EPA-905/9-74-017
US. BIVIRONMOirAL PROHOION AGBCY
REGION V DIOIKEMDIT DIVISION
GREAT LAKES INmATWE CONTRAQ PROGRAM
JUNE 1975
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Copies of this document are available
to the public through the
national Technical Information Service
Springfield, Virginia 22161
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WATER POLLUTION INVESTIGATION: LOWER GREEN BAY
AND LOWER FOX RIVER
by
Dale J. Patterson
Earl Epstein
James McEvoy
WISCONSIN DEPARTMENT OF NATURAL RESOURCES
DIVISION OF ENVIRONMENTAL STANDARDS
In fulfillment of
EPA Contract No. 68-01-1572
for the
U.S. ENVIRONMENTAL PROTECTION AGENCY
Region V
Chicago, Illinois 60604
Great Lakes Initiative Contract Program
Report Number: EPA-905/9-74-017
EPA Project Officer: Howard Zar
June 1975
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This report has been developed under auspices of the Great Lakes
Initiative Contract Program. The purpose of the Program is to
obtain additional data regarding the present nature and trends in
water quality, aquatic life, and waste loadings in areas of the
Great Lakes with the worst water pollution problems. The data thus
obtained is being used to assist in the development of waste discharge
permits under provisions of the Federal Water Pollution Control Act
Amendments of 1972 and in meeting commitments under the Great Lakes
Water Quality Agreement between the U.S. and Canada for accelerated
effort to abate and control water pollution in the Great Lakes.
This report has been reviewed by the Enforcement Division, Region V,
Environmental Protection Agency and approved for publication. Approval
does not signify that the contents necessarily reflect the views of
the Environmental Protection Agency, nor does mention of trade names or
commercial products constitute endorsement or recommendation for use.
m
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The authors of this report wish to thank the many people who contributed
their time and energies to the completion of this project. In particular,
Steve Jaeger and Marc Bryans spent many long hours assembling the data
from past reports and present surveys, Joe Ball headed the field work
operations, James Wiersma (University of Wisconsin-Green Bay) supervised
the water chemistry analysis and finally, Kwang Lee (University of
Wisconsin-Green Bay) developed the hydrodynamic model that made the
development of the Green Bay water quality model possible.
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ABSTRACT
The lower third of Green Bay and the Lower Fox River were intensively studied. Seven
surveys of the Bay were carried out between September 1973 and September 1974. Over
40 stations were sampled for 15 different chemical and physical parameters. In
addition, plankton samples were taken and general groupings and counts were made.
Nearly 5,000 data points were generated and inserted into the STORET system. The
surveys revealed algae blooms over the entire study area. Nitrogen forms showed
fluctuations over 3 orders of magnitude that may be relatable to nitrogen-fixing
algae. Phosphorus concentrations were more stable than nitrogen concentrations,
but appeared to decrease in correspondence to blue-green nitrogen-fixing algae.
Dissolved oxygen concentrations in the Bay were generally acceptable except during
the winter survey. The February survey revealed critical dissolved oxygen levels
over a 50 sq. mile area north of Point Sable.
Computer models of the Lower Fox River and Green Bay were developed and used to
evaluate the effect of the final limits for the present discharge permits at all
point source discharges on the water quality, specifically dissolved oxygen. The
most critical dissolved oxygen case was determined by the model to be the summer
low flow and high temperature condition in the river. The final discharge limits
from the present permits was shown to be inadequate to meet fish and aquatic life
standards with regard to dissolved oxygen (5 mg/1) and may even violate the variance
dissolved oxygen standards now in force. A proposed "waste load allocation" to
maintain 5 mg/1 of DO was developed. The WLA calls for a 37% decrease in BOD and
suspended solids from the final discharge levels on the present permits.
vii
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CONTENTS
Page
Introduction ^
Scope of the Study. 5
The Data Base for Green Bay 7
Water Quality Modelling 75
Lower Fox River Modelling. 76
Lower Fox River Waste Load Allocation 101
Green Bay Modelling 118
Winter Modelling of Green Bay 120
Winter Verifications 128
Winter Prediction Runs 141
Discussion and Conclusions 155
Summary and Recommendations 171
Bibliography 177
Appendix A - Planktonic Algae Survey on Green Bay, 1974 183
Appendix B - Description of Methods for Chemical Analysis of
Water Samples 185
Appendix C - Benthic Oxygen Demand 189
Appendix D - GBQUAL Program Documentation 195
Appendix E - Hydrodynamic Model 293
Appendix F - Green Bay Survey Data 3Q3
ix
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LIST OF TABLES
Page
III-l Sampling Sites 11
III-2 Genera of Algae Observed 68
III-3 Algae Counts 70
III-4 Average Chlorophyll-a and Average Biomass 73
IV-1 Lower Fox River Physical Data 91
1V-2 Fox River Inflow Concentrations for Prediction Runs .... 102
IV-3 Fox River Measured Inflow Concentrations 102
IV-4 Percent Suspended Solids Reductions 104
IV-5 BPT Discharges for the Fox River 106
IV-6 WLA Discharges for the Fox River 112
IV-7 Green Bay Measured Inflow Concentrations 131
IV-8 Green Bay Simulation Inflow Concentrations 142
V-l Sensitivity of the QUAL-II Model on the Lower Fox River . . 162
V-2 Base Conditions for Sensitivity 164
C-l Benthic Demand in Fox River 190
D-l GBQUAL Computing Limits 203
D-2 Summary of GBQUAL Equations 208
D-3 Parameter Values for GBQUAL 222
D-4 ISWTCH Values for GBQUAL Simulations 223
xi
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LIST OF FIGURES
Page
1-1 Green Bay Region 2
1-2 Detail Map of Green Bay 3
III-l Green Bay Sampling Stations 10
III-2 to 111-20 Survey Data Results 18
111-21 to 111-25 Distribution of Dominant Algae 60
IV-1 Fox River Modelling Segments 77
IV-2 to IV-5 June 1972 Verifications 87
IV-6 Chlorophyll-a Data 93
IV-7 to IV-11 July and August 1972 Verifications 94
IV-12 to IV-13 BPT Prediction Simulation 107
IV-14 BPT Dynamic Simulation for Algae Effect HO
IV-15 to IV-17 Waste Load Allocation Simulation 113
IV-18 WLA Dynamic Simulation for Algae Effect H7
IV-19 Long Term BOD at Fox River Mouth and
Fitted Curve 122
IV-20 Temperature Coefficient Correction 127
IV-21 Long Term BOX at 20°C and 4°C 129
IV-22 to IV-24 Green Bay Model Verification for 1967
Winter Data 132
IV-25 Survey Data for 1967 135
IV-26 to IV-29 Green Bay Model Verification for 1974
Winter Data 137
IV-30 to IV-37 BPT Prediction Simulation for 2,400 CFS
and 912 CFS 144
IV-38 Fifty-day BOD for Green Bay Model
Simulation of BPT 152
V-l Lower Fox River Hydrograph for Study Period . . . 166
xiii
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LIST OF FIGURES (Continued)
Page
C-l Benthic Demand in Green Bay 192
C-2 Benthic Demand Measuring Box 193
D-l Green Bay Model Schematization 193
D-2 Green Bay Model Chemical and Biological
Pathways 199
D-3 Continuously Mixed Element 200
D-4 Functional Data Flow in GBQUAL 202
D-5 Solution in T and J Space 205
D-6 Normalized Algae Growth Rates 213
D-7 DYNQUA Flow Chart 224
D-8 INDATA Flow Chart 239
D-9 COEFF Flow Chart 251
D-10 METDAT Flow Chart 262
D-ll QUALEX Flow Chart 268
D-12 GBQUAL Data Set Up 273
D-13 Hydrodynamic Plot 274
E-l Space Staggered Scheme for the Hydrodynamic
Model 297
E-2 Grid Scheme for Green Bay Hydrodynamic Model . . 299
xiv
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SECTION I
I. INTRODUCTION
Green Bay is a long, narrow bay in the northwest corner of Lake Michigan. It has a
length of about 120 miles and averages about 20 miles in width. The Bay extends
over a generally southwest to northeast axis. Several rivers flow into the Bay
from the west and south, none from the east. Figures 1-1 and 1-2 show Green Bay
and its setting.
The most important tributary to Green Bay is the Lower Fox River, which enters at
the extreme southern end of the Bay. The Lower Fox River is approximately 40 miles
long. Several dams subdivide the river into a series of segments and provide
electrical power for a large population and a heavy concentration of paper and
pulp mills. The Lower Fox River provides a source of municipal and industrial waste
which results in pollution problems over a large area of Lower Green Bay. Locally
intense but smaller areas of pollution occur at the mouth of the Oconto, Peshtigo
and Menominee Rivers.
The water pollution in the Lower Fox River and Green Bay region has caused the U.S.
Environmental Protection Agency (EPA) and the Wisconsin Department of Natural
Resources (WDNR) to initiate a series of enforcement actions which involve industrial
and municipal waste discharges in the area. Also, the 1972 Amendments to the Federal
Water Pollution Control Act (Public Law 92-500) require that municipalities shall
provide, as a minimum, secondary treatment, and industries shall achieve "Best
Practicable Technology" (BPT) by no later than 1977. The law also requires that
the industries shall use "Best Available Technology" (BAT) to control water pollution
by 1983.
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FIGUEE 1-1
N
29
SO
IOO
I
SCALE IN MILES
GREAT LAKES 8 ILLINOIS
RIVER BASINS PROJECT
GREEN BAY AREA
MICHIGAN AND WISCONSIN
US DEPT. OF HEALTH. EDUCATION, & WELFARE
FEDERAL WATER POLLUTION CONTROL ADMIN.
REGION CHICAGO, ILLINOIS
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Munlcipal waste treatment plants must apply BPT over the life of the treatment works
by 1983. New public waste treatment plants must use the best available technology
after 1983. The Amendments also require that system water quality standards must
be met.
The purpose of this work was to conduct a survey of the Lower Fox River and of' Lower
Green Bay. Emphasis was placed on those parameters which describe the quality of the
water. In addition, a goal of the work was to predict future water quality conditions
by means of a mathematical model adapted to the Lower Fox River and to the Bay.
The scope of the study is discussed in Section II. The results of past studies and
of the data collected in this study which constitute the data base for Green Bay are
presented in Section III. The data analysis and projection which constitutes the
water quality modelling appear in Section IV. A discussion of the results appears
in Section V. Recommendations appear in Section VI. References are listed in
Section VII. Appendices appear in Section VIII.
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SECTION II
II. SCOPE OF THE STUDY
Task I - Historical Data Analysis: An evaluation of the existing and historical
conditions in Lower Green Bay was carried out and the results published in August
1974 (Epstein et al, 1974). This information was contained in the reports of
studies carried out intermittently between 1939 and 1973. In addition the report
lists the sources and quantity of waste discharge to Green Bay from municipalities
and industries along the Lower Fox, Peshtigo, Oconto and Menominee Rivers.
Task II - Field Sampling; A sampling program was designed to improve the adequacy
of the water quality data for Lower Green Bay and to provide sets of data for
verification of the mathematical model. Seven surveys were conducted over the
period September 1973 to September 1974 in the region below Sturgeon Bay. One
intensive survey was conducted in February of 1974 when the Bay was ice-covered,
a condition which has led to critical oxygen levels in parts of the region below
Sturgeon Bay.
Task III - Effluent Analysis; The Lower Fox, Oconto, Peshtigo and Menominee Rivers
are the major tributaries to Lower Green Bay. The flow rates and concentrations
of various dissolved and suspended materials for these rivers indicate that, as
a quantitative source of pollution, the Lower Fox River exceeds the other rivers
by nearly an order of magnitude. The sources and quantity of both municipal and
industrial discharge to these rivers are presented in the Task I report, Epstein
et al (1974). These data include projections of the waste loadings by industries
of suspended solids and of five-day biochemical oxygen demand (BOD^) to the various
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rivers for the years 1975, 1976 and 1977. These projections are based on the
amounts specified in the Wisconsin Pollution Discharge Elimination (WPDES) permits
for these industries.
Task IV - Data Analysis and Projection; A description of present water quality,
a projection of future conditions and a specification of problem areas has been
made. A water quality model has been prepared for the Lower Fox River and for
Lower Green Bay based in part on models developed for the coastal estuaries of
San Francisco Bay and Pearl Harbor and partly on programs developed specifically
for this task. This package of programs is the principal tool for the projections
of water quality that would result if effluent guidelines established by the EPA
administrator under Sections 301(b)(l)A, 301(b)(l)B, 301(b)(2)A and 301(b)(2)B
of the 1972 Amendments to the Federal Water Pollution Control Act are met. If
stream standards are not met by adherence to the provisions of the law, then
calculations are to be made of those effluent levels which will suffice for the
"protection of fish, shellfish and wildlife and provide for recreation in or on
the water."
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SECTION III
III. THE DATA BASE FOR GREEN BAY
Task I - Historical Data Analysis; Extensive investigations of Green Bay have
been carried out intermittently since 1939. A major emphasis in many of these
investigations has been on measurements of the concentration of dissolved oxygen
(DO) and biochemical oxygen demand (BOD). Measurements of the concentrations
of various nutrients (nitrogen and phosphorus containing species) have also been
a significant part of several of these investigations. However, the effects of
these nutrients on the growth of algae and other species have only recently been
a subject of intensive investigations. The Sea Grant program at the University
of Wisconsin has generated several studies on Green Bay in recent years. A summary
of the results of the Green Bay surveys appear in the Task I report, Epstein et
al (1974). Reference to this report will be made for the purpose of qualitative
comparisons with the results of t'"is investigation.
The following are the major subjects of extensive study in past surveys:
Dissolved Oxygen and Biochemical,Oxygen Demand; The concentrations of these species
were measured extensively throughout Lower Green Bay in 1939, 1956, 1966 and 1967.
The concentration of dissolved oxygen was generally lower for the period when the
Bay was ice-covered. The same general pattern of dissolved oxygen concentration
was observed throughout this period.
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During the period of ice-cover (the months of January, February, March and part
of April), water in the Lower Fox River generally was found to have a dissolved
oxygen concentration greater than 5 mg/1. However, a front of low oxygen
concentration develops in the Bay within Long Tail Point. This front moves northward
along the eastern half of Lower Green Bay for distances of 20-30 miles by the
end of the period of ice-cover. In 1939, concentrations of dissolved oxygen dropped
to values of 3-4 mg/1 in the front. In 1967, no dissolved oxygen was observed
near the bottom of the Bay for a wide portion of the front. Conditions are less
severe during the period of open water due to reaeration. During the late summer
the Lower Fox River has very low or no dissolved oxygen. However, oxygen recovery
in the Bay is rapid, especially north of Long Tail Point.
Biochemical oxygen demand (BOD) has been measured less extensively and intensively
than dissolved oxygen. As a result, it is not possible to make a generalization
about the pattern of BOD concentrations over the past 35 years. However, sufficient
data exists to show that loadings of BOD to the Lower Fox River have not changed
significantly when compared with those of 20 years ago. This is due to improved
treatment by municipalities and industries offsetting a significant increase
in population and industrial production.
Nutrients; The change in concentrations of nutrients (nitrogen and phosphorus
containing species) over the past 35 years is difficult to determine because data
from earlier years is spotty or lacking entirely. The concentration of nitrogen
and phosphorus containing species in Lower Green Bay has been a subject of
considerable interest in the last few years. In addition to concentration,
the dispersal and diffusion, the release and uptake rates by the sediments and
the effect on algae growth rates of these species have been investigated in
Lower Green Bay in past studies.
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Flow Distribution; The flow patterns in Green Bay have not been investigated
directly. Historically, qualitative descriptions of flow patterns have been based
on observations of oxygen concentrations or on the concentration gradients of
other ions.
Benthic Fauna; Several studies since 1939 have measured the populations of bottom
dwelling species. These studies show an increasingly large abiotic area near
the mouth of the Lower Fox River. Throughout the Lower Bay the population of
pollution intolerant species has fallen in relation to pollution tolerant species
in the last twenty years.
Algae Growth; The response of the Bay to the various nutrients has been a subject
of considerable study in recent years. For the period before about 1968, data
is limited. Recent investigations have indicated that the total algae population
may be about the same each summer but that the distribution may vary widely from
year to year.
Task II-Field Sampling; The sampling program included surveys in September
1973, February, May, June, July, August and September 1974. Nearly seventy station
sites were designated in that portion of Green Bay below Sturgeon Bay. Not all
of the stations were visited in the winter survey (February 1974) and not all
parameters were measured in each survey. Several extra sites were visited to measure
DO during the winter survey. The sampling schedule was designed to provide data
from a variety of temperature, flow and nutrient discharge conditions. The
selections of sites and of the parameters to be measured in a particular survey were
based on an analysis of the results of earlier surveys and the requirements and
capabilities of the mathematical model. The station sites and the parameters
measured at these sites are shown in Figure 1II-1 and Table III-l.
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- 10 - FIGURE III-l
Sampling Stations Used for the Green Bay Study Surveys
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TABLE III-l
Station
1
2
3
3a
4
5
5a
6
7
8
8a
8b
8c
9
9a
9b
9c
10
11
12
13
13a
14
I4a
15
16
16a
16b
16c
17
18
19
Winter* Summer*
b
a
b
a
b
a
b
b
b
b
a
b
a
b
a •
b
a
b
a
b
b
b
a
b
a
b
b
a
b
x
a
x
b
b
a
x
b
a
x
b
b
a
x
x
b
a
x
b
X
a
a
b
b
a
b
x
a
a
a
x
x
b
c
a
Station
21
23
24
25
26
26a
27
27a
27b
27c
28
29
30
31
31a
32
32a
32b
32c
33
34
34a
34b
35
36
38
39
40
41
42
43
44
45
Winter
x
X
b
b
a
a
a
b
a
b
x
x
b
a
b
a
a
a
a
b
b
b
b
x
b
a
x
a
b
x
b
x
b
Summer
a
a
b
a
c
x
b
x
x
X
c
c
a
b
x
a
x
X
X
c
a
a
x
b
a
c
a
c
c
a
b
a
b
a DO; temperature; secchi disk
b DO; temperature; secchi disk, plankton samples at 1-1/2 meter depth; water
samples from the top two meters (if the depth exceeded 25 feet, then a water
sample was taken at 5-10 feet from the bottom.
c the same as b except that plankton samples were not taken
x no sample
* The winter survey was taken on February 18-20, 1974. The summer surveys were
taken on September 24-25, 1973, May 20-23, June 3-7, July 8-9, August 12-14,
and September 4-5, 1974.
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The results of the field sampling program in 1973 and 1974 are summarized in Figures
III-2 to 111-20. The details of the data obtained and of the techniques employed
are presented in Appendices E and F.
Dissolved Oxygen: DO concentrations in the summer are generally above 5 mg/1,
through-out the region above Long Tail Point despite the fact that the Lower Fox
River may contain little or no dissolved oxygen. These concentrations reflect
the rapid oxygen recovery due to reaeration. There are exceptions to this generality.
At the end of the summer, when flow rates are relatively low, oxygen concentrations
as low as 3 mg/1 were observed near the bottom. The region where these concentrations
were observed extended for 20-30 miles north of Long Tail Point. This region
coresponds to the maximum northward extension of the front of low DO observed
under the ice during the winter months. The low oxygen concentrations near the
bottom in summer may reflect a combination of effects. Part of the low DO may
be due to the continuing effect of sludge deposits which accumulate at this distance
from the mouth of the Lower Fox River.
Indirect evidence also suggests that a substantial oxygen deficit in these areas
is the result of nitrification activity. During the July and August surveys the
build-up of nitrate in the bottom waters of these areas is most apparent. Levels
as high as 1.0 mg/1 NO^-N were measured. This could account for as much as 4.5
mg/1 of DO deficit. There are two sources of ammonia for this nitrification.
Dead phytoplankton from surface blooms will settle to the bottom bringing along
organic nitrogen and carbon compounds. The sediments also contain organic nitrogen
compounds. These compounds will undergo hydrolysis which results in the release
of ammonia which may nitrify. Support for this theory is found in the nitrate
levels which most noticeably increased during the period of highest blue-green
algae activity (July and August).
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In February 1974, there was a front of low oxygen concentration (about 3 mg/1)
near the bottom in the region about 7 miles north of Long Tail Point. This front,
its position at the time of year and the low oxygen concentration are generally
consistent with observations in other years. Precise comparisons are difficult
because the flow rates in the years 1939, 1966, 1967 and 1974 differ from one
another by more than 10% and the length of time under ice cover is not the same
for all the years. Generally} the BOD loading in 1974 was slightly less than
that in 1967 for the Lower Fox River (230,000 #/day versus 275,000 #/day in 1967).
The observed higher flows during the winter of 1974 compared to 1967 creates
the expectation of generally higher DO levels in the Inner Bay and a front of
low DO further out into the Bay. In 1967 when the average winter flow was 3380.
CFS, extensive areas of zero DO were measured. Zero DO was discovered as close
to the mouth of the Fox River as Point Sable. In 1974 (average winter flow of
4853 CFS) no zero DO concentrations were observed. The lowest values observed
were between 1.5 and 2.0 mg/1 in the Dykesville area, nearly 8 miles further north
than in 1967.
BOD; The BOD concentration within Lower Green Bay varied considerably with the
season of the year. In May and June, when temperatures were still rather cold,
concentrations of about 10 mg/1 were observed within Long Tail and for some distance
beyond. These concentrations then fell rapidly to values of 2-3 mg/1 beyond Long
Tail Point. Later in the summer, values of about 6 mg/1 were observed within
Long Tail Point. These values fell rather slowly to 4-5 mg/1 near Sturgeon Bay.
The concentrations for the spring of 1974 are rather similar to those observed
for the same period in 1939. In June of 1955 values as high as 15 mg/1 were
observed within Long Tail Point.
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In February 1974, concentrations of BOD at the mouth of the Lower Fox River were
about 6 mg/1. Well beyond Long Tail Point values of about 2 mg/1 were observed.
However, at about 10-15 miles beyond Long Tail Point an area of high BOD was observed
along the eastern half of the Bay. Values here were as high as 13.5 mg/1 on the
bottom and 9 mg/1 on the top. The high BOD corresponded to the position of low
dissolved oxygen. In 1939 a similar pattern was observed although the concentrations
were higher at the mouth of the river and lower in the region of high BOD beyond
Long Tail Point.
The consumption of BOD is dependent primarily on the temperature dependent reaction
rates. The observed concentrations of BOD in Green Bay reflect this dependence
quite well.
The surveys of May and June 1974 indicate substantial increases in BOD_
concentration near and slightly beyond the Long Tail Point area. This pattern
coupled with a measurement in the Fox River in July that exceeded 30.0 mg/1,
suggests the possibility that large slug-loadings of BOD to the river-Bay
system occur. This effect could be a physical phenomena resulting from seiche
waves in Green Bay that tend to stagnate the river flow from De Pere to the
mouth of the river. During the period of stagnation, BOD may build up to
high concentrations before being swept out into the Bay by the receding
portion of the seiche wave. The high BOD may, of course, come from slug loads
from dischargers in the Green Bay area.
The seiche effect in the vicinity of the mouth of the Lower Fox River is important
for this regard only when a northeast wind blows large quantities of water back
up into the river stretch from De Pere to Green Bay. No attempt was made to
include this effect in the Bay model since the hydrodynamics of the model are steady
state.
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Nitrate; Concentrations of nitrogen as nitrate vary widely with the season of
the year. In February 1974 the concentration of nitrate ion was approximately
0.10 mg/1 over a wide region of the Inner Bay. This region corresponded closely
to the portion of the Inner Bay which had low oxygen concentrations at the same
time (the region within Long Tail Point plus the region outside Long Tail Point
and along the eastern shore for about 20-30 miles). Beyond this region there
where large negative gradients in concentrations of nitrogen as nitrate and
background concentrations of 0.01 mg/1 and less were observed.
In May, concentrations of nitrogen as nitrate reached values of 0.20-0.40 mg/1 in
some portions of the region within Long Tail Point. Beyond this pointy concentrations
fell slowly to values of 0.02 mg/1 in areas of the Central Bay. However,
concentrations near the bottom were often significantly higher, reaching
values of 0.25-0.50 mg/1.
In June, the concentrations of nitrogen as nitrate reached values of 0.7 mg/1
at some points within Long Tail Point. Beyond, concentrations fell rapidly to
values of 0.05 mg/1 or less.
In August, concentrations were significantly reduced when compared with those
observed during the period of spring runoff. Within Long Tail Point, concentrations
were generally less than 0.10 mg/1. Beyond this point, concentrations fell to
values less than 0.03 mg/1. However, near the bottom concentrations in the range
0.7 to 1.0 mg/1 Were consistently observed. Concentrations in September were
not significantly different from those in August. High concentrations near the
bottom may reflect the effect of release of nitrogen containing compounds by dead
algae. The conversion of these organic nitrogen compounds to nitrate may also
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account, in part, for the low oxygen concentrations near the bottom. The largest
significant increase in nitrate near the bottom corresponds to the period of die-
off of the blue-green algae bloom during late June and early July. According
to Vanderhoef et al (1972) , a large fraction of this nitrate may come from nitrogen
fixation.
Ammonia; Concentrations of nitrogen as ammonia were in the range 0.5-0.7 mg/1
in February 1974 throughout the region of the Bay where low oxygen was observed.
At low temperatures, reduced rates of ammonia decay to nitrite and nitrate cause
high concentrations of ammonia. Reduced concentrations of oxygen also contributed
to a high ammonia concentration. In the spring, runoff brings large quantities
of ammonia. The warmer temperatures and the increased level of oxygen in the Bay
cause the concentration of ammonia to fall rapidly as distance from the mouth
of the Lower Fox River increases. Ammonia utilization by phytoplankton also
contributes to the nearly complete disappearance of ammonia by August.
Phosphorus ; The seasonal variation of total phosphorus concentration as phosphorus
was less than the corresponding seasonal variation in nitrogen concentration as
nitrate. The dramatic rise in nitrogen concentration observed during the spring
runoff was not observed for phosphorus. During the spring runoff, the area of
the Bay in which the concentration of total phosphorus as P was greater than 0.5
mg/1 approximately doubled in size when compared with concentrations in February,
the several-fold increase in concentration observed for nitrate was not observed
for the phosphorus species. The seasonal pattern for orthophosphate paralleled
that of total phosphorus. The ability of the bottom sediments to hold and release
phosphorus containing ions may account for the more stable levels of phosphorus ions
over the various seasons. Local fluctuations in time of the concentrations of
phosphorus containing ions have been correlated with the bloom of certain blue-green
algae. This point will be discussed later.
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Total phosphorus concentrations appeared to reach their minimum values during the
winter months when quiesent water allows particulate phosphorus to settle to the
sediments. Total phosphorus increased between the February and May surveys by about
5-fold. Between the May survey and the June survey the total phosphorus in the
Oconto-Sturgeon Bay area nearly tripled. It is doubtful whether this increase
can be totally accounted for by spring runoff. A significant amount of phosphorus
may be released from sediments that are resuspended by wind and wave action in
the shallow areas and along the shoreline. The release of phosphorus from the
sediments may be enhanced by the mixing of the water during spring (and fall)
turnover.
Temperature; In May, temperatures varied from 16°C at the mouth of the Lower
Fox River to 7-8°C in the central Bay. Variations in temperature from top to
bottom were rarely as much as 1°C. As the summer progressed Say temperatures
not only became warmer but the thermal gradients (top to bottom) increased
dramatically. In August, temperatures near the surface ranged from 23°C at the
mouth of the Lower Fox River to 18-19°C in the central Bay. At this time, gradients
as large as 10"C (top to bottom) were observed in the central Bay.
Chlorophyll-a; Chlorophyll-a concentrations generally increased throughout the
summer. In May» concentrations of chlorophyll-a in the Inner Bay ranged between
10 and 20 ug/1. Beyond Long Tail Point, Chlorophyll-a concentrations were generally
below 10 ug/1. During the summer the chlorophyll-a increased within the Inner
Bay at the rate of about 10 ug/1 per month. Between July and August this rate
of increase jumped dramatically. The concentration went from 30 and 40 ug/1
to as high as 100 ug/1. The month of August showed the highest levels of
chlorophyll-a at all locations. Concentrations as high as 70 ug/1 were found in
-------
- 18 -
FIGURE III-2
Dissolved Oxygen Contours
in Lower Green Bay
The dissolved oxygen was found to be
at or above saturation at the one
meter depth except very close to the
mouth of Lower Fox River. Also dur-
ing the February survey, very low
dissolved oxygen was observed at all
depths in the Red Banks area.
D.O. MG./L
DEPTH = 1 M.
SEPTEMBER 24-25
1973
D.O. MG./L.
DEPTH = 1 M.
JUNE 3-7
1974
D.O. MG./L.
DEPTH = 1 M.
JULY 8-9
1974
-------
- 19 -
D.O. MG./L.
DEPTH = T M.
FEBRUARY 18-20
1974
D.O. MG./L.
DEPTH = 1 M.
AUGUST 12-14
1974
D.O. MG./L.
DEPTH = 1 M.
MAY 20-23
1974
D.O. MG./L.
DEPTH = 1 M.
SEPTEMBER 4-5
1974
-------
- 20 -
FIGURE III-3
Dissolved Oxygen Contours
in Lover Green Bay
Dissolved oxygen levels at the 3
meter depth vere generally high but
slightly below the measured values
at 1 meter depth. In addition to
the areas of lov dissolved oxygen
mentioned in Figure III-2, depressed
DO's vere seen at this depth off the
mouth of the Oconto River.
D.O. MG./L.
DEPTH = 3 M.
JUNE 3-7
1974
D.O. MG./L.
DEPTH = 3 M.
SEPTEMBER 24-25
1973
D.O. MG./L.
DEPTH = 3 M.
JULY 8-9
1974
-------
- 21 -
D.O. MG./L.
DEPTH = 3 M.
FEBRUARY 18-20
1974
D.O. MG./L.
DEPTH = 3 M.
MAY 20-23
1974
D.O. MG./L.
DEPTH = 3 M.
AUGUST 12-14
1974
D.O. MG./L.
DEPTH = 3 M.
SEPTEMBER 4-5
1974
-------
- 22 -
FIGURE
Dissolved Oxygen Contours in
Lover Green Bay
Dissolved oxygen measurements at the
6 meter depth were slightly lower
than those at 1 and 3 meters. During
July, there was an area beyond Long
Tail Point at the 6 meter depth that
had low dissolved oxygen levels.
This area of low DO may be a result
of decaying algae cells or BOD from
the Lower Fox River.
D.O. MG./L.
DEPTH = 6 M.
SEPTEMBER 24-25
1973
D.O. MG./L.
DEPTH = 6 M.
JUNE 3-7
1974
D.O. MG./L.
DEPTH = 6 M.
JULY 8-9
1974
-------
- 23 -
D.O. MG./L.
DEPTH = 6 M.
FEBRUARY 18-20
1974
D.O. MG./L.
DEPTH = 6 M.
MAY 20-23
1974
D.O. MG./L.
DEPTH = 6 M.
AUGUST 12-14
1974
D.O. MG./L.
DEPTH = 6 M.
SEPTEMBER 4-5
1974
-------
- 24 -
FIGURE III-5
Dissolved Oxygen Contours
In Lover Green Bay
Only limited areas of the Lover Bay
are deeper than 9 meters. Dissolved
oxygen at this depth generally
decreased over the course of the
summer. This probably is a response
to decaying algae cells that sink
belov the thermocline.
D.O. MG./L.
DEPTH> 9 M.
JUNE 3-7
1974
D.O. MG./L.
DEPTH > 9 M.
SEPTEMBER 24-25
1974
D.O. MG./L.
DEPTH> 9 M.
JULY 8-9
1974
-------
- 25 -
D.O. MG./L.
DEPTH> 9 M.
FEBRUARY 18-20
1974
D.O. MG./L.
DEPTH> 9 M.
MAY 20-23
1974
D.O. MG./L.
DEPTH 9 M.
AUGUST 12-14
1974
D.O. MG./L.
DEPTH 9 M.
SEPTEMBER 4-5
1974
-------
- 26 -
FIGUBE III-6
Biochemical Oxygen Demand (BODj)
in Lover Green Bay
BODtj was generally less than 5 mg/1
beyond Long Tail Point except in
isolated cases. During the winter
survey, several samples of high BODj
in the area of low dissolved oxygen
were found. Samples in the Inner
Bay revealed BOD? concentrations
averaging more than twice those
further north. Water samples were
taken at the 1 meter depth. In
deeper areas (when stratification
was apparent from temperature or
DO data) a second water sample was
taken 2 meters off the bottom. All
drawings show only the surface sam-
ple.
5 DAY BOD
M6./L.
JUNE 3-7
1974
5 DAY BOD
MG./L.
SEPTEMBER 24-25
1973
5 DAY BOD
MG./L.
JULY 8-9
1974
-------
- 27 -
5 DAY BOD
MG./L.
FEBRUARY 18-20
1974
5 DAY BOD
MG./L.
MAY 20-23
1974
5 DAY BOD
MG./L.
AUGUST 12-14
1974
5 DAY BOD
MG./L.
SEPTEMBER 4-5
1974
-------
- 28 -
FIGURE I1I-7
Suspended Solids Contours
in Lover' Green Bay
Suspended solids were the highest in
all areas of the Bay during the Sept.
1973 survey. Those levels dropped
off dramatically by February 197^.
May shoved a large increase followed
by a general decrease until mid-
summer. Betveen August and September
of 197^, suspended solids vere again
increasing especially beyond Long
Tail Point.
SUSPENDED SOLIDS
MG./L.
JUNE 3-7
1974
SUSPENDED SOLIDS
MG./L.
SEPTEMBER 24-25
1973
SUSPENDED SOLIDS
MG./L.
JULY 8-9
1974
-------
- 29 -
SUSPENDED SOLIDS
M6./L.
FEBRUARY 18-20
1974
SUSPENDED SOLIDS
MG./L.
AUGUST 12-14
1974
SUSPENDED SOLIDS
MG./L.
MAY 20-23
1974
SUSPENDED SOLIDS
MG./L.
SEPTEMBER 4-5
1974
-------
- 30 -
FIGURE III-8
Temperature Contours
in Lover Green Bay
Surface temperatures varied about as
would be expected through the year.
Winter temperatures (not shown) ranged
from 0° C to 3° C. Highest tempera-
tures vere seen in July when 23.5° C
was observed in several areas. In
general the water in the Inner Bay
averaged 1 to 2° above that in the
main area of the Bay.
TEMP. °C.
DEPTH = 1 M.
JUNE 3-7
1974
TEMP. °C.
DEPTH = 1 M.
SEPTEMBER 24-25
1973
TEMP. UC.
DEPTH = 1 M.
JULY 8-9
1974
-------
- 31 -
TEMP. °C.
DEPTH = 1 M.
MAY 20-23
1974
TEMP. °C.
DEPTH = 1 M.
AUGUST 12-14
1974
TEMP. °C.
DEPTH = 1 M.
SEPTEMBER 4-5
1974
-------
- 32 -
FIGURE III-9
Temperature Contours
in Lover Green Bay
Temperatures at the 3 meter depth did
not vary significantly from those at
the surface. The difference between
the Inner Bay and the outer area vas
more significant in most surveys
ranging up to as much as 5° C.
TEMP. °C.
DEPTH = 3 M.
JUNE 3-7
1974
TEMP. "C.
DEPTH = 3 M.
SEPTEMBER 24-25
1973
TEMP. °C.
DEPTH = 3 M.
JULY 8-9
1974
-------
- 33 -
TEMP. °C.
DEPTH = 3 M.
AUGUST 12-14
1974
TEMP. °C.
DEPTH = 3 M.
MAY 20-23
1974
TEMP. °C.
DEPTH = 3 M.
SEPTEMBER 4-5
1974
-------
- 34 -
FIGUBE 111-10
Temperature Contours
in Lower Green Bay
The temperature measurements at 6
meters indicated the beginnings of
significant pattern changes from
those at 3 and 1 meters. Thermal
stratification was evidenced in all
areas of the Bay where the depth was
greater than about 6 meters. The
thermocline occurred at about a
depth of 6 meters.
TEMP. °C.
DEPTH = 6 M.
JUNE 3-7
1974
TEMP. °C.
DEPTH = 6 M.
SEPTEMBER 24-25
1973
TEMP. °C.
DEPTH = 6 M.
JULY 8-9
1974
-------
- 35 -
TEMP. °C.
DEPTH = 6 M.
MAY 20-23
1974
TEMP. °C.
DEPTH = 6 M.
AUGUST 12-14
1974
TEMP. °C.
DEPTH = 6 M.
SEPTEMBER 4-5
1974
-------
- 36 -
FIGURE III-ll
Temperature Contours
In Lover Green Bay
Nearly all the measurements taken at
or below 9 meters were below the
thermocllne. Marked temperature
stratification existed in these
areas. Vertical gradients as much
as 10° C were observed in some areas.
TEMP. °C.
DEPTH>9 M.
JUNE 3-7
1974
TEMP. °C.
DEPTH>9 M.
SEPTEMBER 24-25
1973
TEMP. °C.
DEPTH >9 M.
JULY 8-9
1974
-------
- 37 -
TEMP. °C.
DEPTH ^9 M.
MAY 20-23
1974
TEMP. °C.
DEPTH >9 M.
AUGUST 12-14
1974
TEMP. oc.
DEPTH>9 M.
SEPTEMBER 4-5
1974
-------
- 38 -
FIGURE 111-12
Organic Nitrogen Contours
in Lower Green Bay
Organic nitrogen levels fluctuated
considerably in the Bay, probably in
response to various algae blooms.
During the February survey of 1.97k,
high levels of organic nitrogen were
observed in the Dykesville area indi-
cating a possible winter algal bloom.
Organic nitrogen in the Inner Bay
generally exceeded .75 mg/1 except
for the February and May surveys.
ORGANIC NITROGEN
MG./L. AS N.
JUNE 3-7
1974
ORGANIC NITROGEN
MG./L. AS N.
SEPTEMBER 24-25
1973
ORGANIC NITROGEN
MG./L. AS N.
JULY 8-9
1974
-------
- 39 -
ORGANIC NITROGEN
MG./L. AS N.
FEBRUARY 18-20
1974
ORGANIC NITROGEN
MG./L. AS N.
AUGUST 12-14
1974
ORGANIC NITROGEN
MG./L. AS N.
MAY 20-22
1974
ORGANIC NITROGEN
MG./L. AS N.
SEPTEMBER 4-5
1974
-------
- 40 -
FIGURE 111-13
Ammonia Nitrogen Contours
in Lower Green Bay
Ammonia concentrations shoved a
regular pattern of decrease in the
Inner Bay on all summer surveys.
Concentrations between .8 and .2
mg/1 were regularly found in the
Inner Bay. Only during winter, when
nitrification is slowed by cold
temperatures, did higher ammonia
levels reach as far north as
Dykesville. Concentrations in
the area north of Long Tail Point
generally fell to a very low level
during the summer.
AMMONIA NITROGEN
MG./L. AS N.
SEPTEMBER 24-25
1973
AMMONIA NITROGEN
MG./L. AS N.
JUNE 3-7
1974
. AMMONIA NITROGEN
) MG./L. AS N.
JULY 8-9
1974
-------
- 41 -
AMMONIA NITROGEN
MG./L. AS N.
FEBRUARY 18-20
1974
7 AMMONIA NITROGEN |
J MG./L. AS N.
«.« K AUGUST 12-14
5^ 1974
r^
AMMONIA NITROGEN
MG./L. AS N.
MAY 20-23
1974
AMMONIA NITROGEN
MG./L. AS N.
SEPTEMBER 4-5
1974
-------
- 42 -
FIGURE Ill-Ik
Nitrite Nitrogen Contours
in Lower Green Bay
Nitrite concentrations were highest
in the Inner Bay. The winter survey
revealed the highest concentration of
nitrite observed in this study reach-
ing levels of .030 mg/1. The
concentration in the northern part
of the Bay fluctuated by about one
order of magnitude. The lowest
observed values were seen on the
September 1973 and July 1971* surveys.
NITRITE NITROGEN
MG./L. AS N.
SEPTEMBER 24-25
1973
NITRITE NITROGEN
MG./L. AS N.
JUNE 3-7
1974
NITRITE NITROGEN
MG./L. AS N.
JULY 8-9
1974
-------
- A3 -
NITRITE NITROGEN
MG./L. AS N.
FEBRUARY 18-20
1974
NITRITE NITROGEN
MG./L. AS N.
AUGUST 12-14
1974
NITRITE NITROGEN
MG./L. AS N.
MAY 20-23
1974
NITRITE NITROGEN
MG./L. AS N.
SEPTEMBER 4-5
1974
-------
- 44 -
FIGURE 111-15
Nitrate Nitrogen Contours
in Lover Green Bay
Nitrate nitrogen shoved dramatic
fluctuations in concentration during
the study period. The July 1971*
survey revealed an overall level of
nitrate much lover than in any other
survey. This pattern corresponds to
the bloom of nitrogen-fixing algae.
August and September 197** indicated
significant increases in nitrate in
all locations. Some of this increase
may be due to nitrogen released by
nitrogen-fixing algae cells that have
died and released their nitrogen.
Vanderhoef, et al (1972, 1973) have
suggested that ^0 percent of the
inorganic nitrogen contributed to
the Bay during the bloom period
(mid-June to mid-August) may come
from nitrogen fixing algae.
NITRATE NITROGEN
MG./L. AS N.
SEPTEMBER 24-25
1973
// NITRATE NITROGEN
MG./L. AS N.
JUNE 3-7
1974
NITRATE NITROGEN
MG./L. AS N.
JULY 8-9
1974
-------
- 45 -
NITRATE NITROGEN
MS./L. AS N.
FEBRUARY 18-20
1974
NITRATE NITROGEN
MG./L. AS N.
AUGUST 12-14
1974
NITRATE NITROGEN
MG./L. AS N.
MAY 20-23
1974
NITRATE NITROGEN
MG./L. AS N.
SEPTEMBER 4-5
1974
-------
- 46 -
FIGURE III-16
Total Phosphorus Contours
in Lower Green Bay
Total phosphorus did not fluctuate
nearly as much as the nitrogen forms.
The highest concentrations were con-
sistently found in the Inner Bay and
along the eastern half of the Bay.
Significant decreases in total
phosphorus concentrations occurred
between the July and August 1971*
surveys corresponding to the areas
of the blue-green algae bloom during
this period.
TOTAL PHOSPHATE
MG./L. AS P.
SEPTEMBER 24-25
1973
TOTAL PHOSPHATE
MG./L. AS P.
JUNE 3-7
1974
TOTAL PHOSPHATE
MG./L. AS P.
JULY 8-9
1974
-------
- 47 -
TOTAL PHOSPHATE
MG./L. AS P.
FEBRUARY 18-20
1974
TOTAL PHOSPHATE
MG./L. AS P.
AUGUST 12-14
1974
TOTAL PHOSPHATE
MG./L. AS P.
MAY 20-23
1974
TOTAL PHOSPHATE
MG./L. AS P.
SEPTEMBER 4-5
1974
-------
- 48 -
FIGURE 111-17
Ortho Phosphorus Contours
in Lover Green Bay
Ortho phosphorus concentrations j
shoved a nearly steady increase from
September 1973 until June 1971* at
nearly all locations. During the
last three surveys the concentrations
fell slowly to levels comparable to
the September 1973 concentrations.
ORTHO PHOSPHATE
MG./L. AS P.
SEPTEMBER 24-25
1973
ORTHO. PHOSPHATE
MG./L. AS P.
