton, 1969),
had similar surface and bottom concentrations of nitrate which averaged
0.27 mg-N/1 and 0.28 mg-N/1 respectively, Rousar (1973).
The changes in phosphorus and nitrate between 1976 and 1977 were, as
would be expected, accompanied by decreases in phytoplankton numbers and
chlorophyll "a" concentrations. Primary production results (Table 10)
also imply more nutrient limitation and less response to light in 1977
in the Southern Basin.
Chlorophyll "a"
Other studies have shown statistical relationships between phosphorus
and chlorophyll "a" (IJC Upper Lake Reference Group 1976), (Dobson 1976),
(Rast and Lee 1978). Epilimnetic (upper 20m) values of chlorophyll "a"
(ug/1), and total phosphorus (ug-P/1) for all stations (generally 2 KM
or more from shore) in Lake Michigan were related by regression analysis.
Chlor "a" = 1.0 + 0.18 (total P) for 1976 data Southern Basin
(.15)1 (0.019)1
Chlor "a" = 0.41 + 0.24 (total P) for 1977 data Southern Basin
(0.09)1 (0.017)1
Chlor "a" =1.1 +0.14 (total P) for 1976 data Northern Basin
(0.15)1 (0.019)1
'One standard error of the coefficient.
128
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Using these equations in southern Lake Michigan, total P values between
5.5 and 7.7 ug/1 in 1976 and 6.6 and 8.3 ug/1 in 1977 and in nothern
Lake Michigan, total P values between 6.4 and 9.3 ug/1 in 1976 would correspond
to minimum chlorophyll "a" values (2-2.4 ug/1) associated with incipient
mesotrophic conditions (Table 28). The range of oligotrophic to mesotrophic
indicator transition values (6.5 to 10 ug/1-Table 28) is perhaps high for
Lake Michigan total phosphorus concentrations. No significant regressions
relationships between chlorophyll "a" and total phosphorus were noted
in hypolimnetic waters. These results are probably linked to light
limitation in the hypolimnetic waters. Concentrations of chlorophyll
"a", except for "bays" in the Great Lakes, increases from the least
oligotrophic to the more eutrophic in the Great Lakes (Schelske and
Roth, 1973). Lake Michigan falls in the middle of the five Great Lakes
with respect to chlorophyll "a" concentrations.
Phytoplankton
The establishment of long term trends in the phytoplankton of the open
waters of Lake Michigan is difficult due to the widely varying methodologies
employed and the degree of lumping in our data. However, a study in the
southern basin in 1962-63 by Stoermer and Kopcznska (1967) used methodology
very similar to ours. They sampled every 2 to 3 weeks throughout the navi-
gable season and found populations between 125 and 2700 cells/ml at stations
roughly equivalent to our stations 5a, 6, and 16. In 1977 we found total
populations ranging from 1190 to 6000 cells/ml in this area. These estimates
of populations are conservative, since we used only 400 x magnification while
Stoermer and Kopcznska (1967) used 1200x. Total populations in this area
in 1077 were typically 1.5 to 3 times those observed at comparable times
in 1962-63.
Another interesting comparison between Stoermer and Kopczynska's
results and ours is the relative abundance of the major phytoplankton
groups. In 1962-63 diatoms were the numerical dominates at all stations,
and at all depths throughout the 2 year study. In 1976-77 phytoflage!lates
dominated at virtually all stations throughout the study. The diatoms
were the second most abundant group in the spring (April-June) but were
replaced by bluegreen algae in the summer (August) and early fall (September).
Diatoms remained abundant in the nearshore areas in August, 1977 where
higher silica concentrations and lower water temperatures were recorded
apparently as a result of an upwelling event. The effect of this upwelling
on the phytoplankton population can be seen in highly significant positive
correlations between common diatoms (_F. crotonensis, J_. fenestrata, jA.
Formosa) and silica concentrations.
Schelske and Stoermer (1971) have predicted that continued phosphorus
loading would eventually result in an imbalance with available silica supplies.
The phosphorus stimulated diatom population would then deplete the epilimnetic
silica concentrations to the point where silica would become limiting to the
diatoms. They further hypothesized that this would lead to a shift from
diatom dominance to bluegreen or green algae which do not require silica.
129
-------
This apparently occurred sometime between 1962-63 and the summer of
1971 when Stoermer (1974) observed that as much as 80 percent of total
count was bluegreen algae. Unfortunately the difference in methodology
used in studies intermediate between 1962-63 and 1976-77 is such that
trends in this phenonemon can not he more finely determined.
While blue-green algal blooms were not observed in 1976 or 1977,
several genera commonly associated with them such as Anacystis spp.
and Anabaena spp. were abundant in the summer period. However, the
reporting of bluegreen algal forms as filaments and colonies/ml undoubtly
underestimate their numerical importance. Filamentous bluegreens were
abundant at stations 6 and 19 in August and station 24 in September when
Anahaena spp. comprised 21.6 percent (580 filaments/ml), 9.9 percent
(290 filaments/ml), and 5.3 percent (230 filaments/ml) of the total
counts respectively. What was identified in this study as Oscillatoria
limnetica occurred commonly throughout the hasin in April and June and
was especially abundant at station 16 in September, 1977, when it contributed
3.3 percent (200 filaments/ml) of the total phytoplankton.
The significance of what would appear to be a large increase in small
phytofl agellates since 1962-63 is difficult to determine, primarily as a
result of the lumping of these forms as miscellaneous flagellates in our
data. Stoermer and Kopczynka (1967) reported Cryptomonads and other
flagellates as a numerically minor component of the total plankton. However,
Munawar and Munawar (1975; 1976; 1978) have reported small flagellated forms
to be abundant and frequently dominate on a biomass bases in all the other
St. Lawrence Great Lakes. Based on three samples in July 1973, Munawar
and Munawar (1975) reported that phytoflagellates contributed between 6 and
32 percent of the biomass in Lake Michigan. The small size of most of these
organisms indicates that such a percentage of the total biomass would
require large numbers. Claflin (1975) also found small flagellates
(particularly Rhodomanas spp. and Cryptomonas spp.) to be very abundant
in Lake Michigan along a transect between Milwaukee and Ludington in
1970-71. Whether these have actually increased from the early 1960's
or the increase is a result of differences in methodology can not be
determined with the available data.
The abundance of several species of algae would appear to have changed
between previous plytoplankton studies and our 1977 survey.
Synedra acus has been reported as infrequent in the phytoplankton
hy both Alstrbm (1936) and Stoermer and Kopczynska (1967). This commonly
periphytic species, (Lowe, 1974) while a minor component, was along with
Asterionella formosa, the most commonly occurring pennate diatom in 1977.
While most abundant nearshore, it was common throughout the southern basin.
Cyclotel la spp. were common in the plankton in 1977 yet seldom comprised
more than 5 percent of the total and was never dominant. This contrasts
sharply with reports by Schelski et _a]_. (1971) and Holland and Beeton (1972)
that C_. stelligera was among the offshore dominants. That the entire genus
130
-------
was not among the dominants in 1977 may suggest marked decreases in some of the
oligotrophic species associated with this genus. This however, may also be
the result of the low (400x) magnification used in our study, resulting in
underestimates of the smaller Gentries some of which may be as small as 2.5 urn
in diameter (Holland, 1979).
The presence of Cyclotella in areas of severe silica depletion in August
1977 lends support to reports of changes at the species level. Stoermer
and Tuckman (1979) have reported the recent introduction of C^. comensis to
the southern basin. They report that this species is more capable of tole-
rating higher nutrient and lower silica concentrations than most members of
the genus.
Ankistrodesmus falcatus appears to have increased since Alstrom (1936)
reported it as rare in the 1930's. Stoermer and Kopczynska (1967) reported
that it had increased and commonly occurred in concentrations of 20 to 60
cells/ml in the summer of 1962-63. Our data indicate a further increase
with concentrations between 20 and 610 cells/ml in 1977. While occasional
populations of A,, falcatus are found in the warm season plankton of several
types of lakes, large populations are usually associated with eutrophic
conditions (Stoermer and Ladewski, 1976).
The three species of Anacystis reported from Lake Michigan (A..
cyaneae, ]A. incerta, _A. thermal is) are all characteristic of eutrophic
and hypereutrophic lakes. While high populations have been reported from
the Chicago area (Griffith, 1955) these appear to have been localized
phenomena. Stoermer and Kopczynska (1967) reported low numbers (<5/ml)
in the southern basin. Our data indicates that this genus has increased
dramatically since 1963 (Stoermer and Kopczynska, 1967).
Oscillatoria limnetica would appear to have increased dramatically
in recent years. Neither Alstrom (1936) nor Stoermer and Kopczynska
(1967) observed it in any significant abundance. In April and June 1977 0_.
limnetica was extremely common throughout the southern basin in fairly
substantial numbers. There is however, some indication that this species
was misidentified in our data. Stoermer and Ladewski (1976) report
that 0. limnetica has a high ( ~ 18°C) temperature optimum. The other
common species of Oscillatoria in Lake Michigan (0_. mougeotii) is typically
a spring-early summer form. In our data 0_. limnetica was most common in
April and June suggesting that it may have been 0. niougeottl. Unfortunately
the samples have been discarded preventing the verification of _0. limnetica.
Our data indicate that Rhizosolenia eriensis has decreased markedly
since Alstrom (1936) reported it as abundant. However, Holland (1979) observed
it as abundant or dominant for short periods in the spring or early summer
in 1970, 1971, and 1972. It is possible the relative infrequency of our
cruises could have resulted in our missing the short periods of abundance
of this species reported by Holland.
131
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While there were an insufficient number of cruises in either year to
track seasonal trends, the warming and cooling cycle of the lake appeared
to exert a marked influence on both the number and kinds of phytoplankton
present. Both the increase in total phytoplankton and the replacement
of diatoms by blue green algae appeared to follow the thermal cycle with a
nearshore to offshore, south to north trend. Water temperatures around
6°C and above were associated with large increases in diatom populations
(particularly £. crotenensis) and decreased silica concentrations.
Some areas of the southern basin had higher phytoplankton populations
than others in 1977. These were near major tributaries or population centers
and typically corresponded to higher total phosphorus and conservative ion
concentrations. These include the nearshore Chicago area, near Milwaukee,
station 16b just south of Milwaukee, and stations 20 and 20a just north
of the Kalamazoo River. Some of these stations also frequently had
higher populations or greater occurrences of eutrophic forms in 1977.
These include station 5a off Chicago where Diatoma tenue var. elongatum
occurred on all but the September cruise in concentrations between 60
and 170 cells/ml. Station 5a also exhibited the greatest abundance of
Nitzschia spp. with concentrations between 30 (0.9%) and 720 (15.0%)
cells/ml recorded on all four crusies. D. tenue var. elongatum was also
abundant near Milwaukee where it occurred in small (20 to 170 cells/ml)
quantities on all cruises in 1977.
While the majority of the phytoplankton encountered in 1977 are forms
which long have been associated with Lake Michigan, changes in total numbers
of algae and various species indicate continued deterioration of the southern
basin since 1962-63. A recent study by Makarewicz and Baybutt (1980)
reports algal biomass and eutrophic diatoms in the nearshore Chicago
area began to decrease in the rnid seventies. However, that the southern
basin of Lake Michigan is under stress is indicated by the pronounced
shift from diatoms to blue green algae which accompanied epilimnetic
silica depletion in the summers of 1976 and 1977.
Conservative Ions
A potential new problem in southern Lake Michigan is the increasing
concentrations of sodium which presently ranges from 4-5 mg/1 in this
basin. Makarewicz and Baybutt (1980) observed, along with the changes pre-
viously discussed, an increase in relative abundance of blue green algae.
In their data base blue greens (principally Gomphosphaeria and Oscillatoria)
appeared and increased once annual sodium concentrations averaged 4.6 ug/1.
Several species of blue-green algae require sodium, frequently at
concentrations at 4 to 5 mg/1 or above. (Allen, 1952; Kratz and Myers, 1955;
Allen and Arnon, 1955). There is a large body of circumstantial evidence
which suggests that increased monvalent 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
132
-------
greens has been demonstrated by Jensen et_ aj_ (1976). The role, if any, that
increasing sodium concentrations are playing in southern Lake Michigan is an
area where research is urgently needed. Environmental controls which reduce
phosphates, ammonia, cyanide and phenol discharges will result in the dis-
charge of large quantities of conservative ions (Na, Cl , and $04). These
discharges together with road solution sources of NaCl are projected to
ultimately increase Cl concentrations from the current 8 mg/1 to over 19
mg/1 (Richardson, 1980). If sodium increases proportionately, ultimate Na
levels could be greater than 10 mg/1 throughout the lake.
Sodium concentrations averaged 4.8 mg/1 in 1976-1977 (Table 11,
Figure 38). These values were about 20 to 40 percent higher than the
averages observed by FWPCA (1968a) (3.9-4.0 mg/1) in 1962-1963 and by
Beeton and Moffett (1964) during 1954-55 (3.3 to 3.4 mg/1) in the northern
and southern basin. A complete accounting for the increase is not possible
here, however, sodium values tended to be higher nearshore and in the
southeastern part of the southern basin as did chloride concentration.
Increases in conservative ion concentrations have been noted in Lake
Michigan water going back into the 1800's (Beeton, 1965). Long term build
up of chloride, sodium plus potassium, sulfate, and total dissolved solids,
have occurred. As potassium concentrations seems to be a equilibrium around
1 mg/1 (Figure 37), (Torrey, 1976 Dohson, 1976), the increase in sodium
plus potassium must be due to sodium. Our data shows that chloride, sodium,
and sulfate have continued to increase. Of these ions, the rate of increase
in chloride appears to be accelerating.
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 et_ a]_, 1970). The level may have repre-
sented an equilibrium concentration, however, the data were limited and
sampling locations not identified. By the turn of the century, chloride
concentrations had increased to 3.0 mg/1 (Ackerman _et _al_, 1970) in the
southern basin near Chicago. FWPCA (1968a) observed mean chloride concen-
tration of 6.5 mg/1 at deep water stations which they defined as greater
than 10 miles from shore in 1962-63. Volume weighted means in 1976 and
1977 were 3.1 and 8.2 mg/1 respectively. The 1976-1977 values are 21
percent higher than the 1962-63 FWPCA results.
Since data collection began, nearshore chloride concentrations have
tended to increase from the 1930's through the present at rates of at
least .10 + ,01 mg/l/yr. at Milwaukee, Chicago, and Grand Rapids respectively
(Figure 40j. '
Figure 41 illustrates the increase observed between 1962-63
(FWPCA, 1968a) and our 1976 study. In area's B and C concentrations
of 7.2 mg/1 were observed in 1970 by Schelske and Roth (1973). During the
information on these data sources see Powers and Ayers (1967). Water
Quality and Eutrophication Trends in Southern Lake Michigan. Special
Report #30. Studies on the Environment and Eutrophication of Lake
Michigan, J.C. Ayers and D.C. Chandler. Report #30.
133
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last fifteen years the mean rate of chloride accumulation in the southern
basin of the open lake has been between .10 and .13 ug/1. The rate of
increase appears to have roughly doubled (from about 0.05 mg/l/yr 1860
thru 1960 based on Beeton (1969) data to the current rate greater than
0.10 mg/l/yr. The increase in annual chloride concentrations was 0.10
mg/1 between 1976 and 1977, based on averaging cruise TLVWA results in
the southern basin.
In the 1962-63 study elevated chloride concentrations in comparison
with the rest of the lake were higher in areas D and E (Figure 42). While
the 1976 concentrations were higher than in 1962-63, the peaks in areas D and
E are absent probably as a result of the curtailment of brine discharges in
the Manistee area. Higher concentrations of 9 mg/1 to 10 mg/1 were still
observed in the Manistee-Ludington nearshore in 1976. Due to industrial and
municipal loads in the southern most part of the basin, the highest concen-
trations in the open waters were in these areas and tended toward lower
levels going northward (Figure 42). Lowest values, around 7 mg/1, were
found in the Straits of Mackinac where Lake Huron waters mix with Lake Michigan.
Chloride values decline away from shoreline influences throughout the basin.
The rate of chloride accumulation in the open lake between 1962 and 1976
would correspond to loadings between 8.3 x 1(P and 10.2 x 10^ metric tons/yr.
The volume of Lake Michigan's discharge is about 0.01 of the total volume
( ~ 4900 krrr) (Torrey 1976) and discharge concentrations ranged between 7 to
8 mg/1. The annual load of chloride discharged from the lake would be
between 3.4 x 105 and 3.9 x 105 metric tons. The increased annual chloride
burden for Lake Michigan was between 4.9 x 10^ and 6.4 x 10^ metric tons.
The total tributary chloride load to Lake Michigan's basin was 7.1
x 105 metric tons during 1976 (IJC GLBC, 1978). Point-source estimate for
chloride discharge directly to the lake was 2.0 x 10^ metric tons in
1976 (GLBC, 1978). Atmospheric loading of chloride is estimated at 0.83
x 105 metric tons per year (Anders et. jfl_., 1977). The sum of these estimates
(9.9 x 105 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 even-
tually 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 contribute to increase loadings of chloride.
Southern basin sulfate concentration averaged 21.1 mg/1 in 1976.
This value is 30 percent to 35 percent higher than the mean concentrations
of 16 to 18 mg/1 (Beeton and Moffett, 1964) observed in 1960-61 in the
southern and northern basins and 20 mg/1 (FWPCA, 1968a) in 1962-1963.
Atmospheric dry input of sulfate could be as high as 50 percent of the
total load (785 mt.) (Sievering et a]_, 1979) and may be a possible explan-
ation for the slightly higher epTTimnetic sulfate concentrations.
134
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Grand Rapids Lakeshore
10
9
8
.J
3
s
x
s
6
5
1
Filtration Plant Intake ' '«
. ' . . ,
' ',/'' ' • 12
• ^/' • • _, 10
1 •
-X °
/' -c
• • • XX 6
,/''' ' ' 4
940 1945 1950 1955 1960 1965 1970 1975 1980 1985
Years
Chicago south water
Filtration Plant Intake
. Illinois Standard
• ' ,'''''''''"
,,*'''
. ' ,..••''.'''''*' " : ' ''
;;;,<'' '' '
926 1934 1942 1950 1968 1967 1975
Years
oo
08
Milwaukee Linnwood Ave.
Water Filtration Plant Intake
,,
.,,>•''''''
,'•'
'
1930
1940 1950 1980
Years
Figure 40
Chloride Time Series
At Nearshore Water Intakes
Data Taken From
Water Treatment Plant Records
-------
TABLE 29
ENRICHMENT PROBLEM RELATIONSHIPS APPLIED ON LAKE MICHIGAN DATA
Oligotrophic
Mesotrophic Indicator
Transition Values
Mesotrophic-Eutrophic
Indicator
Transition Values
H.H. Dobson Systems (1976)
Summer Total Phosphorus (ug/1)
Chlorophyll "a" (ug/1)
Secchi Depth (meters)
IJC
The Water of Lake Huron & Lake Superior^
Upper Lakes Reference Group (1976) - Volume 1
Total Phosphorus (ug/1)
Chlorophyll "a" (ug/1)
Secchi Depth (meters)
Rast and Lee (1978)
Annual Total Phosphorus (ug/1)
Summer Mean Epilimnetic Chlorophyll
Secchi Depth (meters)
Surveillance & Research Staff
Aerobic Heterotrophs
Aerobic Heterotrophs - nearshore
«15 meters or <3 kilometers)
Aerobic Heterotrophs - offshore
(>15 meters and >3 kilometers)
"a" (ug/1)
8
2
6
6.5
2.4
8.6
10
2
4.6
120
20
19
5
3
14.1
7.8
2.9
20
6
2.7
2000
200
^Estimates of the mid-range of each parameter were made from page 128 of this report.
•j-36 ••••;.
-------
Chloride mg/l
Open Lake Areas
Mean Plus & Minus Three Standard Deviations
**
I
E 1976
E 1962-63
II
«HP^ .M,
LKJHGFEDCBA
Figure 41
-------
The proximity of the urban-industrial area along the southern shore of
Lake Michigan appears to contribute to the slightly higher sulfate concen-
trations in the southern basin (Figure 33). Based upon climatological data,
emissions of a reactive pollutant such as S02 in the Chicago urban-industrial
area would be expected to oxidize to sulfates and impact north and east of
Chicago (Lueck, 1980). Ozone, another reactive pollutant, has had maximum
recorded values near Waukegan, Illinois (Illinois Annual Air Quality Reports,
1976, 1Q77, 1978, 1979). The conversion of S02 to sulfates 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 S02 from higher stack heights
which were put in place during the past decade and from slightly increasing
total S02 emission loads within the Ohio River Basin of 11.5 million tons
in 1970 to 12.8 million tons in 1975 (Stukel and Keenan, 1980).
Sulfate concentrations have been increasing since measurements began.
The rate of increase projected from data in Beeton (1965) is 0.14 _+ 0.03
mg/1 per year starting in 1877 (6 mg/1) and ending in 1961 (18 mg/1).
The intensive surveys completed by the U.S. Department of the Interior
1962-63 and the present -study would indicate that this linear projection,
appears to be holding. The sulfate concentration in Lake Michigan has
risen 15 mg/1 , the most of any ion since 1877. The mean value in the
open water stations in the southern basin during 1976 was 21.1 +_ 0.4
mg/1 , which is well below Indiana's water quality standards for a single
value, which lists 50 mg/1 as desirable and drinking water standard which
permit 250 mg/1. Mean annual rates of increase at the Chicago, Milwaukee
and Hrand Rapids water filtration plants are .18 _+ .01 mg/l/yr., .09 +_
.02 mg/l/yr., and .31 + .06 mg/l/yr. respectively (Figure 42).1 These
rates appear to be accelerating in the nearshore zone over the last five
years with the exception of the Chicago data. A recent source of additional
sulfate ions is the use of low phosphate detergents. These detergents
contain about twice as much sulfate by weight in their builders as phosphate
detergents (Fuches 1978).
Of all the nearshore records only Chicago's data record indicates
approximately the same accumulation rate over the last 10 years. This may
be due to deep well injection of sulfuric acid which resulted in a reduction
of sulfate being discharged from the Indiana Harbor Canal after 1967.
JLH
pH ranged between 7.5 to 8.8 in the entire lake in 1976 and 7.8 to 8.7
in the southern basin in 1977. FWPCA (1968) results indicate a similiar
range (7.5-8.9) in the deep water for 1962-1963. There was little spacial
variation in pH during a cruise. Seasonal increases in pH tended to occur
between June and August probably reflecting the lower C02 solubility in warmer
waters and its utilization in photosynthetic activity. Uhen C02 dissociates
it is a weak acid. Any action that tends to remove it from the system would
increase the pH values. Nearshore waters tended to have lower pH values. In
'op. ct. Power and Ayers.
138
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GO
Chicago South Water
Filtration Plant Intake
1926 1934 1942 19SO 196B 196'
-t 22
o
I
Milwaukee Linnwood Ave.
Water Filtration Plant Intake
Grand Rapids Lakeshore
Filtration Plant Intake
Figure- 42
Sulfate Time Series
At Nearshore Water Intakes
Data Taken From
Water Treatment Plant Records
1940 1945 1950 1966 1960 1965 1970
Years
-------
1976-77 nearshore pH ranged from 7.8 to 8.6 in the southern basin. In 1962-63
FVIPCA (1968) reported a nearshore range of 6.4 to 9.3. The difference between
the 1962-63 data and this study's data probably results from the 1962-63
study including all stations less than 10 miles from shore in the nearshore
category. Our closest nearshore stations are at least 1 kilometer from shore.
The FWPCA network included many stations several hundred yards from shore
and close to harbor mouths including the Calumet River and Indiana Harbor
Canal. pH was approximately .5 units lower in the hypolimnion than in the
epilmnion, reflecting both C02 introduction via respiratory processes and
the lack of its removal via photosynthesis.
Specific Conductivity
Specific conductance decreased during the season in the epilimnetic water.
The lack of seasonal trends in the two layer volume weighted average suggest
there is a transfer of ionic material from the epilimnion to the hypolimnion.
Transparency
Schelske and Roth (1973) report Secchi disc transparencies for all
seasons in the open waters primarily in the southern basin. During
the period 1954 through 1966 annual means ranged from a low of 5.7 meters
to a high of 7.9 meters while annual maxima ranged from 8.8 to 18.3
meters. In 1976 and 1977 we observed means of 5.5 +^ .2 and 5.9 +_ .2
meters in the southern basin with ranges of 2 to 10 meters and 3 to 10
meters respectively. It would appear that secchi disc transparency in
the southern basin has decreased from that observed during 1954 through
1966. The southern basin transparency appears to be more uniform even
in its deeper areas and lacks the clearer deep zone which still exists
in the northern basin. Secchi depth reading at the northern basin deep
water stations (>50 meters) averaged 8.4 meters with a range of 3.2 to
21 meters. This mean annual value for 1976 is greater than the upper
end of the range Schelske and Roth (1973) reported. This may be due to
either the absence of northern basin stations in the earlier summaries
where secchi disc readings would be expected to be greater than the
southern basin or due to the variable influx of Lake Huron water to the
northern lake basin.
Microbiology
Lakes, like all natural bodies of water, maintain an indigenous population
of bacteria that are a regular part of the lakes' biological complex (Welch,
1952). The significance of these microorganisms in the biological, physical
and chemical transformation of materials in both the sedimentary and aqueous
phases of lake systems has been well documented (Brock, 1966; Welch, 1952;).
Much of the bacterial activity observed in these systems is attributed
to heterotrophic bacteria, presumably the most ecologically important
bacteria occurring in most lakes (Cairns, 1971). Heterotrophic bacteria,
microorganisms that require complex organic compounds of nitrogen and
carbon for their metabolic synthesis, are very sensitive to minute changes
of fluctuations in nutrient concentrations. These minute changes in nutrient
140
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concentrations, which may not he easily detectable or which may otherwise
be considered insignificant, are nevertheless important to the microeco-
system in which the bacteria live. The density and biotypes of bacteria in
the aquatic system are directly related to nutrient supply. Thus, hetero-
trophic bacterial densities can be used to indicate the trophic or nutrition
status of lakes.
Previous studies on the distribution of bacterial densities in Lake
Michigan (FWPCA, 1968a) have shown that the central portion of the lake was
virtually free of any detectable levels of coliform bacteria. Hetero-
trophic counts averaged 5/ml. Bacterial densities were shown to increase
sharply in nearshore zones, especially in harbor areas where organic loadings
to the lake were the most pronounced. These patterns persisted in this study.
Heterotrophic bacteria were used in conjunction with a trophic status
evaluations system that included total phosphorus, chlorophyll "a" and
secchi depth (Table 29).
Trophic Status
Many different systems have been developed for characterizing the trophic
status of lakes. Systems of linear relationships based on empirical observa-
tions from many different water bodies have been derived. The systems
which appear to be most aplicable to the Great Lakes are the systems
developed by the Upper Lakes Reference Group (1976), Oobson (1976) and
Rast and Lee (1978). 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
process of eutrophication which these systems attempt to quantify is
non linear and non monotonic. Table 29 provides a summary of the trophic
status indicator values, which were developed for total phosphorus,
chlorophyll "a", and secchi depth by each observer. Table 29 also con-
tain trophic status indicator transition values for aerobic heterotrophs
which are proposed by the Great Lakes Research and Surveillance staff
and is used together with each of the previous systems to expand their
indicator categories to include microbiology.
The consensus evaluation of the three systems was used as the best
estimate for each station. The consensus or median evaluation of the
four parameters was used as the best estimate of trophic status for each
system. An annual trophic status evaluation for each parameter, total
phosphorus, chlorophyll, secchi depth, and aerobic heterotrophs was
developed using the ranges shown in Table 29 for each station using
averages of seasonal data.
The internal consistency of the three parameter systems fails when
two indicators agree and the third disagrees. However, this does not
necessarily mean that the two are correct and the third is incorrect.
It seems appropriate to comment on the tendencies of each system in this
respect. Some changes in the indicator transition values would lead to
more internal harmony. The following observations are based on maximizing
internal harmony for Lake Michigan data.
141
-------
For Lake Michigan water it appears that (1) the Rast-Lee secchi depth
indicator transition value for oligotrophic-mesotrophic (OM) conditions is
more appropriate, .that (2) the Dohson or Rast-Lee chlorophyll "a" indicator
transition value for mesotrophic-eutrophic (ME) conditions are more appro-
priate, and that (3) the Upper Lakes Reference Groups' phosphorus scale
is more appropriate for Lake Michigan at both OM and ME transition values.
A number of authors, including Godlewska and Lippowa (1976) and Rao
and Jurkovic (1977) indicate that aerobic heterotrophs may be a reliable
indicator of trophic status. Analysis of Lake Huron and Lake Superior
open lake bacteriological baseline data (IJC, ULRG Report, 1977 Vols lib
& Illb) suggested 50 org/ml and 300 org/ml as limits for oligotrophic and
eutrophic classification. This however, is based on data using Foote &
Taylor agar with 7-10 day incubation period and is not comparable to the
data derived using standard methods agar and a 48 hour incubator period at
20°C.
A ranking technique was used in order to test the suitability of the
aerobic heterotrophs data as a trophic index and to develop that index.
Geometric means of all 1977 data at each station were calculated and
ranked from the lowest value to the highest. The trophic status of each
station was determined according to the indicies for phosphorus, chlorophyll
"a" and secchi depth. The trophic status of each station was listed
beside its ranked aerobic heterotroph geometric mean.
If aerobic heterotrophs are a good indicator of trohpic status, all
of the o"i igotrophic stations should be associated with low numbers and .
eutrophic stations with the highest numbers. Initially the eutrophic
stations were reasonably well separated but the mesotrophic and oligo-
trophic samples were severely intermixed indicating that it would not be
possible to distinguish between oligotrophic and mesotrophic conditions.