JUNE 3-7
1974
ORTHO PHOSPHATE
MG./L. AS P.
JULY 8-9
1974
-------
- 49 -
ORTHO PHOSPHATE
MG./L. AS P.
FEBRUARY 18-20
1974
ORTHO PHOSPHATE
MG./L. AS P.
AUGUST 12-14
1974
ORTHO PHOSPHATE
MG./L. AS P.
MAY 20-23
1974
ORTHO PHOSPHATE
MG./L. AS P.
SEPTEMBER 4-5
1974
-------
- 50 -
FIGURE 111-18
Chlorophyll-a Contours
in Lower Green Bay
Chlorophyll-a fluctuated most markedly I
in the lover one-third of the study j
area. Both September surveys shoved i
fairly uniform gradients of chl-a
ranging from 80 H- g/1 at the mouth
of the Fox River to about 20 /< g/1
around Dykesville. Betveen June and
August 1971*, concentrations grew
steadily. Concentrations over
100.0 /< g/1 vere observed near the
Fox River mouth during the August
survey. Phaeo pigments are listed
in Appendix F.
UNCORRECTED
CHLOROPHYLL A
pG./L.
JUNE 3-7
1974
UNCORRECTED
CHLOROPHYLL A
yG./L.
SEPTEMBER 24-25
1973
UNCORRECTED
CHLOROPHYLL A
uG./L.
JULY 8-9
1974
-------
- 51 -
UNCORRECTED
CHLOROPHYLL A
nG./L.
AUGUST 12-14
1974
UNCORRECTED
CHLOROPHYLL A
uG./L.
MAY 20-23
1974
UNCORRECTED
CHLOROPHYLL A
yG./L.
SEPTEMBER 4-5
1974
-------
- 52 -
FIGURE 111-19
Secchi Disc Reading in Lover Green Bay
Secchi disc readings generally corres-
ponded to the extent of the algae
activity. The light penetration was
consistently highest in the areas
furthest from the Fox River. Light
penetration of only 1 to 3 feet vas
consistently measured in the Inner
Bay.
SECCHI DISC
FEET
SEPTEMBER 24-25
1973
SECCHI DISC
FEET
JUNE 3-7
1974
SECCHI DISC
FEET
JULY 8-9
1974
-------
- 53 -
SECCHI DISC
FEET
AUGUST 12-14
1974
SECCHI DISC
FEET
MAY 20-23
1974
SECCHI DISC
FEET
SEPTEMBER 4-5
1974
-------
FIGURE 111-20
Chloride Contours in Lower Green Bay
Chloride concentration appeared to be relatively stable in the Lover Bay. Concentration
gradients ranging from 25 mg/1 at the Fox River mouth to less than 10 mg/1 further north
appear in nearly all surveys.
CHLORIDES
MG./L.
JUNE 3-7
1974
I
Ui
CHLORIDES
MG./L.
JULY 8-9
1974
-------
- 55 -
CHLORIDES
MG./L.
FEBRUARY 18-20
1974
CHLORIDES
MG./L.
AUGUST 12-14
1974
CHLORIDES
MG./L.
MAY 20-23
1974
CHLORIDES
MG./L.
SEPTEMBER 4-5
1974
-------
- 56 -
the Red Banks area. In all surveys the concentrations dropped off sharply with
distance from the Fox River. Concentrations below 20 ug/1 and usually below
10 ug/1 were found north of a line from Dykesville to the Little Suamico River.
It is interesting to note that the percent of the chlorophyll-a that is phaeo-
pigments (inactive chlorophyll-a from dead algae) increased throughout the summer.
In August for example, in the Inner Bay, phaeo-pigments comprised nearly 50% of the
measured chlorophyll-a.
Algae; The purpose of the study was to collect a background of information concerning
the principal types of planktonic algae in the lower third of Green Bay, to be
used as a starting point for further studies and monitoring. This includes
a Biomass estimate, a qualitative analysis of algae present and distribution
patterns of dominant algae.
The following is a qualitative report of observations obtained in the spring and
summer surveys and a description of schematic representation of the dominant
algae at each station based on the number of occurrences. (See Figures 111-21
through 111-25)
Winter 1974 (No figure included)
Limited sampling done through the ice at only two stations in the Lower Bay showed
a predominance of diatoms. Most common were Asterionella, Cyclotella and
Fragilaria. Species of Oscillatoria. rotifers and a few Chlorophyta were also
present. The diatoms constituted about 70-90% of the algae flora.
-------
- 57 -
May 20-23 (Figure 111-21)
A variety of diatoms predominated at most of the sampling stations. There was a
sizeable increase in numbers compared to the winter sample. The most common
genera were Asterionella, Cyclotella, Stephanodiscus, Fragilaria and now Melosira.
These organisms were distributed over the entire lower third of the Bay and may
represent the later stages of a diatom bloom as described by Wiersma 1974 as a
spring peak in April and tapering off in May.
It was interesting to note that Melosira was the dominant organism at the mouth
of the Lower Fox River, a condition that persisted throughout the summer. Species
of green algae, mostly of the genera Scenedesmus and Ankistrodesmus, predominated
in the Lower Bay along the eastern shoreline. Ankistrodesmus along with
Oscillatoria and diatoms predominated at stations, far from the Lower Fox River.
Small concentrations of Microcystis and Anabaena occurred at stations below the
Red River-Little Suamico River transect. Cyclotella and Stephanodiscus were the
outstanding diatoms in the indicated areas.
June 3-5 (Figure 111-22)
A large increase in the variety of green algae and numbers of Oscillatoria
and diatoms occurred in June. Melosira and green algae dominated in the region
below Long Tail Point. Oscillatoria and diatoms dominated above Long Tail Point.
Scenedesmus and several other species of green algae were concentrated along
the eastern shoreline as far as Red Banks.
-------
- 58 -
July 8-9 (Figure 111-23)
A bloom of algae occurred after the first week of June. The bloom extended over the
entire sampling area of the Bay. Blue-green algae dominated this bloom. The
most common genus was Aphanizomenon, except for stations 1 and 2 where Melosira
predominated. At stations 17, 31 and 43, (above Long Tail Point) species of
Oscillatoria predominated. The diatoms Cyclotella and Stephanodiscus were common
but not dominant at station A3, the furthest sampling station from the mouth
of the Lower Fox River. A variety of green algae persisted at some stations in
the Lower Bay and zooplankton concentrations were larger than in prior surveys.
August 12-13 (Figure 111-24)
Bloom conditions continued to persist over the entire sampling area. The extent
of the bloom beyond Sturgeon Bay was not investigated. The dominant organism at
all stations beyond Long Tail Point was Oscillatoria with heavy concentrations of
Aphanizomenon near Sturgeon Bay and along the eastern shoreline below Renard
River. Melosira continued to predominate in the Lower Fox River. Microcystis
was also abundant in the Lower Fox River. Heavy concentrations of Melosira
occurred throughout the Lower Bay as far north as the Red River. Genera of
blue-green algae (Microcystis, Anabaena, etc.) occurred throughout the entire
Bay. The heaviest concentrations appeared within the Lower Bay below the Point
Sable-Long Tail Point barrier and along the eastern shore to Red Banks. Green
algae appeared most commonly along the eastern shoreline from below Point Sable
to Red Banks. A greater number of the Pinoflagellates, most notably Ceratium,
appeared in the upper stations. Greater concentrations of zooplankton than previously
observed occurred at all stations in the Bay, especially in the upper most region.
-------
- 59 -
September 4-5 (Figure 111-25)
A second bloom of Aphanizomenon occurred although not as extensively as the bloom
which began in mid-June, lasting through August. Bloom conditions persisted
throughout the Bay. In the upper regions of the sampling area Oscillatoria was the
dominant organism. A noticeable increase in the concentration of the diatom
Asterionella occurred at these upper stations.
Areas of highest concentration of Aphanizomenon occurred in the Inner Bay and above
Long Tail Point on the western side of the Bay up to the Little Suamico River,
where it dominated the community, an area which previously was dominated by
diatoms and Oscillatoria. The eastern shoreline below the Red River and the
Inner Bay was a massive mixture of many organisms dominated by Aphanizomenon,
Microcystis, Melosira, green algae, Oscillatoria and zooplankton. This condition
extended beyond the Long Tail Point-Point Sable barrier to a transect from
the Little Suamico River to the Red River.
Summary of Survey Observations
Heavy growths of algae were present in Green Bay when intensive sampling began in
late May. Large blooms occurred by mid-June and continued through early September
when sampling was discontinued. By September "pea soup" conditions prevailed in
the Lower Bay and extensive blooms reached the upper regions of the lower third
of the Bay. Field workers described the Bay as "the worst they've ever seen
it."
-------
- 60 -
FIGURE 111-21
PESHTIGO RIVER
MAY 20-23, 1974
OCONTO RIVER
LITTLE SUAM ICO
RIVER
OSCILLATOR IA
DIATOMS
GREEN ALGAE
(ANKISTRODES
&SCENEDESMUS)
**\ (ANKISTRODESMUS
CYCLOTELLA &
STEPHANODISCUS
MELOSIRA
GREEN BAY
-------
- 61 -
FIGURE 111-22
PESHTIGO RIVER
JUNE 3-5,1974
OCONTO RIVER
LITTLE SUAMICO
RIVER
OSCILLATOR IA
MELOSIRA
XXXX GREEN ALGAE
x XX (SCENEDESMUS)
A A A. CYCLOTELLA £
*+• STEPHANODISCUS
GREEN BAY
-------
°*»
1=^-^; — :^:-::^':-::-^: vV^^\No
..•.,..' .. ;•_• .•. •_•.•••;..;••;_•. /^/^"••'.'•;N ^V •
^
-------
-------
•%/>
** V,
X X,
o,
^
^. X^
/c^
Q,
th
^
-------
- 65 -
A variety of algae and zooplankton predominated at different times throughout
the summer. Host prominent of these were the blue-green algae Aphanizomenon,
Qscillatoria and Microcystis; the diatoms Melosira. Cyclotella. Stephanodiscus
and Asterionella; the green algae Scenedesmus and Ankistrodesmus; Pinoflagellates,
Ceratium and the zooplankters Cladoceraus, copepods and rotifers.
Discussion
The relationship between the principal algae tabulated in Table III-3 to one
another at each station at a given time is the basis for determining the dominate
algae and the distribution patterns. This does not imply that the dominant
algae is necessarily the most important in the community, but that it occurred
most frequently. No attempt was made to determine the total algal community
or standing crop from these counts. Comparison of the data from May and June
to the July, August, September sampling cannot be done because of the different
methods of sampling used. It was not possible at this time to correlate these
two methods.
Wiersma (1974) has shown which algae comprise the plankton of that part of lower
Green Bay within the Long Tail Point-Point Sable barrier. This survey attempted
to investigate the characteristics of that portion beyond Long Tail Point as far
out as Sturgeon Bay in addition to the Inner Bay.
The distribution patterns assume a continuous distribution at the 1 to 2 meter level,
but do not take into account the vertical distribution. It is not known at
this time what effect this would have on these patterns, especially the buoyant
-------
- 66 -
blue-green algae. The effects of wind and currents generally contribute to the
concentrations of algal masses along the eastern shore. This condition extended
as far as Sturgeon Bay where abundant concentrations of Aphanizomenon were
observed. Modlin and Beeton (1970) and Sager and Wiersma (1972) observed that
currents from the Fox River flow along the south and eastern shorelines of
the Inner Bay and beyond Point Sable along the eastern shoreline for some distance
causing concentrations of algae in this area.
At all stations sampled on Green Bay Melosira granulata was found in abundant
concentrations at one time or more throughout the season. It attains a peak in
June and a second, generally lesser, peak in August. Holland (1968) found this
to be the case at sample stations in the vicinity of our stations 27, 37, 43.
The other diatoms did not appear to demonstrate this characteristic. Melosira
granulata was found to be very abundant in the mouth of the lower Fox River
(station 1) throughout the entire season. Here it appears to have gained complete
dominance of the community offering excessive competition thereby contributing
to the exclusion of other algae during periods of bloom.
The distribution of the blue-green algae Aphanizomenon correlates fairly well
with the distribution information reported by Vanderhoef (1972) except that we
observed abundant Aphanizomenon concentrations farther out into the Bay than he
did. (See Figure 111-23) It appears as though this may be an increase in
the abundance and spread of the organism, but it may be a "normal" fluctuation
in the population. Further studies and monitoring will be needed to determine
if this is the case.
-------
- 67 -
When the Chlorophyll-A data is segregated according to the zones shown in
Figure III-l, the averages show a correlation to the Chlorophyll-a data of
Wiersma (1974) taken in 1973. The data shown for the zones above Long Tail
Point generally indicate lower Chlorophyll-a than for the Inner Bay zone (see
Table III-4). Indications are from this study that the biomass for May and
June show trends that correlates with the trends of Chlorophyll-a•
Biomass data for July, August and September are unreliable and cannot be
used.
-------
- 68 -
TABLE III-2
Genera of Algae Observed*
CHLOROPHYTA (Green Algae)
Actinastrum Hantzschii
Agmenellum sp.
Ankistrodesmus falcatus
Chlorella ellipsoidea
Closteriopsis sp.
Coelastrum sp.
Crucigenia sp.
Dictyosperium pulchellum
Dictyosperium sp.
Echinosphaerella limnetica
Euglena acus
Euglena elastica
Golenkinia sp.
Hydrodictyon reticulatum
Kirchinella sp.
Micractinium pusillum
Oocystis sp.
Palmella sp.
Pediastrum sp.
Scenedesmus acuminatus
Scenedesmus dimorphus
Schroederia sp.
Selenastrum gracile
Selenastrum sp.
Tetradron trigonum
Tetradron sp.
Tetrastrum sp.
Westella sp.
Zygnema sp.
DESMIDS
Closterium sp.
Staurastrum sp.
Cosmarium reniforme
CYANOPHYTA (Blue-green Algae)
Anabaena circinalis
Anabaena incenta
Anabaena spiroides
Anabaena flos-aquae
Aphanizomenon flos-aquae
Aphanpcapsa sp.
Chroococcus sp.
Coelospherium sp.
Gomphospheria sp.
Counting Unit
single cell
colony
single cell
single cell
single cell
colony
colony
single cell
single cell
single cell
single cell
single cell
single cell
colony
colony
single cells
single cell
colony
colony
single cells
single cells
single cell
colony
colony
single cell
single cell
single cells
colony
filament
single cell
single cell
single cell
filament
filament
filament
filament
filament
colony
single cell
colony
colony (av.
size 0.1 mm )
-------
- 69 -
Lyngbya bergei
Lyngbya litnnetica
Lyngbya versicolar
Microcystis aeruginosa
Oscillatoria limnetica
Oscillatoria subrevis
Oscillatoria tenuis
Oscillatoria sp.
Fhormidium uncinatum
Phormidium sp.
BACILLARIOPHYCEAE (diatoms)
Asterionella formosa
Cyclotella glomerata
Cyclotella sp.
Fragilaria crotonensis
Fragilaria sp.
Melosira binderana
Melosira granulata
Melosira sp.
Stephanodiscus sp.
Synedra sp.
Tabularia fenestrata
Navicula sp.
DINOFLAGELLATES
Ceratium berundinella
Peridinium sp.
Dinobryon sp.
ZOOPLANKTON
Cladocerans
Copepods
Rotifers
filament
filament
filament ~
colony (av. size 0.7 mm )
filament
filament
filament
filament
filament
filament
frustule
frustule
frustule
frustule
frustule
filament
filament
filament
frustule
frustule
frustule
frustule
single cell
single cell
colony
single cell
single cell
single cell
*This table represents the algal organisms observed and does not necessarily mean
they were counted as they may have occurred outside of the counting grid. Where
possible, identification was tentatively carried out to species. Single celled
green algae unable to be identified were tentatively grouped in the Order
Chlorococcales, and filamentous green algae unable to be identified were
tentatively grouped in the Order Ulotrichales.
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^,
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Omitted
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Omitted
(Not sampled)
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Melosira o
Other Diatoms
Anabaena -^
Aphanizomenon
Oscillatoria2
Other Blue Green
Desmids
Dinoflagellates
Ulotrichales1
Other Green3
Other Diatoms
Anabaena ,
Aphaniz omenon
Oscillatoria2 ,
Other Blue Green
3
Desmids „
Dinoflagellates
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Other Green3
Sta. 9b
TABLE III-3 (continued)
Sta. 12
Sta. 13
May
136
328
0
0
125
0
0
5
10
142
130
209
5
0
31
26
0
0
0
260
June
73
432
5
0
120
10
62
5
31
162
224
150
0
5
63
0
21
0
26
499
July
6
2
34
158
60
4
5
1
6
5
Sta.
6
1
65
500
18
16
3
0
6
11
Aug.
7
1
3
17
78
3
7
0
4
0
14
142
21
5
87
36
60
2
0
22
120
Sept.
19
19
1
4
68
6
1
0
4
7
40
3
5
181
42
188
12
0
10
16
May
141
230
0
0
16
16
10
0
26
588
125
449
0
0
162
0
0
10
26
114
June
469
573
0
0
222
183
65
39
130
1461
63
208
0
0
334
0
5
10
83
99
July
1
3
19
273
33
13
0
0
6
12
Sta.
2
4
16
24
135
2
13
1
2
4
Aug.
85
8
4
46
33
46
1
0
5
2
17
30
0
2
12
93
5
3
0
2
4
Sept.
22
2
2
122
21
91
2
0
12
24
50
23
2
47
27
8
3
4
4
9
May
115
240
0
0
26
10
16
0
0
129
89
464
0
0
198
52
0
16
21
255
June
282
302
0
0
50
10
21
0
5
395
10
167
0
0
203
0
0
0
10
31
Juljr
12
13
19
267
48
26
2
0
19
60
Sta.
1
5
9
53
47
2
8
1
3
0
Aug.
393
54
20
138
28
38
22
0
12
68
24
24
2
1
35
94
5
2
0
7
1
Sept.
167
6
22
1047
76
313
22
0
28
16
10
13
3
61
45
7
0
1
4
5
1
2
3
4
No. X 10 filaments/liter
" frustules/liter
" cells/liter
" colonies/liter (predominantly Microcystis)
0 Less than 1 X 10 or not observed
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-------
- 75 -
SECTION IV
IV. WATER QUALITY MODELLING
Introduction: Water quality computer models were developed whose purpose was
to establish the capacity of Green Bay to respond to the input of various pollutants
and other chemicals. The first model to be discussed consists of a version of
the QUAL-II Model developed by Norton et al WRE, Inc. (1974) under EPA
contract no. 68-01-0713-Upper Mississippi River Basin Model Project. The
*
Wisconsin DNR has modified and implemented this model for the Lower Fox River
system.
A second model was based on a program by Water Resources Engineers, Inc., Lee
et al (1974) to simulate two dimensional systems such as Green Bay. This Dynamic
Estuary Model was modified to fit the Green Bay system and to simulate the major
water quality constituents. This model and its modifications are discussed in
detail in Appendix D (Green Bay Model Development and Documentation).
The Qual II model (as modified and used by DNR) is capable of simulating 12
constituents under steady or psuedo-dynamic conditions. BOD and DO are routed as
well as phosphorus, 4 forms of nitrogen, algae, coliforms and up to three
conservative substances. The model uses one dimensional steady state hydraulics
and waste inputs for both steady and dynamic runs. Dynamic simulation allows the
insertion of variable light intensity for evaluating the diurnal effect of algae
photosynthesis and respiration.
-------
- 76 -
NOTE: In 1973 the Wisconsin DNR published a Water Quality Model Study of
the Lower Fox River, Patterson (1973). This study was based on a water quality
model developed by Crevensten, Stoddard and Vajda of EPA. Since that time this
model has been used to produce a Waste Load Allocation for the Oconto River
(Wisconsin DNR, 1974). Since the waste load allocation for the Oconto River
has been completed, no additional simulations for the Oconto River have been
undertaken. The results of the Oconto River modeling are not presented in
this report.
A. Fox River Modelling
The Fox River from Lake Winnebago to Green Bay, a distance of about 40 miles,
was simulated by means of the QUAL-II computer model. The advantage of the QUAL-
II model is its flexibility and capability of simulating simultaneously many
constituents. For instance, four forms of nitrogen can be routed while various
chemical or biological reactions take place.
The QUAL-II model has been extensively modified in its application to the Lower
Fox River. The four most important modifications include: 1) the ability to
simulate organic nitrogen, 2) reformulization of the algal growth kinetics, 3)
inhibiting nitrification rates at low dissolved oxygen levels and 4) allowing
for denitrification during very low dissolved oxygen levels. The first two
modifications are essentially similar to the scheme developed for the Bay model
(Appendix D). The appropriate theory and equations are discussed in the Green
Bay model documentation. The third and fourth modifications are consistent with
observations reported in past literature and commonly accepted theory. With the
exception of the above changes, the model operates as described by the WRE program
documentation, Norton et al (1974).
-------
IV-la
r Modelling Segments
STATUTC MILES
i i i i » •' •* •*""*"*
-------
- 78 -
FIGURE IV-lb
STATUTE IMi.es
i i o .1 .2 .3 jt .3
-------
- 79 -
FIGURE IV-lc
CcfJSOL/DlTfO Ptffts
AffiTTOU
Rl VFRSlDC
free*. Co
STATUTC MltfS
' I ' I i i I I I I
i t t i " •' .2 .3 « *
-------
- 80 -
FIGURE IV-ld
AffiCTOH PtPFK Co
5.TR
STATUTE MILES
-------
- 81 -
FIGURE IV-le
*U*J* S I P
fl ruff SITE f-o*
OF THC Vtit-fr
•5.TP
i I i s o i z a i 5
-------
- 82 -
FIGURE TV-It
I 4 4 o i i 1 S s
-------
- 83 -
FIGURE IV-lg
STATUTE HMI.es
i n r
0 .1 .2 .3 .1 .5
-------
- 84 -
FIGURE IV-lh
MtlPRIHT A/C.
NlCOLFT P^ffK Co
5TVCTUTE MILfS
-------
- 85-
FIGURK IV-li
STATUTE- ^An.rs
-------
- 86 -
The QUAL-II model was then applied to the Lower Fox River. Forty-six river segments
were used to describe the Fox River. Each segment was further divided into an
integral number (from 1 to 20) of computational elements (each of these was 0.1
miles in length). In all, 389 computational elements were used. The waste sources
were located along the system and were used as waste inputs at the appropriate
computational element. The physical schematization is shown in Figure IV-1 and
tabulated in Table IV-1.
QUAL-II was verified using data obtained in the summer of 1972. This is the same
data used to verify the EPA model. The results of the verification run for June
20-21, 1972 are presented in Figures IV-2 through IV-5. Survey data was obtained
during daylight hours only. Data from the 5 automatic monitors is presented to
indicate the duirnal range of the DO during the survey period. The profiles for
DO, BOD5, NH3~N, N03-N, Org-N, and Chlorophyll-a are presented along with the
data that is available. The verification run shows an agreement between the observed
data and the QUAL-II prediction that is very acceptable. It is particularly
interesting to observe the agreement for the nitrogen forms. The only area of
significant disagreement is in the NOo-N profile for run one between mile points
14 and 0. The QUAL-II model indicates a 100% increase in the NO -N concentration
while the data indicates no substantial change in the NO--N level. Since the
other forms of nitrogen show good agreement with the data, one of two possible
things is taking place to account for this discrepancy. Either the DO levels
are low enough near the sediments to stimulate a significant amount of
denitrification at the lower end, or nitrification is not taking place at the
rate used in the model for run one. The first hypothesis is in direct
disagreement with the observed DO profile. Mile 14.0 to 3.0 shows DO levels
much too high to allow for significant denitrification (Figure IV-2) unless
there is a very strong vertical stratification which would allow the DO level
to drop sharply near the water sediment interface. Thus the first hypothesis
is not very likely.
-------
FIGUKE IV-2
12
JUNE 20-21, 1972
DISSOLVED OXYGEN
VERIFICATION
TEMPERATURE 21°C
BOD DECAY .41
BOD DEOXY. .31
40
36
00
I
MILES ABOVE MOUTH
-------
FIGURE IV-3
__ T
JUNE 20-21, 1972
NITROGEN
VERIFICATIONS
RUN ONE
MEASURED VALUES
ORGANIC-N- D
NH3 -N •
N03 -N *
oo
00
24 20 16
MILES ABOVE MOUTH
-------
FIGURE IV - 4
JUNE 20-21, 1972
NITROGEN
VERIFICATIONS
RUN TWO
MEASURED VALUES
ORGANIC-N D
NH3-IM
NO3-N
P04-P (TOTAL)
QUAL- II
ORGANIC-N
REACTION RATES 1/DAY BASE e
NH3-N = 035
N02-N = 0 07
N03-N = 1.00
MAX: N03-N —N2= .40
ORG-N SETTLING = .025
ORG-N
NH3-N
QUAL-II
TOT-PO4-P
oo
VO
40
24 20 16
MILES ABOVE MOUTH
-------
FIGURE IV-5
JUNE 20-21, 1972
CHLOROPHYLL-A PROFILES
I-
REACTION RATES
30.
20.
10
40
o
I
RUN ONE:
GROWTH 1.50
RESPIRATION 20
SETTLING 1.00 ft/DAY
RUN TWO.
GROWTH 1.50
RESPIRATION .20
SETTLING
1.00 ft/DAY
36
32
28
24 20
MILES ABOVE MOUTH
16
12
-------
- 91 -
TABLE IV-1
Physical Dimensions Used to Describe the Lower Fox River
Reach
Number
1.
2.
3.
4.
5.
6.
7.
8.
9.
10.
11.
12.
13.
14.
15.
16.
17.
18.
19.
20.
21.
22.
23.
24.
25.
26.
27.
28.
29.
30.
31.
32.
33.
34.
35.
36.
37.
38.
39.
40.
41.
42.
43.
44. -
45.
46.
Cross
Sectional
Area Ft2
967.
4020.
6978.
11660.
14634.
15065.
9837.
10032.
3670.
1676.
1998.
619.
3648.
4194.
4194.
2660.
4556.
6592.
1492.
3484.
2900.
1476.
6514.
4703.
2420.
2912.
2912.
4428.
5055.
8145.
10146.
9301.
9301.
4889.
10824.
8584.
11665.
15204.
12042.
15002.
12978.
16055.
11880.
9945.
14025.
12194.
Depth Ft.
2.
2.5
3.
4.
4.5
5.5
9.
9.6
6.6
4.
4.5
1.6
5.8
6.7
6.7
3.3
6.7
6.5
2.8
6.3
10.0
2.
4.7
7.5
4.
5.8
5.8
7.7
5.5
5.0
5.7
10.3
10.3
3.4
6.6
7.4
5.6
5.6
9.
13.
21.
19.
20.
13.
16.5
13.
Benthic Demand
GR 02/m2/Day
Verification BPT
Runs Conditions
8.0
8.0
8.0
. 8.0
8.0
8.0
8.0
8.0
8.0
8.0
8.0
5.0
5.0
5.0
5.0
5.0
8.0
8.0
8.0
8.0
8.0
8.0
8.0
8.0
5.0
5.0
5.0
5.0
2.5
2.5
2.5
2.5
2.5
2.5
2.5
2.5
2.5
2.5
2.5
5.0
5.0
5.0
5.0
5.0
5.0
5.0
3.0
3.0
3.0
3.0
3.0
3.0
3.0
3.0
3.0
2.0
2.0
2.0
2.0
2.0
2.0
2.0
2.0
2.0
4.9
4.9
4.9
4.8
4.8
4.8
3.0
3.0
3.0
3.0
2.5
2.5
2.5
2.5
2.5
3.0
3.0
3.0
3.0
3.0
3.0
3.0
3.0
3.0
3.0
3.0
3.0
3.0
-------
- 92 -
We are therefore left with the conclusion that nitrification rates for NH-j-N are
being overestimated. If this is the case, we must account for the fact that the
rate used in the model did in fact predict an ammonia profile that agrees nicely
with the data. A closer look at the nitrogen balance discloses that organic nitrogen
decreased a total of 1.1 mg/1 while ammonia increased .43 mg/1 and nitrate increased
.11 mg/1. (Nitrite concentrations are normally insignificant i.e., <.05 mg/1.)
Since the nitrogen forms do not balance we must conclude that nitrogen is leaving
the system in a manner that is unaccounted for. One could immediately assume
that algal growth could make up this difference. A closer check tells us that
to account for the difference of .55 mg/1 of nitrogen, we would need 6.9 mg/1
of algal biomass (assuming an algae cell is about 8% nitrogen). Using literature
conversion factors, (QUAL-II documentation), 6.9 mg/1 of algal biomass would contain
350 to 690 ug/1 of chlorophyll-a, an extremely high number.
This is in direct conflict with Sager &Wiersma's measurements of chlorophyll-a.
His measurements indicate maximums of about 150 ug/1 in the Menasha area and
typically a 50% decrease from that level as one travels downstream to Green Bay
(Figure IV-6). Secondly, nitrogen contained in the algae would be measured as
organic nitrogen (if the sample was not filtered). We are therefore forced to
assume that organic nitrogen must be leaving the system by sedimentation and
not only by transformation to NH -N. Using this assumption, a second
verification run is displayed in Figure IV-4. The drawn curves indicate a good
fit for all the nitrogen forms. For run two, the observed and calculated total
phosphorous curve is also shown and again the agreement is acceptable.
Verification runs for July 5-6, 1972 and August 14, 1972 were also calculated.
Dissolved oxygen data is again for daytime periods except for automatic
monitoring data. The fits for these dates are net as good as the June
20-21, 1972 run. Data for comparison is not as complete for these simulations.
These runs are diagrammed in Figures IV-7 through IV-11.
-------
140
FIGURE IV-6
CHLOROPHYLL-A PROFILES
SUMMER 1971
DATA AFTER SAGER AND WIERSMA
U)
I
24 20 16
MILES ABOVE MOUTH
-------
CONCENTRATION MG/l
s|°
33 O >
a2 7
°%L
|j
f H O
m I >
33 m H
O w >
°s°
< 3J
m _
-< z
en
g n
00
M :
ai
C/)
,
( uS ,
-------
CONCENTRATION MG/I
Ko b>
N
bo
-------
CONCENTRATION MG/I
O> CO O
- 96 -
-------
CONCENTRATION MG/I
- L6 -
-------
CONCENTRATION
- 86 -
-------
- 99 -
The last constituient to be discussed on the verification runs concerns the
chlorophyll-a concentration. Figure IV-5 shows the calculated chlorophyll-a profiles
for run one and two on the June 20-21, 1972 verification. Unfortunately there
is no data directly available to compare to the chlorophyll-a profile. Thus, no
conclusions about the models capability to simulate algae in the Lower Fox River
is possible at this time. The best information available for this parameter is
a series of chlorophyll-a profiles obtained by Sager and Wiersma during the summer
of 1971. The available data is plotted in Figure IV-6. The most apparent trend
in the plotted data is a lack of consistency. The profiles were developed from
data taken at 10 stations along the Lower Fox River on a biweekly basis. Samples
were taken July 28, August 10, August 25, September 7 and September 21. The highest
concentrations were obtained on the July 28, 1971 survey. During this survey
the upper half of the river had chlorophyll-a levels above 100 ug/1 reaching a
peak in Little Lake Butte Des Morts of 165.1 ug/1. Only 13 days later, on August
10th the highest observed value was 81 ug/1. Nearly all stations had decreased
in concentration by over 50%. The September 7 profile shows a large peak at mile
18.0—nearly 100% larger than any other value taken on that survey. The data
represents values of chlorophyll-a in a water sample taken near the surface (1 meter).
The model, of course, considers the "well mixed" average concentration over each
element. One consistency does'appear in all the fluctuations: the dramatic changes
in chlorophyll-a concentration in the upper part of the river are not matched
by such large fluctuations in the lower half. Thus we observe chlorophyll-a
levels in the Menasha area that range from 10 ug/1 to 165 ug/1, while at the mouth
of the river the range is from 28 to 51 ug/1. The data seems to suggest that
the Fox River provides a more stable environment for the phytoplankton. Whereas
Lake Winnebago is characterized by periodic blooms and dieoffs during the summer,
the entering peaks and troughs of algal activity are distinctly attenuated as the
water proceeds toward Green Bay. This attentuation leads to a 50% decrease in
-------
- 100 -
chlorophyll-a concentration in general in the downstream direction. This pattern
is violated only by isolated peaks along the river and in the area near the mouth
of the river. The higher values at the mouth may be a result of seiche effects
bringing algal blooms from Lower Green Bay into the river.
It is therefore apparent that we are on tenuous ground in trying to predict algal
activity in the Lower Fox River. It appears as if the most significant factor
determining the level of algal activity is the amount of algae entering the system
from Lake Winnebago. We can however, note one interesting point in a comparison
of run one and run two for the June 20-21, 1972 verification. Figure IV-5 indicates
a significant change in the chlorophyll-a concentration between the two runs.
The only apparent reason for this decrease in algal activity is the concentration
of inorganic nitrogen, particularly N03-N, which was significantly reduced in
run two. It can be concluded from this run that the level of inorganic nitrogen
in the Lower Fox River may be an important factor in algal activity! One final
point along this line needs to be explained. Denitrification is allowed in QUAL-
II and is controlled by the dissolved oxygen level in each computational element.
At zero DO, the denitrification rate is maximum at 0.4 day" (base e). The allowed
rate decreased exponentially as the DO rises from zero. One would, of course,
expect higher levels of inorganic nitrogen, particularly N03-N, under high DO
levels. As is shown later, this is in fact what the model predicts. Thus the
enthrophication prospects for the Lower Fox River-Green Bay system may be increased,
from an inorganic nitrogen point of view, under higher DO levels.
In light of the tremendously wide range of algal activity in the Lower Fox River,
it does not make sense to develop a waste load allocation with the expectation
that the algal concentration will be continuously adding to the oxygen levels in
-------
- 101 -
the stream. One can, however, attempt the waste load allocation such that the
algal activity is a low level component in the system. The value of 30 ug/1 of
chlorophyll-a was used to represent a value well within the range observed but
toward the lower end. Under these circumstances, it is reasonable to expect the
point source waste loadings to be controlled so no water quality violation is
encountered. This is the strategy that was used to develop the waste load
allocation for the Lower Fox River that is presented in the next section.
B. Lower Fox River Waste Load Allocation
The QUAL-II model as developed and presented in the section above has shown its
usefulness to simulate the Lower Fox River system. Our remaining task is to apply
the model under various waste load abatement schemes and evaluate the response
of the river system as simulated by the model. The beginning step in this process
involves determining the base line conditions that will be used to do the final
prediction simulations. This involves determining such parameters as the 7 day,
10 year low flow (7Q10)j stream temperature and reaction rates etc.
To determine the 7Q10 low flow, data from the USGS gaging station at Rapid Croche
was analyzed for the years 1918 to 1972. The value of 912 CFS was used as a result
of this analysis. This flow represents the 7 day low flow that can be expected
statistically in any 10 year period. For the low-flow simulations, the flow of 912
CFS was considered to be constant over the entire length of the river. Table IV-
2 lists the various parameters that were chosen at the headwater of the system
(Lake Winnebago). The value of chlorophyll-a was chosen to reflect a low level
of algal activity (for that area) as discussed above. All other values were chosen
to reflect typical concentrations that have been observed in the Neenah-Menasha
area of Lake Winnebago. Table IV-3 presents an assortment of data collected in
this area.
-------
- 102 -
TABLE IV-2
Lake Winnebago Water Quality Used for the QUAL-II Prediction Simulation
Runs of the Lower Fox River
Parameter
FLOW
Dissolved Oxygen
BOD (5-day)
Organic-N
NH--N
NO.-N
N03-N
P04-P
Tot.
Chloroptiyll-a
Temperature
Concentration
912.0 CFS
8.00 mg/1
2.00 mg/1
2.50 mg/1
0.05 mg/1
0.001 mg/1
0.10 mg/1
0.20 mg/1
30.0 ug/1
80°F
TABLE IV-3
Water Quality Parameters Measured in the Neenah-Menasha Area of Lake
Winnebago on various dates
Parameter May 4, 1972 June 21, 1972 July 6, 1972 Oct. 23, 1974 Nov. 11, 1974
DO mg/1 13.0
BOD mg/1
Org-N mg/1 .89
NH3-N mg/1 .02
N02-N mg/1 .002
N03-N mg/1 .1
TOT. P04-P mg/1
Sol. P04-P mg/1
Temperature °C 20.
pH 8.0
Chloride mg/1
Color su
Suspended Solids mg/1 29.0
.5
.04
.010
.22
.01
1.2
.03
.004
.05
.1
.02
11.2
1.8
.64
.29
.23
.15
.092
8.0
8.4
7.0
15.0
9.0
10.1
2.0
.55
.15
.33
.09
.07
7.0
8.2
8.0
20.0
5.0
-------
- 103 -
The design termperature for all prediction runs was 80°F. This temperature was
selected to reflect the data obtained from the five automatic monitoring stations
that have been operated since 1971. Daily maximum temperatures at all five stations
(Menasha, Appleton, Rapid Croche, De Pere, Green Bay), exceed 80°F during July
and August of all years since the monitors have been operated. Some maximums have
gone as high as 84°F.
The benthic oxygen demand used in the simulation runs were calculated on the basis
of suspended solids discharged. The verification runs for June 20-21, 1972, July
5-6, 1972 and August 14, 1972 all were run with the same benthic oxygen demand
pattern. The values appear in Table IV-1 along with benthic oxygen demand values
for BPT conditions. The projected percent reduction in discharged suspended solids
at each point source was used to reduce the benthic oxygen demand in the affected
reaches by an equal percent. As the BOD5 and suspended solids loads were reduced
in the process of finding a set of discharge conditions that would meet 5.00 mg/1
of oxygen, the benthic demand was again reduced by a corresponding amount in the
appropriate reaches. Table IV-4 summarizes the projected reduction in suspended
solids in the various segments of the Lower Fox River.
Prediction Simulations
The conditions discussed above were used to generate a simulation run of the Lower
Fox River for Best Practicable Treatment levels and low flow (912 CFS) condition.'-.
Table IV-5 lists inputs for each waste source considered in the model for this
run. Figures IV-12 and 13 display the QUAL-II predicted profiles. It should also be
made clear that Figure IV-12 represents the daily average dissolved oxygen level
and does not give any information concerning the daily fluctuation from algae activity.
-------
- 104-
TABLE IV-4
Projected Suspended Solids Reductions Used to Determine Benthic
Oxygen Demands under "Best Practicable Treatment" Levels
Suspended Solids (Ib.day)
Dischargers Present BPT
Neenah-Menasha Area (Reaches 1-9)
Neenah-Menasha STP 22500. 5000.
K. C. Lakeview 940. 1100.
K. C. Neenah 2037. 1025.
K. C. Badger Globe
George Whitting 1635. 200.
Bergstrom 18000. ' 3628.
Wisconsin Tissue 1602.
Menasha Sanitary District #4 50. 50.
TOTAL 45162. 12623.
% Reduction 72%
*****
Appleton Area (Reach 10-16)
Riverside Paper 976. 830.
Cons. Paper 10420. 1200.
Appleton STP 20000. 4100.
TOTAL 31396. 6130.
% Reduction 81%
*****
Kimberly Area (Reach 17-18)
K. C. Kimberly 12246. 3000.
% Reduction 76%
*****
Combined Locks (Reach 19-21)
Appleton Papers 6758. 4130.
% Reduction 39%
*****
-------
- 105 -
TABLE IV-4 (continued)
Kaukauna Area (Reach 22-24)
Thilmany Paper 9803. 5900.
% Reduction 40%
*****
(Reaches 25-34 have no significant discharges)
*****
De Pere Area (Reach 35-38)
Nicloet Paper
De Pere STP
TOTAL
% Chai
*****
Green Bay Area (Reach 39-46)
Fort Howard 20000. 12900.
Charmin 14983. 4140.
Green Bay Packaging 343. 1200.
American Can 6761. 8500.
Green Bay STP 23000. 13100.
TOTAL 65087. 39840.
% Reduction 39%
472.
2160.
2632!
.ee
972.
1185.
2157.
18%
-------
- 106 -
TABLE IV-5
Final Permit (1977) Loadings for Lower Fox River Waste Sources
Source
Name
K. C. Neenah &
Badger Globe
Bergstrom Paper
K. C. Lakeview
Neenah Menasha STP
Wisconsin Tissue
Menasha Sanit. Dist. E. & W.
Riverside Paper
Formost Dairy
Consolidated Appleton
Appleton STP
K. C. Kimberly
Appleton Papers
Heart of the Valley STP
Thilmany Paper
Wrightstown STP
Nicolet Paper
De Pere STP
Fort Howard Paper
Charmin Paper
Green Bay Packaging
American Can
Green Bay STP
BOD5
kg/day (Ibs/day)
Suspended Solids
kg/day (Ibs/day)
498.9 (1100)
1077.1 (2375)
816.3 (1800)
2043.5 (4506)
536.9 (1184)
W. 359.6 (793)
394.5 (870)
49.0 (108)
1133.8 (2500)
1859.4 (4100)
907.0 (2000)
1655.3 (3650)
601.8 (1327)
2675.7 (5900)
73.5 (162)
589.6 (1300)
1614.0 (3559)
3945.5 (8700)
3460.2 (7630)
725.6 (1600)
839.0 (1850)
5940.9 (13100)
464.8 (1025)
1645.3 (3628)
498.9 (1100)
2043.5 (4506)
726.5 (1602)
359.6 (793)
376.4 (830)
NA
680.3 (1500)
1859.4 (4100)
1360.5 (3000)
1873.0 (4130)
601.8 (1327)
2675.7 (5900)
73.5 (162)
440.8 (972)
1614.0 (3559)
5850.0 (12900)
3854.8 (8500)
544.2 (1200)
571.4 (1260)
5940.9 (13100)
TOTAL
31,797.3 (70115.)
34,082.1 (75153)
-------
CONCENTRATION MG/I
O) 00
- iOT -
-------
FIGURE IV-13
1.41
35
CHLOROPHYLL-a AND
NUTRIENT PROFILES
24 20 16
MILES ABOVE MOUTH
-------
- 109 -
As can be seen, significant violations of the 5.00 mg/1 dissolved oxygen level
for fish and aquatic life occur at 3 locations along the river. In addition all
three DO sag areas will violate the current standard for dissolved oxygen. A
dynamic simulation run was also done for the BPT condition. (BPT is used in this
report to refer to the discharge levels to be attained by the end of 1977. In
some cases the permits are slightly lower than BPT but in general they represent
Best Practicable Technology.) A portion of the results are presented in Figure
IV-14. This run shows that the dissolved oxygen would be expected to vary by as
much as 1.0 mg/1. In the Menasha, Kaukauna and Green Bay areas this could lower
the DO below 3.0, 2.5 and 1.0 mg/1 respectively during nighttime hours. Under
such circumstances the applicable variance conditions for DO in these areas would
be violated. It is clear from these results that the wasteloads under BPT conditions
will generate water quality violations in at least three areas along the river.
If we compare the predicted DO profile to the fish and aquatic life standard of
5.0 mg/1 we find that nearly 15 miles of the river would be below this level on
a daily average basis I AS mentioned above, nighttime conditions will greatly
enlarge the area and extent of those violations. On the basis of the above results,
it can be concluded that "best practicable treatment" for all point sources on the
Lower Fox River will not achieve a minimum level of dissolved oxygen necessary to
sustain most fish and aquatic life.
The level of treatment required to meet a DO standard of 5.0 mg/1 was determined
using the model in a fashion similar to that described above. The steady state
version was applied for this purpose. Initial conditions were as shown in Table
IV-2. The procedure followed to generate the waste load allocation consisted
of reducing the appropriate discharges (BOD^ and suspended solids) from those
sources that were directly upstream from a given sag in the DO (See Figure IV-
12). Each such discharger was reduced by a flat percentage. The BOD,- and the
-------
- 110 -
FIGURE IV-14
BELOW THILMANY
RCH 24 LAST ELEMENT
UPPER APPLETON
RCH 9 ELEMENT 1
i 2.7 k
O
Q
DIURNAL DO FLUCTUATIONS AT THREE
j FOX RIVER SAG POINTS FOR BPT LOADS
I
12 18 24 30
HOURS AFTER MIDNIGHT OF DAY 18
-------
- Ill -
suspended solids were reduced by equal percentages. The percent reduction in
the benthic oxygen demand was then recalculated on the basis of the new discharges
and those figures were entered in the model. The QUAL-II model was then executed
and the results were screened for any remaining violations. This procedure was
repeated if required.
In this way, various point source effluents were reduced until a profile was
obtained that did not violate the 5.0 mg/1 requirement for dissolved oxygen on
a daily average basis. The results of this procedure are presented in Table
IV-6 and Figures IV-15 and 16. The effluents for this procedure assumed no
change in the discharge of nitrogen and phosphorous compounds. A second run
(Run B) was then made assuming nitrification was installed at all sewage
treatment plants and phosphorous removel to 1.00 mg/1 was accomplished for all
dischargers. The effluents under this condition assumed the following
discharges for all sewage treatment plants:
Organic N - 2.00 mg/1
NH3-N - 1.00 mg/1
NO,-N - 3.00 mg/1
TOT-P - 1.00 mg/1
The results for this run are shown in Figures IV-15 and 17. As can be seen in
Figure IV-15, ammonia reduction at all STP does not alter the DO profile. The
DO was changed by about 0.05 mg/1 in most areas. A comparison of Figures IV-
16 and 17 reveals a definite reduction of NH -N (by as much as 0.2 mg/1) and a
corresponding increase in the concentration of NO^-N (by as much as 0.1 mg/1).
The concentration of NH~-N still, however, attains concentrations in the Green Bay
-------
- 112 -
TABLE IV-6
Waste Load Allocation Loadings for the Lower Fox River Determined by
QUAL-II Simulation to Maintain 5.0 mg/1 of Dissolved Oxygen
BOD5
Discharger kg/day Ibs/day
Kimberly Clark
Neenah
Badger Globe 424.0 935.
Bergstrom Paper 915.6 2019.
Kimberly Clark
Lakeview 693.9 1530.
Neenah Menasha STP 1737.0 3830.
Wisconsin Tissue 456.2 1006.
Menasha Sanitary District
E. & W. 305.7 674.
Riverside Paper Co. 268.0 591.
Formost Dairy 49.0 108.
Consolidated, Appleton 771.0 1700.
Appleton STP 1237.6 2729.
Kimberly Clark, Kimberly 616.8 1360.
Appleton Papers 983.2 2168.
Heart of the Valley STP 401.3 885.
Thilmany Papers 1546.4 3410.
Wrightstown STP 49.0 108.
Nicolet Paper 290.2 640.
De Pere STP 537.4 1185.
Fort Howard Paper 2040.8 4500.
Charmin Paper 1632.6 3600.
Green Bay Packaging 580.5 1280.
American Can 544.2 1200.
Green Bay STP 3960.4 8733.
TOTAL 20040.8 44191.0
% Below BPT 37%
* Based on 20 mg/1 for Design Flow
** Based on 10 mg/1 for Design Flow
*** Based on 25.5 mg/1 for Design Flow
Suspended Solids
kg/day Ibs/day
395.0
1398.2
424.0
1737.0
617.2
305.7
256.2
462.6
1237.6
925.1
1276.6
401.3
1546.4
49.0
163.3
537.4
2267.5
2176.8
435.4
544.2
3960.4
871.
3083.
935.
3830.***
1361.
674.***
565.
**
1020.
2729.*
2040.
2815.
885.*
3410.
108.*
360.
1185.**
5000.
4800.
960.
1200.
8733.*
21116.9
46564.0
-------
FIGURE IV-15
14
DISSOLVED OXYGEN PROFILE
FOR FINAL WASTE LOAD
ALLOCATION DISCHARGES
I I
T = 80°F FLOW = 912 CFS
ALL RATE COEFFICIENTS ARE THE
SAME AS FOR THE JUNE 20-21, 1972
VERIFICATION RUN
QUAL-M
WLA-DO PROFILE
FOR RUN A
ANDRUW B
FISH AND
AQUATIC LIFE
STANDARD
DUAL - I I PROFILE FOR BOD
40
36
28
24 20 16
MILES ABOVE MOUTH
12
-------
CONCENTRATION MG/t NH3-N, N03-N, TOT-P
4*. CD CO O
-------
1 2
FIGURE IV- 17
NUTRIENT PROFILES FOR
WASTE LOAD ALLOCATION RUN
(REACTION COEFFICIENTS AS FOR
JUNE VERIFICATION RUN TWO)
RUN -B
NH3-N REDUCTION ATSTP
20
Ml LES ABOVE MOUTH
16
12
2.0
I
o
-o-
cc
o
2.4
-------
- 116 -
area as high as 0.72 mg/1. This would tend to indicate that the most significant
source of NH^-N (according to the model) is the hydrolysis of organic nitrogen. This
conclusion is supported by the high levels of NH3-N observed on the June 20-21, 1972
survey (Figure IV-4). An ammonia level of 0.72 mg/1 will be toxic to fish life
if the pH is greater than 8.0 and the temperature is greater than 20°C. Since
the pH of the Fox River frequently exceeds 8.0, ammonia toxicity may be a continuing
water quality problem even if nitrification is accomplished at all sewage treatment
plants. Further-more, since the DO profile shows little response to nitrification
at the treatment plants, it appears as if there is little reason to pursue
nitrification as a viable means of improving the water quality of the Lower
Fox River at this time. If, however, higher DO levels significantly increase
the nitrification potential, a dissolved oxgyen deficit of significance may
occur. This is not likely though unless the pH of the river experiences a long
term change to a lower level. According to Srinath (et al 1974) nitrification
ia markedly inhibited at pH's above 8.0. Typical pH values for the Fox River
range from 8.0 to as high as 9.2.
The model simulations discussed above concerning ammonia must be taken as preliminary
only and no conclusions should be based on them. In view of the lack of good data
for ammonia both from the sewage treatment plants and in the river (and a few wood
pulping operations) the main source of the ammonia in the Lower Fox River cannot
be definitely determined. Three sources can be significant contributers: 1) point
source discharges, 2) organic nitrogen entering from Lake Winnebago that hydrolyzes
to ammonia as it travels downstream and 3) sediment release. It would be
beneficial to monitor anmonia and total organic nitrogen at all sewage treatment
plants and any significant industrial dischargers. This type of monitoring
could be made a part of each discharger permit. Until such data is available
and in light of the modelling results, no allocation of ammonia (or Kjeldahl
nitrogen) can be made.
-------
o
Q
- 117 -
FIGURE IV-18
DIURNAL DO FLUCTUATIONS AT THREE
FOX RIVER SAG POINTS FOR WLA LOADS
GREEN BAY
RCH 46 ELEM 1
BELOW THILMANY
RCH 24 LAST ELEM
I
UPPER APPLETON
RCH9 ELEM 1
STEADY STATE
12 18 24 30
HOURS AFTER MIDNIGHT OF DAY 18
42
-------
- 118 -
To answer the question of algae effects a dynamic run was done for the waste
load allocation and reduced NHo-N loading configuration. A portion of that output
appears in Figure IV-18. The plots of diurnal DO fluctuations indicate that
the DO will not violate 5.00 mg/1 under the simulated conditions even during
the lowest point on the duirnal cycle. It should be emphasized, however, that
this does not preclude the possibility of DO standards violations. A high level
of algae (from a summer bloom) coupled with several consecutive days of very
little sunlight could possibly bring the DO below 5.00 mg/1.
With all of the above in mind, it can be concluded that the waste loadings for
BODc and suspended solids shown in Table IV-6 should be expected to meet 5.0
mg/1 of DO in the Fox River under low flow (912 CFS) conditions. Furthermore,
it does not appear to be necessary to require nitrification at sewage treatment
plants as a means of improving the dissolved oxygen. The concentration of NO^-N
can be expected to rise slightly as a result of higher DO levels which will suppress
denitrification. Finally, the listed WLA loadings represent an average of 37%
and 38% reduction over "best practicable treatment" levels for BOD_ and suspended
solids respectively.
C. Green Bay Modelling
As part of this project, a water quality model of Green Bay was developed. The
purpose of this model was to develop a predictive capability of the water quality
of the lower one-third of Green Bay. The model chosen for this activity was
based on the Dynamic Estuary Model developed by Water Resources Engineers.
This model was originally developed for San Francisco Bay and was later modified
for use with Pearl Harbor. The model was obtained by DNR from WRE in February
-------
- 119 _
of 1974. In the process of fitting the model to the Green Bay situation, extensive
modifications were made. A complete description of the model as used in the Green
Bay modelling effort is contained in Appendix D. Flow charts and program listings
along with a data set up description are included.
Two main areas of use were intended for the Green Bay model (GBQUAL). First,
information regarding the response of Green Bay under ice cover was a prime concern.
Surveys of 1939, 1955, 1967 and 1974 (part of this project) all showed extensive
areas of low to zero dissolved oxygen during the ice cover period. For Green
r
Bay, the period of ice cover may range from two to three and one half months.
Ice cover usually begins in early January. The low dissolved oxygen levels have
hindered commercial fishing operations over as much as 150 square miles of the
Lower Bay. This region begins below a line from Long Tail Point to Point Sable
and can extend along the eastern half of the bay to beyond the Renard River.
A question that has received particular attention in this report is: what level
of treatment for point source discharges along the Lower Fox River will be required
to eliminate this problem?
The second main emphasis concerns the eutrophic nature of the Lower Bay. Highly
fertile water from the Lower Fox and other rivers have been contributing vast
quantities of nutrients (particularly nitrogen and phosphorous). These nutrients
enhance the growth of phytoplankton causing nuisance algae blooms throughout
the summer. These blooms are unpleasant from an aesthetic standpoint and serve
to severely limit the recreational uses of the Lower Bay. They also may be partly
responsible for taste and odor problems in water supplies taken from Bay water
further north. To remove these effects requires a significant expense at water
treatment facilities.
-------
- 120 -
Winter Modelling of Green Bay
Winter conditions in Green Bay complicate the water quality problems of the Bay.
Severely cold temperatures in Wisconsin normally serve to form an ice cover on
Green Bay from early January to as late as early April. The ice cover may grow
to a depth of A feet. This ice cover effectively shuts off any available reaeration
that would otherwise maintain high dissolved oxygen levels. If the ice is covered
by an additional layer of opaque snow, any small amount of photosynthesis that
may take place will also be virtually eliminated. Under these conditions, the
only remaining source of oxygen is the inflowing water from the major tributaries.
The Lower Fox River, during December to April, enters the bay carrying about
8-14 mg/1 of dissolved oxygen. Unfortunately, this river water also carries
with it a high load of organic compounds from the numerous dischargers along
the Fox River. Nearly all of this organic load is capable of exerting an oxygen
demand on the Bay water and this oxygen demand severely strains the limited oxygen
resources of the ice-covered Lower Bay.
The temperature of the ice-covered Bay water ranged from 0.0°C to 3.0°C. At
this low temperature, chemical and biological reactions take place at very decreased
rates; however, the reactions do not stop conpletely. The long-term BOD of organically
rich water incubated at low temperatures can be significant. Two important problems
come to the fore at this point. First, we need to have the ability to predict
the long term effect of organic wastes carried in the river water. It is clear
from data obtained from various Green Bay winter surveys that the dissolved oxygen
depletion develops over an extended period of time. This analysis reveals that
the customary 5-day BOD test is inadequate to supply information of oxygen consumption
that may take place over a 60 to 90 day period. The second important aspect
-------
- 121 -
of this prpblem involves the choice of the rate constants required to properly
describe the low temperature BOD uptake. Both of these problems have been
investigated by the author and the results are presented below.
Figure IV-19 illustrates a curve for a long term BOD test on a sample taken from
the mouth of the Fox River. This curve shows the laboratory oxygen demand as
a. function of time over a 60 day period (slightly less than the length of time
Green Bay is ice-covered during a normal winter). This curve is interesting
for several reasons. First, it shows that the 60 day BOD is considerably greater
than the 20 day BOD (frequently considered the ultimate) and is in fact nearly
4 times as great as the 5-day BOD. Secondly, this curve indicates that although
the rate of oxygen consumption is slowing, it is clearly not stopping, even after
60 days I If we attempt to fit this data to a typical BOD equation we immediately
discover that it is nearly an impossible task. Either we fit the data precisely
for the first 5 to 10 days and severely underestimate the ultimate BOD or we
can fit the ultimate range correctly but we can no longer follow the curve exactly.
We are left with the choice: To which portion of the curve can we sacrifice
accuracy? The answer, of course, is that we can fit both ends by merely including
more terms in the BOD equation. If we write the BOD equation as:
3 -k t
L . Z L (1 - e " ) m
i=l X k '
where: L = BOD mg/1
Li = separate ultimate BOD's for each term
k. . = respective decay rates day"-'- (base e)
t = time (days)
-------
FIGURE IV- 19
LONG TERM BOD AT THE FOX RIVER MOUTH
I
SAMPLE # 27Q40
OBSERVED
BOD CURVE
FITTED CURVE
FOR LONG TERM BOD
FITTED CURVE PARAMETERS
K,, = .350
K12 = 050
K13= .006
L, = 10.
= 22.
L3= 67.
25
TIME DAYS
-------
- 123 -
Each term is assumed to start at time zero but to proceed at a different rate
and aim toward a different ultimate. Figure IV-19 shows how this curve can be
fit with a three term equation. As can be seen, each term in the equation reacts
with a much slower decay rate than the preceding terms. This in effect extends
the time over which the total ultimate BOD is reached.
In theory this type^ of approach is separating the waste material into three
individual components and assigning a different decay rate to each. Each
component's percent of the total waste strength is reflected by its ultimate term.
The decay rates for term two and three are usually at least an order of magnitude
lees than that for the first term. This implies that under normal circumstances
the last two terms contribute so little to the oxygen deficit that they can be
effectively ignored. However, there is an important case when this is not true.
Under ice conditions, the reaeration rate is effectively lowered to nearly zero.
As long as this condition exists, any exerted oxygen deficit will accumulate.
It is obvious that under such a condition, the effect of the last 2 terms in
equation IV-1 can be significant.
The above problems are compounded by the fact that very little long term BOD
sampling has taken place at the mouth of the Lower Fox River. There are several
reasons for this. First, until recently, the 5-day BOD measured at the Green Bay
Monthly Monitoring Station was believed to be adequate to characterize the strength
of the waste entering the Bay. This is true if the required information is merely
relative strength of the oxygen demand. The discussion above indicates why a
precise long-term BOD is required. Secondly, a severe sampling problem exists
at the mouth of the Lower Fox River. The monthly monitoring station in Green Bay
-------
- 124 -
is directly upstream of four large dischargers in the Green Bay area. Thus, the
effects of their waste on Green Bay is not included in the monthly monitoring data.
This problem will be further complicated by the new Green Bay sewage treatment
plant since the discharge location is actually a few hundred feet into the Bay
directly off the end of the Lower Fox River. Therefore, any data on pollution
loading to Green Bay from the Lower Fox River will at least be an estimate.
The first attempts to simulate the under-ice DO sag observed in Green Bay used
a single term BOD equation. It became apparent that not enough oxygen deficit
could be generated for the observed 5-day BOD and a normal conversion to ultimate
(usually 1.6 to 1.). (A single term BOD equation with a decay rate of 0.20/day
will yield a rate of BOD ult. to BOD5 of 1.58.) To account for this difference,
the benthic oxygen demand was adjusted until the observed sag was generated.
The result was a set of unrealistically high benthic oxygen demands. Laboratory
and field data both have indicated benthic demands at a relatively low level
(see Appendix C-Benthic Oxygen Demand). All measurements yield numbers in the
range of .05 to 2.0 GR 02/m2/day with a mean of about .2 GR 02/m2/day at 20°C.
Faced with this discrepancy, it was concluded that more attention had to be paid
to the "tail end" effects of the long-term BOD data. The three term BOD supplied
the required "tail end" effects.
It should be noted at this point that the effects predicted by the above described
BOD formulation may imply that significant reduction of short term BOD will not
change the long term BOD by a corresponding percentage. It is very possible
that a treatment system that effectively removes 90% of the 5-day BOD may only
be removing 50% of the ultimate BOD. In other words a 90% reduction in short
term BOD may yield far less improvement than at first expected. All is not lost
-------
- 125 -
however. The slower rates for decay of the last terms indicate that the time
in which the sag develops will be greatly increased, thus allowing considerably
more time for natural diffusion and dilution to decrease the strength of the
waste before severe depletion can occur. The above discussion reveals that the
effects of "Best Practicable Treatment" are not at all clear without some
improvements in the modelling techniques used to describe-the system interactions.
Faced with the above problems, an attempt was made to model the system using
a three term BOD equation. In terms of the computer model, this addition was
quite simple. This was done simply by writing parallel equations for each BOD
term. The difficulty in this approach lies in the fact that we now are dealing
with six unknowns instead of two (3 K rates and 3 ultimates). To facilitate
selection of the 6 unknowns, a simple computer program was devised that used
an iterative method to fit a given long term BOD curve such as Figure IV-19.
The long term curve fitting program selected the K rates and ultimates shown.
As can be seen, the fit is quite close to the observed BOD curve. Kjeldahl nitrogen
in the long term BOD of Figure IV-19 was near 1.0 mg/1. The nitrogen component
of the BOD was therefore less than 5.00 mg/1.
The second problem mentioned above involves the selection of temperature correction
coefficients. The BOD decay rates are input to the model assuming 20°C. The
model internally adjusts each decay rate for the simulation temperature. The
correction equation takes the form:
T-20
~ K20 6 (2)
-------
- 126 _
where: T = temperature °C
K2Q = decay rate at 20°C
Kj = decay rate at T°C
9 = correction coefficient
Most water quality models are run for temperature ranges of 15°C to 25°C. For
this range 6 is usually assumed to be a constant (about 1.047 for BOD). Very
little work has been done for temperatures below 10°C and even less for temperatures
below 4°C. Zanoni (1969) did some work on temperature effects on laboratory
BOD decay rates. He presented his work along with a collection of various other
research efforts along this line. Using the data presented by Zanoni the author
developed a plot of 6 versus T for laboratory BOD rates. This plot is shown
in Figure IV-20. As can be seen, the data generally lies along a straight line
with a negative slope. A linear regression on this data yield the equation:
6 = (-0.003856)1 + 1.140098 (3)
This equation was used in GBQUAL to adjust the BOD decay rates. There is very
little data available with which to verify equation IV-2. Hox^ever, a sample
taken from the Petenwell Flowage on the Wisconsin River in 1971 was located.
This sample is significant for two reasons. First, the Petenwell Flowage receives
large amounts of paper mill wastes from several sulfite and kraft pulp and paper
mills located within 15 miles upstream. This is similar to the Fox River-Green
Bay area. Secondly, the particular sample was split and incubated at two temper-
atures. The incubation took place at 20°C and at 4°C and lasted a total of 150 days.
To verify the temperature equation IV-2, the 20°C curve was first fit with a three
term BOD equation. With a close fit obtained for the 20°C curve, the decay rates
-------
FIGURE IV-20
TEMPERATURE VS 0 FOR BOD RATES
D
2
r
D
j_
a
CO
=
00
p
si-
p
CO
rn
, MOORE 1941
A
(
(
SCHROE
/ I
.
/ |
ZANOIMI 1S
r
GOT/
364 + 1967
kAS 1948
*
| - ------ - -
I
I
I
I
I
1
1
tan— _ -—_... — .
- - __ - _.
-. -_ _H
^FTER - A.E. Z/>
JOURNAL OF W/
\/OL. 41, p. 640, 1
LINEAR REGRE
6 = -.003856
^*
r t
i
1
i —
^NOW
kTER POLLUTIO
969
SSION YIELDS
T+ 1.140098
— (
M CONTROL FEE
I
JERATION
I
H*
to
^4
I
10
15
20 25 30
TEMPERATURE - °C
35
40
-------
- 128 -
were adjusted by equation IV-2. The 4°C curve was predicted and compared to
the 4°C curve actually measured. The results of this procedure are shown in Figure
IV-21. The closeness of the fit between the observed and predicted 4°C curve
is particularly gratifying and lends support to the use of equation IV-3.
A complete list of all parameters used in GBQUAL appears in Table D-3.
Winter Verifications
GBQUAL was verified for two sets of data obtained during the winters of 1967
and 1974. The data for 1967 consists mainly of dissolved oxygen measurements
taken for scattered transects. Although the data is not complete for a good
modelling attempt, valuable information can be obtained by simulating this case.
Average Lower Fox River inflow for this simulation period was 3381.0 CFS.
During the winter of 1974, a survey of Green Bay was designed and carried out
to gather sufficient data to attempt a proper verification of GBQUAL for ice
cover conditions. This survey, as described in Section III, obtained samples
over an extensive area of the Bay that was accessible. Samples for dissolved
oxygen were of primary importance. Measurements of BOD^, ammonia, nitrate and
phosphorous were also obtained as were various other constituents. All these
samples were taken in a five-day period in mid-February and served as the data
base for the 1974 verification.
Both verification runs were executed in the same manner. This consisted of first
developing the hydrodynamic scheme for the given flow rate. Next, the set of
inflowing water quality conditions was chosen to represent the average water
-------
FIGURE IV-21
48
PETENWELL FLOWAGE BOD
SAMPLE NO. 34428
SAMPLE TAKEN NOV. 11, 1971
SAMPLE WAS SPLIT AND RUN
AT 20°C AND 4°C
20°c CURVE'
FIT PARAMETERS
Kn = .2360 L, = 15.0
K12=.0100 L2 = 25.6
K13 = .0027 L = 61.0
MEASURED BOD
AT 20°C
—=- BOD CURVE FIT
USING 3 TERM METHOD
PREDICTED 4°C BOD
CURVE USING 0AS
A CONSTANT Q = 1.047
PREDICTED 4°C BOD
CURVE USING THE
TEMPERATURE
CORRECTION FOR Q
0 = - .003856T + 1.140098
T = °C
100
TIME DAYS
120
140
160
180
VO
I
200
-------
- 130 -
quality condition of the Fox River mouth over the simulation period (Jan. 1 to
Mar. 15). GBQDAL was then executed for a 50 day initializing period to develop
the system status which was stored and used as initial conditions to the ice
cover verification runs. The initializing run assumed low temperature (2°C)
and no ice cover. At this point GBQUAL was run for a 70 day simulation with
the ice cover condition imposed. Prints were obtained at 20 day intervals.
The inflowing water quality for each simulation was determined from measurements
of monthly monitoring data in Green Bay for the appropriate period. Table IV-7
lists data observations for the winter months of 1967 and 1974. Also listed
are the values of various constituents used for the inflow in the model for each
verification run. The three BOD terms in the model (which represent ultimates)
were determined by evaluating the point source discharges of BOD
-------
- 131 -
TABLE IV-7
Green Bay Measured Inflow Concentrations
Analysis
De Pere Dam (Mile 7.2)
2/1/67 2/28/67
Mason St. Bridge
1/24/74 2/20/74
(Mile 1.3)
3/14/74
BOD5
DO
Organic N
NH3-N
N03-N
TOT-P
Temp. °C
FLOW CFS
5.4
10.6
.91
.14
.20
.14
.5
3330.
5.4
10.7
5.0
4590.
4.9
11.0
1.03
.20
.19
.11
1.0
2920.
9.0
5.8
.77
.43
.11
.07
2.0
5230.
4.1
11.2
.84
.07
.18
.07
3.0
6105.
Inflow Concentrations Used for the Simulation Runs
Constituent
BOD ultimate
BOD ultimate
BOD ultimate
DO
Organic N
NH3-N
N03-N
SOL-P
Temp °C
FLOW
(1)
(2)
(3)
1967
15.0
20.0
50.0
10.0
.9
.5
.2
.03
2.0
3381.5
1974
5.0
20.0
50.0
10
0
75
5
15
03
2.0
4852.8
-------
- 132 -
FIGURE IV-22
D.O.
mg/1
1967 Simulation
Day 0
D.O.
mg/1
1967 Simulation
Day 20
D.O.
mg/1
1967 Simulation
Day kO
D.O.
mg/1
1967 Simulation
Day 60
-------
- 133 -
FIGURE IV-23
HH3
mg/1 as N
1967 Simulation
Day 0
NH3
mg/1 as N
1967 Simulation
Day 20
NH3
mg/1 as N
1967 Simulation
Day UO
NH3
mg/1 as N
1967 Simulation
Day 60
-------
- 134 -
FIGURE IV-2U
N03
mg/1 as N
1967 Simulation
Day 0
N03
mg/1 as N
1967 Simulation
Day UO
N03
mg/1 as N
1967 Simulation
Day 20
-------
FIGUBE IV-25
D.O. Stir face
mg/1
February 8-10
1967
D.O. Bottom
mg/1
February 8-10
1967
D.O. Surface
mg/1
March 9-10
1967
D.O. Bottom
mg/1
March 9-10
1967
-------
- 136 -
after 60 days of simulation show concentrations of 1 mg/1 over approximately
the same area that had zero DO. A decreasing concentration gradient occurs in
all directions around this area. The gradients are not nearly as sharp as those
for the DO. Dissolved oxygen was measured in Green Bay on February 8-10, 1967
and March 9-10, 1967. The February survey would correspond to approximately
40 days of ice cover. Direct comparison of this data is possible with day 40
of the simulation run. The model showed a rather linear gradient of DO from
the Fox River mouth to Point Sable. The DO went from 8.0 mg/1 to .5 mg/1. The
measured DO showed levels of 5 and 6 mg/1 in the Bay Beach area and .5 to .1
mg/l near Point Sable. Beyond Point Sable, a large area near Red Banks showed
0.0 mg/1 DO from the top to the bottom. Low DO's near the bottom generally covered
a larger area than those measured near the surface. Measurements during the
March survey only covered areas north of Dykesville. Low DO's were seen in all
areas but only very close to the bottom. Near the surface and at mid depths
the DO's were nearly always above 8.0 mg/1. This survey would correspond to
about 70 days after the ice cover began. The closest simulation printout is
for day 60. This printout reveals a pattern similar to the 40 day printout but
with slightly expanded extent. DO levels above Dykesville generally are above
8.0 mg/1. The Dykesville area is right in the vicinity of the positive DO gradient.
In general the match for the 1967 DO pattern is quite acceptable.
The 1974 verification is much more complete. The data includes measurements
of NH-j-N, NOo-N, organic N, total and soluable phosphate as well as dissolved
oxygen and 8005. The data for the February 18-20, 1974 survey is presented in
Section III. The simulation output for various constituents is shown in Figures
IV-26 through IV-29. Ice cover on Green Bay during 1974 began about January 10th
(private communication, Wiersma 1974). Therefore the February 18-20, 1974 survey
-------
- 137 -
FIGUKE IV-26
D.O. mg/1
19T1* Simulation
Day 60
-------
- 138 -
FIGURE IV-27
NH3
mg/1 as N
1971* Simulation
Day 0
N
Simulation
HH3
mg/1 as N
Simulation
Day 20
mg/1 as N
Simulation
Day 60
-------
- 139 -
FIGURE IV-28
ng/1 as N
197*1 Simulation
Day 0
mg/1 as N
1971* Simulation
Day 20
N03
mg/1 as N
Simulation
Day 60
mg/1 as N
19T1* Simulation
Day
-------
- 140 -
FIGURE IV-29
Ortho Phosphate
mg/1 as P
1971* Simulation
Day 0-60
Organic Nitrogen
mg/1 as N
Simulation
Day 0-60
-------
- 141 -
would correspond to about day 40 of the ice cover simulation. The 40 day printout
shows a 5.0 mg/1 contour covering an oblong area off Red Banks. This corresponds
very well with the measured values in this area shown in Section III. Values
around 3.0 mg/1 DO are indicated in the data in the Red Banks area. This corresponds
nicely with the simulation output.
The ammonia profiles from the simulation output at day 40 appear to be slightly
high when compared to the measured data. The model shows a wide area, from the
center of the bay below Long Tail and Point Sable extending beyond Dykesville
across to the Big Suamico River, that is above 0.6 mg/1 ammonia. Inside this
area levels are calculated as high as .85 mg/1. The survey data shows a long
triangular area centered around Point Sable and extending to Red Banks that has
0.6 mg/1 ammonia. The higher level in the model may well be a result of over
estimating the inflowing concentration of NH^-N in the simulation run. Measured
values at the Mason St. Bridge (shown in Table IV-7) indicate the inflow concentration
should have been .3 to .4 mg/1 ammonia instead of- the .5 mg/1 value. It is worth
noting, however, that the shape of the .6 mg/1 area in the simulation output
is roughly correct and is centered over the same area.
Winter Prediction Runs
Two Green Bay winter prediction runs were made with the model. Both of these
runs utilized all decay coefficients the same as for the verification runs. The
only variable was the flow and concentration of BOD (high flow will of course
dilute the discharged BOD). Table IV-8 lists the inflow conditions used for
these two runs.
-------
- 142 -
TABLE IV-8
Green Bay Simulation Inflow Concentrations
Run 1 Run 2
BOD-1 2.0 5.0
BOD-2 4.0 10.0
BOD-3 30.0 50.0
DO 10.0 8.0
Organic N 0.5 0.6
NH3-N 0.5 0.5
N03-N 0.2 0.2
Sol-P 0.03 0.03
Temp °C 2.0 2.0
FLOW CFS 2400. 912.
-------
- 143 -
Critical flow conditions for the winter case were determined by scanning the
last 15 years of records. The lowest flow (averaged over January, February and
March) for the winter period was found to be 2400 CFS. This flow was used along
with the flow of 912 CFS, the 7 day, 10 year low flow. The results of both of
these runs are shown in Figures IV-30 to IV-37. The flow case for 912 CFS was
run for comparison purposes only. A flow this low over the entire winter period
is unrealistically low. The 2400 CFS flow case more accurately represents the
"worst case" condition for the winter months.
The 2400 CFS run shows that after 60 days of ice cover the minimum dissolved
oxygen level drops to 6.1 mg/1. The main difficulty in accepting this result
lies in our estimation of the ultimate BOD used for the inflowing concentration
at the mouth of the Fox River. Figure IV-38 illustrates two 50 day BOD curves.
The top curve is the same BOD curve shown in Figure IV-19 and is described by
the given 3 term equation. The bottom curve was selected as representative of
the ultimate BOD curve under BPT treatment conditions and 2400 CFS. It was assumed
that the largest percent reduction would be from the most easily oxidizable substances.
Thus LI was reduced by 87.5%, 1^ by 75% and 1,3 by only 40%. Our results show
that under the given ultimate BOD inflow, 5 mg/1 of dissolved oxygen will probably
be met for average winter flows as low as 2400 CFS. However, the sag in DO comes
so close to 5.0 mg/1 that we must conclude that the given BOD ultimate curve
represents the maximum allowable BOD to maintain 5.0 mg/1 at all times under
ice conditions. If our assumption concerning the ultimate BOD curve for BPT
underestimates the actual BOD loading, then water quality violations of the
dissolved oxygen can be expected to continue. In the Green Bay area, (De Pere
to Green Bay), BPT will represent about a 75% reduction in 5 day BOD loading based
on present permits. The curves shown in Figure IV-38 show a 74% reduction at
the 5th day. It therefore appears that our estimation is close to the expected
BPT conditions.
-------
- 144 -
FIGURE IV-30
D.O.
mg/1
15-Year Winter
Low Flow
Pred. BPT Loading
Day 0
D.O.
mg/1
15-Year Winter
Low Flow
Pred. BPT Loading
Day 20
D.O.
mg/1
15-Year Winter
Low Flow
Pred. BPT Loading
Day
Winter
Flow
Loading
-------
- 145 -
FIGURE IV-31
NH3
mg/1 as N
15-Year Winter
Low Plow
ed. BPT Loading
Day 0
mg/1 as K
15-Year Winter
Low Flow
Pred. BPT Loading
Day kO
mg/1
15-Year Winter
Low Flow
BPT Loading
Day 20
NH3
mg/1 as
15-Year Winter
Low Flow
BPT Loading
Day 60
-------
- 146 -
FIGURE IV-32
N03
mg/1 as N
15-Year Winter
Low Flow
Pred. BPT Loading
Day 0
mg/1 as N
15-Year Winter
Low Flow
Pred. BPT Loading
Day 20
N03
mg/1 as N
-Year Winter
Low Flow
Pred. BPT Loading
Day UO
N03
mg/1 as N
15-Year Winter
Low Flow
Pred. BPT Loading
Day 60
-------
- 147 _
FIGURE IV-33
Phosphat
mg/1 as P
15-Y«ar Winter
Low Flow
Pred. BPT Loading
Day 0-60
Nitrogen
mg/1 as N
15-Year Winter
Low Flow
Ted. BPT Loading
Day 0-60
-------
- 148 -
FIGURE IV-3U
D.O.
mg/1
912 cfs
red. BPT Loading
Day 0
D.O.
mg/1
912 cfs
BPT Loading
Day 20
D.O.
mg/1
912 cfs
Pred. BPT Loading
Day UO
-------
- 149 -
FIGURE IV-35
NH3
mg/1 as N
912 cfs
red. BPT Loading
Day 0
mg/1 as N
912 cfs
. BPT Loading
Day 20
mg/1 as N
912 cfs
Fred. BPT Loading
Day
mg/1
912 cfs
. BPT Loading
Day 60
-------
- 150 -
FIGURE IV-36
N03
mg/1 as N
912 cfs
Fred. BPT Loading
Day 0
H03
mg/1 as N
912 cfs
Pred. BPT Loading
Day 20
as N
NO
mg/1
912 cfs
Pred. BPT Loading
Day UO
N03
mg/1 as N
912 cfs
BPT Loading
Day 60
-------
- 151 -
FIGURE IV-37
Ortho Phosphate
mg/1 as P
912 cfs
Pred. BPT Loading
Day 0-60
Organic Nitrogen
mg/1 as N
912 cfs
ed. BPT Loading
Day 0-60
-------
FIGURE IV - 38
ALLOWABLE FOX RIVER
LOADING TO GREEN BAY
PRESENT LOADING TO
GREEN BAY
PRESENT ULTIMATE
BOD CURVE FOR
FOX RIVER WATER
AT THE RIVER MOUTH
WITH 2400. CFSOF FLOW
AVAILABLE FOR DILUTION
REQUIRED MINIMUM
BOD ULTIMATE CURVE
TO MAINTAIN 5 MG/I
UNDER WINTER
CONDITIONS 2400 CFS
Kn = .350
K12= -050
K13 = .006
-------
- 153 -
The final waste load allocation under critical summer flow conditions (developed
earlier) shows an overall 37% reduction in the 5 day BOD loading compared to
BPT loadings. Under the WLA discharge scheme it would be extremely unlikely
that the dissolved oxygen would drop below 5.0 mg/1 during the ice cover. On
the basis of the above studies, it can be concluded that the summer critical
condition in the Lower Fox River represents the "worst case condition" for the
Fox River-Green Bay system. If high levels of DO can be maintained in the river
by limiting the BOD discharges, the winter DO sag in the Lower Bay should be
eliminated.
-------
-------
-155 -
SECTION V
V. DISCUSSION
Dissolved Oxygen
One of the most important objectives of this project consists of determining
the worst case condition for dissolved oxygen in the Lower Fox River-Green Bay
system. The worst case condition acts as the controlling situation in the
determination of the final "waste load allocation". For the Bay itself, the
worst case appears to be the winter ice-cover period. During this time the
dissolved oxygen can go to zero over wide areas of the Bay. This massive DO
sag disrupts potential commercial and sport fishing in the Lower Bay. Also
chemical reactions take place in this region that may enhance the eutrophic
nature of Green Bay.
In the Lower Fox River, the critical condition occurs during the high temperature,
low flow season. During the months of late June to early September, high
temperatures and low flow can cause very low levels of dissolved oxygen over
10 to 20 miles of the Lower Fox River. Levels of DO below 1 mg/1 are not
unconmon. This level of dissolved oxygen virtually excludes the possibility of
fish life in these stretches of the river.
An important question that must be asked at this point is which of these conditions
is most critical to the overall dissolved oxygen balance? The answer to this
question was not at all clear before modelling was undertaken. If we limit BOD
discharges such that the winter problem for DO is corrected, have we done enough
to correct the summer low DO's in the river also? Between the two modelling
-------
- 156 -
efforts developed for this study, the answer appears to be no. The most critical
dissolved oxygen condition will occur during the summer months and will affect
water in the Lower Fox River particularly in the Green Bay area. With all
dischargers limited to "Best Practicable Treatment", serious oxygen problems
will still be present in the Lower Fox River. Figure IV-12 diagrams the expected
result for BPT discharges and the 7 day 10 year (7Q10) low flow. If we study
the expected BPT effect on the ice-covered Bay for low flow conditions, we note
that the DO is expected to drop no lower that about 6 tng/1 (more than enough
for most species of fish). ' We must observe however, that the winter low flow
rate is nearly 3 times the statistical 7Q10 low flow. There are two reasons
for this. First, since the winter sag occurs over a three month period, we must
consider a 3 month average flow. Naturally, the lowest flow over a 3 month
period for a river such as the Lower Fox River will be considerably greater
than the 7Q10 flow. Secondly, the lowest flows never occur during the winter
months. Thus the average flow during January, February and March is considerably
higher than the average flow of July and August. Therefore it is not realistic
to use the 7Q10 flow for the winter prediction runs. The choice of 2400 CFS
was based on the lowest average flow for January through March observed in the
past 15 years of record. If we assume that 2400 CFS represents a logical choice
for the winter low flow and all dischargers are limited to "Best Practicable
Treatment", then based on the Green Bay model, the dissolved oxygen will not
go below 5 mg/1 in Green Bay.
The above conclusion does not guarantee that other conditions will not interact
to lower the DO below 5 mg/1 during the winter months. If a particular winter
has flows lower than 2400 CFS, DO problems may develop. The run made with 912
CFS as the average winter inflow generated a DO sag that went down to 2 mg/1.
-------
- 157 -
Secondly, all the discharge permits allow for maximum levels of discharge that
may range from 1.5 to 3 times the monthly average. If one or more large dischargers
release an effluent that approaches their maximum limit then the DO may be lowered
below 5 mg/1 even if the flow is greater than 2400 CFS. Since there is very
little margin in meeting the 5 mg/1 DO level under BPT conditions it is therefore
manditory that dischargers be regulated very tightly. Maximum discharges should
be no greater than 1.5 times the average. Vigorous enforcement must be maintained
to discourage slug load inputs that could generate a costly fish kill. Improving
water quality should generate higher populations of desirable fish amplifying the
importance of tight enforcement.
At present the Wisconsin Department of Natural Resources allows for a dissolved
oxygen variance in Green Bay. Chapter NR 103.05 (5) states that waters
"southeasterly from the navigation channel and southerly from the north line
of Brown County...shall not be lowered to less than 2 mg/1 at any time" during
the period January 1 to April 1. In light of the conclusions presented above,
Chapter NR 103.05 (5) should be reevaluated. Under the Wisconsin Pollution
Discharge Elimination System (WPDES), all discharges should be meeting "Best
Practicable Treatment" levels by the end of 1977. At that time it can be
concluded that a dissolved oxygen standard of 5 mg/1 should be applied to the
area of Green Bay that is specified in Chapter NR 103.05 (5). The variance
condition that now applies over that region of Green Bay will no longer be
necessary except under the extreme conditions mentioned above. It is most
likely that any violation of 5 mg/1 that may occur will not be very serious and
will surely not require a 2 mg/1 variance.
The dissolved oxygen conditions in the Lower Fox River itself is another matter.
Even with BPT conditions met by all dischargers, violations of the present
-------
- 158 -
variance conditions for dissolved oxygen may occur in at least 3 places along
the river during the 7Q10 flow and high temperatures. Thus by the year 1977,
one can expect water quality violations to continue in the Lower Fox River.
Table IV-6 presents the results of the "waste load allocation" applied to the
Lower Fox E.iver using the QUAL-II simulation model. This Table lists the amount
of BOD5 and suspended solids that each discharger could release such that 5 mg/1
of dissolved oxygen would still be maintained under the 7Q10 flow and high summer
temperatures. This Table lists the maximum discharges that can be allowed under
critical conditions. Figure IV-18 gives useful information as to the size of
the diurnal fluctuations that can be expected as a result of algae activity.
A range of about 1.0 mg/1 in the dissolved oxygen can be expected if the inflowing
chlorophyll-a concentration is about 30 ug/1. If larger amounts of algae are
present the fluctuation will be greater and 5 mg/1 may be violated under nightime
or prolonged overcast weather conditions.
It should be emphasized that Table IV-6 represents only one possible scheme for
a "waste load allocation". In general most schemes will have to be fairly close
to the one given. Tradeoffs in BOD loading between dischargers located very
close together would be possible, however, increasing the discharge at a site
several miles from another that was decreased would not be possible. Secondly,
it is a matter of public interest as to whether a portion of the WLA should be
saved for future municipal or industrial growth. If a portion is to be retained,
a decision will have to be made as to how much each discharger is to be reduced
beyond that allowed in Table IV-6. This type of process will require public
participation to weigh all sides of this issue.
-------
- 159 -
Up to this point, no mention has been made of a safety factor for the WLA discharge
scheme. Table IV-6 leaves very little margin of error to meet the 5 mg/1 dissolved
oxygen standard under critical conditions. In light of this fact, a portion
of the WLA. should perhaps be withheld to allow for a reasonable margin of safety.
Again it must be emphasized that a discharge permit that allows a maximum discharge
of 1.5 to 3.0 times the average discharge will not be permissable if 5 mg/1 DO
is to be maintained. Maximum limits must be held as close to the average limit
as possible. A slug load from two or three dischargers simultaneously could create
a serious dissolved oxygen situation and may result in a fish kill. If part
of the "waste load allocation" were withheld for future growth, then that portion
would be able to act as a safety margin until such time as it is required by
municipal or industrial expansion.
Ammonia reduction at all point sources will not significantly affect the DO profile.
If nitrification had shown itself to be an important oxygen sink in the Lower
Fox River, then nitrification at all sewage treatment plants would have supplied
a useful safety factor in meeting the 5 mg/1 dissolved oxygen level. Secondly,
the concentration of NH^+ is more readily absorbed by algae so a reduction in
ammonia could work to slightly lower the algae activity along the river and in
the Bay. The nitrification rates, however, appear to be very small along the
Lower Fox River (about 0.07 day"1 base e at 20°C). The low nitrification rate
in the river may arise from three sources. First, according to Tuffey et al
(1974), nitrification generally will be the lowest in moderately large streams.
This result is a conclusion based on the fact that nitrifying bacteria like to
grow attached to a surface. A small stream supplies an adequate bottom surface
area to volume ratio to affect good nitrification where as a large stream does
not. In Green Bay itself, nitrification would be expected to occur, according
-------
- 160 -
to Tuffey, since the retention times are greatly increased and suspended material
provide sufficient medium for nitrifying bacteria. The second reason for low
nitrification rates results from the high average pH found along the Fox River.