The list was segregated into nearshore and offshore stations. Near-
shore stations are defined as any station with a water depth of 15 meters
or less or within three kilometers of a major shoreline. The trophic
states were reasonably well segregated after this separation which indicates
that aerobic heterotrophs can he used as a trophic state indicator and
that they act differently in nearshore and open lake waters. This is
to be expected because of the distinctions in the nutrient and physical
characteristics of the two water zones which, in consequence, are supportive
of different base levels of bacterial densities. A higher base level of
bacteria exist in the nearshore areas than in the open lake because (1)
drainage from the watershed provides a constant source of fresh nutrients
utilized by bacteria, participate matter (including suspended food stuffs)
which bacteria prefer as a site of adherence, and large numbers of bacteria
representing a variety of species many of which are transitory and therefore
do not persist long enough to spread very far into the open lake, (2)
generally wanner temperatures and nutrients which enhance the growth of
phytoplankton that ultimately serve as a source of food for bacteria and
(3) topographical characteristics such as embayment, harbors, etc., as
well as wind and water currents which tend to retard dispersion of material
and bacteria into the open lake.
142
-------
The open lake on the other hand, has a lower concentration of nutrients,
and vitamins which may be essential to the growth of certain bacteria. Such
growth factors could be expected to break down before they diffused into the
open lake. The open lake is also less affected by contaminating, transitory
bacteria from land drainage. Also, bacteria carried on the water surface
to the open lake area are subject to a prolonged period of exposure to
the bactericidal effects of the ultra-violet portion of sunlight, thus
adversely affecting their numbers. Bacteria in the more turbid nearshore
waters are more protected from this effect.
Figure 43 shows the Lake's estimated trophic status in 1976 and
1977. The majority of Lake Michigan was classified as an oligotrophic
body of water using the method described earlier in both 1976 and 1977.
The mesotrophic ring around most of the lake appeared to diminish in
1977.
Metals
Comparison of the Great Lakes Water Quality Agreement (GLWQA), objec-
tives with our data from Lake Michigan showed there was not a significant
trace metal problem in Lake Michigan as far as water concentrations are
concerned, but there could be through bioaccumulation of these toxics.
An inductively coupled argon plasms emission spectrophotometer (ICAP)
was used to measure metals in Lake Michigan. While lacking the sensitivity
of atomic absorption, the ICAP could be using to determine over 20 metals
in a single operation. The ICAP was therefore used in 1976 on the Lake'
Michigan samples and in 1977 on a 1:10 concentrate (evaporation) of
selected samples. Most of the results were below the detection limit of
the method and many more were suspected because of their proximity to
the detection limit and/or association with quality control blanks above
the detection limit. Of 1040 analyses of lake water concentrates including
quality assurance replicates, there were a total of 12 analyses above the
GLWQA objectives. None of the samples were verified by a second technique.
Recommendations
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
raises the issue of the appropriate long term nutrient monitoring strategy.
There appears to be evidence that Lake Michigan's total phosphorus concen-
tration change in response to extensive winter ice cover is not unique
to this Great Lake. Since meterological 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 limnological response of the system,
the current monitoring strategy is inadequate. It appears that proper
interpretation of long term trends requires annual determinations of the
ice-out conditions on each of the Great Lakes.
143
-------
figure 43
Lake Michigan
Estimated Trophic Status
MUSKEGON
) GRAND HAv/EN
BENTON HARBOR
MICHIGAN CITY
'$$$& Area Not
-.'••V-A-V'-V Studied I
Studied In 1976
Study Area Involved Open Lake Monitoring
In Northern And Southern Basins.
1976
I
Eutrophic
Mesottophi
MUSKEGON
) GRAND HAVEN
f Mesotrophic
BENTON HARBOR
MICHIGAN CITY
Eutrophic
1977
HAMMOND Mesotrophic
£•££•£ Area Not
'#••&& Studied In
Study Areas Included Nearshore Zones At
Milwaukee, Chicago. Calumet And Green Bay.
Open Lake Monitoring In Southern Basin Only.
1977
-------
Within the intensive field year program, observed changes occurring
between cruises indicated the need for biweekly or weekly monitoring at
selected sites. These stations should be monitored to characterize
shorter term phenomena such as phytoplankton succession and nutrient
cycling, and to increase our knowledge of the biological processes essen-
tial to controlling eutrophication reponses of the ecosystem. Less
frequent monitoring can miss species or short lived blooms. Knowledge
of these events are useful in characterization of the lake's 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. This
means that the synoptical nature of a cross lake transect completed
within one day is a reasonable assumption.
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, depostion, and
resuspension processes. To successfully incorporate these mechanisms
and their relationships to winter meteorological conditions, studies of
winter sedimentation rates in deep lakes are required.
Increasing levels of chloride and sulfate concentration will not
threaten drinking water standards during the next several centuries.
However, increasing concentrations of conservative ions are permitting
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 other more eutrophic Great Lakes. In addition, increasing sodium
concentrations may permit certain bluegreen algae species to grow more
rapidly and out compete more desirable food sources for zooplankton
during the summer in Lake Michigan. Studies of sodium and other conser-
vative 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.
In summary our recommendations are:
The nutrient monitoring strategy should be modified to improve the
ability to predict long term effects of phosphorus control remedial
programs. This modification involves:
a) Determining spring ice-out conditions at selected sites on each
of the Great Lakes each year.
b) Adding weekly to biweekly monitoring at selected intensive field
year sites.
c) Conducting limited mid-winter surveys after an intensive Great Lakes
field year.
Expansion of current knowledge in several significant new problem areas
is recommended:
a) Studies of winter sedimentation processes and incorporation of sedi-
ment transport, deposition and resuspension processes into new or
existing lake modes should be undertaken.
145
-------
b) Studies of sodium and conservative ion effect on phytoplankton
in the southern Lake Michgian Basin should be initiated.
146
-------
ACKNOWLEDGMENTS
The manuscript was much improved thanks to the critical reviews of
Dr. Alfred Beeton, Dr. Russell Moll, Dr. Ruth Holland and Mr. Nelson
Thomas.
We wish to thank the other past and present members of our Surveill-
ance and Research Group including Mr. Terry Moan, Mr. David Lueck, Mr.
Stanley Witt, and Dr. James Clark for their help in formulating the
concepts and in preparing this report.
We also appreciate the clarifications that were advanced by reviewers
including Dr. David Edgington, Dr. Herb Allen, Dr. Eugene Stoermer, Dr.
Ronald Rossman, Dr. Claire Schelske, Mr. Steven Chapra, Dr. Andrew
Robertson and Dr. Paul Rodgers.
We want to thank other and present members of Great Lakes National
Program Office secretarial staff for their dedicated secretarial efforts
in typing and modifications of the report including Mrs. Gail Nabasny,
Mrs. Iris Williams, Mrs. Jean Sharp and Ms. Melody Adams who performed
the vast majority of these labors.
It is not possible to thank everyone who were involved in making
available the data from the water filtration plants. However, we want
to note our appreciation for the personal effort that Mr. Donald Hazelswartz,
Grand Rapids; Mr. Donald Stevlingson, Milwaukee; and Mr. Phillip Reed,
Chicago made in providing the water filtration plant data used in this
report.
The bathymetric chart and morphometric parameters were prepared by
Ratko Ristic and Jovanka Ristic and we thank them for their kind permission
to use their work.
147
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Management Strategies for Lake S. RC Loe'nr, C.S. Martin, W. Rast.
Ann Arbor Science.
Rodgers, P. 1980. Personal communication. DePaul University
Large Lakes Research Station Grosse He, Michigan 48138.
Rossman, R. 1978. Abstracts of Papers p. 153-154 International
Association for Great Lakes Research 21 Conference on Great Lakes
Desearch. U. of Windsor, Ontario May 9-11.
Rossman, R. 1980. Soluble Element Concentrations and complexation
in Southeastern Lake Michigan. Journal of Great Lakes Research.
Rousar, D.C. 1973. Seasonal and spatial changes in primary pro-
duction and nutrients in Lake Michigan. Water, Air, and Soil Pollut.
?.: p. 497-514.
Rousar, D.C. and A.M. Beeton. 1973. Distribution of Phosphorus,
Silica, Chlorophyll "a", and Conductivity in Lake Michigan and Green Bay.
Wisconsin Academy of Sciences, Arts, and Letters. Vol 61 p. 117-141.
Schelske, C.L. and E.F. Stoermer. 1971. Eutrophication, silica
depletion and predicted changes in algal quality in Lake Michigan.
Science 173: p. 423-424.
Sche^ke, C.L., E.F. Stoermer, and L.E. Feldt. 1971. Nutrients,
Phytoplankton productivity, and species composition as influenced by
upwelling in Lake Michigan. Proc. 14th Conf. Great Lakes Res. Int.
Assoc. Great Lakes Res. p. 102-113.
Schelske, C.L. and J.C. Roth. 1973. Limnological survey of Lakes
Michigan, Superior, Huron, and Erie. Great Lakes Research Division
Publication No. 17, U. of Michigan, Ann Arbor, Michigan.
Sievering, 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.
Snow, R.H. 1974. Water Pollution Investigation: Calumet Area of
Lake Michigan. Vol IV. USEPA- Great Lakes Initiative Contract Program
EPA-90519-74-011-A.
Stoermer, E.F. 1974. Statement _J_n_: Conference in the matter of
pollution of Lake Michigan and it's tributary basin in the states of
Wisconsin, Illinois, Indiana, and Michigan, 4th session, Chicago, Illinois
19-21 September 1972. Vol. I. EPA, U.S. Government Printing Office
Washington.
Stoermer, E.F. and E. Kopczynska. 1967. Phytoplankton population
in the extreme southern basin of Lake Michigan, 1962-1963. Proc. 10th
Conf. Great Lakes Res. p. 88-105.
153
-------
Stoermer , E.F. and T.R. Ladewski. 1976. Apparent optimal temperatures
for the occurence'of some common phytoplankton species in southern Lake
Michigan. Great Lakes Res. Div., U. of Michigan.
Stoermer, E.F. and M.L. Tuchman. 1979. Phytoplankton assemblage of
the nearshore zone of southern Lake Michigan. EPA-905/3-79-001 Great Lakes
National Program Office. 89p.
Stoermer, E.F. and R.J. Stevenson. 1979. Green Bay phytoplankton
composition, abundance and distribution. EPA-905/3-79-002 Great Lakes
National Program Office. 103p.
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abundance of dominant plankton diatoms in Lake Michigan. Great Lakes
Res. Div. U. of Michigan, Ann Arbor.
STORE! 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.
Strickland, J.D.H., and T.R. Parsons. 1972. A practical handbook
of seawater analysis. Fish Res. Board Canada. Bulletin No. 167.
Strong, A.E. and R.J. Edie. 1978. Satellite observations of calcium
carbonate precipitations in the great Lakes. Limnol. Oceanogr. 23: p. 877-
887.
Stukel , J. and B.R. Keenan. 1980. Ohio River Basin Energy Study
University of Illinois, Champaign, Illinois.
Texas Instruments Inc. Ecological Services 1975. 1974-1975 Annual Report
Bailly Nuclear-1 Site encompassing April 1974 - February 1975. Prepared for
Northern Indiana Public Service Company, Hammond, Indiana.
Torrey, M.S. 1976. Environmental statues of the Lake Michigan region.
3. Chemistry of Lake Michigan. Argonne National Laboratory, Argonne,
Illinois.
University of Wisconsin Green Bay. 1974. Effects of Wisconsin Public
Service Corporation's Pullian Power Plant on Lower Green Bay (January 1973-
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Wisconsin.
Van Slyke, D.D. and A.J. Millen. 1933. Biochemistry, 102, 499p.
Wahlgren, M.A., D.N. Edgington, and F.F. Rawlings. 1972. Determination
of selected trace elements in natural water samples using spark source mass
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1971. Argonne National Laboratory Rep. ANL-7860 Part III.
154
-------
Wisconsin Electric Power Company and Wisconsin Michigan Power Company.
1972-1977. Non-Radiological Environmental Surveillance Program. Point
Beach Nuclear Plant Units Nos. "> and 2. Annual Reports Nos. 1 through 5
(September 1972 through October 1977).
Welch, P.S. 1952. Limnology. McGraw-Hill Book Company.
Yui, A.K. 1978. The VWA data base at the Large Lakes Research Station.
EPA Large Lakes Research Station Grosse He, System Manual.
Tall, D.M., D. Fisher and M.D. Garner. 1956. Anal. Chern. 23: p. 1665.
Zar J.H. 1974. Biostatistical analysis. Prentice-Hall Inc.,
Englewood Cliffs N.J.
155
-------
APPENDIX A
STANDARDS, CRITERIA AND OBJECTIVES FOR THE PROTECTION OF AQUATIC LIFE IN
LAKE MICHIGAN
Values expressed in mg/1 except color (platinum-cobalt units), threshold odor number
(units), pH (units), and oxygen (mg/1 or * saturation). Values are maximum permissible
concentrations except dissolved oxygen and alkalinity which are minimum permissible
(concentrations. Element concentrations are designated as total or soluble only where
clearly indicated as such in the original source. N.R. indicates parameter considered
ibut no recommendation offered; hyphen indicates parameter not considered. Subt. absent
'= substantially absent; Virt. absent= virtually absent.
[Parameter
(Turbidity
{(suspended solids)
Temperature
Color (mont
,0dor
Threshold odor no.
(daily average)
jTotal dissolved solids
(monthly average)
Hissolved 0?
(daily average)
pH range
(Free CO?
jAsbestos
Alkalinity
|Ammonia-N
(monthly average)
un- ionized
Nitrate-N + Nitrite-N
jPhosphorus
Phosphorus, Total
((monthly average)
Hardness
Chloride
(monthly average)
Sul fides, Total
Hydrogen Sul fide
(unassociated)
Sul fate (Monthly
average)
Al'jminum
Arsenic
Arsenic, Total
Barium
Boron
Boron, Total
Cadnium
Cadmium, Total
ids)
f average)
NAS-NAE
Water
Quality
Criteria
1972
25a,b
a
U.S. Canada
Great Lakes
Water Quality
1972*
¥
Subt. absent
U.S. Canada
Great Lakes
Water Quality
1978*
£/
a
Water
111.
£/
a
c/
c/
Quality Standards
Ind. Mich.
¥ ¥
c/ c/
c/ c/
Wis.
a
a/
a/
6.5-8.5e
N.R.
a/
0.1517
200
6.0
6.7-8.5
a/
N.R.
0.002
N.R.
200 k. 180 200 750
172 500
6.0 90% 80% 6.0 5.0
90%
6.5-9.0 7.0-9.0% 7.5-8.5 6.7-8.5 6.0-9.0
25
a -
0.50 0.02 0.05 - f/
0.02
0.020
a/
0.04
0.03
15
10
0.02
0
10.0
0.007
12.0
50
f/
_g/
0.002
0.050
0.0002
0.01
1.0
1.0
0.01
uu
26
0.05
0.01
I/
f/
f/
f/
f/
I/
I/
f/
f/
f/
A-l
-------
(contd.) APPENDIX A
Parameter
Chromium
Chromium, Total
Chromium, Hexavalent
Chromium, Trivalent
Copper
Copper, Total
Fluoride
(monthly average)
Iron
Iron, Soluble
(monthly average)
Iron, Total
Lead
Lead , Total
Manganese
Manganese, Total
Mercury
Mercury, Total
(average value)
Nickel
Nickel , Total
Selenium
Selenium, Total
Silver
Silver, Total
Zinc
Alkyl benzene sulfonates
(daily average)
Methyl ene blue active
substances
Linear alkylate sulfonates
Carbon-chloroform extract
Oil
Oil (hexane-solubles
or equivalent)
Cyanide
Phenols
(monthly average)
Phenolic Compounds
(tainting subst.)
Aldrin
Chlordane
DDT
DDT ft Metabolites
Dieldrin
NAS-NAE
Water
Quality
Criteria
1972
0.05
I/
-
0.03
-
0.0002
0.00005
i/
-
-
I/
-
-
0.2
_
a,h/
I/
0.005
O.I1
0.00001
0.00004
0.000002
_
0.000005
U.S. Canada U.S. Canada
Great Lakes Great Lakes
Water Quality Water Quality
1972* 1978*
- . 0.050
0.005
1.20
0.300
0.3
0.025
-
0.0002
0.025
0.010
-
0.030
-
-
-
_
Subst. absent
-
-
Subst. absent
0.001
0.001
0.00006
0.00003
-
Water Quality Standards
111. Ind.
—
0.05 0.05
1.0
-
0.02
1.4
1.0
0.30
0.15
0.3
0.05
0.05
-
0.05
0.0005 0.005
-
1.0
0.01
0.01
0.05
0.005
1.0
-
0.5
-
0.2
h/ h/
0.1
0.01 0.01
0.001 0.003
0.001
-
« —
-
-
Mich.
LI
LI
LI
0.3
LI
f/
f/
LI
11
f/
LI
1.0
0.2
-
-
-
f/
Virt.
absent
f/
T/
LI
-
f/
Wis.
LI
LI
LI
f/
f/
LI
f/
LI
f/
LI
f/
LI
-
LI
-
-
-
f/
LI
f/
y,
-
LI
A-2
-------
(contd.) APPENDIX A
Parameter NAS-NAE U.S. Canada
U.S. Canada Water Quality Standards
Water Great Lakes Great Lakes 111. Ind.
Quality Water Quality Water Quality
Criteria 1972* 1978*
1972
Aldrin fi Dieldrin
Endrin 0.000002
Heptachlor 0.0000001
Heptachlor Epoxide
Lindane 0.00002
Methoxychlor 0.000005
Mi rex
Toxaphene 0.00001
Phthalic Acid Esters
Di butyl phthalate
Di (z-ethylhexyl)
phthalate
Other phthalic
acid esters
Polychlorinated 0.000002
hiphenyls, total
Other organic
compounds
Diazinon
Guthion
Parathion
Other Pesticides
. 0.000001
0.00002
0.000001
0.000001
0.00001
0.00004
11
0.00008
0.004
0.0006
0. 0002
n/
i/
0.00008 I/
0.000005 I/ -
0.000008 I/ -
m/
Mich. Wis.
_
f/
f/
-
f/
f/
-
I/
-
-
-
f/
-
-
-
-
™
_
f/
f/
-
f/
I/
-
I/
-
-
-
JV
-
-
-
-
"
*Although the Treaty between the United States and Canada (U.S. Treaties, etc., 1972) does not
apply to Lake Michigan, those objectives are included for comparison.
a. See Torrey (1976) or state sources listed below for discussion and clarification.
b. Maximum concentration of 25 mg/1 suspended solids offers a high level of protection.
c. None other than of natural origin.
d. Limit recommended for cold-water streams and oligotrophic lakes.
e. Nearly maximum level of protection.
f. Permissible levels shall be resolved in accordance with the methods specified in "Water
Quality Criteria, Report of the National Technical Advisory Committee to the Secretary of
the Interior, April 1, 1968."
g. \quatic life should be protected in hard water (total hardness = 100 mg/1 as CaCo^} if
cadmium is 0.03 mg/1, and in soft water (100 mg CaCQ^/l) if cadmium is 0.004 mg/1. Habitats
shnu"M He safe for crustaceans or eggs and larvae of salmon if cadmium is 0.003 mg/1 in hard
water or 0.0004 mg/1 in soft water.
h. f^o visible oil on surface.
i. Applies only to fish.
j. LPSS than detection level.
k. Not to exceed present levels.
1. For protection of aquatic life.
m. Concentration should not exceed 0.05 of the median lethal concentration or a 96-hour test
for anv lira! sensitive species.
n. Not to exceed 0.1 microgram/gram for the protection.
Sources: National Academy of Sciences ..., 1973; U.S. Treaties, etc., 1972; Illinois Pollution
Control Board, 1974; Indiana Stream Pollution Control Board, 1973; Michigan Water Resources
Commission, 1973; Wisconsin Administrative Code, 1973 as quote in Torrey, 1976; and Great Lakes
Water Quality Agreement of 1978.
A-3
-------
APPENDIX B
MICROFICHE - LAKE MICHIGAN
INTENSIVE SURVEY DATA 1976-1977
Errata Units for nearshore primary product!tvity are
milligrams/m^/hr
B-l
-------
APPENDIX C
Vertical Chemical Variation at Open Lakes
Stations 1976-1977 by Basin
C-l
-------
O
2
5
10
20
50-165
2
5
10
20
iO-165
2
5
10
20
50-165
2
5
10
20
50-165
2
5
14-20
22-32
90-165
I
5
15
20
25-35
84-165
2
5-15
20-28
95-130
2
5-15
20-28
95-130
Conduct ivity
(3) 1.6+.7
(3) l.O+.O
(3) 0.9+.1
(3) l.l+.l
(7) 0.8+.1
(9) 1.2+.2
(9) 1.2+.2
(9) 1.0+ 2
(9) .5+.0
(9) .5+.0
(9) .8+.1
(») .9+.1
(9)1 .2+. 1
~"
(9) 20+3
(9) 20+3
(12) 1^7.2
(13) 1.9+.I
(13) l.'+.2
(9) 2.S+.2
(9) 2.6+. 2
(7) 3.0+.2
(9) 2.9+. 2
(11) 3.0+.2
(13) 1.5+.1
(9) 1.7+.1
(11) 1.7+.1
(7) 1.8+.1
(2) 1.5+.1
(3) l.l+.O
(4) 0.9+.1
(5) 0.9+.0
(5) 1.2+.1
(3) 4.5+. 3
(3) 4 l+.l
(3) 4.1+.2
in tol'.i
(9) 7.3+. 5
(9) 6.2+. 5
(9) 5 5+.3
(22) 4 5+.1
(9) 13.0+ 7
(9) 12.7+ 7
(9) 12.4+.7
(9) 7.7+,4
(22) 5.4+. 1
(9) 17.3+.2
(9) 16.8+.3
(9) 15.3+.3
(9) 8.7+, 7
(9) 19.6+0.4
(9) 19.4+0.3
(13) 10.371.2
(13) 4.6+0.1
(9) 21.4+ .4
(9) 21.3+ .3
(7) 20.1+ .5
(9) 15.0+ .9
(11) 8.2+ .3
(13) 5.2+ .1
«,) 19.9+ .1
(11) 19.7+ .2
(7) 8.7+ .4
(12) 5.8+ .2
(3) 13.7+0.6
(4) 13.6+0.6
(5) 9.8+1.4
(5) 4.5+0.2
(3) 27J+1.0
(3) 274+. 6
(3) 275+. 9
(7) 274+ 0
(9) 272+. 5
(9) 2727.4
(9) 273+. 4
(9) 273+. 2
(9) 272+. 3
(9) 272+ 4
(9) 272+. 2
(9) 273+ 3
(22) 274+. 3
(9> 270+.5
(9) 270+.5
(9) 270+.3
9\ ^' — '-
(9) 270+ .6
(9) 269+ .7
(14) 270+ .6
(13) 27J+ .7
(13) 276+ .2
(9) 261+0.".
(9) 262+0.5
(7) 263+1.0
(9) 270+1.4
(11) 274+0.3
(13) 275+0.3
(9) 263+0.7
(7) 27271.9
(12) 275+0.3
(3) 270+0.7
(4) 270+0.6
(5) 273+1.5
(5) 278+0.5
(3) 7.9+. Ob
(3) 7.9+.03
(3) 7.9+. 09
(3) 8 0+.03
(7) 8.0+.05
(9) 8.2+. 04
(9) 8.2+.05
(9) 8.17.05
(9) 8.1+.03
(9) 8.2+.03
(9) 8.2+.03
(9) 8.2+.03
(9) 8.1+.04
(22) 7.9+. 02
(9) 8.4+. 02
(9) 8.4+. 01
(9) 8.4+.03
_2\ 7*9701
(9) 8.4+. 03
(9) 8.4+. 03
(13) 7.9+.02
(9) B.2+.06.
(9) 8.2+.06
(7) 8.2+.09
(9) 8.1+.07
t
ALK NHrN TKN-N N"2+NOj-N Total P Chloride
mg/1 up/1 ros/1 f ***!* uv;^1 TOR'1
(3) 105+.3 (3) 5.3+1.3 (3)
(3) 105+.3 (3) 40+0 (3)
(3) 105+ 3 (3) 4.0+ 0 (3)
(3) 106+1.0 (3) 4.0+ 0 (3)
(7) 106+.4 f3) 4.0+ 0 (3)
(9) 105+1.0 (9) 3.0+0.4 (9)
(9) 104+.6 (9) 2.8+0.3 (9)
(9) 104+.6 (9) 3,2+0.6 (9)
(9) 104*. 4 (22) 4.3+0.4 (22)
(9) 107+.1 (9) 3.1+0.1 (8)
(9) 107+.2 (9) 3.0+ 00 (8)
(9) 107+.5 (9) 3.2+0.1 (8)
(9) 107+.4 (9) 3.0+ 00 (8)
(21) 107+.2 (21) 6.1+0.7 (20)
(9) 105+.3 (9) 3.3+0.2
(9) 106+ 1 (9) 3.6+0.2
(9) 106+.2 (9) 3.3+0.4
(9) lOf>+.4 (9) 4.7+0.8
(22) 106+.4 (20) 5.0+0.4
4
(9) 106+ .5 (7) J.6+U,
(9) 106+ ,8 (7) 3.6+0.4
(14) 106+ .3(11) 6.4+1.4
(13) 108+ .2(10) 3.0+ 0
(9) 102+ .5 (8) 3.8+0,8
(9) 102+ .4 (8) 3.5+0.4
(7) 103+ .6 (8) 8.0+1.2
(9) 106+ .9 (8)28.0+4.8
(U) 109+ .3(10)23.7+5.8
(13) 108+ .4(12) 3.2+0.3
(9) 103+0.9 (6) 3.3+0.2
(6) 107+1.1 (6) 6.5+2.4
(12) 110+0.5 (12) 4.7+l.b
(3) 107+ .1 (3) 3.0+.00
(4) 10b+ .2 (4) 3.0+.00
(5) 107+ .7 (5) 3.0+.00
(5) 109+ .2 (5) l.O+.OO
.21 + . 07
.IJ+.02
.11+ 01
.137.02
.16+.01
.15+.01
.15+. 01
.14+.01
.14+. 02
.12+.01
.15+. 01
.21+. 02
.21+. 02
.31+, 09
.15+.01
(3) .260+. OOf.
f3) .2577.007
(3) .260+. OOf.
'3) .2577.007
(7) ,2607.003
CruUe ft 1976
(6) .230+.010
(6) .227+.009
(6) .235+. 008
(6) .327+. 084
(14) .254+. 004
Crulie »3 1976
(7) .199+. 005
(7) .19 +.004
(7) .217+. 004
(7) .217+. 004
(7) .252+. 002
Crul.e *4 1"76
(9) .138+. 004
(9) .136+.004
(9) .138+ 004
(9) .177+. 005
(20) .268+. 004
Lruise ft 1 976
(9) .l.'+.OUi
(9) ,12+. 003
(14) .13K004
(13) .1»I 012
(13) .28?. 008
Crulae #b '976
(9) .09+, 004
(9) .09+ 004
(7) .094 006
(9) .1W 017
(11) .23<.01b
(13) .30+. 001
Cruise »' 1»76
(9) ,10+ OQ5
(11) ,11+,014
(7) .25+. (116
(12) .30+.006
Crul.e »R 1976
(3) 8.3+1.9 (2) 8.0+.15
(3) 8.7+1.7 (3) 7.9+. 06
(3) 6.7+0.3 (2) 7.9+.00
(3) 6.7+0.9 (3) 8.0+.07
(3) 8.4+1.2 (7) 8.0+.07
(9) 5.2+0.3 (9) 7.9+. 05
(8) 6.2+0.7 (9) 7.9+.06
(9) 6.2+0.6 (9) 7.9+. 05
(9) 6.8+0.9 (8) 7.9+. 06
(22) 6.1+0.3 (23) 7.8+. 02
(8) 6.4+0.8 (9) 7.9+. 04
(6) 6.9+0.7 (9) 7.9+. 03
(8) 6.6+0.5 (9) 7.9+.04
(8) 6.3+0.5 (9) 7.9+. 04
(20) 6.0+0.7 (22) 7.8+.02
(9) 6.7+0.6 (9) 8.1+.05
(9) 6.2+0.3 (9) 8.1+.04
(9) 8.5+0.6 (9) S.1+.04
(9) 9.2+0.3 (9) 8.1+.04
(21) 8.3+0.7 (22) 7.9+.02
(9) 6.0+0.4 (9) 8.2+.04
(9) 7.3+0.4 (9) 8.2+. 10
(14) (1.7+0.6(14) 8.0+.03
(13) '8.3+0.5(13) 8.0+.03
(13) 10.4+0.5(13) 8.0+.04
(9) 5.6+0,4 (9) 8.1+.06
(9) 5.6+0.4 (9) 8.1+.06
(7) 4.9+0,5 (7) 8.1+.05
(9) 6.4+0.5 (9) B.1+.05
(11) 6.6+0.4(11) 8.0+.05
(13) 9.3+0.9(13) 7.9+.03
(9) S.2+0,2 (9) 8.2+.05
(11) 6,2+0.7(11) 8.2+.04
(7) 6.9+0.6 (7) 8.1+.04
(12) 8.9+0.7(12) 8.0+.05
(3) 12 6+7.0 (4) 7.9+. 19
(4) 6.0+0.4 (5) 8.0+. 17
(5) 6.2+0.5 (5) 7.8+.16
(4) 12.0+1.7 (5) 8.0+.06
80 Meters, 1976
Dlss. Reactive
Silica** ins/1
(2) 1. 32+. 005
(3) 1. 33+. 012
(2) 1. 32+. 010
(3) 1. 34+. 003
(7) 1. 36+. 018
(9) .10+. 06
(9) .11+. 06
(9) .11+. 06
(9) .147.04
(22) .30+. 04
(9) .81+. 06
(9) .83+.05
(9) .817.06
(9) .747.03
(21) 1.45+.09
(9) .45+. 04
(9) .44+.04
(9) .43+.04
(9) .42+.04
(22) 1.46+. 11
(9) 0.26+.02
(9) 0.26+.02
(14) 0.27+.01
(13) 0.45+.06
(13) 1.77+.09
(9) 0.30+.01
(9) 0.33+.02
(7) 0.34+.02
(9) 0.41+.04
(11) 0.63+.06
(13) 1,89+. 10
(9) 0.30+.01
(11) 0.32+.02
(7) 0.61+.05
(12) 1.84+.08
(3) 0.50+ 03
(4) 0.51+.02
(5) 0.72+.12
(5) 2.21+.17
A>-iobic
Hi-UTottop
(3) 3+2
(9) 4+1
(1) ~l
(17) 3+1
(9) 6+1
(18) 17+5
(9) 4+8
(6) 17+5
(3) 18+12
(9) 17+4
(9) 21+4
(7) 8+2
(2) 14+9
(2) 11+3
(9) 9+2
(6) 7+2
(6) 7+1
(3) 2+1
(3) 2+1
(3) 3+1
Si'i tt'l
8 "
-------
TABLE C2
Lane Michigan Northerr Ba£ir. Stations* with Total Depth Greater Thar SL mete
o
oo
(Number of Samples
Depth
N
Mater
Te
•p C
Conductivity lou!