Nitrifying bacteria flourish in a relatively limited pH range. That range is
usually reported to be between 7.0 and 8.0. Beyond either end of this range,
the rate of nitrification drops off sharply. Low dissolved oxygen levels during
the summer months also tend to inhibit nitrification. Nitrifying bacteria become
inactive if the DO drops below 2.0 mg/1. All of these conditions reduce the
importance of nitrification in the Lower Fox River, in regard to the oxygen
balance.
The simulation output indicates that ammonia is coming mainly from organic nitrogen
compounds flowing into the Fox River from Lake Winnebago. These organic nitrogen
forms (particularly dead algae) can hydrolyze to ammonia. Ammonia can also be
released from nitrogen compounds in the sediments. Because of the low nitrification
rate, the ammonia tends to accumulate often reaching toxic concentrations. Ammonia
is toxic to most species of aquatic organisms when it exists in the unionized
form. The Water Quality Criteria of 1972 (Blue Book) recommends a concentration
of unionized ammonia no greater than 0.02 mg/1. The toxicity problem is further
amplified by the high pH in the river. The high pH pushes the ammonia-ammonium
balance toward the unionized ammonia form. Thus ammonia toxicity appears to
be a problem that may not be adequately correctable by point source controls.
On the other side of this question, nitrification may be partially enhanced by
sufficient point source control of BOD for two reasons. Adequate treatment of
wastes in treatment plants will raise the dissolved oxygen concentration such
that low DO will no longer be a nitrification inhibiting factor. Secondly,
-------
- 161 -
closer control of the industrial dischargers may act to lower the average pH
of the river. These two effects could be sufficient to stimulate nitrification
to a point where ammonia will not tend to accumulate. The resulting increased
nitrification could cause a alight lowering of the dissolved oxygen in the river.
At present, the QUAL-II model is capable of responding to the relationship between
dissolved oxygen and nitrification. The simulation runs that were done for this
project all showed a slightly higher concentration of nitrate when the dissolved
oxygen was increased. Similarly, the denitrification rate is controlled by the
dissolved oxygen level. Higher DO's tend to eliminate denitrification as a
significant nitrogen sink in the model. These effects may combine to increase
the inorganic nitrogen that flows down the Fox River and eventually into Green
Bay.
A rudimentary sensitivity analysis was done with the QUAL-II model for the Lower
Fox River. The results of this analysis are presented in Table V-l. The base
line conditions are those used for the low flow and BPT simulation run. Table
V-2 lists the base line headwater and reaction rate conditions. The most noteable
effect in Table V-l is the extreme sensitivity of the model to the benthic demand.
Algae growth and respiration rates also have a marked affect on the oxygen level.
In general, there is a correlation between oxygen and ammonia (higher oxygen leads
to lower ammonia) and between oxygen and nitrate (lower oxygen means lower nitrate
concentrations). The rate of organic nitrogen feedback to inorganic forms has a
noticeable affect on the growth of algae. Oxygen levels respond to this change
also. Organic nitrogen settling rate shows almost no effect of this sort.
-------
- 162 -
TABLE V-l
Sensitivity of the QUAL-II
Model on The Lower Fox River
(Base Conditions are for Low Flow and BPT)
Parameter
Altered
Base
Condition
No . Change
Benthic
Demand
Times 1.5
Benthic
Demand
Times 0.5
BOD
Decay
Times 2.0
BOD
Decay
Times 0.5
Org-N
Decay
Times 2.0
Org-N
Decay
Times 0.5
Org-N
Settling
Times 2.0
Org-N
Settling
Times 0.5
Ammonia
Decay
Times 2.0
Ammonia
Decay
Times 0.5
Mile
Point
34.5
19.0
0.1
34.5
19.0
0.1
34.5
19.0
0.1
34.5
19.0
0.1
34.5
19.0
0.1
34.5
19.0
0.1
34.5
19.0
0.1
34.5
19.0
0.1
34.5
19.0
0.1
34.5
19.0
0.1
34.5
19.0
0.1
DO
mg/.l
3.56
2.91
1.83
.74
.14
.00
6.40
5.73
5.21
3.00
2.42
1.11
4.40
3.53
2.50
3.62
3.11
2.06
3.52
2.74
1.52
3.56
2.90
1.84
3.56
2.92
1.83
3.44
2.72
1.33
3.63
3.03
2.24
BOD
mg/1
.96
1.58
2.20
.96
1.58
2.20
.96
1.58
2.20
.33
.75
1.62
1.71
2.58
2.86
.96
1.58
2.20
.96
1.58
2.20
.96
1.58
2.20
.96
1.58
2.20
.96
1.58
2.20
.96
1.58
2.20
Org-N
mg/1
1.995
1.492
.786
1.995
1.492
.784
1.995
1.492
.784
1.995
1.492
.786
1.995
1.492
.786
1.733
1.113
.429
2.136
1.723
1.080
1.852
1.276
.556
2.071
1.615
.941
1.995
1.492
.784
1.995
1.492
.787
NH3-N
mg/1
.479
.799
.928
.490
.833
1.030
.476
.789
.901
.481
.804
.935
.477
.795
.922
.729
1.137
1.182
.343
.589
.697
.468
.763
.824
.485
.819
.991
.441
.693
.673
.500
.861
1.112
N03-N
mg/1
.099
.141
.290
.071
.075
.096
.113
.179
.434
.091
.128
.267
.105
.154
.312
.106
.176
.406
.095
.121
.206
.099
.139
.272
.099
.142
.300
.115
.198
.402
.090
.107
.191
Chl-a
mg/1
27.15
28.55
21.46
27.06
28.22
20.89
27.20
28.77
21.90
27.10
28.45
21.37
27.17
28.64
21.56
29.24
33.05
25.69
25.76
25.19
17.50
27.09
28.26
20.71
27.18
28.70
21.85
26.96
28.04
20.72
27.25
28.82
21.86
-------
- 163 -
TABLE V-l (continued)
Parameter
Altered
Algae
Growth
Times 2.0
Algae
Growth
Times 0.5
Algae
Respiration
Times 2.0
Algae
Respiration
Times 0.5
1500 CFS
Flow
Rate
700 CFS
Flow
Rate
Temperature
84°F
Temperature
72°F
Temperature
35s]?
100 Lang/Day
Mile
Point
34.5
19.0
0.1
34.5
19.0
0.1
34.5
19.0
0.1
34.5
19.0
0.1
34.5
19.0
0.1
34.5
19.0
0.1
34.5
19.0
0.1
34.5
19.0
0.1
34.5
19.0
0.1
DO
mg/1
4.85
5.55
2.07
2.93
1.54
0.0
2.46
.89
0.0
4.20
4.43
3.15
4.93
4.31
3.56
2.80
2.08
.67
2.74
2.17
1.11
5.11
4.37
3.23
10.47
11.17
9.73
BOD
mg/1
.96
1.58
2.20
.96
1.58
2.20
.96
1.58
2.20
.96
1.58
2.20
1.32
1.66
1.74
.76
1.50
2.50
.86
1.44
2.11
1.19
1.86
2.38
2.12
3.21
3.35
Org-N
mg/1
2.011
1.563
1.079
1.989
1.472
.717
2.005
1.486
.719
1.984
1.481
.816
2.171
1.801
1.162
1.875
1.308
.619
1.968
1.452
.746
2.042
1.566
.865
2.176
1.790
1.159
NHo-N
mg/1
.463
.717
.781
.485
.827
1.093
.485
.835
1.137
.476
.777
.855
.333
.594
.844
.576
.908
.923
.519
.875
1.065
.397
.636
.633
.308
.562
.771
NOa-N
mg/1
.104
.163
.314
.096
.121
.078
.092
.106
.055
.102
.157
.374
.099
.117
.221
.097
.153
.284
.086
.105
.201
.133
.234
.500
.101
.114
.161
Chl-a
54.15
101.02
99.99
18.24
11.27
3.10
12.73
5.86
.65
39.64
59.28
81.95
26.84
26.04
21.00
27.74
31.04
20.96
27.47
29.70
21.81
26.69
26.77
20.69
24.54
20.00
12.39
-------
- 164 -
TABLE V-2
Base Line Conditions for Sensitivity Runs *
Inflow Concentrations
Reaction Rates (Base e)
Flow
DO
BOD
Org-N
NH3-N
N03-N
P04-P
Chl-a
Temp.
912 CFS
9.0 mg/1
2.0 mg/1
2.5 mg/1
.04 mg/1
.10 mg/1
.20 mg/1
30 mg/1
80°F
BOD Decay
Org-N Decay
Org-N Settling
NH3-N Decay
Algae Growth
Algae
Respiration
Algae Settling
. 306/day
.035/day
.025/day
.07/day
1.0/day
.2/day
1.0 ft /day
* For benthic demands see Table IV-1.
-------
- 165 -
Nutrients and Primary Production
The nutrient balance in Green Bay is controlled by several factors. The Lower
Fox River is the largest single source of nutrients to Green Bay. Large quantities
of nitrogen and phosphorus are continually being supplied to the Bay. Much of
the nutrients that enter the Bay arrive during the spring runoff period. As
much as 50% of the yearly inflowing nutrients may arrive during the spring period.
Figure V-l illustrates the Lower Fox River hydrograph for the period of this
study. The peak flows in April, May and June carry high nutrient loads washed
off of partially frozen ground. In addition, to the Lower Fox River other rivers
such as the Oconto, Peshtigo and Menominee supply nutrients. These nutrients
stimulate extensive algae blooms through out the Lower and Middle area of the
Bay.
The algae growths represent one portion of a complicated nutrient cycling process.
This process is characterized by algae blooms in spring and early summer that
appear to be nitrogen limited. The nutrients consumed in this phase can be recycled
(particularly in shallow areas) or it can be carried out of the growth zone by
settling of dead algae cells. This phase is followed by an extensive bloom of
nitrogen-fixing algae. The extent of the second bloom appears to be phosphorus
limited. The nitrogen-fixing algae (Anabaena and Aphanizomenon) can contribute
significant quantities of nitrogen to the Bay during their bloom period. The
input of nitrogen from the nitrogen-fixing algae allows the nitrogen dependent
forms to once again bloom. The rotation of algae types occurs at least twice
during the summer period. This pattern was first observed by Vanderhoef et al
(1972, 1974). The surveys taken by the Wisconsin DNR during the summer of 1974
-------
o
o
o
FIGURE V-l
Lower Fox River Hydrograph During the Green Bay Study Period
(Flows in cfs)
o
o
o
CM
O
O
o
o
o
o
o
co
o
o
o
vo
O
O
O
o
o
o
SEPT 73
OGT 73
NOV 73
DEC 73
JAN 74
FEB 74
MARCH 74
-------
FIGURE V-l (Continued)
MARCH 74
APRIL 74
MAY 74
JUNE 74
JULY 74
AUG 74
SEPT 74
-------
- 168 -
support this cyclic nature of the algal types. This pattern is violated in the
Lower Bay only in close to the mouth of the Fox River. High inorganic nitrogen
concentrations exist in this area all year around. For that reason, nitrogen
fixing algae never predominate.
An important aspect of the nutrient cycles in Green Bay concerns the sediment-
water exchange mechanisms. These exchange mechanisms tend to stablize the phosphorus
concentration in the Bay. The 1974 survey data suggests that an important source
of phosphorus may be the resuspension of phosphorus containing bottom sediments
in the shallow portions and along the shore in the Bay. The phosphorus released
in this way can become available for primary production if the necessary chemical
reactions take place to transform the phosphorus into soluable forms. This process
appears to take place faster than algal uptake during the spring and early summer
when growth rates are still low due to cold temperatures. Later on, the growth
of algae may overtake the resoluabilization process causing phosphorus limited
primary production. This explanation is consistent with the observed increase
of phosphorus in May and June, followed by a gradual decrease for the rest of
the summer.
Phosphorus also settles into the sediments. Sinking algal cells and chemical
precipitation carries phosphorus into the sediments. In the deeper areas of
the Bay the sediments usually act as a net sink for phosphorus. However, under
anaerobic conditions phosphorus is resoluabilized at a rate that may be 10 times
faster than under aerobic conditions. Survey data in February 1974 indicated
slight increases in the soluable phosphorus compounds in the same region where
low dissolved oxygen was detected.
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Ammonia levels in Green Bay don't appear to be a problem except for a small area
very close to the mouth of the Lower Fox River. When the temperatures are high,
the ammonia level drops to almost unmeasurable levels over the entire Bay.
Nitrification and algae uptake during the summer account for this low level of
ammonia. Toxicity from free ammonia in Green Bay occurs only within a few
hundred yards of the mouth of the Fox River where inflowing levels are high.
During colder winter temperatures the higher ammonia levels from the Lower Fox
River penetrate into the Bay for as much as 10 to 20 miles. Ammonia measurements
near Red Banks showed 0.6 mg/1 during the February survey of 1974. The higher
levels of ammonia during the winter months do not cause a toxicity problem,
however, due to the low temperatures of the water
It is interesting to observe the rather dramatic increase in nitrate in the deeper
water of the Bay during the summer. The nitrate can be coming from at least
two sources. First; ammonia released from the sediments is trapped below the
thermocline. This ammonia eventually undergoes nitrification to nitrate since
there is not enough light in the deeper waters for primary production. Secondly,
sinking algal cells release nitrogen compounds that will also nitrify. The
accumulated nitrate, however, will not become available to algae until the fall
turnover when the water mixes.
The results of the Lower Fox River modelling effort indicated that higher dissolved
oxygen levels may result in slightly higher concentrations of inorganic nitrogen
entering Green Bay. If this is true, then the early summer blooms of nitrogen
fixing algae may be delayed due to the prolonged predominance of other forms
of phytoplankton. The result would be an upset of the cyclic pattern of algal
species observed by Vanderhoef et al (1972, 1974) and the Wisconsin DNR.
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Improved treatment at municipal sewage plants may reduce the total nitrogen loading
to the Fox River and thereby offset the rise in nitrogen entering Green Bay.
Effective biological treatment, removing combined sewers and ending sewage overflow
bypassing would result in reductions in both total nitrogen and total phosphorous
loading along the Lower Fox River.
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SECTION VI
VI. SUMMARY AND RECOMMENDATIONS
The following list is a summary of the major findings and recommendations of
this study:
1. The most critical dissolved oxygen condition in the study area appears to be
the summer low flow period in the Lower Fox River. Substantial improvements at
point source discharges beyond "Best Practicable Treatment" will be required to
maintain a dissolved oxygen level above 5.0 mg/1 at all times. BPT levels of
treatment are expected to violate variance dissolved oxygen standards at three
locations along the river during low flow and high temperatures.
2. The winter ice cover period (January to early April) has caused frequent low
dissolved oxygen problems in Lower Green Bay in the past. High organic loadings,
together with nearly zero reaeration, have caused as much as 150 square miles of
the Lower Bay to suffer severe DO depletion. The survey of February 1974, a part
of this study, indicated a 50 square mile area with 5 mg/1 of DO or less along the
eastern half of the Bay from Point Sable to the Renard River.
3. The methods presented in this report show that dissolved oxygen modelling of
the winter condition in Lower Green Bay can be accomplished with a sufficient
degree of accuracy to allow conclusions to be made for various abatement schedules.
4. Dissolved oxygen modelling of the winter ice cover period in Lower Green Bay
indicates that "Best Practicable Treatment" at all point sources along the Lower
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Fox River will be sufficient to maintain 5.0 mg/1 of dissolved oxygen in Lower
Green Bay during the winter period. On the basis of this modelling, it is
recommended that the dissolved oxygen variance on Lower Green Bay be removed
effective 1977 when "Best Practicable Treatment" is to be met.
5. Long term BOD (60 days) monitoring should be considered in the Green Bay area
as a means of determining the changes that will take place in the BOD load to
Green Bay during the compliance period with the present permits. This is
especially important since the long term BOD is the prime factor in determining
the severity of the winter dissolved oxygen deficit in Green Bay.
6. Review of the location of the Green Bay monitoring station is highly
recommended. At present, sampling is done at the Mason Street Bridge in Green
Bay. This location is upstream of three large paper mill effluents and the
Green Bay sewage effluent. The concentrations reported at this station do not
reflect accurate representations of the actual loading to Green Bay.
Unfortunately, it is probably not possible to obtain a representative sample in
this area because of the Green Bay seiche effects in the River and the location
of the new Green Bay sewage plant effluent. It may be appropriate to report
concentrations at the mouth of the Fox River (i.e., true loading to Green Bay)
by separately considering the addition from the downstream effluents.
7. Dissolved oxygen modelling of the Lower Fox River indicates that an average
reduction of the 37% below "Best Practicable Treatment" will be required to
maintain 5.0 mg/1 of dissolved oxygen during the low flow and high temperature
period. The waste load allocation developed by the model takes into account
the suspended solids reductions at each discharge location.
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-173 _
Any future modifications to permits affected by the load allocation should use
the waste load allocation as a basis of the permit. This discharge scheme has
been developed to maintain 5.0 mg/1 of dissolved oxygen in the Lower Fox River.
Daily maximum discharges allowable in the permits should be less than one and
one-half times the daily average allowed discharge to avoid shock loads that
could cause a substantial fish kill.
8. The largest single source of nitrogen in the Lower Fox River appears to be
Lake Winnebago. Ammonia toxicity may continue to be a problem in the Lower
Fox River during high temperatures, even if treatment plants are required to
remove ammonia from their effluents. Since nitrification in the river does not
appear to a substantial degree, little dissolved oxygen change will result from
removing ammonia.
9. Higher dissolved oxygen levels in the Lower Fox River may tend to increase
the concentration of inorganic nitrogen entering Lower Green Bay as a result of
decreased denitrification rates. This may be offset by improved treatment and
elimination of bypassing from cimbined storm sewers.
Increased monitoring of nitrogen forms should be included in the discharge permits
especially for sewage treatment plants. Monitoring should include total organic
and ammonia nitrogen forms. This type of monitoring will allow future evaluation
of nitrification as a means of reducing ammonia levels in the Lower Fox River.
10. It is difficult to determine what the phosphorus concentration will do in
the future. All treatment plants serving more than 2,500 people are now required
to remove 85Z of the total phosphorus in the effluent. Bypassing and poor
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treatment at temporary add-on facilities have reduced the effectiveness of the
phosphorus removal program. New treatment systems should correct this problem
at sewage treatment plants. On the other hand, biological treatment of pulp
and paper mill wastes may require nutrient additions, including phosphorus.
Proposed regulations will limit these discharges tp a concentration of 1.0 mg/1
or less. The net effect is unclear at this time, but will probably not be
significant compared to the phosphorus loading from Lake Winnebago.
11. A monthly monitoring station, similar to other monthly monitoring stations
maintained by the DNR, was begun in the Neenah-Menasha area as a result of an
early recommendation of this project. A monitoring station in Green Bay has
been sampled monthly since 1961. Results from the new station will allow
determination of the net effects of discharges along the Lower Fox River.
12. Sampling in Green Bay during the summer of 1974 revealed total phosphorus
concentrations not significantly different from those observed in 1973.
Phosphorus concentrations in 1971 were significantly higher in the Inner Bay
than those observed in 1974. The largest buildup of phosphorus in the Bay occurs
during the spring season, when sediments are stirred by spring storms and high
flows wash large quantities of phosphorus into the Bay.
13. Nitrogen forms fluctuated widely over the year. Several fold changes in
nitrate concentration were particularly evident. Nitrate appears to build up
in the bottom waters of the deep areas over the course of the summer. The most
significant source of this nitrogen is probably from sinking algae cells.
14. Dissolved oxygen concentrations in the Lower Bay recover rapidly from the
low levels of the Fox River during the summer months. Except for a small area
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in the immediate vicinity of the Fox River mouth, the dissolved oxygen level was
not a problem. Some readings taken near the bottom also had depressed DO's
probably as a result of decaying algae cells. The extent of this area was limited.
15. The fluctuations in algae species in the lower third of Green Bay are
dramatic. Blooms in blue-green algae (Aphanizamenon) predominated in July.
June and August saw most of the Bay dominated by Oscillatoria. Aphanizamenon are
capable of fixing nitrogen and, therefore, are more competitive when inorganic
nitrogen falls to a low level. The extent of the Aphanizamenon bloom is
probably controlled by the available phosphorus concentration. Large quantities
of nitrogen are added to the Bay by nitrogen fixing algae.
16. The concentration of chlorophyll-a generally increased during the summer;
however, a larger fraction was in phaeo-pigments (inactive or dead chlorophyll-a)
in late summer.
17. Benthic oxygen uptake in Green Bay above Long Tail Point and Sable Point
will not change significantly as a result of "Best Practicable Treatment". In
the Inner Bay (near the Fox River mouth), improved treatment at several paper
mills and at the Green Bay sewage treatment plant should have a dramatic effect
on the condition of the Inner Bay in the next few years, particularly in regard
to sludge deposits and benthic fauna.
18. A follow-up study should be carried out in 1978 to 1980. The present permits
for "Best Practicable Treatment" will be met by that time. Emphasis should be
placed on winter dissolved oxygen in the Bay and summer conditions in the river.
Measurements of benthic demands should also be carried out to determine the effect
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of reduced loading on existing sludge deposits. Sufficient information should
be available by then from monthly monitoring data in Neenah-Menasha and Green Bay
to assess the value of increasing nutrient control along the Lower Fox River.
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SECTION VII
BIBLIOGRAPHY
Crevensten, Dan, Stoddard, A., Vajda, G.
1973. Water Quality Model of the Lower Fox River, Wisconsin. United States
Environmental Protection Agency Enforcement Division.
Ditoro, D. M.
1969. "Predicting the Dissolved Oxygen Production of Planktonic Algae."
Notes for Manhattan College Summer Institute in Water Pollution Control,
Manhattan College, Bronx, New York.
Epstein, E. F., Bryans, M. A., Mezei, D. and Patterson, D. J.
1974. Lower Green Bay: An Evaluation of Existing and Historical Conditions.
Wisconsin Department of Natural Resources. U.S. Environmental
Protection Agency. EPA-905/9-74-006. August 1974.
Holland, R. E.
1968. "Correlation of Melosira Species with Trophic Conditions in Lake
Michigan." Limnol. & Oceanog. 13:555-557.
Hutchinson, G. E.
1957. A Treatise on Limnology. John Wiley and Sons, Inc., New York.
Lee, A. Genet, Smith, Donald J. and Sonnen, Michael B.
1974. "Computer Documentation for the Dynamic Estuary Model." Water
Resources Engineers, Inc., Contract No. 68-01-1800.
McKeown, J. J., Benedict, A. H. and Lake, G. M.
1968. Studies on the Behavior of Benthal Deposits of Paper Mill Origin,
National Council Technical Bulletin, No. 219.
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- 178-
Modlin, R. F. and Beeton, A. M.
1970. "Dispersal of Fox River Water in Green Bay, Lake Michigan" Proc.
13th Conf. Great Lakes Res. 1970.468-476.
Norton, W. R., Roesner, L. A., Evenson, D. E. and Monser, J. R.
1974. Computer Program Documentation for the Stream Quality Model Qual-II.
Water Resources Engineering. U.S. Environmental Protection Agency,
Contract No. 68-01-0713.
O'Connor, D. J. , Thomann, R. V. , and DiToro, D. M.
1973. Mathematical Modelling of Natural Systems, Manhattan College,
New York, New York.
O'Connor, D. J., Thomann, R. V., DiToro, D. M.
1973. Dynamic Water Quality Forecasting and Management, U.S. Environmental
Protection Agency. Office of Research and Development.
EPA 660/3-73-009.
Palmer, C. M.
1959. Algae in Water Supplies, U.S. Department of Health, Education and
Welfare, PHS Publ. No. 657.
Patterson, D. J.
1973. Results of a Mathematical Water Quality Model of the Lower Fox River,
Wisconsin. Wisconsin Department of Natural Resources, Water Quality
Evaluation Section.
-------
_ 179-
Prescott, G. W.
1951. Algae of the Western Great Lakes Area, Cranbrook Press, Cranbrook
Inst. of Science.
Quirk, Lawler and Matusky Engineers.
1969. Development of a Computerized Mathematical System Model of the Lower
Fox River From Lake Winnebago to Green Bay. Wisconsin Department of
Natural Resources.
Riley, G. A.
1956. "Oceanography of Long Island Sound 1952-1954. II Physical
Oceanography," Bull. Bingham Oceanog. Coll. 15, 15-46.
Sager, Pauls Wiersma, Jim
1971. University of Wisconsin, Green Bay, Unpublished Data.
Sager, P. E. & Wiersma, J. H.
1972. "Nutrient Discharges to Green Bay, Lake Michigan from the Lower Fox
River." Proc. 15th Conf. Great Lakes Res. 1972, 132-148.
Smith, Gilbert M.
1933. The Fresh-Water Algae of the United States, McGraw-Hill Publ. Co.
Hew York.
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- 180 -
Srinath, E. G., Prakesam, J.B.S. and Loehr, R. C.
1974. A Technique for Estimating Active Nitrifying Mass and Its Application
in Designing Nitrifying Systems. 29th Purdue Industrial Waste
Conference, Purdue University, West Lafayette, Indiana.
Thomann, R. V.
1972. Systems Analysis and Water Quality Management, Environmental Science
Services Division, Environmental Research and Applications, Inc.,
New York.
Tuffey, T. J., Hunter, J. V. and Matulewich, V. A.
1974. Zones of Nitrification. Water Resources Bulletin, American Water
Resources Association, Vol. 10, No. 3, pp. 555-564.
Vanderhoef, L. N., Dana, B., Emerich, D., and Burris, R. H.
1972. Acetylene Reduction in Relation to Levels of Phosphate and Fixed
Nitrogen in Green Bay. New Phytol. 71:1097-1105.
Vanderhoef, L. N., Huang, C. Y., and Musil, R.
1974. Nitrogen Fixation (acetylene reduction) by Phytoplankton in
Green Bay, Lake Michigan, in Relation to Nutrient Concentration.
Limnol and Oceanogr. 19:119-125.
Water Quality Criteria 1972.
1973. A Report of the Committee on Water Quality Criteria, At the Request of
the Environmental Protection Agency.
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-181 -
Weber, C. I.
1971. A Guide to the Common Diatoms at Water Pollution Surveillance System
Stations, U.S. Environmental Protection Agency, Natl. Environ. Res. Ctr.
Wisconsin Department of Natural Resources.
1974. Report on the Waste Load Assimilation Capacity of the Oconto River
Near Oconto Falls, Wisconsin. Water Quality Evaluation Section.
Wisconsin Department of Natural Resources.
1973. State of Wisconsin Surface Water Quality Monitoring Data 1969-1972.
Wisconsin Department of Natural Resources.
1972. Summary Report on the Water Quality and Wastewater Discharges During
the Summer of 1972. Water Quality Evaluation Section.
Zanoni, A. E.
1969. Secondary Effluent Deoxygenation at Different Temperatures. Journal
of the Water Pollution Control Federation, 41:640-659.
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- 183 -
SECTION VIII
APPENDIX A
Planktonic Algae Survey on Green Bay, 1974
The plankton suspended in water were collected in February, May and June, 1974,
in a 2 liter Kenanerer at a depth of 1 to 2 meters, preserved with Merthiolate
and concentrated by filtration. Samples taken in July, August and September
were collected in a Clark-Bumpus plankton sampler, preserved with Formalin
and concentrated by sedimentation. All samples were counted by a modified
drop-count method. Biomass estimates and total volatile solids were also
determined.
The water samples for planktonic algae examination were concentrated to 100 ml.
Each sample was stirred and mixed thoroughly; a calibrated pipette was used to
draw-off and discharge 0.05 ml of sample onto a microscope slide on which a 22 mm
square chamber had been constructed and which gave an even distribution of the
sample when covered with a 22 mm coverslip. Each sample was examined under 430X
magnification to identify the organisms present and then counts were made at
100X magnification. Twenty-five ocular fields were examined in cases of sparse
occurrences and 10 Whipple fields were examined when algae concentrations were
greater. A constant pattern of examination was used throughout the study.
Cells touching the top and right side of the Whipple grid were counted while those
touching the bottom and left side were not. Likewise when the full ocular field
was counted those cells which extended from the right side of the field were
counted, while those which extended beyond the left side were excluded.
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Algae were counted as frustules, single cells, filaments or colonies (See Table
III-2, Genera of Algae Observed). In some cases the species observed were not
tabulated because they did not occur within the Whipple grid, but were recorded
as having been observed. Filaments were counted as one regardless of their
length and colonies were counted as one regardless of the size of the colony.
In some cases a colony was considered to have a given size (See Table III-2). In
the case of Microcystis and Gomphospheria, an average size was determined for
counting purposes. Therefore, these criteria may have caused a lower count than
would otherwise have been obtained if definite colony and filament sizes had
been previously determined for all species.
For convenience, Euglena, colonial and single cells of green algae which seldom
occurred, and those called Chlorococcales were collectively tabulated as green
algae, while filamentous green algae were collectively tabulated as Ulotrichales.
The techniques used for identification are described in Prescott (1951), Palmer
(1959), Smith (1933), and Weber (1971).
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SECTION VIII
APPENDIX B
Description of Methods for Chemical Analysis of Water Samples
Ortho-Phosphorus
Water samples were filtered within 12 hours through 0.45u Millipore filters.
The filtrate was analyzed by Technicon Procedure 155-71W using an Autoanalyzer
II System. Results were reported as mg/1 phosphorus.
Total-Phosphorus
Unfiltered samples were digested using the persulfate digestion procedure described
in standard methods (Autoclaved for 30 minutes at 121°C). The digested samples
were then carried through the ortho-phosphorous procedure described above. Results
were reported as mg/1 total phosphorous.
Suspended Solids
A measured volume of sample was filtered through preweighed 0.45u Millipore Filters.
The filter and the collected material were dried overnight at 90°C and then
reweighed. The quantity of suspended matter in a one liter of water was
calculated from the increase in weight and volume of the sample filtered.
Results were reported as mg/1 suspended solids.
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Biochemical Oxygen Demand
The BOD, a measure of the amount of dissolved oxygen utilized by micro-organisms
to stablize the organic material in a water, is made under controlled conditions
usually over a 5-day period at 20°C with nutrients and without light. The sample
dilution factor multiplied by the decrease in dissolved oxygen is reported as
the water's BOD.
Chlorides
Determined by titration with silver nitrate solution to the chromate endpoint
(Mohr Method).
Organic Nitrogen (Kjeldahl)
Unfiltered samples (30 ml) were digested according to standard methods using
300 ml flasks. The digest was made alkaline and the ammonia immediately distilled
off and collected in Boric Acid solution containing a mixed indicator. The
distillate were back titrated with standardized sulfuric acid. Organic-nitrogen
values reported were obtained by subtracting ammonia nitrogen values (see below)
from the total ammonia nitrogen In the distillate. Results were reported as
mg/1 organic nitrogen.
Ammonia Nitrogen
Samples were filtered through 0.45u Milliport Filters. The filtrate was analyzed
for ammonia content by Technicon Auto Analyzer procedure 98-70W. Results were
reported as mg/1 ammonia-nitrogen.
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Nitrate and Nitrite Nitrogen
Samples were filtered through 0.45u Milliport Filters. The filtrate was analyzed
for nitrate or nitrite by using Technicon Auto Analyzer II procedure 100-70W.
Results were reported as mg/1 nitrate or nitrite nitrogen.
Chlorophyll-a plus Pigments
An unfiltered sample (400 ml) was filtered and concentrated using 10 u bolting
cloth. The collected algae were then further concentrated by collecting on 0.45
u Millipore Filters. The filter and the algae were then homogenized in 25 ml
of 90% acetone-10% water solution by grinding the mixture with an air driven
mortar and pestle. The solution was centrifuged and the absorbance of the resulting
solution was measured at 750 nm and 665 nm. After these measurements the samples
were acidified with 0.02 ml of concentrated HC1 and the absorbances again measured
at 750 nm and 665 nm. All absorbances measurements at 750 nm were subtracted
from 665 nm reading to correct for turbidity remaining in the sampler. Results
*} ^
were calculated and reported as mg/1 mj chlorophyll-a and mg/1 m pheophytin
(physiologically inactive pigments). Calculations were made using the equations
on p. 749 of standard methods except that the volume of original filtrate is
substituted for A in the given equations.
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Summary of Analytical Methods Used
for DNR Water Samples
Parameter
Method
Reference Number
Ortho-phosphorus
Total-phosphorus
Suspended Solids
Organic Nitrogen
Nitrate Nitrogen
Nitrite Nitrogen
Ammonia Nitrogen
Chlorophyll-a
Auto Analyzer AAII 155-71W
Persulfate Digestion-followed by
Ortho-P procedure
Gravimetric
Semimicro Kjeldahl
Auto Analyzer AAII 100-70W
Auto Analyzer AAII 100-70W
Auto Analyzer AAII 98-70W
Chlorophyll-a in the presence of
Pheophytin-a
2, 1 P. 526
2
2
1
1
1
2 P. 748
References:
(1) Technical Publication No. TJ1-0268 - Technicon Auto Analyzer II Systems -
Technicon Industrial Systems - Technicon Instruments Corporation - Tarrytown,
New York.
(2) "Standard Methods for the Examination of Water and Waste Water" 13th Edition,
1971. APHA-AWWA-WPCF.
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- 189 -
APPENDIX C
Benthic Oxygen Demand
Considerable effort has been applied recently to try to understand the kinetics
of oxygen consumption and BOD decay. However, it is usually impossible to account
for the observed deficit by BOD decay alone. Classical BOD sag equation (Streeter-
Phelps type) usually do not generate sufficient oxygen deficit. This is particularly
true for paper mill wastes when the observed 6005 loading is input to the equations
with the observed decay rate. Most researchers have attempted to explain this
discrepancy by pointing to sludge banks and attributing the missing oxygen to
benthic consumption. There is no doubt that paper mill sludge deposits can exert
a considerable oxygen demand on a river. However, it is extremely difficult
to estimate the exact extent of the benthic demand. Several laboratory and field
measuring techniques have been cited in the literature. All of these methods
are time consuming, costly and the results are subject to considerable error.
For paper mill deposits, oxygen demand from sludges has been estimated to lie
between 2.0 and 10.0 grams of 02 per square meter per day. (Thomann 1972).
Measurements taken in the Lower Fox River indicate values in and around this
range. Table C-l lists the benthic demand values at several locations measured
during the fall of 1972 on the Lower Fox River. These values represent laboratory
measurements on samples that were extracted from the river with a Peterson dredge.
The samples were placed in 2.5 liter bottles with a closed circuit water circulation
system attached. The flowing water moved past a DO probe which was attached
to a strip chart recorder. The entire apparatus was incubated at 20°C. The
samples were allowed to stablize for at least 2 days before a reading was started.
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TABLE C-I
Benthic Oxygen Demand in the Lower Fox River
Location
Neenah-Menasha Area
Below Appleton Dam
Above Kaukauna
Below Kaukauna
Near Wrightstown
Above De Pere Dam
At the Fox River Mouth
Sample
No.
lOa
lOb
lOc
8a
8b
8c
la
Ib
Ic
2a
2b
2c
3a
3b
4a
4b
4c
5a
6a
Benthic Demand
GR-0?/M2/DAY
7.75
11.28
9.59
5.66
5.38
4.21
4.78
3.99
1.98
7.33
9.02
8.78
4.09
6.17
3.96
3.25
2.33
4.68
1.86
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- 191 -
A second set of benthic samples was -taken in September, 1974, These samples
were obtained from 7 locations in the Lower Bay. The procedure discussed above
was used to evaluate the benthic demand at these locations. The results are
shown in Figure C-l. The values shown are considerably below the rates measured
in the Lower Fox River in 1972. The consistency of the muds varied widely at
the shown locations. Below Grassy Island the samples consisted of non-cohesive
fluid-like silt. The sample off Red Banks had the characteristics of highly
cohesive clay. Above Long Tail Point the sample contained a high amount of fine
sand. The sample off the end of Long Tail Point contained mostly large-grained
sand.
In addition to these laboratory measurements, two attempts were made to measure
the benthic oxygen demand in situ. A large rectangular metal box was constructed
for this purpose. The box was 2' x 2' x 1'. A flange was attached around the
bottom to support the box and prevent it from sinking too deeply into the sediments.
A Yellow Springs DO probe with a mixing device was sealed in the box. Figure
C-2 is a diagram of the apparatus. A float was anchored above the location of
the box and the instrumentation was attached to the float. The instruments
consisted of the DO probe, strip chart recorder and battery for the mixing
device. The box was lowered from the surface (no diver was used) and left in
place about 12 hours. The results at the two locations are shown in Figure C-l.
Both values are several times higher than the laboratory measurements. Since
the test was only run for 12 hours, the unusually high values may be the
result of suspended sediments trapped in the box when it was put in place.
From these results it appears that it would be desirable to allow a day or
two for this condition to clear itself before taking a measurement. In order
to do this, a method would have to be devised to change the water or raise the
DO before beginning the measurement run.
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FIGURE C-l
Benthic Oxygen Demand in Lower Green Bay
in GR 02/m2/Day
I I Values measured with
box device.
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- 193 -
FIGURE C-2
BENTHIC OXYGEN DEMAND MEASURING DEVICE
TO SURFACE
FLOAT
PLEXIGLASS
WINDOW
CORDS FOR
DO PROBE
AND MIXER
CABLE ATTACHMENT
POINTS
METAL IS 1/8" THICK
AREA = 3639.11 cm2
VOLUME ABOVE FLANGE = 109.76 LITERS
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- 195 -
APPENDIX D
GBQUAL Program Documentation
Program History
GBQUAL as used in the Green Bay study consists of six FORTRAN computer routines.
These six routines are derived from the "Dynamic Estuary Model" documented by
Lee et al., Water Resources Engineers (WRE) in May 1974 under contract no.
68-01-1800. The model, as described in WRE's report, has been significantly
altered to fit the Green Bay situation. Since the program changes have been so
extensive, a relatively intense program description is necessary to benefit future
users. This descriptipn is not intended to fully replace the documentation
prepared by WRE. Future users of this model are encouraged to obtain a copy of
WRE's documentation if they plan to do extensive work with the model and especially
if they will require program modifications. The enclosed descriptions, however,
should be complete enough to: (1) allow a user to prepare a data deck and run
the model; (2) understand the basic flow of information and know where various
calculations are made; (3) acquaint the user with the capabilities and the
limitations of GBQUAL. With this in mind, the following sections will present
a general description of the quality model plus a detailed description of each
subroutine. In addition, a separate section describes the data input setup
required to run GBQUAL. The last section describes the theoretical
considerations used in formulating the reactions allowed by GBQUAL. This
section includes a table of estimated parameter ranges for the various
coefficients used in the model.
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General Description of the Green Bay Model
The water quality model attempts to simulate the significant physical, chemical
and biological reactions that take place in Green Bay. The quality model was
constructed to route the following constituents through the Bay:
1. Coliform
2. Carbonaceous biochemical oxygen demand
3. Dissolved oxygen
4. Organic nitrogen (not in phytoplankton)
5. Ammonia nitrogen
6. Nitrite nitrogen
7. Nitrate nitrogen
8. Soluable phosphate phosphorus
9. Total nitrogen as a conservative (or any conservative)
10. Phytoplankton 1 biomass
11. Phytoplankton 2 biomass
12. Temperature
A network of interconnecting channels (links) and junctions (nodes) is used to
describe the physical system. The junctions each describe an element of water
(of varying size and shape) which is assumed to be well mixed. All reactions
take place inside the junctions. The size and shape of the junctions are chosen
to coincide with the geometry of the system being represented. Secondly, the
size (volume) of the junctions must be chosen so that a reasonable time step
may be used in the model consistent with channel lengths and velocities.
-------
-197 -
The numerical model performs a mass balance on each constituent plus and minus
any sources or sinks of that constituent for each junction or water volume in
the Bay. A total of 87 nodes are used to describe the system. This is shown
in Figure D-l. Each element or node is described by its surface area, average
depth and total volume. Each node is also connected to the surrounding nodes
by a series of channels. The channels are described by average depth, flow length
and surface area. In addition to the physical data used to describe each node
and channel, the program requires a list of all channels entering each node (a
maximum of 8) and the nodes connected by each channel (maximum of 2). The flow
of water in each channel therefore describes the advection of water for a given
simulation run. Water is also allowed to diffuse between nodes by means of an
eddy diffusion coefficient that is variable by channel.
Figure D-2 illustrates the possible chemical and biological reactions that the
model considers. (Temperature and coliforms are not shown). These reactions
are carried out in each node at each time step. The numerical model assumes
that an element is continuously mixed and all reactions take place within the
element after advection, diffusion, inflows and outflows have been accounted
for. Figure D-3 illustrates the principle of a continuously mixed element.
Program DYNQUA is the master control program and it also contains the main water
quality routing loop. As the program executes, control is passed from DYNQUA
to INDATA through which all necessary data required for a given simulation is
pulled into the program and printed for display. INDATA calls two separate
subroutines (COEFF and METDAT) which are designed to read in separate blocks of
data. After all necessary data has been read, control passes back to DYNQUA
where various system parameters are initialized. The main quality loop is then
entered and the program cycles for the designated number of iterations.
-------
FIGURE D-l
N
., 21 "
J
Shown here is the system of elements and channels
used to describe the Green Bay system in GBQUAL.
vo
00
-------
- 199-
A - Aeration-Deaeration
BO - Oxidation
D - Decay
0 - Oxygenation During
Algae Growth
UR - Uptake From Respiration
UD - Uptake From Decay
G - Uptake From Growth
R - Resolubilized During
Respiration
RD - Resolubilized During Decay
S - Settling
P - Precipitation
FIGURE D-2
Chemical and Biological Paths Allowed in GBQUAL
-------
- 200 -
FIGURE D-3
c,
c.
A. a continuously stirred tank reactor, CSTR
Qou QIN
VOLUME
TDS
BOD
DO
TEMP
•
•
ALGAE
ZOO
FISH
B. an idealized hydraulic element
A CONTINUOUSLY STIRRED TANK REACTOR (CSTR)
AND AN IDEALIZED HYDRAULIC ELEMENT
(After Water Resources Engineers, Inc.)
-------
- 201 -
If temperature is being simulated, each quality cycle (time step) will include
a call to TEMPER (an entry point in METDAT) where the heat budget is calculated
and new temperatures are determined. After the proper number of cycles have
been completed, a full or partial print out of the current system status is made.
If desired the system constituent status is stored for later use in subroutine
QUALEX. After the requested number of cycles, a second report is generated by
QUALEX giving the minimum, maximum and average concentration of each constituent
during the number of cycles requested. After all cycles have been completed,
DYNQUA can transfer the current system status to a storage tape or file so that
the system can be restarted with the same conditions that it ended with during
the last simulation run. Thus the final conditions become the new initial
conditions. In this manner, it is possible to route the model through any
simulation period (say a year) in a piece-wise fashion without having to
reinitialize for each run. Figure D-A illustrates the informational flow in
the program as described above.