NIcranhi/M pH Alk
Dissolved
at 25°C SO «9/l '1^/1"
Dissolved Total
NO?.NUi-N P
naf
m
,/f
U9/I
s
Tot-Dls Total Chloride Olss. Reactive
P Suspended ^ Sl)1ca
U9/1 Carbon («9/l) m^/\
Suspended Chlorophyll
Silica ug/l
•9/1
•t- Seech t
Depth
N
Cruise 1- Apr!)
0-6 (13) 3.0*.
6-12 (13) 3.07.
12-24 (13) 3.0*.
24-36 (5
36-60 (15
60-100 (16
100-175 (19
175-275 (7
2
2
9*.
97.
3.07.
3.|7.
3.37.
(3)8.3.
(3)8.3.
(3)8.37
(2)8.3*
(3)8.3*
(4)8.37
(6)8.37
-02 (13)110.0.4 (7) S.I. 0. (131.230.
•01 ~ (II) 4.17 0. (13). 23)7
•02 (9) 7.77 3. Il3).23l7
.04
.04
3) 5.0. 1. (5
.1 (14
14) 4.8 > 0.7 (14
14)11.7 i .4 (14
28)17.2 i 1.0 (28
14 17.3 t .2 (14
15)14.9 t 1.9 (14
14)10.8 i 2.2 (14
26) 8.8 1 1.0 (31
22) 0.0 i 0.8 (31
(7) 3.3 . 0.4 (9
15) 7.9 t 0.6 (IS
(4) 6.2 t 0.8 (4
12) 6.6 t 1.0 (12
n) 1.0 t 0.4 (26
24 7.6 » 0.4 (27
19)16.5 t 0.7 (\'l
.'«) 4.9 i 0.4 (32
23) 4.8 t U.3 (30
(7) 4.3 I 0.9 (•)
.121
.127
.142
.185
.200
.224
.239
.^45
.264
.269
.141
.142
.143
.173
.201
.257
.264
.272
.267
.003 (14
.UUo (14
.006 (14
.006 (2U
.007 (14
.007 (IS
.006 (14
.004 (Jl
.003 (31
.004 (9
6.9
7.6
8.0
9.2
9.7
8.1
6.1
7.0
9.7
11.8
.002 (10)
.002 (31
.003 (9!
.009 (20]
.009 (21
.004 (12
.002 (U\
.002 (22]
.004 (6)
7.2
6.6
7.0
7.9
7.4
6.0
6.B
9.2
12.2
SI M
S! N
8:! Is!
0.6 13
11 i-
1.0 (9)
3.5. .3 (}«
3.4 « .3 <
3.5 , .5 «
4.0 * .3 '
4.0 « .6 «
3.5 « .3 *
3.5 , .2 <
3.7 * .2 '
5.9 t .3 I 3
7.2 t .6 <8
0.319
0.268
0.280
0.331
0.308
0.200
0.160
0.110
0.090
0.099
Cruise 5- October
0.9 (3)
2.0 ,
0.6 I2'
!'.! (»>
0.9 (6
0.6 (15)
1.0 (25
2.9 (9)
47*1? (15)
4.7 « 1.2 (J
2.5 t 0.5 I?
3.1 « 0.3 3
2.6 « 0.2 J
2.5 t 0.2 (JJ
5.3 t 1.4 '}
4.9 « 0.4 ( O
6.3 « 0.9 (9)
0.259
0.263
0.260
0.180
0.180
0.178
0.122
0.096
0.131
.026 0
.068 jl
.094 (1
.018 (2
.021 (1
.018 (1
.007 (1
.015 3
.005 (3
.013 (
1) 7.9 0.03
• 7.9 0.03
1 7.8 0.02
1) 7.8 0.04
1 7.8 0.08
> 7.8 0.08
1 7.7 0.08
7.8 0.05
7.8 0.07
)) 7.9 0.02
.010 (15
.018 (4
.020 (12
.011 (26
.008 (27
.018 (19
.007 (32
.004 (30
.018 (9
8.0 t 0.07
8.0 t 0.04
8.0 > 0.03
8.0 t 0.02
8.0 t 0.02
7.9 t 0.02
7.9 t 0.02
7.9 t 0.02
7.8 t 0.03
14)0.17 i .02 (
14)0.20 t .04
13)0.20 t .03
28)0.37 l .04 j
14)0.41 t .06
15)0.59 l .06
14)0.84 t .05
31)1.01 t .05
31)1.51 t .07 -
(8)1.68 t .17
3)0.26
4)0.31
4)0.38
7)0.42
4)0.44
4)0.50
4)0.47
1)0.55
1)0.72
9)0.51
15)0.36 i .02 (|5)0.32
(4)0.32 t .02 (4)0.30
12)0.35 « .03 (12)0.28
26)0.50 t .05 (26)0.28
27)0.60 l .05 27)0.29
19 0.84 t .04 (19)0.25
32)1.15 . .05 (32)0.39
30)1.59 « .07 (29)0.53
(9)2.04 « .22 (9)0.55
.02 (
.03
.03
.02
.03 |
.03 |
.02
.06
.07
.09
14)1.21
14)1.44
14)1.89
14)1.44
14)2.55
15)2.01
14)1.38
31)0.86
31)0.42
(9)0.15
.02 (
.07
.03 (
.02
.02
.02
.03
.04
.07
13)0.97
(4)1.00
10)0.95
25)0. 75
25)0.54
16)0.22
31)0.13
31)0.12
(9)0.07
.07 (14)6.1 t .5
.08
.16
.08
.23
.14
.07
.06
.04
.03
.13 (4)6.5 t .1
.04
.07
.06
.05
.03
.01
.02
.01
•Northern Basin Stations Umbers 4. 7. 8. 9. 14-20. 23. 24. 27. J4-J/. 42. 67. 68
-------
Lake Michigan Southern Basin Stations* With Total Depth Greater Than 80 Meters, 1977
'(Number of samples) mean +_ std error of mean)
O
1
M
2 (8)
5 (9)
10 (9)
20 (9)
50 (^
95-141 (12)
2 (9)
5 (9)
10 (10)
20 (9)
50 (7)
67-135 (9)
2 (9)
5 (9)
10-15 (10)
16-21 (10)
22-25 (7)
75-153 (9)
2 (9)1
5 (9)1
10-15 (8)1
,7-20 (8)1
^2-30 (11)1
76-152 (13)0
TU
- 0 — 0 — —
+1+1 +1+1 +1+1
.7+. 1
'.7+!o
.7+.0
.7+.U
.6+.1
.7+.1
.6+. 1
.7+ 1
.7+.0
. 3+. 1
. 3+.1
.2+. 2
.2+.1
. 3+.1
.8+.1
Water
Cf
(9) 2.6+0.2
(8) 2.3+0.2
(8) 2. HO. 2
(8) 2.2+0.2
(8) 2 2+0.2
(13) 2.1+0.2
1
-------
APPENDIX D
Biological Data
D-l
-------
TABLE D1
COMMON PHYTOPLANKTON SPECIES
SOUTHERN LAKE MICHIGAN
Cruise 1 (April 19-24, 1977)
STATIONS
Species
Cyclotella spp.
Diatoms tenue var. elongatum
Fragilaria crontonensis
Fragilaria intermedia
Melosira spp.
Nitzschia spp.
Rhizosolenia longiseta
Synedra acus
Synedra ulna
Synedra spp.
Tabellaria fenestrata
Cryptomonas erosa
Cryptomomas ovata
Cryptomonas spp.
Dinobryon spp.
Miscellaneous flagellates
Oscillatoria limnetica
Ankistrodes.-.ius falcatus
Oocystis spp.
Percent of Total
Total Diatoms
Total Flagellates
Total Blue Green Algae
Total Green Algae
Tnt.al Phvtonlankton
t
#/ml
on
OU
91 n
L ID
en
DU
pyn
o/U
on
OU
390
o.in
O 1 U
inn
IUU
150
9qn
L y\j
inn
1 UU
60
270
en
DU
830
9n
£(J
inn
A f\
40
2840
2210
100
240
5390
>a
1 C
I . o
O. J
1 1
1 • 1
i e 9
1 o. <_
1 C
1 . D
7.2
C 0
J. O
1 Q
1 .0
2.8
fi i
i P,
1 . o
1.1
5.0
1 A
1 . H
16.1
On
. 4
i a
1 . O
07
. /
74.6
52.7
41.0
1.8
4.4
E
#/ml
9.0
1 90.
1 i.\J
°,n
550
140
60
•^n
9.n
OU
140
n 10
4 1 U
960
on
OU
1370
1540
60
60
3030
ib
i n
1 . U
4n
• U
i n
1 . U
Q f\
y* o
18.1
4 6
2.0
1 0
1 . U
i n
1 « U
i n
1 . U
4.6
IOC
1 O. -J
31.7
i n
1 . U
94.1
45.0
50.8
2.0
2.0
c
#/ml
"3Rfl
200
60
on
OU
30
200
290
120
880
550
0
120
1550
99
J
12
C
3
i
i
1
12
18
7
98
56
35
7
% #/m'
c
.9
Q
. O
.9
-. .
Q I
•o «
•9 -1
.7
.7
.1
.8
.5
0
.7
6 (
% #/m
29Q
200
30
30
60
30
3
30
3 60
230
670
200
700
1020
0
260
1980
5a
o/
14 6
10.1
1 5
1 .5
3.0
i 5
1.5
3.0
1 1 6
33.8
10.1
92.4
35.3
51.5
0
13.1
(
#/m
90
60
1450
170
200
120
200
90
90
30
30
290
290
1250
200
140
2500
2500
260
230
4910
5b
i «
1 2
29 5
3.5
4.1
2.4
4.1
1.8
1 .8
0 6
0.6
5.9
5.9
25.4
4.1
2.3
95.7
50.9
39.1
5.3
4.7
-------
o
I
CO
TABLE Dl
COMMON PHYTOPLANKTON SPECIES
SOUTHERN LAKE MICHIGAN
Cruise 1 (April 19-24, 1977)
STATIONS
Species
Asterionel la formosa
Cyclotella spp.
Diatoms tenue var. elongatum
Fragilaria crontonensis
Fragilaria intermedia
Melosira spp.
Nitzschia spp.
Rhizosolenia longiseta
Synedra acus
Synedra ulna
Synedra spp.
qabellaria fenestrata
Cryptomonas erosa
Cryptomomas ovata
Cryptomonas spp.
Dinobryon spp.
Miscellaneous flagellates
Oscillatoria limnetica
Anki strodesmus falcatus
Oocystis spp.
Percent of Total
Total Diatoms
Total Flagellates
Total Blue Green Algae
Total Green Algae
Total Phytoplankton
9
#/ml %
90 1.6
1850 33.6
460 8.4
120 —
60 1.1
120 2.2
90 1.6
200 3.6
30 0.5
640 11.6
230 4.2
1220 22.2
90 1.6
90 1.6
-- 96.2
3020 54.9
2210 40.2
90 1.6
180 3.3
5500
9a
#/ml %
140 4.6
— —
190 6.2
500 16.4
40 1.3
20 0.7
20 0.7
20 0.7
40 1.3
460 15.1
380 12.5
1000 32.8
20 0.7
120 3.9
— 96.7
930 30.4
1920 62.9
80 2.6
120 3.9
3050
10
#/ml
60
80
20
100
20
40
20
100
190
60
20
— :_
320
330
60
20
730
%
8.2
10.9
2.7
13.7
2.7
5.5
1.0
13.7
26.0
8.2
2.7
97.3
43.8
45.2
8.2
2.7
1
#/ml
140
120
30
780
60
60
30
30
30
140
200
60
350
90
—
1250
olO
0
120
2180
1
6.4
5.2
1.4
35.8
2.7
2.7
1.4
1.4
1.0
6.4
9.2
2.7
16.0
4.1
97.2
57.3
37.1
0
5.5
1
#/ml
30
60
870
120
490
30
30
30
410
60
160
—
1630
440
60
160
2290
2
6.4
2.6
38.0
5.2
21.0
1.3
1.3
1.3
17.9
2.6
7.0
100.0
71.2
19. 2
2.6
7.0
13a
#/ml %
100
40
60
120
170
270
20
100
80
—
200
^GO
60
200
1020
9.8
3.9
5.9
11.8
16.7
26.5
2.0
9.8
9.8
94.1
19.6
J4.J
5.9
19.6
13
#/ml %
60 2.2
90 3.3
30 1.1
350 12.9
120 4.4
120 4.4
30 1.1
30 1.1
30 1.1
90 3.3
f
350 12.9
1010 37.1
30 1.1
290 10.7
— 95.7
950 34.1
13oC 50.0
90 3.3
320 11.8
2720
-------
TABLE Dl
COMMON PHYTOPLANKTON SPECIES
SOUTHERN LAKE MICHIGAN
Cruise 1 (April 19-24, 1977)
STATIONS
Species
Aster ionel la formosa
Cyclotella spp.
Diatoms tenue var. elongatun
Fragilaria crontonensis
Fragilaria intermedia
Melosira spp.
Nitzschia spp.
Rhizosolenia longiseta
Synedra acus
Synedra ulna
Synedra spp.
Tabellaria fenestrata
Cryptomonas erosa
Cryptomomas ovata
Cryptomonas spp.
mnobrvon <;nn.
Miscellaneous fl acipl latp<>
O^r* "i 1 1 f*i~ CIY* i ^ ] imr\e*i~ T c a
Ankistrodesmus falcatus
Oorv^t i s ^nn.
Percent of Total
Total Diatoms
Total Flagellates
Total Blue Green Algae
Total Green Algae
Total Phytoplankton
1
#/ml
20
170
i —
870
60
20
40
20
310
1140
40
190
—
11 GO
1510
40
210
2920
6
0.7
5.8
29.8
2.0
0.2
1.4
0.7
10.6
39 0
1 4
6.5
98.6
39.7
51.7
1.4
7.2
f/ml
150
80
60
580
40
20
40
20
140
40
310
580
40
20
101U
1070
40
60
2180
16b
6.9
3 7
2 7
26.6
1 8
0.9
1 .8
0 9
6.4
1.8
14.2
26 6
1.8
0 9
97.2
46.3
49.1
1.8
2.7
1
#/ml
40
/in
tu
270
20
40
20
100
on
20
—
370
200
20
20
510
7
6 6
C f.
0. D
44.3
3.3
6.6
3.3
16.4
•3 -\
O. O
3.3
93.4
60.7
32.8
3.3
3.3
U
#/ml
An
HU
i cn
1 bU
680
dn
20
20
150
iRn
on
OU
20
—
970
320
100
40
1430
!
% #/m
O Q
£• O
In c
U. b
47.5
y Q
£• O
1.4
1.4 I
10.5 o
c
in c "c
1 U« 3
n
c c
b. D
1.4
94.4
67.8
22.4
7.0
2.3
19 20a
1 % #/ml %
i A n ? n
IHU <-• U
i on i ~7
\
-------
TABLE Dl
COMMON PHYTOPLANKTON SPECIES
SOUTHERN LAKE MICHIGAN
Cruise 1 (April 19-24, 1977)
STATIONS
a
i
on
Species
Aster ionel la formosa
Cyclotella spp.
Diatoms tenue var. elongatum
Fragilaria crontonensis
Fragilaria intermedia
Melosira spp.
Nitzschia spp.
Rhizosolenia longiseta
Synedra acus
Synedra ulna
Synedra spp.
Tabellaria fenestrata
Cryptomonas erosa
Cryptomomas ovata
Cryptomonas spp.
Dinobryon spp.
Miscellaneous flagellates
Oscillatoria limnetica
Anki strodesmus falcatus
Oocystis spp.
Percent of Total
Total Diatoms
Total Flagellates
Total Blue Green Algae
Total Green Algae
Total Phytoplankton
21
#/ml
60
60
20
580
60
40
120
20
80
230
60
870
140
—
980
1240
20
180
2420
%
2.5
2.5
0.8
24.0
2.5
1.6
5.0
0.8
3.3
9.5
2.5
35.9
5.8
96.7
40.5
51.2
0.8
7.4
21
#/ml
100
100
720
60
80
80
140
40
230
70
20
100
—
1160
1090
0
60
2390
a
5.5
5.5
39.6
3.5
4.4
4.4
7.7
2.2
12.6
3.8
1.1
5.5
95.6
47.7
44.9
0
2.5
22
#/ml
20
60
120
640
80
40
60
170
80
380
660
60
—
1040
1290
0
60
2390
%
0.8
2.5
5.0
26.8
3.4
1.7
2.5
7.1
3.5
15.9
27.6
2.5
99.2
43.5
54.0
0
2.5
23
#/ml
60
150
150
40
20
20
60
20
20
230
750
140
140
—
370
1020
140
140
1820
24a
% #/ml %
3.3
8.2
8.2
2.2
1.1
1.1
3.3
1.1
1.1
12.6
41.2
7.7
7.7
98.9
20.3
56.0
7.7
7.7
40
270
140
100
230
440
40
230
150
1280
20
1040
—
1610
2550
120
0
4240
0.8
5.7
2.9
2.1
4.8
9.3
0.8
4.8
3.2
26.9
0.4
21.9
93.9
38.0
60.1
2.8
0
24
#/ml %
30
120
1590
700
30
60
320
90
230
290
170
1590
550
1970
60
610
—
3380
4660
120
730
8990
3.0
1.3
17.9
7.9
0.3
0.7
3.6
1.0
2.6
3.3
1.9
17.9
b.Z
__ _
0.7
6.7
94.6
38.0
52.4
1.4
8.2
-------
o
TABLE D1
COMMON PHYTOPLANKTON SPECIES
SOUTHERN LAKE MICHIGAN
Cruise 1 (April 19-24, 1977)
STATIONS
Species
Aster i one! la formosa
Cyclotella spp.
Diatoms tenue var. elongatum
Fragilaria crontonensis
Fragilaria intermedia
Melosira spp.
Nitzschia spp.
Rhizosolenia longiseta
Synedra acus
Synedra ulna
Synedra spp.
Tabellaria fenestrata
Cryptomonas erosa
Cryptomomas ovata
Cryptomonas spp.
Dinobryon spp.
Miscellaneous flagellates
Oscillatoria limnetica
Ankistrodesmus falcatus
Oocystis spp.
Percent of Total
Total Diatoms
Total Flagcllatos
Total Blue Green Algae
Total Green Algae
Total Phytoplankton
25
#/ml %
20
20
310
20
20
20
80
640
80
1040
140
450
lo4'J
0
140
2430
0.8
0.8
12.8
0.8
0.8
0.8
3.3
26.3
3.3
42.8
5.8
98.3
18.5
71;. 7
0
5.8
25a
60
20
270
60
40
330
890
450
1 i2c_!0
0
100
1770
3.4
1.2
15.2
3.4
2.3
18.6
50.3
94.3
25.4
C.J. 3
0
5.6
26
#/ml %
20
60
190
620
20
20
20
80
20
380
330
140
20
...
970
UVJ
180
20
1980
1.0
3.0
9.6
31.3
1.0
1.0
1.0
4.0
1.0
19.2
16.7
7.1
1.0
97.0
49.0
/i r> 'i
9.1
1.0
27
80
380
20
60
80
60
230
120
40
20
...
580
4'JJ
100
20
1 1 90
6.
31.
1.
5.
6.
5.
19.
10.
3.
1.
91.
48.
41.
8.
1.
—
28a 28
#/ml % #/ml %
7
9
7
0
100
100
440
60
20
20
5.1
5.1
22.6
3.1
1.0
1.0
7 8 170
0 <* 20
33 80
4
7
6
7
j
4
7
-
° 460
230
170
820
7JJ
230
0
1950 -
8.7
1.0
4.1
23.6 !
11.8
8.7
95.9
42.0
~/.4
11.8
0
—
-------
a
TABLE D2
COMMON PHYTOPLANKTON SPECIES
SOUTHERN LAKE MICHIGAN
Cruise 2 (June 11-16, 1977)
STATIONS
Species
Asterionella formosa
Cyclotella spp.
Diatoms tenue var. elongatum
Fragilaria crontonensis
Fragilaria intermedia
Melosira spp.
Nitzschia spp.
Rhizosolenia eriensis
Rhizosolenia longiseta
Synedra acus
Synedra ulna
label! aria fenestrata
Cryptomonas spp.
Cryptomonas erosa
Cryptomomas ovata
Dinobryon spp.
Miscellaneous flagellates
Oscillatoria limnetica
Ank i strodesmus f al catus
Oocystis spp.
Quadrigula lacustris
Percent of Total
Total Diatoms
Total Flagellates
Total Blue Green Algae
Total Green Algae
Total Phytoplankton
#/ml
60
90
170
430
60
720
200
120
200
30
580
30
90
120
1560
90
30
—
2] 4U
2410
60
180
4790
5a
%
1.2
1.9
3.5
9.0
1.2
15.0
4.2
2.5
4.2
0.6
12.1
0.6
1.9
2.5
32.6
1.9
0.6
95.5
44.7
50.3
1.2
3.8
#/ml
30
30
260
120
230
90
120
30
260
460
90
—
ylu
920
120
150
2100
5b
%
1.4
1.4
12.4
5.7
10.9
4.3
5.7
1.4
12.4
21.9
4.3
13.6
43.8
5.7
7.1
5
#/ml %
60 2.0
30 1.0
120 4.1
30 1.0
200 6.8
30 1.0
30 1.0
290 9.9
30 1.0
980 33.3
780 26.5
120 4.1
60 2.0
--- 93.7
bUU 1 / . U
2080 70.8
150 5.1
210 7.1
2940
#/ml
90
290
30
230
30
120
170
290
30
30
140
1680
90
60
—
yyu
2170
180
120
3460
6
%
2.6
8.4
0.9
6.6
0.9
3.5
4.9
8.4
0.9
0.9
4.1
48.5
2.6
2.0
94.1
62.7
5.2
3.5
6a
#/ml
30
30
90
170
520
90
170
810
60
30
—
^U
1590
90
240
2240
%
1.3
1.3
4.0
7.6
23.2
4.0
7.6
36.2
2.7
1.3
89.2
14. J
71.0
4.0
10.7
6b
#/ml
140
350
60
30
60
90
60
230
260-
60
60
1040
60
30
30
—
lUbU
1450
90
90
2680
%
5.2
13.1
2.2
1.1
2.2
3.3
2.2
8.6
9.7
2.2
2.2
38.8
2.2
1.1
1.1
95.2
Jj.
-------
a
i
CO
TABLE D2
COMMON PHYTOPLANKTON SPECIES
SOUTHERN LAKE MICHIGAN
Cruise 2 (June 11-16, 1977)
STATIONS
Species
Asterionella formosa
Cyclotella spp.
Diatoms tenue var. elongatum
Fragilaria crontonensis
Fragilaria intermedia
Melosira spp.
Nitzschia spp.
Rhizosolenia eriensis
Rhizosolenia longiseta
Synedra acus
ynedra ulna
Tabellana fenestrata
Cryptomonas spp.
Cryptomonas erosa
Cryptomomas ovata
Dinobryon spp.
Miscellaneous flagellates
Oscillatoria limnetica
Ankistrodesmus falcatus
Oocystis spp.
Quadrigula lacustris
Percent of Total
Total Diatoms
Total Flagellates
Total Blue Green Algae
Total Green Algae
Total Phytoplankton
#/ml
17 n
/O
1 9n
1 L\J
r r\
OU
350
290
or\n
£UU
120
30
120
rr\
oU
9"3fl
c5\J
840
ocn
ODU
120
1500
60
170
on
3U
on
yu
1750
2810
210
410
5180
9
%
.
0
60
j
3
5 380
120
30
460
90
Z3U
— —
1480
990
180
320
2970
%
A 7
H. /
9O
. (3
30.3
o n
-J. U
2.0
12.8
4.0
1.0
15.5
3.0
/./'
93.8
49.8
33.3
6.1
10.8
n
#/ml
on
ou
10
IAD
I tU
120
90
30
260
30
90
290
810
60
OU
440
1480
120
120
2160
%
1 4
1 . H
1 4
C C
5.6
4.2
1 4
12.0
1.4
4 2
13.4
37.5
2.8
l.t
93.2
20.4
68.5
5.6
5.6
12
#/ml
30
60
30
fin
30
30
200
490
30
30
140
1820
120
\J\j
470
2510
210
120
3340
% #/r
0.9
- _ _ _
1.8
0.9
u. -o
1 8
0.9 I
09 «-
6.0 =
T
14.7
0.9
0.9
4.2
54.5
3.6
i • >
1 . 0
9^.o
14.1
75.2
6.3
3.6
13a 1
nl % #/ml
60
170
170
200
60
90
' 260
" 90
3 200
3
D 520
30
60
380
1240
60
120
'W
1480
2230
210
420
4340
3
%
1.4
3.9
3.9
2.1
4.6
1.4
2.1
6.0
2.1
4.6
12.0
0.7
1 4
8.7
28.6
1.4
2.8
i 7
OO. H
34.1
51.4
4.8
9.7
-------
i
i-O
TABLE D2
COMMON PHYTOPLANKTON SPECIES
SOUTHERN LAKE MICHIGAN
Cruise 2 (June 11-16, 1977)
STATIONS
Species
Act AK* i nnpl 1 A "Fnv^mfic ^
»\ j t* Cl 1 l_M IvT 1 1 Q 1 U I IIIVJO Q
Cyclotella spp.
Diatoms tenue var. elongatum
Fragilaria crontonensis
Fragilaria intermedia
Melosira spp.
Nitzschia spp.
Rhizosolenia eriensis
Rhizosolenia longiseta
Synedra acus
Synedra ul na
TA HP 1 1 ay* i a "Fono c t")" 3 *t~ A
i uL/c i i at la 1 cut. o W a La
Cryptomonas spp.
Crypt omonas erosa
Cryptomomas ovata
Dinobryon spp.
Miscellaneous flagellates
Oscillatoria limnetica
Anki strodesmus falcatus
Oocystis spp.
Quadrigula lacustris
Percent of Total
Total Diatoms
Total Flagellates
Total Blue Green Algae
Total Green Algae
Total Phytoplankton
1
#/ml
?nn
L_ \J\J
60
120
60
30
350
30
30
or\
380
30
170
690
30
90
60
—
910
1270
30
150
2360
6
10
8 5
U» -J
2.5
5.1
2.5
1.3
14.8
1.3
1.3
1 1
I . O
16.1
1.3
7.2
29.2
1.3
3.8
2.5
100.0
38.6
53.8
1.3
6.4
16b
#/ml %
fin i d
\j\j i • "
30 0.7
120 2.7
290 6.6
230 5.2
60 1.4
60 1.4
200 4.5
30 0.7
?n n 7
tj\J \J • /
900 20.4
90 2.0
60 1.4
350 7.9
1390 31.6
60 1.4
260 5.9
— - 95.9
1110 25.2
2790 63.4
90 2.0
410 9.3
4400
1
#/ml
fin
\J\J
350
90
30
30
30
30
Qn
j\J
90
60
230
30
140
—
1000
380
30
200
1610
7
01
10
1 7
s> • /
21.7
5.6
1.9
1.9
1.9
1.9
C £T
5.6
3.7
14.3
1.9
8.7
90.8
62.1
23.6
1.9
12.4
#/m
60
30
290
610
30
30
30
30
200
90
30
610
60
200
—
1140
990
60
200
2390
18
2.5
1.2
12.1
25.5
1.2
1.2
1.2
1.2
8.4
3.8
1.2
25.5
2.5
8.4
95.9
47.7
41.4
2.5
8.4
#/ml
Qn
_7VJ
30
350
120
30
30
60
30
1 ?0
490
60
1240
660
60
90
860
2450
90
180
3580
19
? 5
L_ • -J
0.8
9.8
3.3
0.8
0.8
1.7
0.8
'\ 1
•J •
-------
TABLE D2
COMMON PHYTOPLANKTON SPECIES
SOUTHERN LAKE MICHIGAN
Cruise 2 (June 11-16, 1977)
STATIONS
Species
A^1" PK* "i nnpl IP. "Fnvmnc;}
Cyclotella spp.
Di 3 toms tGHUG var • GlonQaturn
CM a rt i "1 ay* i a pv*nn'f"nnpnci c
' " " j ' 1 Qi 1 Q \* I VJIILL/ri^lljiJ
Fragi 1 ar i a i ntcrmodi a
Mplo^iK'/i ^ nn
Nit7^rhia ^ n n
Rhizosolenia eriensis
Rhizosolenia longiseta
S vnprlK* A 3r 1 1^
Synedra ulna
T aKp"| "I ay* -j a 'FpnP^t"f*flt"3
1 Q U t. 1 1 Qi IQ I C 1 1" o L. I Qua
Cryptomonas spp.
PK* vni" nmn n^Q py n Q ,^
(Yvntnmnmas rwata
v/l j'JJUwHlVJItlQo U V Q U Q
Dinobryon spp.
Miscellaneous flagellates
Oscillator! a limnetica
Ankistrodesmus falcatus
nnrv<^ti<; <;nn
Di i rirlp i ni 1 1 f\ 1/^riiQl'K'iQ
Percent of Total
Total Diatoms
Total Flagellates
Total Blue Green Algae
Total Green Algae
Total Phytoplankton
f
#/ml
60
30
30
90
290
170
140
30
610
30
90
—
670
7ou
30
180
1660
1
3.6
1 8
1 R
5 4
17.4
10.2
8.4
1.8
36.7
1.8
5.4
94.3
40.4
47.o
1.3
10.8
f
#/ml
30
i ?n
30
120
fin
60
30
380
30
3240
460
30
60
fin
—
530
4110
60
240
4840
0.6
•3 fi
0 6
2.4
1 7
1 . L-
1.2
n fi
7.7
n fi
65.6
9.3
0.6
1.2
1 7
96.2
10.7
83.2
1.2
4.9
f
#/rnl
j U
60
n o r\
^O L/
fin
DU
170
fin
DU
30
350
on
950
520
60
120
—
930
1830
60
150
3020
12
o n
O. U
2.0
id ?