GBOUAL has certain limits that are necessitated by the size and speed of present
day computers. Table D-l lists the present dimensional limits of the model along
with constituents allowed. If a user wishes to extend these limits, the common
blocks in the program will have to be extended. Of course, there is a trade
off in the resolution of the physical system and the length of any computational
time step. Care must be taken to avoid advecting a significant fraction of any
elements volume during a single time step since this may lead to instabilities
in the solution. The hydrodynamics for a given simulation run must be steady
state over the simulation period. The program can be restarted, however, with
a new hydrodynamic solution at any user defined interval if varying flow conditions
are desired. With the present set-up for Green Bay, time steps of 3 to 6 hours
-------
0*
I
- 202 -
FIGURE D-U
FUNCTIONAL DATA FLOW IN PROGRAM GBQUAL
HYDRODYNAMIC
DATA FILE
INDATA
METDAT
COEFF
RESTART FILE
TEMPER
PRINTOUT ROUTINE
QUALEX
SUMMARY REPORT
STOP
NEW RESTART
FILE
-------
- 203 -
TABLE D-l
GBQUAL Limitations and Routable Constituents
Quality Program:
Item Maximum Number
Junctions 200
Channels 400
Channels Per Junction 8
Water Quality Constituents 14
Wastewater Return Units 20
Quality Multiplication Factors 10
Junctions for Printout 200
Weather Data Points (per day) 25
Constituents that can be modelled are:
Constituent Constituent
1 Temperature, °C
2 Dissolved Oxygen, mg/1
3,4,5 Biochemical Oxygen Demand, mg/1
6 Organic Nitrogen, mg/1
7 Ammonia Nitrogen, mg/1
8 Nitrite Nitrogen, mg/1
9 Nitrate Nitrogen, mg/1
10 Phosphate phosphorus, mg/1
11 Chlorophyll-a(l) ug/1
12 Chlorophyll-a(2) ug/1
13 Coliforms, MPN/100 ml
14 Total Nitrogen, mg/1
-------
- 204 -
seem reasonable. The computer code which was run on an Univac 1110 computer requires
approximately 60K words of core for an execution. With a 6 hour time step, a
run simulating all parameters for 75 days of actual time requires about 2 1/4
minutes of computer time. Therefore GBQUAL can simulate an extended real-time
in a very acceptable amount of computational time.
It should be noted that GBQUAL solves for the concentration of each constituent
in a step wise fashion through time. Thus the concentration in any element at
time t is a function of the concentration at (t - At) and all reactions during
At. This is illustrated in Figure D-5. The solution is therefore an explicit
algorithm.
-------
FIGURE D-5
Solution of the Green Bay Model Differential Equations in T and J Space
o
Ln
(information from up to 8 other
(junctions for each computation.
J-i
Junction Number
J
-------
- 206-
Theoretical Considerations of the Water Quality Model
Conservation of mass must be applied at all node points in the numeric scheme.
To account for this conservation, whether it be the water itself or a particular
constituent, we must look at all inflows and outflows. These consist of advection,
diffusion, any external inflow (such as a waste source) or any external withdrawal
(such as a water supply system) . If we apply these conditions to a given element
j we find:
Inflow Outflow
where: V. = volume of j at the end of a time step
V = volume of j at the beginning of a time step
°J
C . = concentration of C at the end of a time step
C = initial concentration
n = number of channels into j
A = area of channel i
xi
U. = velocity in channel i
C* = 1/4 point concentration of C in channel i
At = time step
K = diffusion coefficient
df
Ac = concentration gradient
xi
X = channel length
i
n = inflow
in
0 = outflow
^ oi
C = concentration of C in the inflow
in
-------
- 207 -
nin = number of inflows
noi = number of outflows
This balance accounts for the physical transport of any constituient between
nodes. The mass balance equation is the most important equation in the system.
Equation D-l requires that a balance between all inflows and outflows must occur
at all nodes. If this condition were not true, the model would be "creating or
losing mass" which is not physically possible. Thus care must be taken that
this condition be met at all points in the system.
In addition to this balance, the internal chemical and biological reactions must
be considered. Exchanges between the sediment and water interface or the air
water interfaces must also be accounted for. Figure D-2 illustrates the basic
paths that the various constituents simulated may follow. This conceptualization
is obviously a simplification of a real system and yet it allows one to mathematically
describe the major reactions that affect the system. As our understanding of
the phenomena involved increases we will undoubtably refine our conceptual diagrams
and also the mathematical descriptions of them.
The next sections will describe the mathematical formulas used in the Green Bay
Water Quality Model. Most of these reactions have been seen before, however,
some new considerations have been included and will be elaborated on. A summary
of all differential equations solved in GBQUAL is shown in Table D-2.
-------
TABLE D-2
Summary of Differential Equations Solved by the GBQUAL Model
Description
QUALITY PROGRAM:
E"uat1on
Advectlon Diffusion Inflow
Chemical or
Respiration Biological Heat Exchange
Outflow Decay Sedimentation Or Release Transformation Uptake or Reaeration
c)f IT ' , (AxuC)i + , (AxKdf }i + ((!inCin>J ' , "W'j « ' c^nnels; J - inflows or outflows per junction)
Temperature (T):
CoUfbn, Bacteria (F): |VF
A™>nia Nitrogen (H,): l
VH0(1 - »5) - VA
Kl
O
00
Nitrite Nitrogen (NZ): !^ .[^ (A^). + j^ (A^^). + ^ (Q.^).
VN^l - „,)
Nitrate Nitrogen (N3): .
Phosphate Phosphorus (P):
|f- =[ £ (A^P), +j
^), +.£ (Q1r,P)j -.£ (QouP)j]
(1 - S2)
-VAa(p -
Algae (A):
A_ . (AuA}. + .
.^ (Q1nA)j - . (QOUA).
VA(P-P-OI)
Organic Nitrogen:
3VN0 „ I
SN J J
dsr'i+* («inN0)j - '
J I J — I
-------
TABLE D-2 (continued)
Description
Equation
Advection Diffusion Inflow
Outflow
Respiration
Decay Sedimentation Or Release Transformation
Chemical or
Biological Heat Exchange
Uptake or Reaeration
Dissolved Oxygen (0): 8VO
(Q1nO).
-VB(1-B4) -
Carbonaceous BOD (B): 3VB
Rate coefficient time and
temperature changes:
""k
2 3 4 5 • R(T-20) e"3.*.6.M.
,^,J.4.b RN N EjD)Fe
"l
"
(1 - e
o
>£>
-------
- 210 -
Phytoplankton
GBQUAL has the capability of routing two seperate algae populations. The growth
of both groups of algae are considered to follow Monod kinetics. The limiting
factors considered are phosphate concentration, inorganic nitrogen concentration,
light availability and temperature. The mathematical formula is given by:
U =
,T-20
MAX
PO.-P
4
NH3-N
(2)
where: K
MAX
PO.-P ,
4 /
NO -N >
SP
3
"SN
r
maximum growth at 20° C
temperature correction coefficient
temperature °C
concentrations
half saturation constant for phosphate
half saturation constant for inorganic nitrogen
fraction of the maximum growth rate as a result of light
intensity
All of the above terms have been discussed in past literature except the term r. The
factor r is a function of light penetration, depth of the water, and a normalized
growth function for light intensity. Figure D-6 presents a diagram from the
EPA publication Dynamic Water Quality Forecasting and Management (O'Connor,
Thomann, Ditoro, 1973). This series of graphs illustrates the normalized growth
rate function and its comparison to three sets of observations. To elaborate
on this relationship it is necessary to describe the effects of algal populations
-------
- 211-
and the resultant light penetration. Light penetration is normally described
by an extinction coefficient. Various equations have been developed to account
for changes in the extinction coefficient as a result of changes in the algal
density. One such equation is shown below.
= kQE + .00268 (CHL-a) + .01645 (CHL-a)2/3 (3)
where: v = actual extinction coefficient (I/ft)
k-p = extinction coefficient as a result of things other than
algal
CHL-a= total concentration of Chl-a in ug/1
This formulation contributes a "self-shading" effect to dense algal populations.
A concentration of 100 ug/1 of Chl-a (frequently observed in Lower Green Bay)
will contribute 0.62/ft to the extinction coefficient. Light penetration of
between 5 and 10 feet (Secchi Disk) is a typical value if we exclude the algal
self-shading. With a conversion of 1.9/(Secchi depth) we would have a range of
.38 to .19 fpr Ke. Thus the self-shading effect of algae in Green Bay may be
an important limiting factor in algal growth. The extinction coefficient may
increase by 200 to 300% as a result of a dense algae population.
The light intensity at any depth can then be given in terms of Ke as:
1(2) = I e-(kEZ) W
o
-------
- 212 -
where e = base of natural logs
I = intensity
2 = depth (positive downward)
I = intensity at the surface
Based on the data of Ryther (Figure D-6), Steele has proposed a formulization
for the normalized growth of phytoplankton as a function of light. The equation
developed by Steele relates the normalized growth rate of algae as a function
of light intensity and a saturated light intensity. It is given by:
(5)
where: F - normalized rate of growth
I = local light intensity
I = saturated light intensity
8
To obtain the average normalized growth rate over a volume element during a given
time step, we must integrate this expression over the depth and time step At.
The intensity of light is, of course, a function of depth as given above and
is also a function of the time of day. We can assume that I is constant over
a given time step if we use a sinusoidal light intensity function with time and
evaluate the intensity at half time steps. Then the fractional growth rate r
is given by:
D .f
dtdS
= I f I f Iae
D 1 T \ I
'o Jb
-------
CO
UJ
X
t-
>
CO
o
h-
o
X
0.
Lu
O
UJ
<
o:
Q
LL)
N
_J
- 213 -
FIGURE D-6
(Taken from EPA publication 66013-73-009)
1.0.-
(a) P/Ps 0.5
tb)
1.0,-
0.
1.0
(C) P/ps 0.5
0
10
Chlorophyta
10
Diatoms
10
O
(d) P/PS 0.5
0
Flagellates
10
LIGHT INTENSITY (FOOT CANDLES x I03)
Normalized Rate of Photosynthesis vs. Incident
Light Intensity: (a) Theoretical Curve after
Steele (b,c,d) Data after Ryther
-------
- 214 -
where: D = depth
T = hours in At
f = hours of daylight in At
Ia = average light intensity at the surface over At
We can integrate this fonnulization to obtain:
ef -Al -Ao)
r = TT—^ (e - e ' (7
where:
a
A = I
o s
Now it remains to determine a reasonable range of values for Is. Steele's formula
was based on 2000 footcandles as being the average saturated growth intensity.
However, most measurements of sunlight are given in terms of langleys (g cal/cm^)
which is an energy term. The conversion from footcandles to langley depends
on the frequency of light you are considering. For the visible spectrum it appears
that Is will be in the range of 0.05 to 0.15 langleys per minute. Water Resources
Engineering has suggested a half saturation constant for light as .03 langleys/
minute. If we set F(I) equal to 0.5 and la to 0.03 and solve for Is we obtain
a value of 0.13 langley per minute.
-------
- 215 -
The death of phytoplankton is considered to be dependent on temperature only.
The death rate is given by:
(1 - a'20 At) (8)
where: p = local death rate
P2Q = death rate at 20°C.
Phytoplankton can also leave the water system by settling to the bottom. Normally
a settling rate of between .5 and 2.0 ft/day is appropriate. The mass balance
of algae applied to any element j then looks like:
Growth Death Settling
VA.. = VA + VjAj (Pj - Pj - Oj ) (9)
where: A. = algae biomass after At
VA = mass balance from equation 1
a = settling rate in ft/DAY/DFPTH
Nutrient Cycles
The nutrients considered in GBQUAL consist of 4 forms of nitrogen and soluble
phosphate. Nitrogen is allowed to transform from organic compounds to ammonia
and then to either be utilized by plankton or to nitrify. Nitrate is also utilized
by plankton. In addition, ammonia may be released from decaying organics in the
sediments. To complete the cycle, nitrogen associated with plankton can either
leave the system by settling or resolubilize as free organic compounds. It is
important to realize that the organic nitrogen routed by the model refers only
to the free organic N not bound up in algae.
-------
- 216 -
Phosphate can be released from sediments, precipitate to the sediments, or be
utilized by algae. The cycle is again completed by resolubillzation from respired
algae or settling to the bottom out of the system.
Nitrogen Kinetics
Organic nitrogen is assumed to decompose to ammonia via a first order reaction.
The differential equation for the reaction takes the form:
dN
= a P A - « N dO)
where: NQ = Org. -N concentration
-------
- 217 -
where: N = ammonia nitrogen
Y., = release of NH -N by sediments per surface area per time
A = surface area
s
(3. = rate of nitrification of NH^-N (temperature dependent)
N
1 = fraction of nitrogen used by algae that is NHo-N
N1+N3
Nitrite nitrogen is allowed to decay to nitrate only. The only source (other
than inflows) is the end result of NtU-N decay. The reactions again are first
order:
dN-
• " - « 02)
where: i^ = nitrite nitrogen
3 2 = rate of N02-N to N03~N
Nitrate nitrogen can only be utilized by algae or created by nitrite decay. No
other sources or sinks are accounted for aside from inflow and outflow. The
equation is:
dH / N \
- - °
dt
where: N^ = nitrate nitrogen
N
fraction of algae nitrogen that comes from nitrate
A possible addition to the model at this point would be the inclusion of a
denitrification term that would allow NO.-1J to leave the system (as N£ gas)
under low dissolved oxygen conditions. This would insert an additional nonlinearity.
-------
- 218 -
Phosphate (soluble) is allowed to be both used and released by algae. In addition,
phosphate is precipitated to and released from the sediments. The equation takes
the form:
^ = a3 (p - u ) A - 02 + Y2 (AS) (14)
where: p = phosphate phosphorus
e»3 = fraction of algae biomass that is phosphorous
°2 = rate of phosphorus precipitation to the sediment
Y2 = release rate of phosphorus per area per time
As = area
Coliform Bacteria
Coliforms are assumed to decay by a first order reaction that is temperature
dependent.
= - kcC
dt kcC
where: C = coliform (MPN)
c = decay rate
-------
- 219-
Carbonaceous BOD
The BOD in the system is represented by an equation consisting of 3 parallel
terms. This equation is given by:
- k, ,t - k t - k t
L - Lx (1 - e ) + L2 (1 - e ) + L3 (1 - e ±J ) (16)
where L = BOD mg/1
L , L?, L = ultimate BOD for each term
k k > k = first order decay rate I/day base e
This equation describes a long term BOD curve that consists of three separate
terms that are exerted simultaneously. The total ultimate BOD represented by
equation 16 is the sum of L^, 1,2, and Lj. If L£ and L-j are zero then equation
16 reduces to the classical BOD equation. (See discussion of Long Term BOD in
Section IV-C).
The decay of BOD can be represented by the equation:
f - kliLi (16a)
Each term also contributes its oxygen deficit to the total oxygen balance. Of
course, when using the ultimate BOD, care must be taken to remove the nitrogenous
portion either by inhibiting nitrification during the long term BOD test or
measuring the Kjeldahl nitrogen and subtracting its potential oxygen deficit.
-------
- 220 -
Dissolved Oxygen
The concentration of dissolved oxygen is a function of reaeration pressure, net
algae production of 02 and the oxidation of BOD and inorganic nitrogen forms.
In addition, oxygen is consumed at the sediment interface as a result of decaying
organics. This can be represented by the following equation:
(17)
» „ ,« , 3 ,
IF = k2 (°s ' 0) - \ ^i - Wl - &2a5N2 + (ra6 " °'7) M8 ~Y 3 (As)
where: o = dissolved oxygen
0 = saturation at the given temperature
3
k_ = reaeration rate (temperature dependent)
a, = oxygen required per unit of ammonia oxidized
a = oxygen required per unit of nitrite oxidized
a, = On production per unit of Chl-a
o *
a? = Q£ respiration per unit of Chl-a
r = algal activity factor previously defined
a. = ratio of Chl-a to algal biomass
Y. = 02 uptake from bottom sediments per area per time
A = algal biomass
Equation 17 is straightforward except for the 5th term which determines the algal
contribution. The formulation used here was developed byRyther and Yentsch and
reported by DiToro (1969). The relationship predicted maximum photosynthetic
production as a function of Chl-a concentration.
-------
- 221 -
PMAX = °'25
-------
- 222 -
TABLE D-3
Estimated Parameter Values
Parameter
Decay Rates, Per Day Base E
BOD-1
BOD-2
BOD-3
Org-N
NH0-N
Coliform
Growth Rates
ALGAE-1
ALGAE-2
Respiration Rates
ALGAE-1
ALGAE-2
Half-Saturation Constants
ALGAE-1
(NH -N + NO--N)
PO -P
Light (saturation constant)
ALGAE-2 - Blue Green N Fixers
P04-P
Light (saturation constant)
Stoichemetric Equivalence
NH
NO;?
(algae
O2
CHL-a
CHL-a (algae 2)
Temperature Coefficients 6 = a^
a,
Value Range
0.1 - 0.5
0.01 - 0.1
0.001- 0.5
0.01 - 0.01
0.01 - 0.2
0.2 - 2.0
0.1 - 3.0
0.5 - 3.0
0.5 - 3.0
0.01 - 0.1
0.05 - 0.5
0.02 - 0.4
0.005- 0.05
5.0 -10.0
0.0001 (a small
a zerp
0.005- 0.05
5.0 -10.0
3.5
1.2
.25
.25
Units Reliability
Day"1
Dayli
Day"
Day".
Day"
-1
Day"
Day"1
Day
mg/1
mg/1
langley/hr
Good
Good
Good
Fair
Good
Good
Fair
Fair
Fair
Fair
Fair
Good
Fair
Fair
value is required to avoid
divide)
mg/1 Fair
langley/hr Fair
mg/mg
mg/mg
ug/mg
ug/mg
Very Good
Very Good
Fair
Fair
Reliability
BOD-1
BOD-2
BOD-3
Org-N
NH--N
NO:-N
Coliforms
ALGAE-1 Growth
ALGAE-2 Growth
Sediment Oxygen
Miscellaneous
1.140098
1.140098
1.140098
1.047
1.2134705
1.2134705
1.047
1.047
1.047
1.100
Ratio CHL-A 1/ALGAE-l Biomass
Ratio CHL-A 2 /ALGAE-2 Biomass
-0.003856
-0.003856
-0.003856
0.0
-0.0107843
-0.0107843
0.0
0.0
0.0
-0.00175
0.025-0.10 mg/mg
0.025-0.10 mg/mg
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
0.0
Good
Good
Good
Fair
Fair
Fair
Fair
Fair
Fair
Fair
Fair
-------
- 223 -
Program Documentation
This section presents the logical flow chart for the main program and each subroutine
in GBOUAL. This is followed by a complete listing of each subroutine.
Main Program DYNQUA
This routine is the master control routine for GBQUAL and contains all the necessary
equations to route all constituents except temperature. This routine calls in
all data, cycles through the main quality loop and creates a printed report at
desired intervals. The flow chart is illustrated in Figure D-7 and is followed
by the listing. The system is controlled by a set of flags called ISWTCH(I).
These values are read in INDATA and determine if a given constituent is to be
calculated. Table D-4 lists the ISWTCH control values. In addition to the ISWTCH
array there are several other internal flags that determine printing times and
summary intervals.
Table D-4
ISWTCH(I) flags. Set ISWTCH(I) equal to 1 to simulate a constituent group and set
to 0 to skip.
I Constituents
1 Coliforms
2
Org-N, NH -N, N02~N, NO -N,
PO.-P, CHL-a-1
"4
3 CHL-a-2
4 Total Nitrogen (or any conservative)
5 BOD and DO
6 Temperature
-------
START
- 224 -
FIGURE D-7
FLOW CHART FOR DYNQUA
CALL
BLOCK
DATA
CALL
INDATA
INITIALIZE
SYSTEM
v* ~"
ENTER
QUALITY
LOOP
SET TEMPERATURE
ADJUSTED
COEFFICIENTS
CALL
TEMPER
CALCULATE
COLIFORM
CONCENTRATION
-------
- 225 -
FIGURE D-7
DYNQUA FLOW CHART (CONTINUED)
CALCULATE SOLAR
INTENSITY, ALGAE-1,
ORG-N, NH3-N,
N02-N, N03-N, POlj-P
(Total nitrogen or any con-
servative is calculated automatically)
UPDATE
CONCENTRATION
ARRAYS
PREVENT
NEGATIVE
CONCENTRATION
-------
- 226 -
FIGURE D-7
(Continued)
PRINT
DEPLETION
CORRECTION
MESSAGES
CHECK
CONCENTRATIONS
AGAINST SPECIFIED
LIMITS
STOP
STORE INFORMATION
FOR LATER
AVERAGING
STORE.
CONCENTRATIONS
FOR RESTARTING
-------
- 227 -
FIGURE D-7
(Continued)
PRINT
CONCENTRATIONS
STOP
-------
- 228 -
1
2
3
4
b
6
7
B
10
1 1
12
13
14
1 b
16
17
10
10
T
20
21
22
23
24
2b
26
27
2b
29
3U
31
32
33
34
35
36
37
3B
3V
4b
41
•M
43
44
45
46
47
4t>
4V
bU
bl
b" 2
C
C
c
c
c
c
L
c
c
c
c
c
c
c
c
c
c
c
c
c
c
c
c
c
c
c
PhOuRAM DYmvUA
ENVIRONMENTAL PROTECTION AGENCY
DYNAMIC tSTUARY Ai-,U TIDAL TEMPERATURE MODEL
(VRE lb CONSTITUENT ECOLOGIC VERSION
THE PROGRAM LOGIC IN THIS DECK *AS ORIGINALLY DEVELOPED FOR THE
NETi.uRKS REPRESENTING THE SAN FRANCISCO BAY-DELTA AND THE
SAN UIEGO bAY SYSTEMS. ITS PwESENT FORM. A MOD 1 1" I C A T I ON OEvELOpEu
FOR PEArtL HAKflURi INCLUDES CAPABILITY Tu SIMULATE 1H CONSTITUENTS
AND THEIR INTtRACT IU.,5 IN A VERTICALLY MIXED CLOSED BAY OR
ESTUARY. THE DUALITY CONDITIONS AT TH& SE*ARu BOUNDARY MOST
oE SPECIFIED. APPLICATION TO OTHER SY^TEl-lS MAY REQUIRE
SuhE PROGRAM MODIFICATIONS.
CUrthOI\/ijEOM/YNE., (2DU) iVuLwlN(20U) iVOL(2UO) >A50R(2(jOI i g I H ( 2UU ) »
1 NCHANl2uOi8),UlFFK.(400)»V(4UO)>!«(40L))>AREA(400)»
2 d(4UU)iCLEN(4UU),R(4UO)iCN(4U(J),NJUNC(HUUi2)
3 »6|NET(2UU),Y(20U),WOUT(2UO)iVOLyOU(20a)
4, YBAK ( 20U) iJbW » JS |NC iNJ
CO|V|HUN/MISC/ALPHA(8U) ,CuIFFK,ClNt 14>1 ) iCLlMlTl 14> iCONST(20f 1MI
A. CTEMp(14)»UELl.DTb,EB6CONl4B,l4)«EXR.FACTR(l'»NJSTRT(lHilO> .NODYNiNOPKT
Ei NwCYCiN«PRT,NKSTRfiNSPEC>NSTOP,NTAG>NUMCON,NUNITS»NIOiN20
F> uJQiNtO»KETFAC(20fl'<)tNEX»i&lhTCH(iu)iNAHE(20>iiNAnL(SilH)
la i DELT^.KDONE .MARK1 ,MARK2
COi1hoN/lHFL/TEMPIM2UO)iOXYINt2UO),BODlN(200»3)iCORGIN(200)i
S CNH31t4<20P04iN(200)»
£ ALGlNlt2QU)iALGlN2(200)>COLlN(2uO)>T,MlN(200)i
$ CHAIIiM(2QCl)»CHA2iN(2UO)
COiinuN/tONC/TtnPJ2UO) .0AY(20u) iBOU(2ou»3) >COR&(2uO) fCNHJ(200) i
4 CN02(20U),CH03(2QO)tP04(2lJO)|ALGl(2Uu)»AL(i2(2UO)>
i COL(20U)tTN|2DU)tCHLAl(2QU>tCHLA2(2Uij)
COiil«iuN/l')ASS/TEp|pMt2UO) ioXYM(20U) ,BOUM(200«3) .CORGM2QO) iCNH3M(2UU)
S iCNU2M(200),CN03i1l20U).P04Ml200)iALGlh(2UO)i
i ALG2M(20U)n:oLM(200)iTNM(20a)iCHLAl«l20u)t
4 CHLA2M(2UU)
i) iCNH3PK(20U) .
b4 5 CORGDK(2UD),EXPB02(20U)tAGSNKl(200),AGSNK2(20Q)»
b5 S> CN02DM200) ,POSINKt20U) »0*YBEN(20Q) iCNHBEN<2UO) i
b6 4 StChI (2uU ) ,pMAA I I 2UO ) >PMAX2(2UU) tAGChAlI2UU) •
-------
- 229 -
b7 5 AGCMA2«2UU> .PUHtoEN^UO) »PKES1 «2UO) iPnES2(2UU) •
bfci S bFb 101 I 3 ) (DFCOLl 200) «uFNH3( 200) •
S9 » Df- NU2(2uO ) iuFU^IM(2uU) tDFBI02 (2UU) > EXPbEii I 2 00 ) .
60 4 tXPBOl ( 20U ) , tXPfaOO ( 2uO , 3 ) .LXPCOL ( 200 ) iEXPNH3 ( 2UO I .
61 * EXPNU2 ( 200) ,EXPOK(j(2UO) • C NBEN I 200 ) iCbAT (200) »
62 $ OX6EN(200) ,OXUELT(20U» iPOBEN»2QO) .CFBOO.ALG1P.
71 CUHi10W/«TMS/wC(2UU>»TAA(2&ilUl
73 bi TAilA(25ilU)>APA(2b>10)iCL.OUU(2b>lU)tlt.QTErtlv)iVZONE(10»2>
74 Ci (,KNtT(20u)iAX(S)ibX(M)iALPH(6)iBETAla)»Pltii. bOiQTOK
7& C
76 C
77 COMMUN/lCrlECK,/Jl
-------
- 230 -
i 1 1
115
116
117
118
11?
12U
121
122
123
121
12S
126
127
12&
129
130
131
132
133
13H
13b
136
137
13b
139
ISO
1 HI
112
1H3
1HH
115
116
117
118
119
150
Ibl
152
153
Ibl
Ibb
156
157
158
1S9
160
161
162
163
161
165
166
167
168
169
170
3b; KEEP=NJUNC(N, 1 )
NJUNC(Nil)=NjUNC(N»i!)
NJUNC(N>2)=KEEP
«
IF( ISATCHC61 .EU.O) GO To 353
DU 3b5 J=JStNJ
c
c
£
c
c
c
c
c
353
353
776
;so
• • t • *
CT( J)«TEMP(
CONT 1NOE
CALCOLA TE
00 760 J«l i
VOL< J) =ASUR
CO NT I Nut
CALCULATE
J)
JUNC T I ON
Nj
( J)*Y ( J)
INITIAL
ViJLiiMtS AT RFCiINrJlhir OP" QIMIM A T I n M P P tf I fi n
» u *- U I™ ^ ^ " ' D (- vj i "» is t IM (3 u r 3inUL"*^vfii • t f> 1 u u
MASS IN JUNCTIONS
00 3/6 J» I
»K)» C(J.K) *
CHLA 1 M ( J) "CHLA1 ( J) »VOL ( J)
CHLA2MlO)»CHLA2» J)*VOLl J)
COfJTINUE
CONTINUt
EUDY DIFFUSION CONSTANT
STEP
377
37b
C
c
C * » » *
C
c
c
C
C
(.«*«*
C
3ba CONTINUE
(.
C . . . . . ..... . ...... STEP 6
c..... STOKE. INITIAL CONDITIONS ON EXTKACT ISUHHARY) TAPE
C
C******** ************************************************ ******
C BEGIN MAJN WUALITY LOOP
ORIGINALLY THE EDDY DIFFUSION COEFFICIENT WAS KEAO IN HERE
N0rt THE DIFFUSION COEFFICIENTS AKE KEAD IN IN SUBKOUTINE COEFF
. ........... STEP b
COMPUTE VOLUMES OF I NFLOrt-OU TFLOW
DO 308 J=l »NJ
VOLiJIN( J)
J)»DtLTW
DO b36 1CYC-INCYC iNWCYC
NUCYCC = ICYC
STEP
STEP
-------
- 231-
171 c**»«« UETERrtlNE FLO»« DIRECTION AivO COMPUTE 1/4 POINT CONCENTRATION
172 L
1/3 UU416i^=lfNC
174 vOLFLft = o|(N) » DEl-Ty
1 7 b N L = N J 0 N C I N i 1 )
176 NH=NJUNCIN,2)
177 C UX=VIN)»DELTQ
17B C F=DA/CLEN(N)
179 C IF(F.GT.O.b) F=u.b
18U F=0»25
181 f ACTUK = UUS-F
182 IMSlfO.GE.O.U) FACTOrt=u.b+F
183
1 8 H 412 DO M14 K«1|NUMCON
ISb IFlCINiK,1).LT.-9.E+19) GO Tu 41H
186 yiaKAi) = C(Nt-iK) - CINH.K)
Ifa7 COiMC = C(NH>K) + fACTOK • «GKAD
IBS C
139 C STEP 10
19U c*»«*» AUVECT10N AND li I fFUS I 0,<
191 C
19^ ADMASS « CONC » VOLFLH»
19J olMASS = UlFFK(N) » OELTij • AREA(N) » Q&RAU /CLEwlN)
194 CMASi(Nri,M = CMASSlNHiK) + ADHASb + DlMASS
19b CHASbtNLfK) = CMASSlNL.Kl - ADMASS - OlMASS
196 414 CONTINUE
197 S16 CONTINUE
198 C
199 C STtp 11
200 (.••••• AUD WASTE DISCHARGE ANu DIVERSION MASSES TO THE JUNCTIONS
201 C
202 DO 434 J=JS»NJ
2U3 JF( VOLQ1NC J) .6E.O.O) IjO TO H30
201 DO 431 K=1|NUMCON
2Qb S31 CMASS(J»K)=CMASS( J iK )-CSPEC U iM «VOL0 Tu 592
219 C
220 C CALL TEMPERATURE SIMULATION ROUTINE FOR CALCULATION OF
221 C TEMPERATURES AT THE £NU OF THE (jUAHTY TIME STEP
222 C
223 CALL TEMPER(TEMP,TEMPMiVOUiASOR)
22H C
22b C STEP 13
226 C ASSIGN TEMPERATURE ADJUSTED COEFFICIENTS
227 C
-------
- 232 -
228 592 CONTINUE.
229 00 bdU J.JSiNJ
230 TEMPI J)=TEMPMU)/VOL< Jl
231 I T « T £ M P ( J J
232 lF(ISttTCril6>.Eg.i) 1 T = C T ( J )
233 JF(lT.LT.l) IT-l
231 IfllT.GT.SU) 1 T = b 0
23S DFfaCuiJil)=E.APBODllTil)«bGUlJMJil) + 1.
236 OFbOO(ji2)»ExPBuD(IT,2)»BOOOK.(Ji2) + 1.
237 OFbOa(ji3)=EXPBOOin»3)»bODOl<.lJ. 31 + 1.
236 OFCOL(J)=EXPCOL11T)«COI-OKIJ> + 1«0
239 UfNH3(J)»ExPNH3CIT)«CNH3UK(J)+l.U
210 OFN02(J)«EXPM02tIT)«CNOiUKtJ)+l.U
241 OFOGMJ)*£XPORt,(lT)*COR^OK(Jl + l.U
242 oFb 101 ( J)=EXPbOl ( JT )
213 UFBI02 ( J)=EXPB02< I T)
211 OXB£N(J)=OXYatlMlJ)*tXpbc.N(IT)»ASuh(J)
PUbEulJ)=POtb£lMCJ)»tXfbt.MlT)»ASllF<(J)
217
218
219
250
2B 1
2S2
253
251
255
256
257
258
259
260
261
262
263
261
265
266
267
26b
269
SBU
C
C
562
b6U
C
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CONl INoE
IFIlbnTCH(l).Eoi.l) GO
00 b62 J = J S i N J
COLMIJJ=COLMIJ)*OFCOL
C 0 N 1 1 N U E
IF< lSwTCH<2> .E«. 1 ) GO
HOoKS= JCYC»OELT
10AYS»hOoRS/23. 99999
To S60
( Jl
1 f. A E
U ** H C.
To 610
Ti«£=HOOKS-FLOAT<21*IoArS)
1J=10AYS+1
DT !HE=TlME-D£LT/2.
SET = SRI 1 IJ1+HDL1 IJ)
1F(OTIME .LT. SHl(U)
SOAVE»TL( IJ)/HDL( I J)
.OR. DT
STtP 11
SItP IS
.QT. SET) GO TO 20UO
SONET»SOAV£»(1.-COS(2.*3.111S92»(UT1ME-SKM1J))/HOL(IJ)))
271 GO TO 2U10
272 20UU SON£T»U.
2.73 2CI1U CONTINUE
271 DO 6bO J=JS»NJ
27S ICriECK = JIGNOK(J)
276 If- ( 1CHECK.GT.U) GO TO 600
277 C
276 c ..... ALGAE ^RO^THI KESPIKATION AND SETTLING RATES
27V C
280 PMU1=0.
281 PMU2=0.
2B2 FKrtAXl«0.
283 FfiMAX2'0.
281 IF(SOUET .LE. 0.) GO TO 602
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- 235-
39V 44B CONTINUE.
400 c
HOI C . . . STEP 20
402 (.»•*•« PREVENT NEGATIVE CUNCEu T R AT I ON AND SUPERS A T OR A T 1 OH
403 C
404 DO 464 K=I.NUMCON
405 IF(C1NIK.1).LT.-9.E+1 V) GO To 461
406 DO 466 J*JS«NJ
407 IF(C(J,M .GE.U.O) &0 TO 466
408 IF(KUCOP.E8«2) 60 TO 462
109 45a iVK 1 Tt(6 i460) J . I C YC . K . C ( J , K )
110 460 FOKMATI39H DEPLETION COKRtCTION MADE AT JUNCTION I3»7H CYCLE Hi
111 • ^1H FOR CONSTilUtNT NO. 11»12H. CONC. ((-AS F10«2)
112 462 CU»iO • 0.0
113 CMASS Li(M»C(L»H),M=l,NUMCOi\i)
44V 481 FOKMAT(I8>b(I4i&11.4)/Bxi7(»4»<3ll«4)J
450 CALL EXIT
4 51 48oCONIINOt
45i! &0 fO 4d<:
453 14B2 CONTINUE
454 DO 14faO J=1«NJ
455 1 4BO C ( JiM=0.0
-------
- 236-
456 4B2 CUNTlNUt
457 C
458 C SliP 23
459 C»... WRITE JUNCTION QUALITY ON TAPE FOR LATER AVERAGING
460 C
461 IFIN1U .£«. U) GO TO 6000
462 IFUCYC .LT. IwRITEJGU TO 6000
46J KOONTT=KOONTT+1
464 wKITt(NlO) ICYC,,P04IJ).CHLAllj),CHLA2NJ)
476 WKITb(6iblB> ICYC,ICYCTF.NTAG
477 518 FOKMATI lHl///47h RESTARi DECK TAPE ».AS LAST WRITTEN AFTER CYCLEI5/
478 • 50H MYDRAOL1C CYCLE ON EXTRACT TApE FOR RESTARTING • I5/
479 » 8H NTAG « I3///»
480 RtrilNON3Q
481 &2u CONTINUE
482 C
483 C STtP 2b
t84 c***** PRINT QUALITY OUTPUT
48b C
486 IF I ICYC-IPRT) 424.524,524
487 S24 IPRT=IPKT+N«PRT
488 528 HOUKS « DELTQ * FLOAT (JCYC) / 3600.0
489 KDAYS « HOURS / 23.V99V9
490 HUUKS • HOURS - FLOAT (^4 » KUAYS)
491 KUAYS=KUAYS+1
492 WRITE(6.530) ICYC,KUAYS . HOURS
493 530 FORMATfIOX,'SYSTEM STATUS AFTER DUALITY CYCLE*.
494 114,5X.tDAY'.13.»HOU«',F4.1»//.
495 2' JUN TEMP(C) OxY OtJODl Ua002 UBOu3 ORG-N N
496 3H3 N02 N03 P04 CHLA-1 CHLA-2 COL/MPN TOT-N1
497 4,/.lax.'MG/L MG/L MG/L MG/L HG/L MG/L MG/L
49B 5 MG/L MG/L UG/L UG/L MG/L'.//)
499 00 534 I •1 i NOPRT . I H I
500 J=JPKT(I)
501 ARITt(6.b'32) JiTEMP(J)>OXY(J)>BOD(J>l)lDOOtJi2)>bOU(J.3)iCORG(J).
502 1 CNH3(J).CN02(J).CN03(JJ,PU4(J).CHLA1(J),CHLA2(J)»COL(J).TN(J)
503 53^ FORHATlIX.13..12F9.3.E9.2.F9.3)
504 534 CONT1NOE
505 C
506 C STEP 26
507 C..... PRINT HEAT BUDGET INFORMATION AT EACH PRINT INTERVAL IF DESIRED
508 C
5QV 1F( lt-8TtM.E<*.0) GO TO 4*4
510 bT02=QRNET(J)»1327.29
511 *M Tt I6i92)
512 92 FORMATl 50HI RAUUTlOw TERMS AND EQUILIBRIUM TEMPETATURE
-------
ON3 SSS
11X3 Tim bSS
ess
zss
11X3 11VD (0«f VOt>N ' Jl TSS
HH«SI« IV a313"ldWOD NfHiVTnWts AlllVftfc HZCliVWNOJ ZttS OSS
6hS
QCN
I 9trS
ONV SNOI1ION03 XinvOB 1VI1INI JO
•> ct-s
• *•••»»»••••••«•»•*••»»« ••••••••••••••••••••••••it**********************') ?trS
dooi Ainvnfi NIVW ON3 5 t^s
**•*»*•***•**********»»*****••******•*«•***•*******•** »*»»«»»««»»»*»»»»D
9C5
SfS qfS
X3Tvnt) THO 5CS
DA3i = ?NNvw nnns ires
scs 01 o"5 rts
01 O1) (XNI«»T '^3' llNnOM)-!! ZCS
01 o^ (0 *f)?' niM)ji ics
{D3l')«snja CZS
ir i 3h
PZ5
415
ei?
(/ "> 930 HA'I nifl TV-iX HnZ)^«yi/q /. 15
t? 9IS
o71/e <5IS
niq ? his
t /T cic.
-------
- 238 -
Subroutine INDATA
This subroutine controls the input of data to the model. It also writes various
reports detailing the data used in the program. INDATA calls two other routines
that handle particular blocks of data (COEFF and METDAT). If the particular
run is the first run in a series, then initial conditions are looked for in the
data input. If this is a restart run, initial conditions are pulled in from
a seperate restart tape or storage file. The only exception to this is the temperature.
Temperature initial conditions are input in the data deck for every run unless
it is being simulated. INDATA also allows the user to alter the restart initial
conditions by a multiplication factor applied over any group of junctions.
-------
-239 -
FIGURE D-8
FLOW CHART FOR INDATA
ENTRY CALL
FROM DYNQUA
READ PROBLEM
DIMENSIONS
READ ALL
PHYSICAL DATA
_L
READ INTEGER
CONTROL FLAGS
AND CYCLE NUMBERS
READ
ISWTCH VALUES
READ INTEGER
CONTROL FLAGS
FOR REPORT
GENERATION
READ TITLE
PRINT PROBLEM
DEFINITION REPORTS
-------
CALL
COEFF-
- 240 -
FIGURE D-8
(Continued)
CALL
METDAT
READ SOLAR
INTENSITIES
FOR ALGAE
SIMULATION
READ LIMITING
CONCENTRATIONS
PRINT PHYSICAL DATA
YES
-------
- 241 -
FIGURE D-8
(Continued)
READ INITIAL
CONDITIONS
READ INITIAL
TEMPERATURES
READ & PRINT INFLOW
QUALITY BY
JUNCTION
READ INITIAL
CONDITIONS
FROM RESTART
TAPE OR FILE
READ INITIAL
CONDITION FACTORS
TO ADJUST
INITIAL CONDITIONS
PRINT
INITIAL
QUALITY
CONDITIONS
READ AND PRINT
BOUNDARY
CONDITIONS
RETURN
-------
- 242 -
I SU3KOOTINE INUATA
2 C
3 COMMON/GEOM/YNE«<200)iVOL«lN(20Q)»VOl_<200)»ASUR{2CJO)»QIN(200)»
4 1 NCHANt 200.6) ,UIFFK(HUO> >V ltOO> »M400) .AKEA1400) •
5 2 b(400).iCLEN(400) ,R(400) •CNCHOGJ .NJONC(4U0.2)
6 3 iQNET (200) .Y (200) »yOUTt2GQ) »VOUQOU4200>
7 4, YfaAK ( 20U ) iJutl ,JS,NC .NJ
8 COMMON/MISC/ALPHA(80)iCDIFFK.,CIN(l4«l).CLlMlTUM ( 2UO I i BOO 1 N ( 200 . 3 ) .CORG1N(200) •
19 S CNri31N(200) ,CN021N(200) .CM03IN1200) tpOHlNl200) ,
20 S ALG1N1 (200) i ALG1N2(200) iCOLIN(200)iTNlN(200)>
21 S CHA1 INI200I ,CHA21N(2UO)
22 C
23 C
2t CUMMON/CONC/TEMP(200),OXY(2UO)»BOD{2Qu»3).CORG(2uOI»CNH3«2UO)i
25 $ CN02I200) .CN03(200) iPOt(200) ,ALG1(200)>ALG2(200>i
26 £ COL<200 ) ,TN(20U>,CHLA1(200) .CHLA2I20u)
27 C
28 C
2V CO|1MUN/ttASS/T£MPM(200)»OXYM(20a>>BOUM(200>3)iCOR6M(2aO>iCNH3M(2QO>
3U S iC.-JUiM I 2UU ) i CNO JM I 20U ) »POMM ( 20U ) i AL& 1 H ( 200 ) >
31 S ALG2MI2UO) (C.OLMI200) |TNM(200) >CHLA1M( 20U) «
32 * CHLA2M(200>
33 C
31 C
3b CUriMUN/KATE/REuX(2(JO)iCOLUK(200)*BODDK(200i3)>CNH3DK(200)i
36 S COKbDK(200) tEXPb02(2uU) lAbSNKt(200) >AGSMK2(200I •
37 i> CN02UK(200) >POS1NK(200) iOXYBEN(200) iCNHbEN(200) >
38 S SECHI(200) ,PMAX11200) »PMAX2(2UO) »AGCnAl (200) .
39 * AGCHA2(200) ,P04bEN(200) .PRESJ(200) iPRES2(200)»
4U S UFBI01 (200) , DFUOD(200t3 ) i UFCOL(200) .UfNH3(200) .
HI S DFN02 I 2uU ) ,uFObM 2QU I .L/FB 102 ( 20U) .ExpbENI 20U) .
42 S EXPbOl (200) ,EXPBOD(2uU ,3) .ExPCOL(200 I iEXPNH3(200) i
H3 S EXPN021200) ,EXPOKG(200) .CKBEN1200) .CSAT(200) .
44 $ OXBEN(200)tOXUELT(200)tPObENI200)>CFbOD>ALGlPi
MS S AUGlN.PiPl .FSN1 .PSL1 ,ALt2P.AUG2N.PSP2tPSN2»PSL2«
46 S OXNH3.0XN02,OXRtSl ,0Ah£S2iOXFAC 1 •OXFAC2•DKBODi
47 S UK.CUL iRAC IN ,RACEX
48 C
4V C
50 COMMON/bUN/ TLt365) . SR I (36b) .HDL(36b)
51 C
52 C
53 COHMUN/ATHS/yC(2UO)fQ*l200).U(E(2UU).EyTEMl200).XuNS(200).QTOT(200)
SH A. (1|NSI2bl10)i(jNAl25ilQ)tQRNETA(2StlO)iOWlNDA<25»10)>TAA(25llU>
5B Bi TA^IA (25i 10) ,APA(2b i 10) fCLOOU(25i 10) • IEQTEM, JWiONE( 10.2)
56 C. i»KNET 1200) .AX 14) »BX(4) ,AUPHl 8) iBETA (8) .PI ...bO.DTOK
-------
- 243-
57
58
59
60
61
62
63
61
65
66
67
68
69
70
71
72
73
74
75
76
77
78
79
80
81
82
83
84
85
86
87
88
8V
90
91
92
93
94
95
96
97
98
9V
100
101
102
103
10H
105
106
107
108
109
11U
1 1 1
1 12
1 13
COi-IMON/lCHECK/JIGNOR(20u)
DIMENSION JUNMb)iJON2CMASS<200.14) iCSPEC(200. 11)
EQUIVALENCE (C(ltl)iTEMp(l)),(CMMSS(lil),TEMPM(l))
S , (CSPECf lil) .TEMPlNt 1 ) )
REAU CONTROL AND
...... STEP
HYDRAULIC DATA
10U1
bd
N
READlSi 1001) NJiNC»uELT
FORMAT(215iF10.0»
READ(5i88> (JlbNOR(J)i
FOKMATI40I2J
REAO(5i80) (1 TAPE( 1 ) i 1 = 1 ,5 I
00 82 1 = 1 >4
N«ITAPE< I )
1FIN.6T.O) REWIND
a2 CONTINOE
NIO'ITAPECI)
N20=ITAPE12J
il30*ITAPE<3)
N40«1TAPE(4)
bO FOKMAT116I5)
MM«1
READ(5i1002J
1002 FURMAT120A4)
READ(5t-
J-l.NJ)
IALPHA1 I ) * 1 = 1
RtAU(5.-
KEAOIb,-
KEADIbi-
RlN)
>MC)
( CLElM IN) >N*
( (NJONCINt 1
RtAO(5i- ( Y(J)iJ=
RtADlSi- (ASOR(J).J*
READ(5i- (INCHANlJiK)
DO 9003 ME!iNC
9003 Q(N)=0.0
REAO(bt-) (Q(N). N"
DO 9000 N=liNC
AKEAIN) » b(N)»h(N)
V IN ) = u(N)/ARtAIN)
AT£IM10=10.0»»6
DO 9001 J"l»NJ
A50RIJ) = IASOR(J))
i J=l i2 )
lUJ)
iN-1 ib) > J=
inC>
>NJ)
9000
90U1
• ATEN10
C
(.»«•» RtAU INUEPENUEin CONTROL DATA
STt-P
3, lNCrC|N(i|CYCiKZOPiKDCuPiNTA(jiJiiIEXC
84 FURMAT(7I5)
REAU(5iHO) (ISt«TCH(I)il = li6)
4u FORMAT(1015)
REAL)t5i80) 1PRT
IWRlTE,
IftRINTiNOPKT
-------
- 244-
111 KiAOlSil92)ljPr*T(l)»I*liNUPKT>
lib 192 FORMAT!11 I b >
116 «RlTE(6»lOb) < ALPHA I 1) • 1 = 1 »t>0)
117 1 0 b F 0 R M A T ( it(20Xi20A4>/ ))
lib UtLTu( = OELT*36GU.
119 UtLTQl»DELT
120 OtuTw2*UELTuil*FLOAT (NSlpRT)
121 8»MTt (6 » 107 ) 1NCYC.NUCYC. DEL f W2 , uEL T U 1
122 1U/ FuRrtATt10X.•INITlAL QOALITY CYCLE* • i I b • / i
123 1 10X»«FINAL «OAL1TY CYCLE ••»ibt/»
124 2 IQXi'OuTpUT INTtRvAc HOORS= • i F 10.3 i / ,
125 3 lUXi'TlME STEP rtOURb • ' »F1U.3t///)
126 »RjTE{6»l06MITAPt 4brt FlLt CONTAINING KtSTAKT DATA t!3i///>
132 taKJTE16 i 109) IPKT
133 109 FOKMAT(31H PhiNTOUT IS TO BtGlN AT CYCLE It//)
13H DTU * DELTdil / 21.
13b NUMCON=11
136 IF(JS.Lt.O) JS=l
137 C
138 C . . . i STEP t
139 C.«... PRINT CONSTITUENT SELEcTEO FOR SIMULATION
ItO C
1H1 WK1TE(6»120)
IH2 120 FORHATI 60H THE FOLLOWING CONSTITUENTS ARE BtING CONSJQERED
143 SIN THIS RON •/.» CONSTITUENT ttQ. CONSTITUENT')
1HH 4*1
lib IF ( I SvkTCHl 6 ) >Ew>0) rtK I TE ( 6 t 1 22 ) J I ( I N AME ( K i J ) i K= 1 , 5 )
146 IF( I5ATCM(5) .Et|. I ) bO TO b2
It/ HKITL(6i 122) 1J• I INAME(KiJ) tK«I >b ) iJ = 2»b)
IH8 b2 CONTINUE
ItV IF(1SwTCH(2).Ew«i) ^0 To 50
1SU ftR!TE(6il22) ( Ji I INAMElKiJ) »K=1 ,5) .J«6,U)
151 bUCONTlNUt
Ib2 J=12
153 IF ( I SWTCH(3).EUtO) OR ITt(6i122 ) 4 • t 1 NAME(K,j) , K=J , 5 )
I5t IF ( 1 SwTCHl 1 ) .EtJ. I ) 00 To 5t
15b J=13
1 b 6 WKlTt(6>1^2) Jf(INAi1E(K,j)iK-lib)
157 bH CONTINUE
1&ri J=1t
159 »KITt(6«122) J , I 1 NAME < K , J) |K,= 1 ,b)
160 12^ fURMATI IS i 1UX«bAt)
161 JF< I5>*TCH<6» .Ew.l ) uO Tu 125
162 C
163 C CALL FOK WEATHER UATA
164 C
16b CALL METQATlOELTtj)
166 C
167 12b CONTINUE
160 IFI1SATCHI2) .£U. 1) GO TO 802U
169 H = FLUAT I INCYC-U»UELT
170 It/U = H/23.V99V
-------
- 245-
172 HeFuOATlNwCYC)»L>ELT
173 IUD2=n/^3»9999
171 DO 8UOO KK=IDDilUD2
17b btiOO REhU(btdOlO) 1L(KK ) • Sk 1 (KK ) »HDL(KK)
176 aUiU FOKHAT<3F1U«4>
177 8U20 CONTINUE
1 78 C
179 C
180 C CALL SOdROUTlNE COEFF TO READ AND PKIi-»T bYSTEM COEFFICIENTS
181 C
182 CALL COEFF
133 C
184 C STEP b
Idb Ct.,.. READ MAXIMUM ALLOWABLE CONCENTRATIONS
186 C
187 lib FOR.1AT ( BF10.0)
189 CLIMlT/A AND HYU« KAUIuS AND X-SE.C 1 I ON AL AKEA OF
198 *ChANNELi •*•**«»»•«»«•»«»»*«///
179 « aUH*«* »**»»*•*•»*»*«•*»»«*»••»•» ChANNEt DATA •»••»»»*
2QU •••*«•»•»»••••**•*•••• /
201 • SUH CHANt LENbTH AlDTH AREA MANNING ^ET FLOW HYU.
202 »K/iUiUS JUNC.ATENUS /)
2U3 l9<4) (N>CLEN(N)ib(N)lAKeA(N)tCr\(N)iil|NLT(N)i
2QM * R ( N ) , ( N J U N C ( N , K ) , K = 1 i 2 ) , N = 1 , l-l C )
20S 194 KOKMAT I ISi2F8.0 iF9.UiFd,3 iF12.2iK!U. 1 • I V , 16)
206 AK I Tt I 6 • 1 9b 1
207 19b FORhATl66H»*»*»«****»***»»»»»»»» JUNCTION DATA »•••*»»»•«•••••
208 *»*»»»»««•• /H3H JUNt. INFLOW AREAIFT2) HEAD CHANNELS/)
210 1V6 FOWMATlHXi I1* ,F9. 1 ,3X,f U ,U »F7.2i Ibi7 If )
211 ArtlTL(6»910l)
212 WRITE! 6 19103) ||J(N), N°1»NC>
213 9101 FORhAT(30H FLO«t Q I S TR 1 tiU T I ON BY CHANNEL)
214 9103 fURMATl 10Ffa.2)
21b C
216 IF(NHO.t>T.O> faU TO 124
217 C
218 C ...... . ..... • « . • . STEP 7
219 C ..... KEAu INITIAL JUNCTION DUALITY
220 C
221 UO 126 L=l,Kj
222 RtAOtS,200> J 1 f J2 » 1 C TEMp ( K ) . K= 1 •
223 2uu FOKMAT(2I5I/F 10.0/8F10.U)
224 IFiJ^.Ei^.O) &0 TO 130
22b DO 129 J»J1 » J2
226 DO 1^8 K=1,MUMCUN
227 12b Ct J»K)=CTEMP(K)
-------
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-------
- 248 -
342 230 CONTINUE
343 U0232i=l,NUMCuN
344 IFCNGKOUP ( 1 ) )231 ,23 1 , 2J2
345 231 ft K I T 216)1
346 232 CONTINUE
347 D0238rt=l,^UMCuN
348 IFItVGROOP ( M ) ) 238 , 238 , 233
349 233 N fa = N G K 0 U P I M )
35U uO 236 K=l,N&
351 NJ1 = NJSTftT (MiK)
3b2 NJ2 = IMJSTOP(M,K)
353 UO 234 J=NJl,NJ2
354 C(J»r1)»C(J»M)*pACTRlMiK)
355 234 COrtUNUt.
356 236 CONTINUE
357 23tt CONTINUE
358 23V CONTINUE
35V c
36U C STtp 15
361 C * • « > t PRIivT INITIAL I* U A L 1 T ¥ CONDITIONS
362 C
363 NN s: Stj
364 uO 25D J=JS»NJ
365 TEi1P( J)=CT( J)
366 IF(NCHANfJ,I ) .E«.OJ GO TO 2bO
367 NN=NN+1
368 lMNn.LL.50) GO TO 252
36V KN=l
37U rtHlTLl6,24l)
371 241 FOf{MAT(47Hl INlllAL CONDITIONS (MG/L EXCEPT AS NOTED) /
372 $« JUIM TEMPIC) OXY UB001 UB002 UBOD3 OHG-N N
373 Sh3 N02 N03 P04 CHLA-1 CHLA-2 COL/MPN TOT-N*
374 $/)
375 252 CONTINUE
376 ttKJ Tt (6 <242 > J t ( C ( J • K ) f f, = 1 i NOMCON )
377 CHL«1(JJ=ALG1(J)
37b CHLA2 ( J)=«Lt.2l J)
37V ALG1(J)=ALGl(d)/AfaCMA11J)
380 ALG2(J)=ALG2(J)/AGCHA2(J)
381 242 FOKMAT< 1XiJ3,12F9.3»E9.^ ,F9.3 )
382 2bO CONTINUE
383 c
384 C STEP 16
385 <;*•*** KEAu ANU PRINT bOUHDARy CONCENTK AT i ONS
386 C
387 KEAUlb,dQ)(KbOPlM),M«l,uuMCUN)
388 DOl87M«l,NUMCON
389 Ibb KtAl)(5,184) C1N(M,1)
390 IFlClNln.l) .LT. 0.) CIMM,1 )--V.9E+I 9
391 104 KORMATiaFlO.O)
392 187 CONTINUE
393 Clul11,1)=CIN(11,1)/RACtX
394 ClNl 12,1 )=C1N( 12, 1 )/RACtX
39b 191CONT1
396 L
397 KETUKN
398
-------
- 249 -
Subroutine COEFF
This subroutine reads in all spatially variant and spatially invariant system
coefficients. After reading all coefficients, a report is generated listing each
coefficient for each junction. A second report is generated detailing the
nonvariant coefficients.
Before control leaves COEFF, an array of temperature adjustments for each coefficient
is generated. These arrays are used in DYNQUA to set the coefficients that are
temperature affected during each time step. Figure 10 is the flow chart for COEFF.
If the user desires, COEFF will also calculate the reaeration coefficient internally.
All coefficients are input for 20°C, and assumes base e. COEFF adjusts the coefficients
according to the time step used in the simulation.
-------
- 250 -
Subroutine COEFF
This subroutine reads in all spatially variant and spatially invariant system
coefficients. After reading all coefficients, a report is generated listing
each coefficient for each junction. A second report is generated detailing the
nonvariant coefficients.
Before control leaves COEFF, an array of temperature adjustments for each coefficient
is generated. These arrays are used in DYNQUA to set the coefficients that are
temperature affected during each time step. Figure 10 is the flow chart for
COEFF. If the user desires, GOEFF will also calculate the reaeration coefficient
internally.
All coefficients are input for 20°C, and assumes base e. COEFF adjusts the
coefficients according to the time step used in the simulation.
-------
- 251 ~
FIGURE D-9
FLOW CHART FOR COEFF
CALL FROM INDATA
READ REAERATION
COEFFICIENTS
CALCULATE
KEAERATION
COEFFICIENTS
READ REMAINING
COEFFICIENTS
WRITE SPATIALLY
VARYING COEFFICIENTS
READ AND WRITE
SPATIALLY INVARIENT
COEFFICIENTS
ADJUST COEFFICIENTS
FOR TIME STEP
DETERMINE
TEMPERATURE
ADJUSTMENT
ARRAYS
RETURN
-------
- 252 -
1 SUBROUTINE COEFF
2 C
3 C THIS SOOKOUTIIME READS v'ALUE-S FOR NUHERuub COEFFICIENTS AND CONVERTS
4 c irith AS NECESSARY ro EQUIVALENT VALUES FOK THE COMPOTATIONAL TIME
5 c
6 CUMHON/tjEOh/YNE»«(20U)iVOL«lM2!JO)iVOL(2UO)»ASUR(200)» ii>l( 400 ) » AKEA( 4UO ) i
8 2 8(400)|CLEN(400).R(4UO)»CN(400)|NJUNC<400.2)
V 3 »t)NET t 200) i Y l 200 ) »«OOT ( 20Q I » VOLQOUI 200 )
10 4 i YbAK(2UU)iJk,M»JSlN(.iNJ
11 COMMUN/MISC/ALPHA(80).CulFFK>ClN(lSiJ)>CLlMlTllH)iCONSTl20.1M)
12 A, Cl£MPllH).DEl-T»DTbtEBBCON(Ha,l'|)iEX«iFACTK(l'(«10)iIEXC
13 B. INCYCtlNTt>IiiIPRTilT*PEib)cOKblNI200)«
22 4 CNH3IN1200J |CN021N(200) »CN031N(20Q) ipGHiNt200) »
23 i AL^lNl(200)>ALGiN2(200)iCOLiN(200)iTl\INl200)i
2H * ChAllN(200)tCHA2iN(2uO)
2b C
26 C
27 COMI10N/CONC/TEnP(20u),OxYl200)iBOU(200»j).CORfa(2t.O)»CNH3(20u)»
2b S C(M02(2Ua| ,Cn03(20U) .POH120U) i ALbl 1200) »ALCi2(200) •
29 4 COL(200) ,TN(200) .CHLAU200 1 ,CHLA2(2Uu )
3U c
31 C
32 CUi1l1Ui AliSrvK. 1 ( 200) i AQXYDtN(200) ICNHBENI200) i
41 4 SECH1 (200) IPMAXH200) »PMAX2(20U) . AGChAl (20U) ,
BEN(200 ) i
4b S EXPbOl (200) iEXPBOD(2U0.3) »EXPCOL(200) tEXPNH3(200) •
46 4 EXPN02I 200) tEXPORGt200) iCNBEN(200) tCSAT(2UO ) t
47 S OXbEN(200)lOXOELT(200)>POBEN(20U)iCFoODiALG1P>
48 4 ALG1U.PSP1 •PSNI .PSL1 , ALG2P .AL&2N|PSP2»PbN2>PSL2>
49 4 OXNH3iOXN02,OX«ESl »OXKES2»OXFAC 1 . OXF«C2iDKBOD»
bO S DKCOLiRACIN.RACEx
51 C
&2 C
S3 C^i-lMUN/iOlV TL( 36bl >SRl I 36b)
S4 C
b& C
56
-------
- 253 -
57
5d
b9
60
61
62
63
64
6b
66
67
68
69
70
71
72
73
74
75
76
77
78
79
80
81
82
33
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A, ai10)»IE«TEM,.JW20N£(lO,2)
C, t)KNET(20U),AX(4),cX('«),ALPri(8)»DETAI8),Pl,ftBO»UTOK
COMMON/ICHECK/J1GNOK120U)
DIMENSION C(20U,l4)iCMAi>S(2tJO,14)iCSPEC(200,14l
EQUIVALENCE (C(l,l)>TEMp(l)),lCMASS(l,l),TEMPM(l)l
$ , (CSPECl 1,1) ,TEhPlN< 1 ) )
DIMENSION jUNl(b) ,JUN2(b) »CQEF(5)
DIMENSION AU10( 10,31
REAEKATION
-------
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-------
- 258 -
342 362 CONTINUE
343 GO TO 36U
3*44 364 CONTINUE
345 3?u KEAU(SilUQ) ( JUN1 1 I ) fjUn2( I ) ,COEFU ) ,I«i ,5)
346 DO 372 1=1,5
347 J1=JUN1(I)
348 IF(JI.EH.U) GO TO 374
349 J2=JUN2lI)
3SO DO 372 J = J1»J2
351 AGCMA2(J)=COtFli)
352 372 CONTINUE
3S3 GO Tu 370
354 374 CONTINUE
355 C
356 C EDDY DIFFUSION CUEFIClENfS KEAO HERE BY JUNCTIONS
357 C
358 1LJUO KEAU(bilOU) I JUN1 U ) , JulM2< i ) ,COtM 1 ) • 1 = 1,b)
359 DU 1UU2 I = l»B
36U J1=JUN111)
361 IF (Jl.Etj.U) GO TO 1004
362 J2=JUN2l1)
363 DO 1UQ2 J = Jl i J2
364 OIFFM j)» COEFI 1 )
365 10U2 CONTINUE
366 GO TO 1000
367 1DU4 CONTINUE
368 C
369 C . . STEP 4
370 C IftKiTE bPATIALLY VAKYING COEFFICIENTS
371 C
372 AKITE(6i14Q)
373 DO 180 J=l ,Nj
374 IF(NLHANIJ,1).Ey.U) GO TO 180
37* WR1TE(6>141) JiKEOX(J).BODUK(J,l).BODOKlJ.2).'BODL
-------
- 259 -
399
4UO
an]
i U *
102
403
104
105
406
107
10t)
409
4 t 0
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111
112
113
4 14
lib
416
117
11 0
119
120
121
122
123
424
125
426
427
428
429
430
431
432
433
431
435
436
437
43b
439
140
411
112
143
144
lib
146
117
lib
449
450
451
452
453
454
455
R E A 0 I S . 1 I 0 ) RAC1N.KACEX
C
C * • » • . TEN PET A TORE COEFFICIENTS
C
00 913d 1=1,10
913b KE«Dlb,9l37) tAwlOll.J), J-li3)
* 1 3 / FORMAT(3F10«U>
C
C STOICH10METRIC EyU I V ALcMCtS
C
C
(.••••• PRINT SPATIALLY INVARIANT COEFFICIENTS
C
AKlTt.(6i 136)
138 FOrcClAT(lHl,///,45H SPATIALLY 1 N v A K I A N T SYSTEM COEFFICIENT //)
•-RITE16.14D ClAG|10{l,J)>J=l»3)iI = l,10)
144 FORMAT I // ,40H « 1 0 TEMPEnATOKE COEFFICIENTS
4 40H COLUORM DIE OFF
$ 40H bOO-i OECAY
4 40h bOD-2 OECAY
S 4UH bOD-j UECAY
4 40H AMMOMA DECAY
s iuH N j TRI f E DECAY
4 4UH ORGAr, 1C SEDIMENT OECAY
4 4UH ORGANIC iv DECAY
4 4UH ALG-1 GROATH ANo RESPIRATION
S 4CJH ALG-2 GKO.VTH ANO RESPIRATION
H.R1TE16.146) OAN02,OXNH3,OXRES1 ,OXRES2iOXFACl,Ox
146 FORhAT ( // »43h STO I CH I (JME TR i C EQUIVALENCE BETWEEN
S 4UH NITRITE DECAY
S 4UH AMMOlNlAUECAY
4 4L)H ALG-1 RESPlRAlION = OXR£Sl«CHL-
4 IUH ALG-2 RESPlRATIO!i = OXRES2»CHL-
4 IUH ALG-1 GROWTH =OXF AC 1 »CHL- A
S> IUH ALG-2 GROWTH =OxF AC2»CHL- A
»K1TE(6»11&) HSP1 ,PSP2,PSN1 »PSN2,PSL1»PSL2
14b tuRMAT(//4oH hALF-SATuRATION CONSTANTS FOR ALGAE
i • ALG-1 P« , 10X,F lu.3i 10X, • ALG-2 P«»10X
* • ALG-1 N' , 10A ,Flu .3, lUX, • ALG-2 N'.lOx
4 • ALG-1 L • , 10X.F1U.3, 10X» • ALG-2 L'.IOX
k>RlTE(t»150> ALG1P,ALG2K,ALG1N,ALG2N
150 FURCiAT RACIu,RACEx
155 FOKMAT(//,40H RATIO OF CHLOROPHYLL A TO ALGAE
*" 4Oh FOK ALL lNf-LO«S
4 40H FOR EXCHANGE
C
(.••«•• AOJOST COEFFICIENTS FOK TIME STEP
C
OK,BOu = BOODK3(FlOi3)/
.31F1U.3) /
,3(F 10.3)/
,3(F lu.3)/
• J(F 10. 3)/
,3(F 10.3)/
>3(F 10.3)/
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-------
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— 01 I I U 0 vj < X Ml .J
o_
-------
- 261 -
Subroutine METDAT
This subroutine consists of two separate sections (METDAT and TEMPER). The first
section is called from INDATA and is used to input all required meterological
data needed by the simulation run. (If temperature is not simulated, METDAT
and TEMPER are never called.) METDAT reads in the number of weather zones, and
the number of observations in the data deck. It produces a report listing the
information. Before returning to INDATA, METDAT calculates the initial best balance
for the simulation run. TEMPER (an entry point of METDAT) is called during the
main quality loop. Its purpose is to calculate the best budget as the simulation
proceeds through time. Figure 11 provides the flow chart for METDAT.
-------
- 262 -
FIGURE D-10
FLOW CHART FOR METDAT AND TEMPER
CALL FROM
IlfDATA
ENTRY POINT
TEMPER
FROM DYNQUA
READ WEATHER
DATA INFORMATION
CALCULATE NEW
HEAT BUDGET
PRINT WEATHER
DATA REPORTS
CALCULATE
NEW WATER
TEMPERATURES
COMPUTE
SHORTWAVE
RADIATION
CALCULATE
EQUILIBRIUM
TEMPERATURE
IF WANTED
COMPUTE
LONGWAVE
RADIATION
RETURN
PRINT CALCULATED
INFORMATION
RETURN
-------
TOT <200
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- 264 -
b7
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HA = PI * ( TlMt - 12.0 - DELIS ) / 12.0
S 1 N A = 11 + T2 • COM HA )
RAU « ,,60 * blNA
AI = U.128 - O.bbl • ALuiilOl 1.0 / A B S < 5 I N A ) )
TA = TURB • Al / SlUA
KAU = RAO / EXP( TA )
RAD = RAO • (1.0 - .6b * CLU»»2)
NC= 2.0 • (CLD +1.0)
1FICLU .Gl. O.Ob .AND. CLU .L T. U.9b) GO TO 1 b 0
NC«=1
1FICLD .GT, 0.9b) NC = <4
IbO ALbEUO = A(NC) « ( b7.3 * ASIN( blNA ) ) ** B(NC)
WNS(NN,L)=RAD*(1.0-ALBEUU)
131 CONTINUE
1 30 CONT 1 Nut
FINT=FLOAT( INT)
C
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C.
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.... PRIhiT REMAINING ft E A T H E R DATA
AKlTt(6»H2)
1 12
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SOLAR(CALC) /
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-------
- 266
1 SUBROUTINE DLUCK.
2 C
3 C THIS bi-OCK. UATA SUPPLIES SPECIFIC INVARIANT INFORMATION
t C
b
6
7 b i mCYC»lNTbl&»lPKTilTAPElS),l*KINTtIWRITE,JOlVl(2U)»JDIV2(20)
8 C. JPRTl3GU)iJfiEriUu).JHtT2<2U)»KBOp(lt).KDCuP,KZOP»MM»NEXTPR
COMMoiWMlSC/ALPHAl&U) >CL>1FF*..CIM Iti 1 ) • C11 M i T ( It) ,CUNST(20i It)
«. CTEMp(lH)iDELIiDTuiEaoCOMtfe>lt)ttXKtFACTK(ltilU)iIEXC
bi lriCYC»lNTbl&»lPKTilTAPElS),l*KINTtIWRITE»JOlVl(2U)»JDIV2
o C. JPRT (300) i JfiET 1 Uu) • JHtT2( 20 ) »KBOp( 1 t ) .KDCoP»KZOP »MM»NEX ,
V U i Nit.XT(,K»NiiKOuP(lt)>NJSTOP(ltilO)«NJSTRl(lt»lO)»NODYN»NOPRT
[0 E, rNulPKTiNKSTK Ti'* SPEC. NSTOP.N TAG.NUMCON,NUN ITSiMUiN20
12 G, OELTw
13 C
It C
Ib COMMON/ATMS.
16 A i QNSl2b(10),mNA(2b«lUlt»TAAl2S,10>
IB Ct i,KNET < 2GU I » At t ) ,ot t > • Ai_PH( 8) »bETA I 8) iP I tWBOtDTOR
IV t
20 (_••••• COfobTIlUEuT TITLES
21 C
22 DATA I NAME/ MuTthlP i HHEKAT .HrtURE >4H ,th
23 A, tHDISS i tHOLVc. • tHU OX 11H YO.EN , t H
2t b, thCAKdi
26 Vi thCAKB!
27 C, tHORuA.thNlC ,tHN1TR•HHobEN,tH
28 U, thAMMU.tnNIA ,tHNITRitHOGEHitH
2V E, tHNlTK.thlTE ,tMMTR i tHOfaErt , tH
30 Ki tHNlTR»tHATE ,tMN1TR•HHOfaEN.tH
31 b, tHPHOS.tHpHAI,tHE PH,tHOSPH>tHOROS
32 2, thCHLOitHKuPMitHYLL itH*--l,tH
33 1, tHCriLO,t"ROPo«triYLI- «thA — 2»tH
3t H, tHCOLlithKORH ,tH BACitHTER1,tHA
35 J, tHTOTA.trtL N 1 , t HT KOG . t HEil ,tH
36 C
37 (.««..« IMI TIALUAT ION OF METEKGLOfclC CONSTANTS
38 C
3V UATA XUNS/2QOO ,\j/
tO DATA ALPH/6.0b,b.10,2.6b,-2.0t,-V.9t,-22.2V,-t0.63»-66.VO/
11 DATA BETA/0«B22.0.710.0.V&t.1.26b.1.6SV,2.Ibl »2.76 1 t3.blI/
t2 DATA A/1.IB(2.20.0.Vb,0.3b/
H3 DATA B/-0.77 ,-0. 97 t-0. 7t,,-0.t&/
tH DATA PI/3«ltlbV/, hUO/0.3333333/» OTOK/0.017t5/
tb NtTUKN
t6 EMD
-------
- 267 -
Subroutine QUALEX
QUALEX produces a summary of all water quality information that is handled by
the simulation over a specified time. Information concerning the concentrations
of each constituent at each junction and time step can be stored on tape or file
during every time step if desired. At user intervals, QUALEX then produces a
specified summary of all stored data, determining the minimum value, the maximum
value and the mean during the interval for each junction. A report is generated to
display the calculated summaries. The flow chart for QUALEX is shown in Figure 13.
-------
- 268 -
FIGURE D-ll
FLOW CHART FOR QUALEX
CALL FROM DYNQUA ]
DETERMINE TIME
OF SUMMARY
READ STORED DATA
FOR ALL
CONSTITUENTS
DURING SUMMARY
PERIOD
DETERMINE MINIMUM,
MAXIMUM AND MEANS
IN EACH JUNCTION
DURING SUMMARY
PERIOD
PRINT REPORT
FOR EACH
JUNCTION
RETURN
-------
- 269 -
1
2
3
4
5
6
7
8
9
10
1 1
12
13
14
Ib
16
17
16
19
20
21
22
23
21
2tJ
26
27
26
29
30
31
32
33
34
3S
36
37
38
39
40
HI
42
43
44
45
46
47
48
4V
50
51
52
53
54
55
56
SUBROUTINE
WUALLX
,VC|_wiN{200).VUL (200)
NCHAN(200,8),DlFFK(4JU)iVl4uO).W(400)iAKEAl4UO)»
»QOUT(2UQ)>VOL«OU(200)
2 B
3 »QNET<200)iY(200)
4i YBAh(20D) » Jt,«V
COtlMON/MlSC/ALPhA(80liCDlFFKtClNll4il)»CLlMIT(14)iLONST(20>14l
A CTEMPtl4),0El_T,QTu.EBbCONl48,lKDCuP»'^20PiMMiNEXTPR
0 NtxT».R|NGROoPU4),NJSTOP<14ilU)iNjSTRT(14ilO)»NODYNiNOPRT
E NliCYC>NQPKT.NRSTRTiNSPECiNbTOP»NTA(a»NOMCON,NUNITS.N10tN20
F N3QiN4UiRETFAC(2U>14)»NEXilSttTCH(10l,NAME(20liINAME(5tl'(J
5 DELTQ >KOONE iMARK 1 iMARK2
,OXYlN(2UO)iBOuJM2oOf3) i COKfa 1 N I 2UO ) >
CNH3IN(200),CN021N(200)iCN031N(200)lpO'>TNlN(2UO)(
CHA1 IM200) ,CHA21N(200)
COMMON/CONC/TEMP(200),OAY<2bO)i8ULi<2gO,3)iCORG<2oO)iCNH3(200).
S CN02(200),CN03(200),P04(200)|ALGl(2Uu)»ALG2(20a)»
S COL(200)»TN(200)iCHLAl(200)»CHLA2(200>
COrtHUN/MASS/TEMPM(200)fUXYH(2UO)tbOOh(200«3J iCOR&M(2UO) »CNH3«(200>
S «CN02Ml200)lCN03M(200)|P04M(200)>AI-Glh(2UO)i
CHLA2M(200)
COKt>UK(200>i£XP&02(200)tA6SNKl(2QO>tAt>SNK2(200)t
CNU20K(2UO)iPUSiNK12UO)iOXYBEN(2UO)iCNhbEN(200)>
SECHl(200)«PMAXl(200MPMAX2(200)tAGCHAl(200)i
AGCMA2l200),p04bEN(2UQ)»PKESlt2UO)iPRES2l20U)»
OFbI01(200)lDFbOU(2UU>3)iDFCOL(200)iUFNH3(200)t
DFN02(200)tUFOt>N(20a>iOFBi02{2GO)»EXPBEM200>i
EXPb01(200)iEXPBODI2UU>3)i£XPCUL(200)iEXPNH3(200}«
EXPN02(200)l£XPORG(200J>CNBEN(2UU)>CSAT(2UO)i
OXE>£N(200)»UXPiLl<200)tPOdEM2oa)tCF80DiAL.l>i
OXNh3iOXN02,OXKESIfOAKE52.0xFACJ.OXFAC2»DKBOD«
UKCOL.RACIN.RACEX
CUMrtON/SUN/ TLU65) »SRl 136S) |HDL(365)
/ ATHS/tjC ( iOO I »QA ( iDU ) i(jE(20U) >E<4TEM(200) iXuNS(200) , QTOT (2UO)
uNS(25,10)tQNA(2b>lO)fURNETA(2b>10)iOAlNDA(25»lU)iTAA<2&tlD)
TAKA(25ilO)iAPA(2bilO)iCLOuO(25ilO)iI£yTEM,JHZONE(10i2)
QKNET<200)iAX(4)ibX(4)lALPH(8)iBETA(e)iPI>ABOiDTOR
CUririON/ ATHS/tjC ( iOO I
A •
B,
C.
-------
- 270 -
S7 C
58 Curtf1uN/lCM£CK/JIG!MOK(20u)
S9 C
6 U DIMENSION C<2UU.14>>CMAbSl2UO>i'n>C:>PEC(2U0.1 1 > >TEKp(1 )) • "DELT-DELT
7b HOUKS2=FLOAT(MAKK2>»UELT
76 KUAYSl=HOUKS|/24.9999
77 Kl/AY:>2 = HOURS2/23.9999
76 HOUKS1 = HOUKS1 - FLOAT (24 • KUAYS1)
79 HUU«b2 = HOUK52 - FLOAT (2t • KDAYS2)
8U KDAYS1
81
82
83 C
8H C . . . STEP 2
8b C«.... PKiNT bUMMARY HEAU1N&S
86 C
87 111 FOKMAT(IHl////7^H»«*«»*»•*»•*•»»»*»»•»••»• DUALITY SUMMAKY
88 *•***************••*****/
89 • Sbn SUMMAKy STAKTb AT SUMMARY ENDS AT/
90 i 6M CYCLt»15.6H (UAY iJ3f6H HOUH .F5.1.13H) CYCLE »
91 « lb,2H (|l3i5H DAYSiFb.1»7H HOUKS)/////)
92 C
93 C . STEP 3
9t C DETERMINE MAXIMUM. MINIMUM ANO AVEKAbE
9b C
96 lit Rfc.AUU.lU) ICYCw , ( (CX(J.K) iK=l .NUMCONi >JsJS.Nj)
97 IKCICYCW - MARK1 ) 111. Ub. 1 J6
98 lib DO 117 J«l(NJ
99 tic/ i j6 K«I .NUMCON
100 CAVE(J.K) K Q.b *CX(J.K)
1U1 CMINIJ,K) BCX(J.K)
102 CflAXU.K) BCX(J.K)
103 116 CONTlNUfc
tOH 117 CONTINUE
lOb GO TU 11H
106 11BD012HJ=1,NJ
107 uo .122 K = I .NUMCON
108 CAVE(J,M » CAVt-(J.K) +CX(d»K>
109 IF(CilIMj.K) -CX ( J.K) ) 120 • 1 19» 1 I V
110 1 19 CMMJiM *Cxt J.K)
111 (.0 TO 122
112 12u IK ICHAXIJ.K>-CX(J.K)) 121(121.122
113 121 CMAX(J .K)«CX(J.K)
-------
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— — W 3
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z -• .n ^ -* x
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u H — — a: u — H — ii— z — x -z ~s t- a
3 -M -• u. a: o zoj-Z'j.za:oJ:oo-iJiij2
O.ZZ — ^l»- 2u3->Z — Z«aSU.JKi:uJ
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o r~ 33 y-
-------
- 272 -
Data Preparation for GBQUAL
GBQUAL requires several blocks of data to be input in the runstream for any given
simulation. Some of the blocks of data originate from other computer programs.
There are 3 major blocks of data that must be prepared and merged to form the
full input requirements of the model. There are: (1) Physical data and quality
simulation parameters and coefficients, (2) The hydrodynamic data that determines
the spatial movement of water during the simulation period, (3) Meterological
information. Each of these blocks of data originate from a different source
and must be prepared according to GBQUAL formats. Figure D-12 illustrates the
flow of data required to construct an operationally complete deck. The next
section describes the formation of these blocks of data. (Since the formulation
of the hydrodynamics portion is really a separate program, that portion will
not be described. Figure D-13 illustrates the type of flow data required by
GBQUAL.) The input format and order will be described in the same way it is
read by GBQUAL. A listing of a sample deck will appear at the end.
Input Data Description
This section lists the exact format and order of all data necessary for a simulation
run of GBQUAL.
-------
-273 -
FIGURE D-12
FUNCTIONAL DATA FLOW TO CREATE A DATA INPUT SET FOR GBQUAL
HYDRODYNAMIC
; FLOW PATTERN
t FROM
\ HYDRODYNAMIC
MODEL
INTERFACE
PROGRAM
GBQUAL
FLOW PATTERN
DATA
FILE
/
[' GBQUAL DATA FOB —
I QUALITY RUN \
FILE
MANIPU-
LATION
/METEORO
< • — 1 LOGICAL
V DATA
DATA FILE
WITH QUALITY
AND FLOW DATA
COMPATIBLE
WITH GBQUAL
-------
FIGURE D-13
Typical Hydrodynamic Input to GBQUAL
HEAD OF GREEN BUY
-------
- 275 -
System Setup Parameters
Card
Type
1
2
3
4
5
6
7
8
9
10
11
12
Card
Column
—
1-5
6-10
11-20
1-80
1-5
6-10
11-15
16-20
1-80
1-80
1-80
1-80
1-80
1-80
1-80
1-80
Format
None
15
15
F10.0
4012
15
15
15
15
Physical
80A4
None
None
None
None
None
None
None
FORTRAN
Name
IIII
NJ
NC
Delt
JIGNOR
ITAPE(l)
ITAPE(2)
ITAPE(3)
ITAPE(4)
Description
Controls print interval. A value of 1 will
print all junctions, 2 will print every
other junction, etc.
Number of system junctions.
Number of channels
Time step (hours)
NJ numbers are read here in 4012 format.
If JIGNOR(I) is set to 1 then that junction
is ignored in the calculations. Set to 0
to keep it in the calculations.
Unit for internal scratch file.
Hydrodynamic extract file.
Unit to store last cycle for future restart.
Unit for reading restart data.
Data to Describe Simulation System
ALPHA(80)
CN(NC)
R(NC)
B(NC)
CLEN(NC)
NJUNC
(NC,1),
NJUNC
(NC.2)
Y(NJ)
ASUR(J)
A four line alpha description.
Mannings N for each channel.
Hydraulic radius for each channel (FT) .
Width of each channel (FT) .
Length for each channel (FT) .
A pair of numbers for each channel. This
describes the junctions that any channel
connects .
Depth of junction (FT)
Surface area of each junction in units of
million sq. ft.
13 1-80 None NCHAN One card is read here for each junction. It
(NJ, 1...8)lists the channel numbers that touch that
junction.
-------
- 276 -
Card
Type
14
Card
Column
1-80
Format
None
FORTRAN
Name
Q(NC)
Description
Flow in each channel (ft /sec). Flows are
positive if they move in the +x or +y
direction.
Simulation Control Options
15
16
1-5
6-10
11-15
16-20
21-25
26-30
31-35
(To
1-5
6-10
11-15
16-20
21-25
26-30
15
15
15
15
15
15
15
simulate a
15
15
15
15
15
15
INCYC
NQCYC
KZOP
KDCOP
NTAG
JS
IEXC
Constituent
Initial quality cycle.
Final quality cycle.
Option to summarize output by zones. (This
is no longer used. Set to 2)
Control option to print depletion correction
messages. Set to 2 to delete messages.
Set equal to 1.
Number of the first junction to be
simulated. Usually set equal to 1
Set equal 0
Selection
given group, set its ISWTCH value to zero)
ISWTCH(l)
ISWTCH (2)
ISWTCH (3)
ISWTCH (4)
ISWTCH (5)
ISWTCH(6)
Coliforms
For the group (Org-N, NH3-N, N02-N, N03-N,
P04-P and Algae 1)
Algae 2
Total nitrogen as a conservative
BOD and DO
Temperature
Print Control Options
17
1-5
6-10
11-15
15
15
15
IPRT
NQPRT
IWRITE
Initial cycle for quality print out.
Number of time steps between prints.
Initial cycle for storage of data for
16-20
21-25
15
15
quality summary.
IWRINT Number of time steps for quality summary
print.
NOPRT Number of junctions printed in each quality
print.
-------
- 277 -
Card Card FORTRAN
Type Column Format Name Description
Printing Order
18 1-70 1415 JPRT This array lists the printing order (by
(NOPRT) junction) of the quality print out.
Meteorological Data
(Card Types 19 through 21 contain data required to compute diurnal
temperature fluctuations. If temperature is not being simulated,
card types 19-21 can be deleted.)
19 Data limits, 1 card
1-5 15 NWZONE Number of weather zones.
6-10 15 NPTS Number of data points used to describe one
day's weather.
11-15 15 NQCSM Number of quality time steps between the
start of the quality simulation and
midnight.
16-20 15 NRCALC Net radiation calculation switch; if NRCALC
= 1, net radiation will be calculated from
sun angle and cloud cover.
21-25 15 IEQTEM Equilibrium temperature calculation switch,
if IEQTEM = 1, the equilibrium temperature
will be calculated.
26-30 15 IDAY Day of the year.
Repeat Card Types 20 and 21 for NWZONE weather zones (one set per
weather zone).
Weather zone general data, 2 cards
20 1-5 15 JWZONE(I,l)First junction in weather zone I.
6-10 15 JWZONE(I,2)Second junction in weather zone I.
11-20 F10.0 XLAT Latitude of the study area, degrees.
21-30 F10.0 XLON Longitude of the study area, degrees.
31-40 F10.0 EPS Site location code:
-1. = West longitude
+1, = East longitude
41-50 F10.0 TURB Atmospheric turbidity factor. Values
range from 2.0 for clear unpolluted
atmosphere to 5.0 for highly polluted
atmosphere.
-------
- 278 -
Card
Type
21
22
Card
Column
51-60
61-70
FORTRAN
Format Name Description
F10.0 AA Evaporation Coefficient "a" (usually 0.0
F10.0 BB Evaporation coefficient "b" (usually 1.5
x 10~9).
Atmospheric data, NPTS cards (one card per weather data point)
1-10
11-20
21-30
31-40
41-50
51-60
(This
for
1-10
11-20
21-30
F10.0 QRNETA Net incoming radiation (leave blank if
NRCALC=1) kcal/sq. Meter/sec.
F10.0 UWINDA Wind speed, meters/sec.
F10.0 CLOUD Cloud cover, fraction.
F10.0 TAA Dry bulb temperature, °C.
F10.0 TAWA Wet bulb temperature, °C.
F10.0 APA Atmospheric pressure, millibars.
Solar Intensity
is needed only if algae is simulated. There must be 1 card
each day of simulation including partial days.)
F10.0 TL Total amount of incident solar radiation
in langleys.
F10.0 SRI Hour of sunrise
F10.0 HDL Number of hours of day light.
Chemical, Physical and Biologic Coefficients
(Card types 23 through 27 contain the reaction rate constants and
other coefficients for those constituents being modeled.)
Spatially varying coefficients
(Repeat Card Type 23 as necessary to input spatially varying
coefficients over the total network. (5 sets of junction and
coefficient values per card for each of the listed coefficients.)
Terminate each set of coefficient data with one blank set of data).
For each coefficient in the list below:
23 1-4 14 JUN1(1) First junction for which the coefficient
applies.
5-8 14 JUN2(1) Last junction for which the coefficient
applies.
-------
- 279 -
Card
Type
Card
Column
9-16
65-68
69-72
73-80
Format
F8.0
14
14
F8.0
FORTRAN
Name
COEF(l)
e
JUN1(5)~>
JUN1(5) V
COEF(5)J
Description
Coefficient value
Five sets of junctions
and coefficients per
card
The following coefficients are input in the above manner and in the
order listed.
FORTRAN
Name Coefficient
Data (Decay rates
Units are all base
e)
REOX Reaeration (if reaeration is to be calculated
set COEF(l) = -1.)