1 H. £
o n
c. U
5.6
7 n
£. U
1.0
11.6
i n
31.5
17.2
2.0
4.0
97.1
30.8
62.2
2.0
5.0
#/m
en
DU
60
')cr\
cuu
•JO
OU
30
fin
DU
30
380
fin
60
640
30
200
—
560
1040
90
290
1980
23
1 %
3n
. U
3.0
TOT
1 O. 1
1 c.
1 . 0
1.5
3n
• u
1.5
19.2
Q n
3.0
32.3
1.5
10.1
95.7
28.3
52.5
4.b
14.6
2i
#/ml
on
oU
60
fin
DU
A i n
T'J U
i 9n
1 cU
Tn
o U
i yn
140
TO
oU
60
OCfl
OOU
580
-7vJ
170
920
30
170
—
1430
1760
Isu
200
3540
la
% #/m
On
. 0
1.7
1 7
1 . /
19 1
1 <-. \
•j . ^
OQ
. O
o 4.
J. T-
3.9
On
«o :
1.7 c
9
-------
TABLE D2
COMMON PHYTOPLANKTON SPECIES
SOUTHERN LAKE MICHIGAN
Cruise 2 (June 11-16, 1977)
STATIONS
25 25a 26 27
Species #/ml % #/ml % #/ml % #/ml
Asterionella formosa 60
Cyclotella spp. 30
Diatoms tenue var. elongatum 90
Fragilaria crontonensis 920
Fragilaria intermedia 290
Melosira spp. 90
Nitzschia spp. 30
Phi 7ncr\l on "i ;? OK* i one i c
r\Ml£UoUlCiliu cr Icilblo
Rhizosolenia longiseta
1
Synedra acus ° 30
Synedra ulna ^
^ -_ _
j
Tabellaria fenestrata ^ 120
Cryptomonas spp. . 1160
Cryptomonas erosa
Cryptomomas ovata
Dinobryon spp.
Miscellaneous flagellates
Oscillatoria limnetica
Ankistrodesmus falcatus
Oocystis spp.
Quadrigula lacustris
Percent of Total
Total Diatoms
Total Flagellates
Total Blue Green Algae
Total Green Algae
Total Phytoplankton
30
350
350
580
30
200
120
—
1690
24 /U
30
500
4720
1.3 120
0.6 90
1.9 30
19.5 920
6.1
1.9 350
0.6 60
-in
—
*,v
30
0.6 5 90
0
c
I 30
2.5 a 120
24.6 ^ 640
0.6
7.4
7.4
12.3
0.6
4.2
2.5
94.6
35.8
bZ.6
0.6
10.6
120
380
260
—
60
90
60
—
1900
IHUU
150
180
3660
28a 28
% #/ml % #/ml %
3.3 30
2.5 30
0.8 30
25.1 580
9.6 90
1.6 60
n B
0.8 3 60
2.4 ° 60
0.8 £ 30
3.3 .§ 170
17.3 ^
3.3
10.4
7.1
1.6
2.5
1.6
94.8
51.9
OO. L.
4.1
4.9
' 290
60
1.1
1.1
1.1
21.3
3.3
2.2
2.2
2.2
1.1
6.2
10.7
2.2
900
60
90
30
30
—
120)
UjJ
90
180
2720
33.1
2.2
3.3
1.1
1.1
95.5
44.1
40.0
3.3
6.6
-------
ro
TABLE D3
COMMON PHYTOPLANKTON SPECIES
SOUTHERN LAKE MICHIGAN
Cruise 3 (August 20-25, 1977)
STATIONS
Species
Asterionella formosa
Cyclotella spp.
Diatoms tenue var. elongatum
Fragilaria crontonensis
r~ • i * "A. J -£
Fragilaria intermedia
Melosira spp.
Synedra acus
Tabellaria fenestrata
Cryptomonas erosa
Cryptomomas ovata
Cryptomonas spp.
Dinobryon spp.
Miscellaneous flagellates
Anabaena spp.
Anacystis spp.
Aphanothece spp.
Chroococcus spp.
Coelospaerium kuetzingianum
Gomphosphaeria lacustris
Ankistrodesmus falcatus
Crucigenia quadrata
Oocystis spp.
Quadrigula lacustris
Scenedesmus quadricauda
Percent of Total
Total Diatoms
Total Flagellates
Total Blue Green Algae
Total Green Algae
Total Phytoplankton
5
30
140
i ~? n
1 /U
580
90
1C f\
bO
350
"7 Of\
780
230
1130
1010
460
60
120
30
60
430
30
30
—
1190
2520
1710
580
6000
a
0.5
2.3
2O
. O
9.7
1.5
2r
. b
5.8
3.' 8
18.8
16.8
7.7
1.0
2.0
0.5
1.0
7.2
0.5
0.5
98.0
19.3
42.0
28.5
9.7
5t
#/ml
30
30
_ _ —
—
— — ..
30
— _ —
30
90
1390
_ _ _
380
290
60
30
—
120
30
—
—
180
1630
760
180
2750
)
1.1
1.1
_ _ — _
-_ _ — —
1.1
_ _ - -
1.2
30
. 6
3.3 .
50.5
— — — —
13.8
10.5
2.2
1.1
4.4
1.1
----
94.5
6.5
59.3
27.6
6.5
5
...
30
— M> «
---
— — —
—
60
140
950
260
260
60
30
90
on
JU
30
30
—
30
1530
700
120
2380
x-
______
1.3
_ _ _ -_
~ — — —
—
2.5
U7
. /
5.9
39.9
10.9
10.9
2.5
1.3
3.8
i i
1 . J
1.3
1.3
97.5
1.3
64.3
29.4
5.0
(
#/ml
260
60
^o
•JU
90
90
60
90
580
•J\J\J
120
30
60
30
_ _ _
_ _> —
—
560
1210
820
90
2680
5 %
9.7
2.2
i i
i . i
3.4
3.4
2.2
74 fi
C.H. O
3.4
21 6
t_ 1 • v
4.5
1.1
2.2
1.1
i i
1 • 1
_ _ _ _
81.6
20.9
45.1
30.6
3.4
6
#/ml
60
. 90
430
170
90
550
120
610
870
30
\J \J
580
230
90
60
60
60
30
60
...
—
930
2180
1170
390
4760
a
1.3
1.9
9.0
3.6
1.9
11.5
1 1 • v/
2.5
12.8
18.3
0.6
12.2
4.8
1.9
1.3
1.3
1.3
0.6
0.6
88.1
19.5
45.8
24.6
8.2
6
#/ml
90
90
*30
*J w
120
520
200
60
430
"*J*J
120
1010
380
170
60
30
60
120
90
30
, i-\
uU
1110
1620
760
330
3820
b
2.4
2.4
Of)
X
• \J
3.1
13.6
5.2
1.6
11 3
1 I « *J
3.1
26.4
10.0
4.4
1.6
0.8
1.6
3.1
2.4
0.8
1 . 6
96.2
29.1
42.;
19.9
8.6
-------
TABLE D3
COMMON PHYTOPLANKTON SPECIES
SOUTHERN LAKE MICHIGAN
Cruise 3 (August 20-25, 1977)
STATIONS
Species
Asterionella formosa
Cyclotella spp.
Diatoms tenue var. elongatum
Fragilaria crontonensis
Frag il aria intermedia
Melosira spp.
Synedra acus
Tabellaria fenestrata
Cryptomonas erosa
Cryptomomas ovata
Cryptomonas spp.
Dinobryon spp.
Miscellaneous flagellates
Anabaena spp.
Anacystis spp.
Aphanothece spp.
Chroococcus spp.
Coel ospaer i urn kuetzi ngianum
Gofnnho<: nhspr i fl Ipniclric
Ankistrodesmus falfritus
Crucigenia quadrata
Oocystis spp.
Quadrigula lacustris
Scenedesmus quadricauda
Percent of Total
Total Diatoms
Total Flagellates
Total Blue Green Algae
Total Green Algae
Total Phytopl ankton
#/ml
200
60
30
290
60
30
30
30
230
200
1070
140
90
60
30
90
760
1590
320
180
2850
9
%
7.0
2.1
1.0
10.2
2.1
1.0
1.0
1.0
8.1
7.0
37.5
4.9
3.2
2.1
1 0
3 2
92.6
26.7
55.8
11.2
6.3
9a
#/ml
90
140
30
580
30
60
200
200
1360
260
120
60
•3(1
140
990
1320
470
140
3420
%
2 6
4.1
0.9
16 9
0 9
1.7
5.8
5 8
39.3
7.6
3.5
i 7
n Q
U. 3
4 i
96.5
28.9
53.2
13.7
4.1
10
#/ml
60
90
200
90
1160
60
170
90
60
cri
DU
30
470
1340
300
60
2250
%
2 7
4 0
8.9
4.0
51.5
2 7
7.6
4.0
2.7
y 7
£• /
1 3
92.0
20.9
59.6
13.3
2.7
#/m
30
120
380
380
?n
140
200
60
£n
t)U
•an
•jn
30
910
490
60
1490
11
il %
2 0
8.0
25.5
25.5
y n
9.4
13.4
4.0
A n
4. U
o n
9 0
£« U
98.0
2.0
61.1
32.9
4.0
#/ml
on
y\J
fin
on
ou
30
430
fin
640
460
380
90
"3n
ou
en
uu
330
1190
1050
120
2690
12
%
o o
0. 0
y ?
i i
1 . 1
1.1
16.0
7 y
23.8
17.1
14.1
3.3
11
. I
9 7
(-•c.
87.7
12.3
44.2
39.0
4.5
1
#/ml
i ')n
\t-\J
•sn
ou
on
-7U
fin
i ?n
1 / U
on
oU
140
520
i yn
1 <-U
1330
780
140
140
nn
yu
^n
OU
on
JU
-jn
OU
620
2110
1240
120
4090
3a
%
•) Q
C.m !?
n 7
U. /
y y
Cm (-
1 £>
40
. c.
07
. /
3.4
12.7
9 Q
c. 3
32.5
19.1
3.4
3.4
29
. d.
i) 7
U. /
n 7
u. /
n 7
u. /
94.1
lb.2
51.6
30.3
2.9
13
#/m1
Qn
OU
on
yu
O7n
o/U
•\An
1 HU
•?n
JU
90
140
i yn
1 C-\J
610
520
140
30
•3fl
OU
/*n
bU
'it \
ou
Tfl
jU
\ZM
960
840
130
3230
%
On
. y
9 o
L. O
'JC Q
c.o. y
A "?
t. o
On
. y
2.8
4.3
-3 7
0. /
18.9
16.1
4.3
0.9
n Q
u. y
. y
00
. y
OQ
. y
91.0
J8. /
29.7
26.0
5.6
-------
TABLE D3
COMMON PHYTOPLANKTON SPECIES
SOUTHERN LAKE MICHIGAN
Cruise 3 (August 20-25, 1977)
STATIONS
Species
Aster ionel la formosa
Cyclotella spp.
Diatoms tenue var. elongatum
Fragilaria crontonensis
Fragilaria intermedia
Melosira spp.
Synedra acus
Tabellaria fenestrata
Cryptomonas erosa
Cryptomomas ovata
Cryptomonas spp.
Dinobryon spp.
Miscellaneous flagellates
16
#/ml %
30
30
140
30
90
60
520
120
520
1.4
1.4
6.4
1.4
4.1
2.7
23.8
5.5
23.9
16b
#/ml %
30
90
660
60
1070
0.7
2.1
15.6
1.4
25.3
17
#/ml
30
30
140
140
230
430
920
%
0.9
0.9
4.2
4.2
6.9
12.9
27.6
18
#/ml
60
30
30
30
90
720
170
%
2.1
1.0
1.0
1.0
3.1
24.8
5.9
1
#/ml
60
90
30
120
550
30
1070
9
2.0
3.1
1.0
4.1
18.7
1.0
36.4
20a
#/ml %
60
60
290
60
60
580
90
350
1.7
1.7
8.5
1.7
1.7
16.9
2.6
10.2
20
#/ml %
60
230
430
380
60
30
30
60
60
580
1.7
6.7
12.5
11.0
1.7
0.9
0.9
1.7
1.7
16.8
Anabaena spp.
Anacystis spp.
Aphanothece spp.
Chroococcus spp.
Coelospaerium kuetzingianum
Gomphosphaeria lacustris
Ankistrodesmus falcatus
Crucigenia quadrata
Oocystis spp.
Quadrigula lacustris
Scenedesmus quadricauda
Percent of Total
Total Diatoms
Total Flagellates
Total Blue Green Algae
Total Green Algae
Total Phvtoolankton
230
i ?n
1 /U
90
on
oU
10.5
7 &
1 • O
4.1
1 A
1 . r
1040
i?n
60
on
y j
i A n
l
-------
o
I
TABLE D3
COMMON PHYTOPLANKTON SPECIES
SOUTHERN LAKE MICHIGAN
Cruise 3 (August 20-25, 1977)
STATIONS
Species
Asterionella formosa
Cyclotella spp.
Diatoms tenue var. elongatum
Fragilaria crontonensis
Fragilaria intermedia
Melosira spp.
Synedra acus
Tabellaria fenestrata
Cryptomonas erosa
Cryptomomas ovata
Cryptomonas spp.
Dinobryon spp.
Miscellaneous flagellates
Anabaena spp.
Anacystis spp.
Aphanothece spp.
Chroococcus spp.
Coelospaerium kuetzingianum
Gomphosphaeria lacustris
Ankistrodesmus falcatus
Crucigenia quadrata
Oocystis spp.
Quadrigula lacustris
Scenedesmus quadricauda
Percent of Total
Total Diatoms
Total Flagellates
Total Blue Green Algae
Total Green Algae
Total Phytoplankton
2
#/ml
610
60
30
430
30
140
30
460
140
1240
60
—
1330
1900
60
3290
1
%
18.5
1.8
0.9
13.1
0.9
4.3
0.9
14.0
4.7
37.7
1.8
98.2
40.4
57.7
1.8
2
#/ml
90
90
30
1160
490
60
30
290
490
1300
460
490
30
60
90
120
30
—
2300
2740
210
240
5490
la
%
1.6
1.6
0.6
21.1
8.9
1.1
0.5
5.3
8,9
23.7
8.4
8.9
0.5
1.4
1.6
2.2
0.5
96.7
41.9
49.9
3.8
4.4
2
#/ml
30
120
60
400
120
720
120
90
30
60
—
150
1330
240
60
1780
2
%
1.7
6.7
3.4
22.5
6.7
40.4
6.7
5.1
1.7
3.4
98.3
8.4
74.7
13.5
3.4
2
#/ml
230
30
430
—
—
—
30
230
90
350
230
60
—
50
_~_
60
—
—
690
700
350
60
1800
3
%
12.8
1.7
23.9
1.7
12.8
5.0
19.4
12.8
3.3
3.3
____
3.3
100.0
38.3
38.9
19.4
3.3
2
#/ml
120
30
230
580
30
60
90
490
120
550
1010
200
60
60
30
30
60
60
—
1230
1250
1360
180
4020
4a
%
3.0
0.7
5.7
14.4
0.7
1.5
2.2
12.2
3.0
13.7
25.1
5.0
1.5
1.5
0.7
0.7
1.5
1.5
94.8
30.6
31.1
33.8
4.5
2
#/ml
120
60
430
120
580
90
870
30
750
260
60
30
30
120
30
—
640
1780
1130
240
3790
4
%
3.2
1.6
11.4
3.2
15.3
2.4
22.9
0.8
19.8
6.9
1.6
0.8
0.8
3.2
0.8
94.5
16.9
47.0
29.8
6.3
-------
a
i
TABLE D3
COMMON PHYTOPLANKTON SPECIES
SOUTHERN LAKE MICHIGAN
Cruise 3 (August 20-25, 1977)
STATIONS
Species
Asterionella formosa
_ _
Cyclotella spp.