COLDK(l) Coliform bacteria dieoff rate
BODDK(l) Coliform bacteria dieoff rate
BODDK(2) BOD decay rate
BODDK(3) BOD decay rate
CNH3DK Ammonia decay rate
CN02DK Nitrite decay rate
CORGAK Organic nitrogen decay rate
AGSNK1 Algae sink rates
AGSNK2 Algae sink rates
PRES1 Algae respiration rate
PRES2 Algae respiration rate
POSINK Phosphate precipitation rate
P04BEN Source rate of phosphate
OXYBEN Benthic uptake of oxygen
CNHBEN Release of ammonia from sediments
SECHI Secchi disc depth
PMAX1 Algae max. specific growth rate
PMAX2 Algae max. specific growth rate
AGCHA1 Ratio of chlorophyll a to algae biomass(mg/mg)
AGCHA2 Ratio of chlorophyll a to algae biomass(mg/mg)
DIFFK Eddy diffusion rate
24 Algae related coefficients, 2 cards. Repeat Card 24 for the second
algae type. Both cards are required.
1-10 F10.0 ALGIP Phosphorus content of Algae -1, fraction
of total biomass.
11-20 F10.0 ALGIN Nitrogen content of Algae -1, fraction
of total biomass.
21-30 F10.0 PSP1 Phosphate half-saturation constant, mg/1
as phosphorus.
31-40 F10.0 PSN1 Nitrogen half-saturation constant, mg/1.
41-50 F10.0 PSL1 Light saturation constant, langleys/hour.
-------
- 280 -
Card
Type
25
Card
Column
Spatially
1-10
11-20
21-30
31-40
41-50
51-60
Format
invariant
F10.0
F10.0
F10.0
F10.0
F10.0
F10.0
FORTRAN
Name
coefficients
OXN02
OXNH3
OXRES1
OXRES2
OXFAC1
OXFAC2
Description
: stoichiometric equivalences, 1 card
Stoichiometric equivalence between
and nitrite, mg/mg.
Stoichiometric equivalence between
and ammonia, mg/mg.
Stochiometric equivalence between
respiration and Chl-a.
Oxygen produced by photosynthesis
of Chl-a.
Oxygen produced by photosynthesis
of Chl-a.
Oxygen produced by photosynthesis
oxygen
oxygen
per mg
per mg
per mg
of Chl-a.
26 Algae related coefficients, continued, 1 card
1-10 F10.0 RACIN Ratio of chlorophyll a_ to algae biomass
in all inflows.
11-20 F10.0 RACEX Ratio of chlorophyll a^ to algae biomass
at the exchange junction.
Temperature Correction Coefficients
27 1-10 F10.0 AQ10(lf>>
11-20 F10.0 AQ10(2) f Three coeff. for temperature correction for
r each temperature adjusted coefficient.
21-30 F10.0 AQ10(3)__J
AQ10 1 thru 3 are used in the following equation:
- = AQ10(1) + AQ10(2)* T + AQ10(3)* T* T
where T is the temperature in °C.
Card 27 is read for each of the following list in the given order:
Decay Coefficient
1. Coliform decay
2. BOD-1 decay .
3. BOD-2 decay
4. BOD-3 decay
5. Ammonia decay
-------
- 281 -
Card Card FORTRAN
Type Column Format Name Description
6. Nitrite decay
7. Benthic oxygen demand
8. Organic nitrogen decay
9. Alg-1 activity
10. Alg-2 activity
Input Data cards 28-30 and 32 require data for each of 14 constituents.
The following data order must be used to insure that the data are stored
in the correct positions in the storage array.
Constituent No. Constituent
1 Temperature
2 Dissolved oxygen
3 Ultimate biochemical oxygen demand
(BOD-1) •
4 Ultimate biochemical oxygen demand
(BOD-2)
5 Ultimate biochemical oxygen demand
(BOD-3)
6 Organic nitrogen
7 Ammonia nitrogen
8 Nitrite nitrogen
9 Nitrate nitrogen
10 Phosphate phosphorus
11 Algae-1
12 Algae-2
13 Coliforms
14 Total nitrogen
Maximum Allowable Concentrations
Card Type 28 sets maximum concentrations for all constituents.
Simulation terminates when any of these values are exceeded.
28 Concentrations, 2 cards
1-10 F10.0 CLIMIT(I)"^ Maximum allowable concentration for the
/ fourteen constituents. Two cards are
\required with eight values on the first and
71-80 F10.0 CLIMIT(I+6Msix on the second.
If this is a restart deck then skip card type 29 and 30. If
temperature is not being simulated then do card type 31. If
this is not a restart deck then do Card type 29 and 30 and skip
31.
Initial Concentrations
Repeat Card Types 29 and 30 until all initial quality groups are
given. Terminate data with two blank cards.
Initial quality group concentrations, 1 card.
29 1-5 15 Jl First junction of an initial quality group.
-------
- 282 -
Card Card FORTRAN
Type Column Format Name Description
6-10 15 J2 Last junction of an initial quality group.
11-20 F10.0 CTEMP(1)~") Temporary read array for entering
?• the initial concentration of the first
71-80 F10.0 CTEMP(7)J seven constituents.
30 Initial quality group concentrations, continued, 1 card
1-10 F10.0 CTEMP(8)~) Temporary read array for entering
£ the initial concentration of the last
71-80 F10.0 CTEMP(14)J seven constituents.
Initial Temperature for Restart
(Do only if temperature is not being simulated and this is a restart
deck. Use the same format as for card type 23.)
31 1-4 14 JUNCl(l) First junction for which the temperature
applies.
5-8 14 JUNC2(1) Last junction for which the temperature
applies.
9-16 F8.0 COEF(l) Temperatures.
65-68 14 JUNC1(5)~") Five sets of junctions and initial
69-72 14 JUNC1(5K
73-80 F8.0 COEF(5) \ temperatures per card
One blank set should appear to terminate this input.
Inflow/Outflow Quality
Repeat Card Types 32, 33 and 34 until all junctions with inflow/outflow
are listed. Terminate with three blank cards.
32 Inflow/outflow description, 1 card
1-80 20A4 NAME Description of the inflow or outflow
33 Inflow/outflow rate and concentrations at junction, 1 card
1-80 18 JJ Junction number
9-16 F8.0 QQ Inflow or outflow rate, inflows are
positive and outflows are negative.
17-24 F8.0 CTEMP(l) Temporary read array for entering the inflow
concentration of the first eight constituents.
73-80 F8.0 CTEMP(8) Leave blank if this is an outflow.
34 Inflow concentration, continued, 1 card
1-16 16X Blank
17-24 F8.0 CTEMP(9) ~) Temporary read array for entering the inflow
s. concentration of the last six constituents.
65-72 F8.0 CTEMP(15)\ Leave blank if outflow.
-------
- 283 -
Card
Type
Card
Column
FORTRAN
Format Name
Quality Adjustment Factors
Description
(Card Types 35 and 36 contain initial quality concentration adjustment
factors by constituent for areas described by given junctions.)
Repeat Card Types 35 and 36 for each constituent (I). If a constituent
is not going to be altered, set NGROUP(I)=0 and card 36 can be omitted.
If no factors are going to be applied to the remaining constituents, set
NGROUP=-1 and do not repeat for each constituent.
35 Data limit, 1 card
1-5 15 NGROUP(I) The number of groups of junction numbers
for which it is desired to increment the
initial concentrations of constituent I
which was previously read as input. There
is no limit (up to NJ) to the number of
junctions, comprising a group but the
numbers must be consecutive. Max.
number of groups = 10.
36 Adjustment factors by constituent and group, NGROUP/5 cards
(5 groups per card)
1-5 F5.0 FACTR(I,K) Multiplication factor to be applied to the
initial concentration of constituent I at
those junctions in group K.
6-10 15 NJSTRT The first (lowest) junction number in the
(I,K) sequence of junctions comprising group K
for constituent I.
11-15 15 NJSTOP The final (highest) junction number in the
(I,K) sequence of junctions comprising group K
for constituent I.
61-65 F5.0 FACTR ~~N
(I, K+4) /
66-70 15 NJSTRT \. Five junction groups per card for
(I, K+4) j constituent I.
71-75 15 NJSTOP
(i, K+4y
Boundary Junction Quality
(Card Types 37 through 38 describe constituent concentrations at the
seaward boundary of the system throughout the tidal cycle.)
37 Control options, 1 card
1-5 15 KBOP(l) "^ Control option for specifying concentrations
|_ • C of each constituent at the boundary. If
f * \ the concentration is constant over all
71-75 15 KBOP(15) 1 cycles, KBOP=1; if variable, leave blank.
-------
- 284 -
Card Card FORTRAN
Type Column Format Name Description
Use one card with one concentration (CIN(I,1)) for each constituent (I).
If the constituent is not to be modeled, set CIN(I,!)=-!. All fourteen
constituents must be listed.
38 Boundary junction concentration
1-10 F10.0 CIN(I.J) ") Boundary junction concentration
C at each time step (J) in the tidal
71-80 F10.0 CIN(I,J+6))cycle.
Output Description
The Quality Program will produce two types of output: (1) printed reports, or
(2) a binary (file/tape) restart data file.
Printed Reports
Printed output includes: echo reports of much of the input data and a report at
selected time intervals of the quality at specified junctions. The use of various
printout options also allows printing of a summary of all water quality parameters
at each junctions over a specified number of cycles. This report gives the
minimum, maximum and average value for any constituent in each requested junction.
It is possible to use this output form as a check on the steady state of the
system. If a given run is given steady hydrodynamics and steady inflowing quality,
then a steady state in the system will eventually be attained. This can be checked
by comparing the maximum versus minimum value of a constituent (particularly
a conservative) during the summary period. An example input deck and output
reports for a typical model run appear in the next section.
-------
- 285 -
The binary restart file is used to feed the final conditions of a completed run
into the next run as the initial conditions. In this way, the user can keep
continuity between runs and still have flexibility in updating inflowing quantity
and quality and/or temperature of the system. Depending on the computer system
the restart file can be written to a tape or a mass storage file. It is also
possible to direct this output to a card punch and develope the restart information
in the form of punched cards.
-------
- 286 -
DATA SET FOR GBQUAL
1
o/ 182 6.0
0 O O 0
O O 0 0
0 u 0 o
lo
-------
- 287 -
6572.
9658 •
•492V.
4929.
8215.
4929.
6572.
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6b72.
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6572.
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1 8
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20 21
47 51
84 51
12 44
36 42
41 4B
45 52
49 5U
53 61
SB 67
62 63
73 68
71 75
72 76
81 67
2.89
9.91
13.58
12. 07
Id. 31
39.66
56.89
4U.91
90.29
21 .56
32.34
64.69
64.69
1 91 .06
388. 12
377.34
97.03
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8215.
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31 29
9 32
17 18
16 37
47 84
27 32
29 7
36 39
41 44
45 49
50 53
53 56
59 67
63 68
9 12
65 66
76 74
63 87
7.91
25. 82
1 I .38
22.41
23.39
44.85
55. 45
9.15
12.27
21 .56
161.72
43.12
129.37
64.69
301 .87
97.03
172.50
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37 24
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47 24
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46 48
S9 51
53 54
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63 64
68 82
76 73
HI 77
6.40
6.40
1.71
1 1 .22
14.04
43.34
39.07
38. 84
51 .90
21 .56
21 .56
21 .56
32.34
75.47
226.40
43.12
323.43
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1 ISUI .
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1 Ibul .
31217.
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Ibul .
8073.
26208.
3144.
3144.
2 10
6 10
30 32
12 16
21 22
28 25
67 60
33 34
24 51
42 43
55 64
Si 60
54 56
60 76
61 68
68 80
73 78
77 63
7.41
10.37
31.50
20.64
24. 1 1
19.91
21 .69
/.58
25.29
21 .56
21.56
301 .87
129.37
258.75
43.12
43. 12
97. U3
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3286.
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1 1501 .
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1 1501 >
9358.
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2 11
29 30
32 12
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84 56
51 52
55 56
34 16
64 65
66 69
74 73
78 82
9.91
10.50
16.40
16.90
33.50
1 1 .58
13.94
65.91
44.72
21.56
53.91
64.69
86.25
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26283.
2 5
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24 42
43 49
84 59
60 65
50 61
60 72
64 69
69 80
72 74
82 80
7.91
25.56
17.91
4.89
7.35
39.24
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20.64
7.45
32.34
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16 19
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25 26
40 9
67 B6
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48 44
52 85
85 76
56 62
61 73
65 69
69 70
74 78
80 81
14.57
5.54
13.91
24.90
34.61
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3.48
39.57
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215.62
32.34
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-------
- 293 -
APPENDIX E
HYDRODYNAMIC MODELLING
The circulation patterns used in the water quality simulation in this report were
generated by using a separated hydrodynamic model developed independently. This
appendix provides a brief presentation of the formulation and the structure used
in the hydrodynamic model. The broad objective of the model was to investigate
the hydrodynamic response of Green Bay to the meteorological input at the surface,
to the effects at open boundaries in the Bay, and to the river inflows. The
flow in the Bay is affected by the boundary conditions at the shore and the
bottom as well as the open ends. The model is designed to calculate Bay-level
disturbance and water circulation generated by wind fields over the region in
a numerically reproduced combined river-shallow sea system.
Fundamental Hydrodynamic Equations
The flow in the Bay is basically unsteady and three dimensional. The equations
which describe the circulation -in the Bay can be written in the form of a set
of nonlinear partial differential equations for conservation of mass and
conservation of momentum in the Eulerian form. The Cartesian coordinate system
is chosen where X and Y are taken in a horizontal plane of the undisturbed
surface with X eastward and Y northward and Z is vertically upward. The basic
governing equations for a three dimensional model and two-dimensional model for
an estuary were thoroughly discussed and derived by Pritchard (1971). Considering
Green Bay, a fresh water estuary, one can assume a two-dimensional model with the
following equations:
-------
- 294 -
15 ' a>
|Z + u |X + v |V = _ 1 > _ |h _ + 1 (T - T ) (3)
dt dx oy p dy 3y H
where the notation is as follows:
h = elevation of water surface
f = Coriolis parameter
P = surface atmospheric pressure
a
p = vertical mean water density
E = bottoE elevation (z = -H)
g = acceleration due to gravity
(U,V) = vertical mean horizontal velocity averaged from the water surface to
the bottom in (x,y) direction
(T ,T ) = surface wind stress in (x,y) direction
wx' wy
(T., ,T_ , = bottom frictional stress in (x,y) direction
tsx oy)
These equations are similar to those used by Leendertse (1970) in his work on the
Jamaica Bay simulation.
-------
- 295 -
Surface and Wind Stress and Bottom Frictional Stress
The bottom frictional stress, T and T_ , is expressed in the form:
OK ay
TBx • PgU
+ V
(4)
By = pgV
/U'+V2
(5)
where C is the Chezy coefficient. The Chezy coefficient depends on the roughness
of the bottom and the depth of the water. The Chezy coefficient may be related to
Manning's roughness coefficient, n, by the familiar formula:
C - (1.49/n) H
1/6
(6)
The Chezy coefficient in the formula has the units ft ' /sec and H is in ft. An
appropriate unit conversion should be made because the model computation is made
in the cgs system. The value, n, changes as the type of bottom varies.
The wind stress at the water surface is approximated by assuming the validity
of a logrithmic distribution of wind velocity with height. Therefore:
T » C p U U
wx w a w w
(7)
T « C p V V
wy w a w w
(8)
-------
- 296 -
where p& is the air density, U and V are the wind velocity compontents measures
at a height 10 meters above the water surface and C is the wind stress coefficient.
Wu (1969) suggested two approximate formulas for the wind stress coefficient based
upon the compiled data of thirty observations. C =0.5 (wind speed) for
light wind, lm/sec<(wind speed)<15m/sec. C = 2.6 x 10 for strong winds
(>15m/sec). For breeze, C = 1.25 x 10~3/(wind speed)±/2'
Numerical Scheme
A set of finite difference equations are used to replace the governing
differential equations. The numerical scheme used is a space-staggered scheme where
velocities, water levels, and depths are described at different grid points.
Figure E-l illustrates the scheme. The water level h is described^at integer
values of j and k, the velocity U is described at integer and one half values of
j and integer values of k, and the velocity V is described at integer values of
j and integer and one half values of k. The basic scheme is widely used by many
investigators (Platzman, 1959; Heaps, 1969; and Leendertse, 1970). The scheme
has the advantage that in the equation for the variable operated upon in time,
there is a centrally located spacial derivative for the linear term. A detailed
mathematical formulation can be found in Lee (1974). The operation consists of
two successive tiiae intervals. The first time level is taken from time n to
time n-t-r- and the second time level is taken from time n-br to n+1. The field
111
variables h (n+2}, Un+2 and Vn+2 are obtained from h(n), U(n) and V(n). The
process involves solving h and U implicitly and V explicitly. In the second
time level, the variables hn+2, Un+2~ and Vn+J are used to compute hn+1, Un+1,
and V . The operation is implicit in h and V and explicit in U.
-------
- 297 -
SPACE-STAGGERED SCHEME
k-1
1
j -
J +1
+Water Level
• Depth (h)
— U velocity (u)
| V velocity (v)
Figure E-l.The Space Staggered Numerical Scheme
-------
- 298 -
Finite Difference Grid Network
The finite difference grid for the model covers the lower half of Green Bay from the
mouth of the Fox River at its southwest corner to the northeast 10km above Sturgeon
Bay. There are 55 grids eastward and 53 grids northward. Each grid is 1016m by
1016m. The water depth or the elevation is measured at the center of each grid.
Figure E-2 illustrates the grid network used in. the computation. The land-water
boundary is not a fixed boundary in order to account for the possible flooding
of some area near the shore.
Boundary and Boundary Conditions
The boundary of the problem includes a solid boundary at the shore and bottom,
an open boundary at the surface, an open boundary at the River mouth and an open
boundary at the open Bay. Because the numerical scheme is designed in accordance
with the type of boundary conditions, the numerical operations in the two time
levels are postulated differently. Therefore, an extensive system is developed
for the purpose of tracking the boundary and boundary conditions and matching
an appropriate numerical scheme efficiently. The flooding in the shallow flat
area around the bay was also considered.
The boundary conditions at the free surface are specified by the atmospheric
pressure, wind speed and direction patterns. For the case studies made in the
report, seasonal statistical means were sought using the office records of the
U.S. Weather Service at Austin Straubel Field in Green Bay for the years 1968
through 1974. In each case, a calm sea state was used as the initial condition.
The Chezy roughness coefficients at the bottom of the Bay vary with the depth and the
Manning's n. The n values varied from 0.036 for sand and gravel bottoms to 0.075
for shallow weed beds.
-------
- 299 -
Figure E-2.The Finite Difference Grid for the
Hydrodynamic Model of Green Bay
O
f
I
I
c
-f
-------
- 300 -
The river inflow to Green Bay was calculated by using the data at the Rapide Croche
Dam for the corresponding period. Since there is no measured physical data to be
used as the boundary condition at the open Bay, a numerical scheme is imposed to
insure the mass balance at the boundary. Furthermore, the boundary is located
far from the interested region so that the local boundary effect at the open Bay
would be minimal.
-------
- 301-
References
Heaps, N. S.
1969. A two-Dimensional Numerical Sea Model, Phil. Trans. R. Soc. Lond.
A265, 93-137.
Lee, K. K.
1974. A Hydrodynandc Model of Green Bay, presented at the Technical
Conference on the Water Quality of Lower Green Bay and its Drainage
Basin, Green Bay, Wisconsin, November 1974, (Manuscript in
preparation).
Leendertse, J. J.
1970. A Water-Quality Simulation Model for Well Mixed Estuaries and Coastal
Seas: Volume 1, Principles of Computation, MR-6230-RC, Rand Corporation.
Platzman, G. W.
1959. A Numerical Computation on the Surge of 26 June on Lake Michigan,
Geophysics, Vol. 6, No. 3-4, pp. 407-438.
Pritchard, D. W.
1971. Hydrodynamic Models, Estuarine Modeling: An Assessment, Chapter 11,
pp. 5-33, Water Pollution Research Series, 16070, DZV 02/71,
Environmental Protection Agency.
Wu, Jin
1969. Wind Stress and Surface Roughness at Air-Sea Interface, J. of
Geophysical Res., V. 74, No. 2, pp. 444-455.
-------
-------
- 303 -
APPENDIX F
STORE! RETRIEVALS OF THE
DATA GENERATED BY THE
GREEN BAY STUDY
-------
- 304 ~
o
o
o
o
o
a
Statistical Analysis Of All Survey Data
At All Stations During The Period Of Study
— x
(M CL
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3 a o -o a* r- op
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a — ^
o en i- IT
-iJ O
o a 3 CM a
-j 3 CD in 3-
a * a "oo • —
-• 3- -* o <*i — •
cs r*. •—.—.-• —
— X x vj
rw a. is u
(si as 3 a:
•*> -J a:
x < o
O -D J "O -O 3- —
O 3 j -. O -O —
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* rg a -o » T** o
o • a • a • o
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a o t
O _l
X
o o o a) o (^ ^o
a o a o <*i (h M
O o o o r*. co ao
• o a • a • • PV T
fs. O * O fsj • T
_ 3- rsj ». r\j T- •
O Jl o r*. —
—• • o -* o> <
f-1 Q <
a o Q
a CD
o o a I*- o -o
o o a eo o x-
— 2 VI _»
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00 O S
c o o M r*. o co
o 3 a — J r- «j
a o o P»- — — (N*
• r- a a) O O -O
T o • • • • in
O f*> -• t
00 O
a o o -H r*. o o
o o o -* — >o o
CD O O <*1 (N * <
• 1*1 O O *M —• Is*
a — -* j» o* r*j 3-
— • O -* «• M •
(M -• O • O * —
« o_ — in
r*» i/i x cr
o z u uj
C3 •< - I/I Z
O O O T Jl f*l •<)
o o o o
3" Q O 1*1 3" -O O)
o e>
oa:
a o o o — ao j>
o o o oo L/I <*i ao
D a o (M *• co ao
• a o 3~ — o* 1/1
o —» o «*» —• 01 o
« • o 3- cw f •
(NJ :T 3 * * • —•
O Q O -J) 0* O
C C C X -0 IS,
o a a r»- o* o
• -o a a- eg co
1*4 • Jl 00 Is* P*.
CT* GO * * • •
o- —• — co r-v M
O I
O J1
O O
a o o oo o r
C C C -
o a o « -o 3-
• >o 03- a r* i
o ui rj r^ x o s
— n o -o o -o
(M " O O O O
o
— ac.
a u
O O O O) 3- 3" CO
o a o in <*> -o —
o o o o* (*i 3- o
• m a in ui T- a-
CO * O • • 3" C-
(M r^ a ^ — • 3-
o M o -. 3- >o *
— .-. Q.
a o a: e)
x o s:
o o*- a <•> t> f* ao
o o- o -o n 3- rs.
D o^ o •*» r^ o* N-
• o* o 03 a Ji »n
co <*t —« o* o co N.
o-o o a o D co
K It, >•
-« o <
O < -« UJ < ^ O
z z z: z; > in u
UJ
s u. >-
— o <
SJ — ** z «. Z u.
^. x z < or < uj
z> < — UJ <: t— o
2 z z: a: > in u
h- O O
< or i-
o u.
O 2
X O
o —
O t-
d l/l
O 2
X O
O -1
O I-
X <
O h-
o in
-------
- 305 -
a
o
a
o
Statistical Analysis of All Stations During Each Survey
333
3 a 3
• * 3
M ^o a*
in • in
• sO *
3-
CO
3
•
003-
• ^D •
•O • 3-
a *o
• •
a 3 —
~o • •
CO -O
J> 3
• in
3
0
o
0 O -0
• a in
CO Q 0-
• N CM
—• » •
in a z
a ~ 1
jJ 3 3 3 -O c*> 3" -0 3 3 3 -O 33 3> "1 3 3 3 X "^ <*1 • • 3 in • —• <
C3_J Z 3-OO' OOOin-Oinrx
fxC/lICC 33O^m3-*" O33r*133~-O 3 3 O in 3" 'O —«
3ZL^UJ O O 3 D CO 3- —• 333[*1O*3"O 3O33~COC03"
3'n
in OH-UJUJ 3" » • • IT rg (N( COOOCOCOf*}*^ O • tfl • " 3" ^ Lf) • C3 • -^ •<) O
F** 3*^tJ 33(*13"»*CO ^•3tntxjLnO^ 3-CO
(X. Ul LjJuJQ? uJUJQt UiUQf UJ UJ iK
uj uj £z: ua< ££ u a <: ££ u.o< ££ u o <
OU. X 3 3 Z > X33 Z > K33Z » a: 3 3 Z ^
£u.>- z x: z < cc < uj £xz(nu Z££x>mu z££r>tnu z£££>tnu
— a — a — a -•
a DO o o o o
UJ£X XX XX XX
t— o o o x O«MX f*»inx -o^ox
-------
STORET RETRIEVAL DATE 75/04/10
QOOUQOQO UOOOOOOOOOO
DATE
FROM
TO
71/07/01
MONTH
71/08/00
71/08/01
MONTH
71/09/00
71/09/01
MONTH
TIME DEPTH
OF
DAY FEET
NUMBER
MAX IMUM
MINIMUM
MEAN
VARIANCE
STAND DEV
COEF VAR
NUMBER
MAXIMUM
MINIMUM
MtAN
VARIANCE
STAND DEV
COEF VAR
NUMBER
MAXIMUM
MINIMUM
MEAN
VARIANCE
STAND DE.V
COEF VAR
00010
WATER
TEMP
CENT
136.000
27.5000
9.00000
19.3912
16.8215
1. 10110
.21 1508
161 .000
23.0000
9.00000
la. 0329
1 1 .7553
3.1ZB61
.190130
121 .000
22.0000
13.0000
17.H215
1 .79622
1 .31023
.0769298
00299
00
PROBE
M&/L
133. 0(10
lO.SOnO
1 .50000
7.099 1 7
1.17315
2. 1 15n5
.2979.10
161 .OnO
10.60nO
2.20000
6.86111
3.73171
1 .93176
.281511
121 .000
1 1 .10nO
1. 10000
8.18171
2.69967
1 .61307
. 19371 8
Q007S
TKANSP
SECCHI
M E T E K S
17.0000
2.10000
.300000
1 .35631
.252101
,502097
.370166
17.0000
2.10000
.150000
1 .31212
.306312
.553155
.112373
15.0000
2. 10000
.300000
1 .32355
.300137
.518121
.111129
00310
BOD
5 DAY
MS/L
21.0000
30.0000
2.50000
6.79583
28.7369
5.36069
.788820
31 .0000
7.1QOOO
3.3QOOO
1.9Q322
.976318
.988086
.201518
30.0000
7.10000
2.50000
1.16333
1 .61581
1 .28290
.287132
00312
BOD
6 DAY
MG/L
7 .00000
7. 100UO
3. 1 0000
1. 71285
1 .97292
1 . 10160
.296152
00910
CHLORIDE
CL
MG/L
31 .UOOO
10.0000
5.00000
10.2903
36.7163
6.06187
.589085
31 .0000
21 .0000
3.UUOUU
10.6152
19.0366
1.36310
.109867
30.0000
28.0000
5.00000
10.7833
30.5161
5.52688
.512539
Q053u
RESIDUE
TOT NFUT
Mfa/L
31 .0000
20.1000
.100000
5. 11838
22. 1092
1.70205
.913306
31 .0000
36.1000
. 1 OOUuO
6. 19351
71 .2052
8.13832
1 .36211
31 .QOQO
71.0000
1 .20000
11.9096
261 .719
16.1787
1 .08512
71/10/00
-------
STORET RETRIEVAL DATE 75/06/10
OUOOQOOO UOOOOOOOOOO
DATE*
FROM
TO
73/09/01
MONTH
73/10/00
71/02/01
MONTH
71/03/00
71/05/01
MONTH
71/06/00
71/06/01
MONTH
TIME OEpTH
OF
DAY FEET
NUMBER
MAXIMUM
MINIMUM
MEAN
VARIANCE
STAND OEV
COEF VAR
NUMBER
MAX IMUM
MINIMUM
MEAN
VAR 1 ANCE
STAND DEV
COEF VAR
NUMBER
MAX IMUM
MINIMUM
MEAN
VARIANCE
STAND DEV
COEF VAR
NUMBER
MAX IMUM
M I NIMUM
MEAN
VAR 1 ANCE
STAND DEV
COEF VAR
00671
pHOS-DIS
ORTHO
MG/L P
36.0000
.0110000
.OulOOQO
.0075277
.OU00721
.Q08S103
1 . 130S3
23.0000
.0320000
.OOluOOO
.OU90000
.0000610
.ouaoooo
.888693
26.0000
.0200000
.0010000
.01)91923
.0000265
.0051461
,bS9821
30.0000
.0300000
.0020000
.0090000
.0000305
,005521 1
.613162
U066C,
PHOS-TnT
MG/L p
36.UOOO
.356000
.003UOnO
.0829162
.0081575
.0919615
1 . 10912
23.UOHO
.3D9QnO
«0o2oonu
.018QBA8
.0012063
.06185^,6
1 .31872
28.0000
.210000
.0130000
.0629998
.0021718
.0166025
.739771
30.0000
. 1700DO
.0500000
.0863329
.0012376
.0351811
.1075?8
0.06US
ORG N
N
MG/L
36.0000
1 ,00000
.OUOOOoO
.3361 1 1
.U789113
.280970
.835916
2J.OOOO
1 .60000
. 1000UO
.273913
. 1 15652
.310076
1 .21155
28.0000
.500000
. 1 00000
.235711
.U161551
. 128277
.511208
3U.OOJO
1 .10000
. 100000
.533333
. 16781 6
.109653
.768101
006 18
N03-N
D1SS
MG/L
36.0000
• 1 13000
.00 10000
.0367199
.0001159
.021 1 152
.571566
23.0000
• 122000
.0030000
.0663910
.0017017
.0112862
.62 1891
28.0UOO
.600000
.020UOOO
. 181128
.U205755
.113112
.790625
30.0000
.73QUOO
.0100000
. 1 79666
.0103751
.200936
1 . 1 1839
00613
N02-N
DISS
MG/L
36, DOUG
.0070000
.0000000
.0021911
.0000019
.0013902
.633197
2 3 . 0 0 0 LI
.0350DOU
,0050000
.01 68695
.OQOOB6B
.0093 19 1
.552120
28.000U
.0320000
.0020000
.0123211
.0000126
.0065266
.529699
30.0000
,05700uO
.0020000
.01 iloon
.0001 169
.0108138
.750957
00610
NH3-N
TOTAL
MG/L
36.0000
.571000
.QOOUQOO
. 111172
.0231 131
.152030
1 .07163
23.0000
.716000
.0210000
.380013
,0659876
.256881
.675925
28.000U
.570000
.0000000
.211000
,0166969
. 136737
.638958
30.0000
.72UOOO
.0100000
. 167333
.0339161
.181161
1 . 10058
3221 1
CHLRPHTL
A UG/L
CORRECTS
36.0000
70.0000
3.0UOOCI
23.1*11
110. 101
20.2510
.873U98
3.00000
15.9000
9.7QOOO
12.1333
10.9136
3.3Q81 1
.272617
1 3.0000
11.600U
I .50000
10.0538
17.5111
1. 18162
•116221
17.0000
22.800U
5.1QOOO
12.2171
33.1B76
5.7B6B5
.17250*
32218
PtitoPhTN
A
Uu/L
31.0000
26.QOUO
1 .00000
B, 02911
18.3931
6.9s>652
.866379
3.UOOOU
2.10QOO
.OOUOOOO
1 .33333
1 .19333
1 .22202
.'16515
8.00000
l.bUUOO
1 .20000
2.85000
1 .77715
1 .33310
.167753
16.0000
8.8UOOO
.OOUOOOO
• 3.63121
5.13829
2.33201
.612208
71/07/00
-------
STORE! RETRIEVAL DATE 75/06/10
OUOOQUOO OOUOOOOOOOO
DATE
FROM
TO
71/07/01
MONTH
71/08/00
71/08/01
MONTH
71/09/00
71/09/01
MONTH
•
TIME DEPTH
OF
OAr FEET
NUMBER
MAXIMUM
MINIMUM
MEAN
VARIANCE
STAND DEV
COEF VAR
NUMBER
MAXIMUM
MINIMUM
MEAN
VARIANCE
STAND DEV
COEF VAR
NUMBER
MAXIMUM
MINIMUM
MEAN
VAN I ANCE
STAND UEV
COEF VAR
U0671
pHOS-DIS
OHTHO
MG/L P
31 .0000
.0260000
.0030000
.OUB8709
.QU00217
.00166Q1
.525319
31 .0000
.0360000
.U030DOO
.0131290
.0000722
.OU81999
.617113
31 .0000
.0639V99
.0020000
.0121613
.OuQ2070
.0113877
1 . 18307
G066S
PHOS-TOT
MG/L P
31 .0000
. 1 780(10
.0210000
.0616128
.001 1579
•0310566
.5527<;2
31 .00(10
. 123QHO
• 01300(10
.039U9A7
.UUU87S2
.0295811
.736690
31 .0000
.331000
.oiioono
.0636771
.OCI8U8R8
.0899376
1 .Q71S2
00*05
ORG N
N
MG/L
3 1 .OUUU
1. 10000
. 100000
.711933
.707182
.810911
1 . 13311
31 .0000
1 . 10000
. 100000
.161290
.1)581517
.21 1 768
.5211 12
31 .0000
1 .90000
. louooo
.116129
. 176731
.120391
1 .01025
00618
N03-N
DlSS
MG/L
31 .0000
1 . 13000
.OObOUOO
. 1 15061
.(J612137
•2&3161
1 .71725
31 .UUOO
1 .08000
.0250000
.216119
. 1 18661
•311172
1 .3979]
31 .OUUO
.910000
.02UOUOU
. 197096
.0662078
.257309
1 .3Q550
00613
N02-N
DISS
MG/L
3 1 . o o LI e
.137000
.UO lOOuO
.Q2U58ufc
.U007655
.0276680
1 .31137
31 .OOUO
.0230000
•UO lOouU
.U0770V ;
.00001 1 B
•U061663
. 8 3 8 7 ! H
31 .ooun
.0809999
. U 0 2 0 0 u 0
.01 20001)
.000209 1
.01 1161 1
1 .2051?
00610
NH3-N
TOTAL
MG/L
31 .OUUU
3.57000
.0000000
. 193226
,108996
.639528
3.30975
3 1 .0000
.330000
.0 100000
.0525801
.UOV2331
.0960891
1 .82718
3 1 .0000
1 .01000
.0 1UOOOU
. 137967
.0388730
.197162
1 .12905
3221 1
CHLRPHYL
A UG/L
CONKECTD
1 7.00UU
57.6000
3.60000
19.8117
188. 9u6
13-7113
.6*3711
17.0000
75.20UO
.0000000
1 1 .0112
131.695
20.81V3
1 .B8B33
1 6.UUUO
6 1 .8JuO
.0000000
15.1200
3(5.081
1 ;.7bu5
1.15111
32218
PHEOPHTN
A
UG/L
1 5.QOOU
1 1 .100U
• 20CIUOD
1.72666
13. 1993
3*63303
.760635
1 7. OOUO
71.QOOU
3. luooo
33.U11 1
619. 3BU
25.162V
.771219
1 6 .UOUU
69.3UUU
.OOUUOUU
21 .6b62
182. ^72
21 .9653
1 .01127
7t/10/00
-------
STORET RETRIEVAL DATE 7S/U4/06
72028 72029
DATE TIME DEPTH AZIMUTH DISTANCE
FROM OF FR SOUTH FR SOUTH
TO DAY FEET DEGREES FEET
73/09/17
73/09/17
73/09/17
73/09/17
71/05/22
71/05/22
71/05/22
7M/05/22
71/06/03
71/06/03
71/06/03
71/06/03
71/07/09
71/07/09
71/07/09
71/07/09
71/07/09
71/07/09
71/OB/ 12
71/08/12
71/08/12
71/08/12
71/08/12
71/08/12
71/08/12
71/08/12
71/09/01
71/09/01
71/09/01
71/09/01
01303
0007
0010
0020
0003
0007
0013
0030
0003
0007
0013
0030
0003
0007
0010
0016
0023
0030
0003
0007
0010
0013
0016
U02CI
0023
0026
0003
0007
0020
0030
OS3002 1290AC053002
11 32 10. D (JUS 00 30. U
GREEN BAY STUDY DNR STA I
55 WISCONSIN
LAKE MICHIGAN
000 10
IVATER
TEMP
CENT
18.0
1B.O
18.0
15. b
15.5
16.0
18. 0
17.5
14.5
25.0
21,0
22.0
22.0
21.0
23.0
22.0
22.0
21 .0
20.0
19.0
19,0
19.0
22.0
20.0
19.0
21K1S 21 1 1202
2 0026 FiET
00299 00078 00310 00312 00
DO TRANSP BOD BOD CHLO
PROBE SECCHI 5 DAY 6 0X1 c
MG/L METERS Mli/L MG/L Mb
4.0 0.1
1 1 .0
o.Q
6.0
a.B o.s
9.8
8.8
7.6
7.2 0.6
9.8
7.2
6.2
6.2 0.9
30. uL
1.9
3.3
2.9
2.6
b.7 0.6
1.5 1.9
3.6
3.1
3.0
2.9
2.8
2. a
7.2
b.7
6.5
6.0
DEPTH
OU53Q
RESIDUE
TOT NFLT
MWL
20
20
2b
053002 129UAC053002
11 32 to.ci oae oo 3o.o
6REEN BAY STUDY DNR STA 1
55 HIISCONSIN
LAKE MICHIGAN
21»!S
2
DATE
FROM
TO
73/09/17
71/05/22
71/06/03
71/07/09
71/08/12
71/09/01
TIME DEPTH
OF
DAY FEET
0007
0007
0007
0007
0007
0007
00671
pHOS-OIS
OKTHO
MG/L P
0.011
0.017
0.012
0.026
0.011
O.OQ9
006&C, Q06Q5
PHOS-TOT
MG/L p
0.217
0.210
0.170
0.111
0.076
0.111
ORG
N
N
MG/L
1
0
0
1
0
0
.000
.100
.700
. 100
.600
.800
006 IB
N03-N
DISS
MS/L
0.
0.
0.
0.
0.
0.
03
16
28
07
07
12
00613
N02-N
OISS
MG/L
0.002
0.016
O.Olb
0.015
0.012
0.006
00610
NH3-N
TOTAL
MG/L
0.101
U.32U
0.62U
3.5/U
0.28U
0. 110
21 1 1202
OL26 FEET DEI
3221 1
CHLKPHYL
A UG/L
CORRECTD
51 .UO
13. JU
17.10
27.00
75.20
31.20
32218
PHEOPHTN
A
UG/L
26.00
1 .bO
6.1U
7.9U
31.70
11.90
-------
STORE! RETRIEVAL DATE 75/04/06
72028 72029
DATE TIME DEPTH AZIMUTH DISTANCE
FROM OF FR SOUTH FR SOUTH
TO DAT FEET DEGREES FEET
73/09/17
73/09/17
73/09/17
73/09/17
71/05/22
7H/OS/22
71/05/22
71/05/22
71/06/03
74/04/03
71/06/03
71/06/03
71/07/09
71/07/09
71/07/09
71/07/09
71/08/12
71/06/12
71/08/12
71/09/01
71/09/01
71/09/01
71/09/01
0003
0007
0010
0016
0003
0007
0010
0016
0003
0007
0010
0020
0003
0007
0010
0020
0003
0007
0010
0003
0007
0010
0023
053U03 1290AC05300J
11 32 25.0 008 00 I1.D
GREEN BAY STUDY DNR STA 2
55 MSCUNStN
LAKE MICHIGAN
00010
,
-------
STORET RETRIEVAL DATE 75/06/06
053001 1290AC0530Q1
11 33 08.0 087 SI 53.0
GREEN BAY OPEN (VATER DNR STA 3
55 WISCONSIN
LAKE MICHIGAN
72028 72029
DATE TIME DEPTH AZIMUTH DISTANCE
FROM OF FR SOUTH FR SOUTH
TO DAY FEET DEGREES FEET
73/09/17
7t/OS/22
7t/OS/22
7M/05/22
7t/06/03
7t/06/03
71/06/03
71/07/09
71/07/09
71/07/09
71/07/09
71/08/12
71/08/12
71/08/12
71/OV/OM
71/09/Ot
71/09/01
0003
0003
0013
0023
0003
0013
0023
0003
0010
0016
0023
0003
0013
0023
0003
0010
0023
00010
TEMP
CENT
IS.5
11.5
1 1 .5
17.5
16.5
IS.O
22.0
21.0
20.0
20.0
20.0
20.0
19.0
1 V .U
le.o
18.0
00299
tiO
PROBE
MG/L
8.8
v.o
10.0
/.U
7.6
8.5
3.5
3.1
3.1
3.5
1.1
1.1
1.6
1.5
6.2
6.5
21H.IS 211 1202
2 OU26 FEET
00078 00310 00312 00
TRANSH 600 600 CHLO
SECCHI 5 DAY 6 DAY C
METERS M&/L MG/L Mb
7. 1
7.0
O.H
o.e
o.a
0.1
DEPTH
0053Q
RESIDUE
TUT NFLT
MG/L
053UOb 1290AC05300&
It 32 55.0 087 58 56.0
GREEN uAY OPEN WATER UNK STA 3A
55 WISCONSIN
LAKE MICHIGAN
21WIS
DATE
FROM
TO
/02/M
TIME
OF
DAY
>
DEPTH
FEET
0003
72028
AZJMUTH
FR SOUTH
DEGREES
72029
DISTANCE
FR SOUTH
FEET
QOOlO
WATER
TEMP
CENT
00299
DO
PROBE
Mfa/L
9.6
2
00078
TRANSP
SECCHI
METERS
00310
BOD
5 DAY
MG/L
21 1 1202
0026 FEET
00312 00
BOD CHLO
6 DAY C
MG/L Mb
DEPTH
0053Q
RESIDUE
TUT NFLT
M6/L
-------
STORET RETRIEVAL DATE 75/06/06
72028 72029
DATE TIME DEpTH AZIMUTH DISTANCE
FROM OF FR SOUTH FR SOUTH
TO DAr FEET DEGREES FEET
73/09/17
73/09/17
73/09/17
73/09/17
71/05/22
71/05/22
71/05/22
71/05/22
71/06/03
71/06/03
71/06/03
71/06/03
71/06/03
71/07/09
71/07/09
71/07/09
71/07/09
71/08/12
71/08/12
71/08/12
71/08/12
71/09/01
71/09/01
71/09/01
71/09/01
0003
0007
0016
0026
0003
0007
0013
0023
0003
0007
0010
0020
0026
0003
0007
0013
0026
0003
0007
0016
0033
0003
0007
0013
0033
0530U6 1290ACQS3006
11 33 53.0 087 5* 21.0
4REEN BAY OPiN WATER DNR STA 1
55 WISCONSIN
LAKE MICHIGAN
000,10
«ATER
TEMP
CENT
16.0
16.0
16.0
15.0
16. 0
13.0
1 1 .0
17.5
16.0
15.0
11.0
22.0
19.0
18.0
20.0
20,0
18.0
20.0
18.0
18.0
00299
DO
PROaE
MG/L
6.6
6.2
b.O
V.5
9.5
9.2
10.2
7.2
7.6
9.5
9.7
5.1
1.0
3.7
6.9
6.2
1.6
9.1
6.7
6.8
21*15
2
00078 00310
TRANSP BOD
SECCHI 5 DAY
METERS MG/L
0.3
6.1
0.9
7.0
0.6
0.9
6.5
0.8
5.3
0.1
1.9
2111202
0026 FEET DEPTH
00312 OU9SQ 0053U
BOD CHLORIDE RLS1DUE
6 DAY CL TOT NFLT
MG/L MG/L MG/L
17
1U 31
11.0 15 17
9 7
16 21
17 31
0530J6 l29UACOb3006
11 33 53«0 087 59 21.0
SREEN BAY OPEN WATER DNK STA 1
55 WISCONSIN
LAKE MICHIGAN
21*15
2
DATE
FROM
TO
73/09/17
71/05/22
71/06/03
71/07/09
71/08/12
71/09/01
TIME DEPTH
OF
DAY FEET
0007
0007
0007
0007
01)07
0007
00671
pHOS-DIS
OKTHO
MG/L P
0.008
0.012
0.012
0.006
0.011
0.011
0046=,
PHOS-ToT
MG/L P
0.239
0.095
0. 160
0.073
0.058
0. 168
00605
ORG N
N
M6/L
0.8DO
0.500
1 . 100
0.600
0.70U
1.200
00618
M03-N
D1SS
MG/L
0.02
0.18
U.36
O.I 1
0.12
0.08
00613
N02-N
DISS
MG/L
0.002
0.020
0.025
0.011
0.015
0.012
00610
NH3-N
TOTAL
MG/L
0.260
0.260
0.72U
0.200
0.060
U.530
211
0026
3221 1
CHLRPHYL
A UG/L
CORRECTU
19.00
21 .7U
26.60
5.00
5.20
1202
FEET DEI
322|8
PHEUPHTN
A
Uto/L
19.00
1 .20
1 1 .20
71 .UU
69.30
-------
STORET RETRIEVAL DATE 75/06/06
053007 129UAC053U07
41 31 H8.0 087 58 37.0
(.KEEN BAY OPEN WATER ON* STA b
S5 WISCONSIN
LAKE MICHIGAN
72028 72029
DATE TIME DEpTH AZIMUTH DISTANCE
FROM OF FR SOUTH FR SOUTH
TO DAT FEET DEGREES FEET
73/OV/17
73/09/J7
73/09/17
7S/05/22
71/05/22
7«(/05/22
7S/06/03
71/06/03
71/06/03
71/07/09
71/07/09
71/07/09
71/08/12
71/08/12
71/08/12
71/08/12
71/08/12
71/09/01
71/09/01
71/09/01
0003
0007
0010
0003
0013
0032
0003
0010
0016
0003
0016
0030
0003
0007
0013
0020
0026
0003
0010
0020
000 lQ
WATER
TEMP
CENT
15.0
15.0
12.0
1 1 .0
1U.5
11.5
11.5
11.0
21.0
17.0
17.0
18.5
18.0
17.0
16.0
16.0
19.0
17.0
J7.U
00299
DO
PROBE
MG/L
8.7
8.7
11.6
11.1
1 1 .0
10. b
10.3
10. M
6.7
5. 1
3.1
6.7
5.7
1.8
2.6
2. a
8.7
6.7
6.0
21 A IS 2111202
2 0026 FEET
0007S O0310 00312 00
TRANSp tJOD BOD CHLO
SECCHI 5 DAY 6 DAY C
METERS MC./L M&/L Mt,
0.5
5.5
1 .3
0.9
1 .2
1 ,2
o.t)
DEPTH
0053Q
RtSlOUE
TUT NFLT
MG/L
053007 H290ACOb3007
11 3H 18.U OB7 5B 37.U
GStEN BAY OPtN WATER UNK STA 5
55 WISCONSIN
LAKE MICHIGAN
DATE
FROM
TO
/09/n
TIME
OF
DAY
r
DEpTW
FEET
0007
00671
PHJS-DIS
OKTHO
MG/L P
0.005
OQ66i;
PHOS-TOT
MG/L P
0.091
Q06Q5
ORG N
N
MG/L
0.6QO
00618
N03-N
DISS
MG/L
0.001
21*1!