Diatoms tenue var. elongatum
Fragilaria crontonensis
Fragilaria intermedia
•^
Melosira spp.
r* i
Synedra acus
label! aria fenestrata
Cryptomonas erosa
Cryptomomas ovata
Cryptomonas spp.
Dinobryon spp.
Miscellaneous flagellates
Anabaena spp.
Anacystis spp.
Aphanothece spp.
Chroococcus spp.
Coelospaerium kuetzingianum
Gomphosphaeria lacustris
Ankistrodesmus falcatus
Crucigenia quadrata
Oocystis spp.
Quadrigula lacustris
Scenedesmus quadricauda
Percent of Total
Total Diatoms
Total Flagellates
Total Blue Green Algae
Total Green Algae
Tntal Phvt.nnl ankton
#/ml
400
_ «. —
660
— — —
— — —
•3fl
OU
(\f\
yu
60
840
170
1130
— — —
«_ •
90
—
1360
22'M
___
90
3650
25
%
11.0
~ "• "" ""
18.1
« _ — «
•"-• — —
n a
u. o
2C
. D
1.6
23.0
4.7
31.0
— — — —
« .. _ ->
2.5
95.1
37.3
oil. J
____
2.5
2
#/ml
140
•an
JU
350
i on
1 c(J
•jn
90
780
90
430
60
60
230
cr\
DU
670
1450
120
320
2560
5a
%
5.5
i ?
i • f-
13.7
47
. /
1 7
I . (-
3.5
30.5
3.5
16.8
2.3
2.3
9.0
9 7
£. J
96.5
26.2
56.6
4.7
12.5
2
#/ml
90
70.
1790
in
ou
?nn
C.\J\)
60
520
120
900
120
90
TD
90
i?n
1 L.U
—
2170
1600
270
240
4280
6
%
2.1
n 7
41.8
n 7
A 7
1.4
12.1
2.8
21.0
2.8
2.1
n 7
2.1
? R
97.9
i r \ -7
^\J» 1
37.4
6.3
5.6
2
#/ml
60
60
430
30
90
380
30
920
120
60
60
90
—
DOU
1450
240
90
2360
7
2
2
18
i
3
16
1
39
b
2
3
98
24
61
10
3
--
2
% #/ml
.5
.5
.2
.3
.8
.1
.3 '<•
•° I
-c
n
.1
.5
.8
.7
.6
.4
.2
.8
--
8a 2£
% #/ml
60
_ •» —,
60
580
140
60
60
90
260
= 140
n 610
3
3
3 , .,_.
170
60
140
—
—
990
1100
290
290
' 2670
}
%
2.2
. — _ —
2.2
21.7
5. 2
2.2
2.2
3.4
9.7
5.2
22.8
6.4
2.2
5.2
91.0
37.1
41.2
10.9
10.9
_ _ _ —
-------
o
I
TABLE D4
COMMON PHYTOPLANKTON SPECIES
SOUTHERN LAKE MICHIGAN
Cruise 4 (September 17-24, 1977)
STATIONS
Species
Asterionella formosa
Cyclotella spp.
Diatoms tenue var. elongatum
Fragilaria crontonensis
Melosira spp.
Nitzchia spp.
Rhizosolenia eriensis
Rhizosolenia longiseta
Synedra acus
Tabellaria fenestrata
Tabellaria flocculosa
Cryptomomas ovata
Cryptomonas spp.
Dinobryon spp.
Miscellaneous flagellates
Anabaena spp.
Anacystis spp.
Aphanothece spp.
Chroococcus spp.
Gomphosphaeria lacustris
Microcoleus lyngbyacus
Oscillatori a limnetica
Ankistrodesmus falcatus
Crucigenia quadr.ata
Crucigenia rectangularis
Percent of Total
Total Diatoms
Total Flagellates
Total Blue Green Algae
Total Green Algae
Total Phytoplankton
5
#/ml
60
170
—
30
140
30
140
30
90
• 260
750
30
1130
90
90
30
30
30
—
570
1190
1400
120
3280
a
1.8
5.2
0.9
4.3
0.9
4.3
0.9
2.9
. 7.9
22.7
0.9
34.5
2.9
2.9
0.9
0.9
0.9
95.7
17.4
36.3
42.7
3.6
5
#/ml
60
120
30
550
200
60
170
200
30
810
30
580
90
60
—
1280
1040
790
3110
b
1.9
3.9
1.0
17.7
6.4
1.9
5.5
6.4
1.0
26.0
1.0
18.6
2.9
1.9
96.1
41.2
33.4
25.4
#/ml
60
30
60
30
60
60
230
30
490
90
120
90
—
240
810
300
30
1380
5
4.3
2.2
4.3
2.2
4.3
4.3
17.4
2.2
35.5
6.5
8.7
6.5
98.4
17.4
58.7
21.7
2.2
#/ml
90
430
30
30
460
920
490
30
30
—
550
1410
550
2510
6
3.6
17.1
1.2
1.2
18.3
36.6
19.5
1.2
1.1
99.8
21.9
56.2
21.9
#/ml
30
30
150
120
30
60
30
30
580
320
1040
580
90
120
60
30
—
450
2000
820
120
3390
6a
0.9
0.9
4.4
3.5
0.9
1.8
0.9
0.9
17.1
9.4
30.7
17.1
2.6
3.5
1.8
0.9
97.3
13.3
59.0
24.2
3.5
6
#/ml
30
60
30
60
30
200
230
430
30
980
140
60
120
120
90
90
—
180
920
1480
210
2790
b
1.1
2.1
1.1
2.1
1.1
7.2
8.2
15.4
1.1
35.1
5.0
2.1
4.3
4.3
3.2
3.2
96.6
6.4
33.0
53.1
7.5
-------
o
CO
TABLE D4
COMMON PHYTOPLANKTON SPECIES
SOUTHERN LAKE MICHIGAN
Cruise 4 (September 17-24, 1977)
Species
Asterionella formosa
Cyclotella spp.
Diatoms tenue var. elongatum
Fragilaria crontonensis
Melosira spp.
Nitzchia spp.
Rhizosolenia eriensis
Rhizosolenia longiseta
Synedra acus
label 1 aria fenestrata
Tabellaria flocculosa
Cryptomomas ovata
Cryptomonas spp.
Dinobryon spp.
Miscellaneous flagellates
Anabaena spp.
Anacystis spp.
Aphanothece spp.
Chroococcus spp.
Gomphosphaeria lacustris
Microcoleus lyngbyacus
Oscillatoria limnetica
Ankistrodesmus falcatus
Crucigenia quadrata
Crucigenia rectangularis
Percent of Total
Total Diatoms
Total Flagellates
Total Blue Green Algae
T..4--.1 fl*,r\r\rt fllnaO
9
I /ml %
90
60
290
30
90
90
610
30
950
610
60
30
30
30
60
590
1710
760
270
2.7
1.8
8.7
0.9
2.7
2.7
1C. 3
0.9
28.5
18.3
1.8
0.9
0.9
0.9
1.8
91.3
17.7
51.3
22.8
8.1
STATIONS
9a 10
#/ml % #/ml %
290
30
170
30
60
30
30
30
1010
170
1390
460
30
30
30
90
640
2600
520
120
7.5
0.7
4.4
0.7
1.5
0.7
0.7
0.7
26.0
4.4
35.8
11.?
0.7
0.7
0.7
2.3
99.3
16.5
67.0
13.4
3.1
120
150
640
60
520
980
30
150
30
30
270
1250
1190
30
4.4
5.5
23.4
2.2
19.0
35.8
1.1
5.2
1.1
1.1
98.8
9.8
45.6
43.4
1.1
1
#/ml
140
60
60
120
180
30
30
170
610
120
380
400
60
60
620
1280
460
120
1
%
5.6
2.4
2.4
4.8
7.3
1.2
1.2
6.8
24.6
4.8
15.3
16.1
2.4
2.1
97.3
25.0
51.6
18.5
4.8
#/ml
230
150
60
120
30
90
150
120
170
950
2310
1180
60
90
120
120
30
980
3430
1480
180
12
%
3.8
2.5
1.0
2.0
0.5
1.5
2.5
2.0
2.8
15.6
38.1
19.4
1.0
1.5
2.0
2.0
0.5
98.;
16.1
56.5
24.4
3.0
13a
#/ml %
200
120
200
90
90
640
30
1360
30
30
30
90
120
290
30
610
2120
590
30
6.0
3.6
6.0
2.7
2.7
19.1
0.9
40.6
0.9
0.9
0.9
2.7
3.6
8.7
0.9
100.0
18.2
b. 3
17. b
0.9
13
#/ml %
290 6.4
30 0.7
200 4.4
40 0.9
90 2.0
290 6.4
1560 34.5
1450 32.1
90 2.0
120 2.6
90 2.0
120 2.6
--- 96.6
560 12.4
1940 42.9
1660 36.7
~~n 8.0
A COr i
-------
o
I
TABLE D4
COMMON PHYTOPLANKTON SPECIES
SOUTHERN LAKE MICHIGAN
Cruise 4 (September 17-24, 1977)
Species
Aster ionel la formosa
Cyclotella spp.
Diatoms tenue var. elongatum
Fragilaria crontonensis
Melosira spp.
Nitzchia spp.
Rhizosolenia eriensis
Rhizosolenia longiseta
Synedra acus
Tabellaria fenestrata
Tabellaria flocculosa
Cryptomomas ovata
Cryptomonas spp.
Dinobryon spp.
Miscellaneous flagellates
Anabaena spp.
Anacystis spp.
Aphanothece spp.
Chroococcus spp.
Gomphosphaeria lacustris
Microcoleus lyngbyacus
Oscillatoria limnetica
Ankistrodesmus falcatus
Crucigenia quadrata
Crucigenia rectangularis
Percent of Total
Total Diatoms
Total Flagellates
Total Blue Green Algae
Total Green Algae
Total Phytoplankton
#/ml
290
120
1270
60
30
60
90
140
170
840
30
2140
170
30
120
2060
3210
490
330
6090
16
4.8
2.0
20.8
1.0
0.5
1.0
1.5
2.3
2.8
13.8
0.5
35.1
2.8
0.5
0.5
3.3
0.5
2.0
95.7
33.8
52.7
9.0
5.4
STATIONS
16b 17
#/ml % #/ml %
380
120
30
260
30
60
30
60
690
290
1270
260
30
30
60
1000
2250
320
240
3810
10.0
3.1
0.8
6.8
0.8
1.6
0.8
1.6
18.1
7.6
33.3
6.8
0.8
1.6
94.5
26.2
59.1
8.4
6.3
60
30
30
30
430
60
460
400
60
30
120
1040
580
120
1860
3.2
1.6
1.6
1.6
23.1
3.2
24.7
21.5
3.2
1.6
1.6
87.1
fa. 4
59.1
31.2
6.4
18
#/ml %
30
60
430
690
30
1590
90
60
.511
1180
1770
60
3040
1.0
2.0
14.1
22.7
1.0
52.3
3.0
2.0
98.1
l.U
38.8
58.2
2.0
19
#/ml %
90
90
90
90
640
1360
520
60
30
150
lou
2090
760
30
3150
2.9
2.9
2.9
2.9
20.3
43.2
16.5
1.9
0.9
4.8
99.2
0. /
66.3
24.1
0.9
20a
#/ml %
60
30
30
30
60
750
580
720
120
140
90
30
ISO
1420
1100
60
2730
2.2
1.1
1.1
1.1
2.2
27.4
21.2
26.4
4.4
5.1
3.3
1 • 1
96.6
5.5
52.0
40.3
2.2
20
#/ml %
150
150
920
60
90
550
1160
1110
90
60
3U
30
1280
1830
1290
120
4490
3.3
3.3
20.5
1.3
2.0
12.2
25.8
24.7
2.0
1.3
0.7
0.7
97.8
aa.s
40.8
28.7
2.7
-------
ro
o
TABLE D4
COMMON PHYTOPLANKTON SPECIES
SOUTHERN LAKE MICHIGAN
Cruise 4 (September 17-24, 1977)
Species
Aster ionel la formosa
Cyclotella spp.
Diatoms tenue var. elongatum
Fragilaria crontonensis
Melosira spp.
Nitzchia spp.
Rhizosolenia eriensis
Rhizosolenia longiseta
Synedra acus
Tabellaria fenestrata
Tabellaria flocculosa
Cryptomomas ovata
Cryptomonas spp.
Dinobryon spp.
Miscellaneous flagellates
Anabaena spp.
Anacystis spp.
Aphanothece spp.
Chroococcus spp.
Gomphosphaeria lacustris
Microcoleus lyngbyacus
Oscillatoria limnetica
Anki strodesmus falcatus
Crucigenia quadrata
Crucigenia rectangularis
Percent of Total
Total Diatoms
Total Flagellates
Total Blue Green Algae
Total Green Alqae
21
#/ml %
350
170
170
1330
60
120
90
120
90
350
350
230
810
750
2800
260
30
150
200
—
3200
4650
500
260
4.1
2.0
2.0
15.4
0.7
1.4
1.0
1.4
1.0
4.1
4.1
2.7
9.4
8.7
32.5
3.0
0.3
1.7
2.3
97.8
37.2
54.0
5.8
3.0
STATIONS
21 a 22
#/ml % #/ml %
60
90
60
60
120
430
350
1470
30
140
90
30
—
180
1060
1710
1.9
2.8
1.9
1.9
3.8
13.6
11.0
46.4
0.9
4.4
2.8
0.9
99.8
6.1
35.6
58.0
60
60
60
60
30
400
140
430
30
1530
90
30
30
—
180
1060
1710
2.0
2.0
2.0
2.0
1.0
13.6
4.7
14.6
1.0
51.9
3.0
1.0
1.0
99.8
6.1
35.9
58.0
23
#/ml %
120
60
870
1160
90
840
90
—
180
2030
1020
60
3.6
1.8
26.4
35.2
2.7
25.5
2.7
97.9
5.5
61.7
31.0
1.8
24a
#/ml %
120
30
30
120
720
1010
640
120
30
—
180
1850
790
30
oocn
4.2
1.0
1.0
4.2
25.3
35.4
22.5
4.2
1.0
98.8
6.3
64.9
27.7
1.0
24
#/ml %
60
—
60
920
610
230
2250
30
—
60
1650
2540
60
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1.4
1.4
21.3
14.1
5.3
52.2
0.7
96.4
1.4
38.3
5.3.9
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