2
00613
N02-N
UISS
MG/L
0.001
&
OU610
NH3-N
TOTAL
MG/L
0.072
21 1
OU26
32211
CHLRPHYL
A UG/L
COKRECTU
31.00
1202
FEET DL
3221B
PHEOPHlN
A
Ut,/L
12. Ou
-------
STORET RETRIEVAL DATE 75/04/06
053008 t290ACOS3008
HI 31 M.O 087 57 26.0
GREEN BAY OPEN WATER DNR STA 5A
55 WISCONSIN
LAKE MICHIGAN
72Q28
DATE TIME DEPTH AZIMUTH
FROM OF FR SOUTH
TO DAY FEET DEGREES
72029 OOG10
DISTANCE WATER
FR SOUTH TEMP
FEET CENT
71/02/19
71/02/19
OU03
0010
00299
00
PROBE
MG/L
9.2
7.8
21*15
2
2111202
0006 FEET
DEPTH
OQ07B 00310 00312 00910 00530
TRANSP BOD BOD CHLORIDE RESIDUE
SECCHI 5 DAY 6 DAY CL TOT NFLT
METERS MG/L MG/L Md/L MG/L
-------
STORET RETRIEVAL DATE 75/06/06
05,3009 429UAC053009
44 3b 46.0 087 59 46.0
GREEN BAY OPEN WATER ONK STA 6
55 IVISCUNSIN
LAKE MICHIGAN
21V, IS 2111202
DATE TIME
FROM OF
TO DAY
73/09/17
73/09/17
74/05/22
74/05/22
74/05/22
74/06/03
74/06/03
74/06/03
74/07/09
74/07/09
74/07/09
74/08/12
74/08/12
74/08/12
74/09/04
74/09/04
74/09/04
72028 72029
DEPTH AZIMUTH DISTANCE
FR SOUTH FR SOUTH
FEET DEGREES FEET
0003
0007
0003
0007
0010
0003
0007
0010
0003
0007
0010
0003
0007
0013
0003
0007
0010
0001Q
HATER
TEMP
CENT
14.5
16.0
16.0
1 1.5
15.0
15.0
23.0
19.0
19.0
19.0
19.0
18. 0
00299
DO
PROBE
MG/L
9.2
11.3
11.3
9.4
1U.U
10.2
a. 2
5.3
7.5
7.7
10.2
7.6
2
0007fi
TRANSP
SECCHI
METERS
0.6
O.V
0.9
0.9
1 .0
1 .U
UU09 FEET DEPTH
OU310 00312 OU9tu UUS30
dOD riOD CHLOK1DE RESIDUE
5 OAY 6 DAY CL TUT NFLT
MG/L MG/L Mb/L MG/L
3.4 11
7.6 7 11
9.4 10 10
7.8 13 4
4.1 14 3
6.5 12 10
0&3009 4290AC053009
44 35 46.0 Ob7 59 46.0
GREEN BAY OPEN *ATER ONR STA 6
55 WISCONSIN
LAKE MICHIGAN
2 IV. 1 S
2
DATE TIME
FROM OF
TO DAY
73/09/17
74/05/22
74/06/03
71/07/09
74/08/12
74/09/04
DEPTH
FEET
0007
0007
0001
0007
0007
0007
00671
PHOS-DIS
ORTHO
MG/L P
0.006
O.OQ9
0.013
0.005
0.014
0.010
OU66^
PHOS-TOT
MG/L P
0.071
0.08U
0. 100
0.068
0.028
U.076
Q0605
URS N
N
MG/L
0.7QO
0.300
1 .000
0.600
0.6QO
0.6QQ
00618
N03-N
DlSS
MG/L
0.001
0.03
0.05
0.01
0.06
0.03
00613
N02-N
DlSS
MG/L
0.001
0.014
0.012
0.010
0.007
0.003
00610
NH3-N
TOTAL
MG/L
0.025
U. 120
0. 160
0.06U
0.010K
0. 1 1U
21 1
U009
3221 1
CHLRPHYL
A UG/L
CORRECTD
21 .UO
12. bO
B.HU
26.00
o.uo
6.70
1202
FEET DEI
32216
PHEOPHTN
A
UG/L
12.00
4.2CI
7. 60
70. VO
29. 2U
-------
STORE! RETRIEVAL DATE 75/06/06
72Q28 72029
DATE TIME DEpTH AZIMUTH DISTANCE
FROM OF FR SOUTH FR SOUTH
TO DAT FEET DEGREES FEET
73/09/18
73/09/18
73/09/18
73/09/18
71/02/19
71/02/19
71/02/19
71/05/22
71/05/22
71/05/22
71/06/03
71/06/03
71/06/03
71/06/03
71/07/09
71/07/09
71/07/09
71/07/09
71/08/12
71/08/12
71/08/12
71/08/12
71/09/01
71/09/01
74/09/01
71/09/01
0003
0007
0010
0030
0003
0007
0016
0003
0007
0016
0003
0007
0010
0020
0003
0007
0013
0020
0003
0007
0010
0020
0003
0007
0010
0020
Q53010 1290AC0530IO
It 35 00.0 087 56 SB.O
GREEN BAY OPEN »ATER DNR 5TA 7
55 WISCONSIN
LAKE MICHIGAN
00010
ATER
TEMP
CENT
15.0
15.0
15.0
1 .0
13.0
13.0
12.0
13. b
13. 5
13.0
22.0
21 .0
16.0
IV. 0
19.0
18.0
20.0
17.0
17.0
00299
00
PROBE
MG/L
9.0
8.0
7.7
7.3
7.0
7.0
1 1 .7
1 1 .7
10. 1
10.1
10.6
10.0
8.2
7.5
2.7
7.9
7.6
6.2
V.8
7.1
7.1
21»1S 2111202
2 0009 FEET
00078 00310 00312 00
TRANSP SOD BOD CHLO
SECCH1 5 DAT 6 DAY C
METERS MG/L MG/L MG
o.e
1.0
2.3
1 .0
12.0
1 .2
8.6
1.2
7.0
1.5
1.1
0.9
1.5
DEPTH
40 0053Q
CHLORIDE RESIDUE
TOT NFLT
M6/L
28
13
0.1
053010 1290AC053010
11 3S> 00.0 OH7 56 58-0
GREEN BAY OPEN WATER DNR STA 7
55 WISCONSIN
LAKE MICHIGAN
21*15,
2
DATE
FROM
TO
73/09/18
71/02/19
74/05/22
71/06/03
71/07/09
71/08/12
74/09/04
TIME DEPTH
OF
DAY FEET
0007
0007
0007
0007
0007
0007
0007
00671
PHOS-DIS
ORTHO
MS/L P
0.006
0.007
0.010
0.009
0.007
0.018
0.010
0066?
PHOS-ToT
MG/L p
0.101
0.060
0.073
0.060
0.06b
o.oia
O.O'I
00605
ORG N
N
MS/L
Q.IOO
0.100K
0.100
0.800
U.5QO
0.700
0.5UO
OU618
N03-N
oiss
MG/L
0.03
0.12
0. 15
0.10
0.01
U.01
0.02
00613
N02-N
D1SS
MG/L
0.002
0.021
0.01 1
0.010
0.008
0.005
0-003
00610
NH3-N
TOTAL
MS/L
0.126
0.59V
0.360
0.110
0.010K
Q.010K
0-070
21 1 1202
0009 FEET OE
3221 1
CHLRPHYL
A US/L
CORRECTS
27.00
12.30
9.10
17.30
0.80
0-UQ
322|8
PHEOPHTN
A
US/L
10.00
2.10
3.00
U.60
12.50
15-10
-------
STORET RETRIEVAL DATE 75/06/06
D-ATE TIME
FROM OF
TO DAY
73/09/18
73/09/18
73/09/18
73/09/18
73/09/18
71/02/18
71/02/18
71/02/18
71/02/18
71/OS/22
71/05/22
71/05/22
71/06/03
71/06/03
71/06/03
71/07/09
71/07/09
71/07/09
71/07/09
71/08/12
71/08/12
71/08/12
71/09/01
71/09/01
71/09/01
DEPTH
FEET
0003
0007
0010
0020
0030
0003
0007
0010
0020
0003
0013
0030
0003
0013
0029
0003
0013
0016
0020
0003
0010
0020
0003
0010
0023
72Q28 72Q29
AZIMUTH DISTANCE
FR SOUTH FR SOUTH
DEGREES FEET
15.0
063011 1290ACU53011
11 36 16.0 087 55 12.U
GREEN BAY OPEN WATER DNR STA 6
56 WISCONSIN
LAKE MICHIGAN
21*15
2
OOOlO
WATER
TEMP
CENT
00299
00
PROBE
MG/L
00078
TRANSp
SECCH1
METERS
00310
BOD
-------
O O
f —
o* a:
O 3
O -I
1*1 Q
o o
O 00
o i/i i—
^j o
a: •—
3- —
> X
O O
O -I
03 uJ O
13 O_ IJ
O l/l \
ft "» 03 —
-O I < X
o m t- ,3
O X O E
• a: ji < -. cr a. — i/)
' >3 i/> _l (M"M r*.(/)XQC
— Z U1 _J
O I (/I X
O fM « 13
o o a E
•o I in
o
-------
STORET RETRIEVAL DATE 75/06/06
72028 72029
DATE TIME DEpTH AZIMUTH DISTANCE
FROM OF FR SOUTH FR SOUTH
TO DAY FEET DEGREES FEET
71/02/18
71/02/18
71/06/03
71/06/03
71/06/03
71/06/03
71/07/09
71/07/09
71/07/09
71/08/12
71/08/12
71/09/01
71/09/01
0006
0016
0003
0007
0010
0016
0003
0007
0016
0003
0007
0003
0007
053011 l290ACOS301't
11 37 08.0 087 52 12>0
GREEN BAY OPEN WATER ONR STA 8C
55 WISCONSIN
LAKE M1CHI.GAN
oooio
«AT£R
TEMP
CENT
0.8
0.8
15.0
15.0
11.0
21.0
23.5
23.0
21 .0
21.0
18.0
.17.0
00299
00
PROgE
MG/L
1.3
3.H
1Q.8
10. 1
9.2
9.6
9.2
8.6
10.6
10.6
8.6
9.0
21M5
2
0007B 00310
TRANSP BOD
SECCHI 5 OAY
METERS MG/L
1 .0
0.9
7.1
0.6
7.1
H.9
21 1 1202
0019 FEET
00312 00
BOD CHLO
6 DAY C
MG/L Mb
9.8
DEPTH
0053Q
RESIDUE
TOT NFLT
MG/L
12
12
15
8
IB
11
I
u
OS3U11 1290ACOS3011
11 37 08.0 087 52 12.U
GREEN BAY OPEN WATER DNK STA 8C
55 WISCONSIN
LAKE MICHIGAN
2 1 U I S
2
DATE
FROM
TO
7t/06/03
71/07/09
7H/08/I2
7M/09/OM
TIME DEPTH
OF
DAY FEET
0007
0007
0007
0007
00671
PHOS-DIS
ORTHO
MG/L P
O.OOS
0.008
0.015
0.010
0066%
PHOS-TOT
MG/L P
0. 100
U.087
0.095
0.067
00605
ORG N
N
MG/L
0.8QO
0.500
0.700
0.300
00618
N03-N
DISS
MG/L
U.22
0.03
0.01
0.09
00613
N02-N
01SS
MG/L
0.019
0.010
0.007
O.OU3
00610
NH3-N
TOTAL
MG/L
0.170
0.210
0.010K
U.090
21 1
OU19
32211
CHLRPHYL
A UG/L
CORRECTD
18.00
21.20
13. 30
2.bO
1202
FEET DEI
32218
PHEOPHTN
A
UG/L
b.50
3.3U
bB.bO
53. SO
-------
STORET RETRIEVAL DATE 75/06/06
72028 72029
DATE TIME DEPTH AZIMUTH DISTANCE
FROM OF FR SOUTH FR SOUTH
TO DAY FEET DEGREES FEET
73/09/18
73/09/ 18
73/09/18
73/09/18
71/02/18
7S/02/18
71/02/18
71/02/18
71/02/18
71/02/18
71/0b/20
71/05/20
71/05/20
71/06/03
71/06/03
71/06/03
71/06/03
71/07/09
71/07/09
71/07/09
71/08/12
71/08/12
71/08/ 1 2
71/08/12
71/09/01
71/09/01
71/09/01
0003
0007
0010
U020
0003
0007
0013
0020
0023
0026
0003
0010
0020
0003
0010
0020
0030
0003
0016
U030
0003
0013
0023
0026
0003
0013
0030
OS30I5 129UACU53015
It 39 22.0 087 53 19.D
GREEN BAY OPEN WATER ONR STA 9
55 WISCONSIN
LAKE MICHIGAN
21»1S 211 1202
2 OU26 FEET DEPTH
Q0010
IATER
TEMP
CENT
15.5
IS.O
15. 0
o.e
.0
.u
.3
.0
.1
9.0
9.0
6.0
12. b
12. &
12. 0
1 1 .0
22,0
2U.U
11.0
I?. 5
IV. b
19.0
Ib.U
19.0
18. D
17.0
00299
DO
PKOBE
MG/L
9.8
9.1
8.6
17.6
lb.0
10.7
a.s
8.0
8.3
1 1 .1
1 1 .3
1 l.B
10.1
1U.2
10.0
9.3
8.b
b.9
b.2
a.t
8.3
8.1
2. a
H.I
7.3
7.2
00078 00310 00312 ODVtO
TRANSP BOD bOO CHLURlOt
SECCHI b OAT 6 DAT CL
METERb MG/L MG/L Mb/L
1 .U
1.3
2. 1 9
3.1 17
1 .2
1 .6
1 .8
1.8
1 .S.
OOb3Q
RESIDUE
TUT NFLT
Mii/L
18
0.5
9
2IAIS
2
DATE
FROM
TO
73/09/18
71/02/18
71/02/18
TIME DEpTH
OF
DAY FEET
0007
0007
0023
U0671
pHOS-DIS
OKTHO
MG/L P
0.008
0.002
0.007
0066^
PHOS-ToT
MG/L P
U.OS8
0.011
U.017
00605
ORG N
N
MG/L
0.100
0.200
0.1QOK
00616
N03-N
01SS
MG/L
0.05
U.02
U.I1
00613
N02-N
UISS
MG/L
0.003
O.U08
U.026
00610
NH3-N
TOTAL
Mfi/L
0. 126
u.oav
0.611
Q53Q15 1290AC053UI5
11 39 22.0 087 b3 19.0
GREEN BAY OPEN WATER DNK STA y
5b IIISCONSIN
LAKE MICHIGAN
2111202
Uu26 FLtT DEP
32211 32218
CHLRPHKL PHEOPHlN
A UG/L A
COhRECTO UG/L
5| .00
25.00
-------
STORET RETRIEVAL DATE 75/06/06
72028 72029
DATE TIME DEPTH AZIMUTH DISTANCE
FROM OF FR SOUTH FR SOUTH
TO DAY FEET DEGREES FEET
00010 00299
AATER DO
TEMP PROBE
CENT MG/L
71/02/18
7H/02/18
7M/02/18
0003
0020
0026
1.0
1.5
1.6
16.t
8.8
6.3
053016 H290ACQ530I6
Ml 10 16.0 087 52 39.0
GREEN BAY OPtN WATER DNR STA 9A
SB WISCONSIN
LAKE MICHIGAN
21UIIS
2
2111202
0026 FEET
BEPTH
00076 00310 00312
TRANSp BOD BOD
SECCH1 S DAY 6 DAY
METERS MG/L MG/L
00910 0063Q
CHLORIDE RESIDUE
CL TOT NFLT
MG/L
-------
STORE! RETRIEVAL DATE 75/06/06
72028 72029
DATE TIME DEpTH AZIMUTH DISTANCE
FROM OF pR SOUTH FR SOUTH
TO DAY FEET DEGREES FEET
74/02/1S
71/02/18
71/02/18
71/05/20
71/05/20
71/05/20
71/05/20
71/06/01
71/06/01
71/06/01
71/06/01
71/06/01
71/07/09
71/07/09
71/07/09
71/07/09
71/08/13
71/08/13
71/08/13
71/08/13
71/08/13
71/09/01
71/09/01
71/09/01
71/09/01
0007
0020
0026
0003
0007
0013
0030
0003
OU07
QUIU
0020
0030
0003
0007
0013
0030
0003
0007
0010
0023
0026
0003
0007
0015
0030
053017 1290ACOS30I7
11 39 11.0 087 51 OS.O
GREEN BAY OPEN HATER OUR STA 9u
55 WISCONSIN
LAKE MICHIGAN
00010
SATER
TEHP
CENT
1 .5
0.9
I .2
B. s
8.5
8.5
8.0
12.0
12.0
12.0
10.5
22.0
21 .0
12.5
20.0
20.0
19.5
16.0
18.0
18.0
18.0
00299
00
PRObE
MG/L
5.7
5.1
3.3
1 1 .8
1 1 .U
1 1 .6
11.8.
9.6
9.6
9.1
7.2
8.5
8.0
1.3
8.1
7.9
7.5
5.9
/.9
7.2
5.9
2 1 f. I S
2
00078 00310
TRANSp 80p
SECCHI b UAY
METERS MG/L
2.1
1 .2
1.6
1.6
1.9
1.8
1.9
1 .5
3.3
21 1 1202
0022 FEET DEPTH,
00312 OQ9io OOS3Q
BOO CHLORIDE RESIDUE
6 DAY CL TOT NFLT
MG/L Mb/L MG/L
17 1
t.S 10 9
8 2
9 I
9 O.IK
6 6
053017 4290ACQ53017
11 39 11.0 067 51 05.0
GREEN BAY OPEN HATER CNR STA 9e
55 WISCONSIN
LAKE MICHIGAN
21H1S
2
DATE TIME
FROM OF
TO DAY
71/02/18
71/05/20
71/06/01
71/07/09
71/08/13
71/09/01
DEPTH
FEET
0007
0007
0007
0007
0007
0007
00671
PHOS-DIS
ORTHO
MG/L P
0.008
0.001
0.010
0.008
0.010
0.009
006Ai;
PHOS-ToT
MG/L p
0.016
0.077
0.060
0.012
0.011
0,033
00605
ORG N
N
MG/L
O.IOOK
0.300
0.200
0.300
0.30U
0.100
00618
N03-N
D1SS
MG/L
0.10
0.06
O.US
0.03
0.06
0.10
00613
N02-N
DISS
MG/L
0.02C
0.007
0.008
0.008
0.005
0.003
00610
NH3-N
TOTAL
MG/L
0.598
0. 160
U.06U
0.1 10
0.01UK
0.020
211
0022
32211
CHLRPHYL
A OG/L
CORRECTD
12.60
9.10
1 1 .30
0.00
3.30
1202
FEET DEPTH
32218
PHEOPHTN
A
OG/L
1.00
1 .80
11.20
18. Ill
-------
STORET RETRIEVAL DATE 75/06/06
72Q28 72029 OOQiO
DATE TIME DEpTH AZIMUTH DISTANCE «»ATER
FROM OF FR SOUTH FR SOUTH TEMP
TO DAY FEET DEGREES FEET CENT
7H/02/18
7H/02 '18
0003
0023
00299
DO
PROBE
MG/L
1B.Q
H.O
053018 H29UAC05301S
<4H 38 59.0 087 H9 1t.0
GREEN BAY OPEN WATER DNR STA 9C
55 WISCUNSIN
LAKE MICHIGAN
2II0IS
2
2111202
0022 FEET
DEPTH
00078 00310 Q0312 009<40 00530
TRANSP BUD bOO CHLOKIOt RESIDUE
SECCHI 5 DAY 6 DAY CL TUT NFLT
METERS M&/L MCi/L MWL MG/L
053019 M290ACO&3019
SI 39 06.0 087 S9 &8.0
GREEN BAY OPEN flATER UNR STA 9tB
SB WISCONSIN
LAKE MICHIGAN
u>
I
DATE
FROM
TO
71/02/18
7M/02/18
71/02/18
TIME DEPTH
OF
DAY FEET
0003
0013
0020
72028
AZIMUTH
FR SOUTH
DEGREES
72029
DISTANCE
FR SOUTH
FEET
00010
tiATEK
TEMP
CENT
0.7
0.8
1 .5
00299
DO
PROBE
Mb/L
It.Q
10.8
2.6
2 1 V. I S
2
00074 00310
TRANSP SOU
SECCHI 5 DAY
METERS MG/L
21 1 1202
JU19 FEtl
00312 Ou
BOD CHLU
6 DAY C
MG/L MG
UtpTH
OOS30
RESIDUE
TOT NFLT
MG/L
-------
STORET RETRIEVAL DATE 75/06/06
72028
DATE TIME DEpTM AZIMUTH
FROM OF FR SOUTH
TO DAY FEET DEGREES
73/09/17
73/09/17
71/02/19
71/02/19
71/05/22
71/05/22
71/04/03
71/06/03
71/07/09
71/08/12
71/08/12
71/09/01
0003
0007
0003
0007
0003
0007
0003
0007
UQ03
0003
0010
0003
053020 1290ACU53U2U
11 32 1U.O 087 59 00.D
GREEN BAY OPEN HATER DNK STA I
55 WISCONSIN
LAKE MICHIGAN
2 1 K 1 S
72029
DISTANCE
FR SOUTH
FEET
000 10
ftATER
TEMP
CENT
00299
on
PROBE
MG/L
2
00078
TRANSP
SECCH1
METERS
OU310
BOD
b DAY
MG/L
21 1 12U2
OU06 FEET
00312 00
BOD CHLO
6 OAY C
MG/L MG
DEPTH
17.5
5.2
0.1
1 .0
Ib.S
lb.0
16. S
16. S
23.0
22. S
22. b
19.0
10
10
8
V
6
6
1
6
6
b
. 1
• 1
.8
.3
• 2
*2
.2
.9
.7
.S
0
0
0
0
0
.7
.6
.8
.1
.3
7.1
6.1
18
OUS3Q
RESIDUE
TOT NFLT
MG/L
60
bl
00671
DATE TIME DEpTH pHOS-DIS
FROM OF ORTHO
TO DAY FEET MG/L f
73/09/17
71/02/19
0007
0007
0.009
0.032
Ob3020
-------
STORE! RETRIEVAL DATE 75/06/06
72028 72029
DATE TIME DEpTH AZIMUTH DISTANCE
FROM OF FR SOUTH FR SOUTH
TO DAY FEET DEGREES FEET
73/09/17
73/09/17
71/02/19
71/02/19
71/05/22
71/05/22
71/06/03
71/06/03
71/07/09
71/07/09
71/08/12
71/08/12
71/09/01
71/09/01
0003
0007
0003
0007
0003
0010
0003
0010
U003
0010
0003
0010
0003
0007
053021 1290ACOS302I
11 32 03.U 067 57 05.0
GREEN BAY OPEN WATER DNK STA
55 WISCONSIN
LAKE MICHIGAN
QOQlO
dATER
TEMP
CENT
17.0
15.5
lb.0
16.5
16.5
21.0
22.5
22.0
22.0
19.0
18.0
00299
DO
PROBE
MG/L
1.2
9.8
8.9
11.1
10.6
7.1
7.5
8.2
3.2
7.8
7.8
8.1
6.9
21«IS 2111202
2 0006 FEET
00078 00310 00312 OU
TRANSP BOD B°D CHUU
SECCHI 5 DAY 6 DAY C
METERS MG/L MG/L MG
0.1
1.6
0.9
0.8
0.9
0.6
0.3
OEPTH
00530
RESIDUE
TOT NFLT
MG/L
32
053021 1290ACQ53021
11 32 03.0 087 57 05*0
GREEN BAY OPEN WATER DNR STA
55 WISCONSIN
LAKE MICHIGAN
00671 00661;
DATE TIME DEpTH pHOS-DIS PHOS-ToT
FROM OF ORTHO
TO DAY FEET MG/L P MG/L p
2 1 V. I S
2
00605
ORG M
N
MG/L
00618
N03-N
DISS
MG/L
00613
N02-N
DISS
MG/L
00610
NH3-N
TOTAL
MG/L
21 1
0006
3221 1
CHLRPHYL
A UG/L
CORRECTD
1202
FEET OE,
32218
PHEOphTN
A
UG/L
73/09/17
D007
0.023
0.251
0.100
0.01
0.001
0.325
61 .00
1 1 .OU
-------
STORET RETRIEVAL DATE 75/06/06
053022 1290AC053022
11 32 27.0 087 56 02.0
GRLEN BAY OPEN WATER ONR STA 12
55 WISCONSIN
LAKE MICHIGAN
72028 72029
DATE TIME OEpTH AZIMUTH DISTANCE
FROM OF FR SOUTH FR SOUTH
TO DAY FEET DECREES FEET
73/09/17
73/09/17
71/02/19
71/02/19
71/05/22
71/05/22
71/05/22
71/06/03
71/06/03
71/06/03
71/07/09
71/07/09
71/07/09
71/08/12
71/08/12
71/08/12
71/09/01
71/09/01
71/09/01
0003
0007
0003
0007
0003
0007
0010
0003
0007
0010
0003
0007
0010
0003
0007
0010
0003
0007
oni n
00671
DATE TIME DEPTH pHOS-DIS
FROM OF OKTHO
TO DAY FEET MG/L P
73/09/17
71/02/19
71/05/22
71/06/03
71/07/09
71/08/12
71/09/01
0007
0007
0007
0007
0007
0007
0007
0.006
0.007
0.016
0.001
0.007
0.022
0.061
00010
MTER
TEMP
CENT
00279
DO
PROSE
MG/L
21V, IS
2
00078
TRANSP
SECCH1
METERS
00310
BOD
5 DAY
M&/L
21 1 1202
OOU9 FEET
00312 OO
SOD CHLO
6 DAY C
MG/L MG
16.0
18.0
DEPTH
7.1
0.7
1 .3
Ib.B
15. 5
11.5
17.0
17.0
21.5
23.0
22.0
22.0
19.0
12.8
6.2
11.1
11*1
10.0
10.0
9.8
9.7
9.3
a. 2
8.2
10.0
0.9
0.9
0.6
1.3
8.6
8. 1
6.5
5.7
9.8
7.0
18
13
11
15
17
21
CJb3U22 1290ACUS3U22
11 32 27.0 0
-------
STORE! RETRIEVAL DATE 75/04/06
72028 72029
DATE TIME DEPTH AZIMUTH DISTANCE
FROM OF FR SOUTH FR SOUTH
TO DAr FEET DEGREES FEET
73/09/17
73/09/17
71/02/19
71/02/19
71/02/19
71/05/22
-•1/05/22
71/05/22
71/04/03
71/04/03
71/04/03
71/07/09
71/07/09
71/07/09
71/08/12
71/08/12
71/08/12
71/09/01
71/09/01
71/09/01
0003
0007
0003
0007
0010
0003
0007
0010
0003
0007
0010
0003
0007
0010
0003
0007
0010
0003
0007
0010
14.0
053023 1290AC053023
11 33 01.0 087 57 OB.O
GKEEN BAY OPtW WATER UNR STA 13
55 WISCONSIN
LAKE MICHIGAN
21K1S
00010
«ATER
TEMP
CENT
00299
DO
PROBE
MG/L
2
00078
TRANSP
SECCHI
METERS
00310
BOD
5 DAY
MG/L
211 1202
OUU9 FEET
00312 UO
BOO CHLO
6 DAY C
MG/L M6U
6I.BU
32216
PHEOPHTN
A
Ub/L
1 1 .00
1 .20
5.2O
b.lU
71. UU
U.UU
-------
STORET RETRIEVAL DATE 75/06/06
053021 4290ACOS3024
41 33 26.0 087 55 37.0
GREEN BAY OPEN WATER ONR STA 1JA
55 WISCONSIN
LAKE MICHIGAN
DATE TIME
FROM OF
TO DAY
74/02/19
74/02/19
74/02/19
74/05/22
74/05/22
74/06/03
74/06/03
74/07/09
74/07/09
74/08/12
74/08/12
74/09/04
74/09/04
0003
0007
0010
0003
0010
0003
0010
0003
0010
0003
0010
0003
0010
72028 72029
IEPTH AZIMUTH DISTANCE
FR SOUTH FR SOUTH
EET DEGREES FEET
0003
0007
0010
0003
0010
0003
0010
0003
0010
0003
0010
0003
0010
00010
irATER
TEMP
CENT
1 .0
IS. 5
15.0
16.5
16.5
24.0
24.0
22.0
22.0
19.0
18.0
00299
DO
PR08E
MG/L
9.5
9.5
6.8
11 .6
11 .0
9.9
10.0
9.2
9.4
8.1
7.2
9.9
6.1
21*1,5
2
00078 00310
TRANSP BOD
SECCH1 5 DAY
METERS MG/L
3.4
0.9
0.8
0.9
0.8
0.6
21 11202
0009 FEET
00312 00
BOD CHLO
6 DAY C
MG/L MS
DEPTH
14
00530
RESIDUE
TOT NFLT
MG/L
1 1
053024 4290ACOS3024
44 33 26.0 087 55 37.0
GREEN BAY OPEN WATER DNR STA 1
55 WISCONSIN
LAKE MICHIGAN
I
ro
to
I
2I»IS
DATE
FROM
TO
TIME
OF
DAY
00671
DEPTH pHOS-DIS
ORTHO
FEET MG/L P
0066*
PHOS-ToT
MG/L p
O'OiOS-
ORG N
N
MG/L
00618
N03-N
DI5S
MG/L
•« 2
00613
N02-N
DISS
MG/L
00610
NH3-N
TOTAL
MG/L
21 1
0009
32211
CHLRPHYL
A UG/L
CORRECTD
1202
FEET DEPTH
32218
PHEOPHTN
A
UG/L
74/02/19
0007
0.001
0.051
0.lOOK
0.12
0.030
0.688
-------
STORE! RETRIEVAL DATE 75/06/06
72028 72029
DATE TIME DEPTH AZIMUTH DISTANCE
FROM OF FR SOUTH FR SOUTH
TO DAY FEET DEGREES FEET
73/09/18
73/09/18
73/09/18
73/09/18
71/02/19
71/02/19
71/05/22
71/05/22
71/05/22
71/06/03
71/06/03
71/07/09
71/07/09
71/07/09
71/08/12
71/08/12
71/08/12
71/09/01
71/09/01
71/09/01
0003
0007
0010
0013
0003
0007
0003
0007
0010
0003
0007
0003
0007
0013
0003
0007
0010
0003
0007
0010
053025 1290AC053U25
11 31 16.0 087 55 OS«0
GREEN BAY OPEN WATER DNN STA in
55 WISCONSIN
LAKE MICHIGAN
00010
WATER
TEMP
CENT
15.5
15.5
15.0
15.0
15.0
13.5
15.5
15.0
25. 0
21.0
21 .5
21 .0
18.0
00299
DO
PROBE
MG/L
B.I
8.3
8.0
8.9
6.3
1 1.2
1 I .1
8.6
9.5
9.6
10. 1
9.8
8.1
8.1
9.6
21KIS 2111202
2 0009 FEET
00078 00310 00312 00
TRANSP 800 SOD CHLO
SECCHI 5 DAY 6 DAY C
METERS MG/L MG/L Mt,
O.S
0.9
11.0
0.9
8.2
0.6
9.1
0.8
6.5
0.6
DEPTH
6.5
18.0
IB
11
11
16
13
00530
RESIDUE
TOT NFLT
MG/L
27
11
10
1
12
7.2
Q5302S 1290ACOS302S
11 31 16.0 OB7 55 05.0
GREEN BAY OPEN WATER ONR STA 1M
55 WISCONSIN
LAKE MICHIGAN
00671
DATE TIME DEPTH pHOS-DIS
FROM OF ORTHO
TO DAY FEET MG/L P
73/09/18
71/05/22
71/06/03
71/07/09
71/08/12
71/09/01
0007
0007
0007
0007
0007
0007
0.027
0.009
0.008
0.006
0.036
0.015
21*IS
00661
PHOS-TOT
MS/L P
0.182
0.125
0. 130
0.103
0.103
0.12S
00605
ORG N
N
MG/L
O.lQO
0.200
1 .100
0.600
0.600
0.3QO
00618
N03-N
OlSS
MG/L
0.09
0.39
0.12
0.02
0.11
0.08
2
00613
N02-N
DISS
MG/L
0.007
0.013
0.015
0.005
0.023
0.003
00610
NH3-N
TOTAL
MG/L
0.264
0.390
0.380
0.110
0. 180
0.050
2111202
0009 FEET
DEPTH
32211 32218
CHLRPHYL PHEOPHTN
A UG/L A
CORRECTD UG/L
31.00
13.OU
13. 10
57.60
9.20
20. 10
12.00
1.00
8.80
5.60
27.00
25. 10
-------
STORET RETRIEVAL DATE 75/06/06
053027 1290ACOS3027
HI 35 H1.0 087 51 16>0
CjREE.lv BAY OPEN WATER DNR STA 1
55 WISCONSIN
LAKE MICHIGAN
7202B
DATE TIME DEPTH AZIMUTH
FROM OF FR SOUTH
TO DAY FEET DEGREES
73/09/18
73/09/18
73/09/18
73/09/18
71/02/19
71/02/19
71/05/22
71/05/22
71/06/03
71/06/03
71/07/09
71/07/09
71/08/12
71/08/12
71/09/01
71/09/01
0003
0007
0010
0013
0006
0015
0003
0016
0003
0010
U003
OO07
0003
0013
0003
0010
72029 00010
DISTANCE A'ATER
FR SOUTH TEMP
FEET CENT
15.0
15.0
15.0
15.5
11.0
15. U
15.0
23. U
23.0
21 .0
21.0
18.0
17.0
00299
00
PROBE
Mb/L
9.6
9.5
9.1
5.2
5.7
11 «1
1U.2
10.8
10. a
9.1
8.5
8.7
8.7
8.7
a. 4
21*15 211 1202
2 001J FEET
00078 00310 00312 00
TRANSp BOD BOD CHLO
SECCHI 5 DAY 6 DAY C
METERS MG/L MG/L MG
0.8
0.8
0.9
0.8
0.6
0.9
DEPTH
0053Q
RESIDUE
TOT NFLT
MG/L
12
00671
DATE TIME DEPTH pHOS-DIS
FROM OF ORTHO
TO DAY FEET MG/L P
053027 1290ACU53027
11 35 11.0 087 51 16.0
GREEN BAY OPEN WATER DNR STA.15
55 WISCONSIN
LAKE MICHIGAN
2 1 ft I S
Q066R
PHOS-TOT
MS/L p
00605
CRG N
N
MG/L
00618
N03-N
OISS
MG/L
2
00613
N02-N
DISS
MG/L
U0610
NH3-N
TOTAL
MG/L
21 1
QU13
3221 1
CHLRPHYL
A UG/L
CORRECTS
1202
FtET DE
32218
PHEOPHTN
A
UG/L
73/09/18
0007
0.008
0.5QO
0.07
0.003
19.00
8.00
-------
STORET RETRIEVAL DATE 75/06/06
72028 72029
DATE TIME DEPTH AZIMUTH DISTANCE
FROM OF pR SOUTH FR SOUTH
TO DAY FEET DEGREES FEET
73/09/18
73/09/18
73/09/18
73/09/18
71/02/18
71/02/18
71/02/18
71/05/20
71/05/20
71/05/20
71/05/20
71/06/03
71/06/03
71/06/03
71/07/09
71/07/09
71/07/09
71/08/13
71/08/13
71/08/13
71/09/01
71/09/01
0003
0007
0010
0020
0003
0007
0013
0003
0007
0013
0023
0003
0010
0020
0003
0010
0023
0003
0010
0023
0003
0023
053028 1290ACOS3Q28
11 37 34.0 087 SI 02.0
GREEN BAY OPEN HATER ONR STA 16
55 WISCONSIN
LAKE MICHIGAN
00010
(HATER
TEMP
CENT
IB. 5
15.5
lb.0
0.6
0.8
9.0
9.0
9.U
11.5
11. S
13.0
23.0
22.0
22. a
2U.O
20.0
17.0
18.0
17.0
00299
00
PROBE
MG/L
8.7
8.5
B.I
b.2
5.2
3.7
1 1.2
11*2
1 1 .3
10.8
10. 6
9.0
8.5
7.9
7.6
8.0
7.9
7.8
8.2
8.0
211.IS 211 1202
2 OU1M FEET
00078 00310 QU312 00
TRANSP BOD BOD CHLU
SECCHI 5 DAY 6 DAY C
METERS MG/L MG/L Mb
0.9
2.1
0.9
1.9
1 .0
2.1
1.6
1.3
DEPTH
00530
RESIDUE
TOT NFLT
MG/L
20
18
18
10
OS3028 1290ACU53028
11 37 31.0 OB7 51 02.0
GREEN BAY OPtN WATER DNR STA It,
55 WISCONSIN
LAKE MICHIGAN
21*15
2
2111202
0013 FEET
DEPTH
DATE TIME
FROM OF
TO DAY
73/09/18
71/02/ 18
71/05/20
DEPTH
FEET
0007
0007
0007
00671
pHOS-OIS
ORTHO
MG/L P
0.005
0.020
0.006
0066=1
PHOS-TOT
MG/L p
0.063
0.015
0.086
00605
ORG N
N
MG/L
0.500
0. 1UOK
0.500
00618
N03-N
D1SS
MG/L
0.11
0.10
0.11
00613
N02-N
D1SS
MG/L
0.001
0.011
0.012
00610
NM3-N
TOTAL
MG/L
0.038
0.172
0. 190
3221 1
CHLRPHYL
A UG/L
CORRECTD
50* UO
13.10
32218
PHE.OPHTN
A
UWL
IS. 00
-------
STORE! RETRIEVAL DATE 75/04/06
72a28 7202V
DATE TIME DEpTH AZIMUTH DISTANCE
FROM OF FR SOUTH FR SOUTH
TO DAT FEET DEGREES FEET
73/09/lfl
73/09/18
73/09/18
73/09/18
71/02/20
71/02/20
71/02/20
71/02/20
71/02/20
71/02/20
71/02/20
71/02/20
71/02/20
71/02/20
71/02/20
71/05/20
71/05/20
71/05/20
71/06/01
71/06/01
71/06/01
71/07/09
71/07/09
71/07/09
71/08/13
71/08/13
71/08/13
71/09/05
71/09/05
71/09/05
0003
0007
0010
UU20
OOOU
0002
0005
0006
0007
0010
0013
0015
0020
0023
0026
0003
0010
0020
0003
0013
OU23
0003
U010
0020
0003
001U
0020
0003
0010
0023
315.0
315.0
315.0
4000.0
4000.0
CjOUlO
nATER
TEMP
CENT
15.5
00299
DO
PROBE
MG/L
9.0
15.5
IS. 5
0.0
0.0
u.o
U.2
0.0
0.2
O.I
0.1
1 .0
1 .0
9.0
9.0
9.0
11.0
14.0
14.0
24.0
23.0
24.0
20.0
19.5
19.5
18.0
18.0
18.0
9.0
9.0
9.2
12.1
11.8
12.6
a. 2
5.4
2.5
2.5
1 .8
1 .7
12.4
12.0
12.0
9.5
V.I
9.4
9.2
8.9
8.8
8.4
8.3
a. 3
9.6
9.6
9.5
053029 4290ACOS3029
MS 39 1 I-0 087 17 12*0
GREEN BAY OPEN WATER DNR STA |6A
55 WISCONSIN
LAKE MICHIGAN
21M5
2
21 I 1202
0019 FEET
DEPTH
00078
TRANSp
SECCHI
METERS
1 .2
00310 00312 0094t) OU530
800 BOD CHLORIDE RESIDUE
5 DAY 6 DAY CL TOT NFLT
M6/L MG/L Mb/L MG/L
IS
21
053029 429UACOS3U29
11 39 11.0 087 HI 12.0
GREEN BAY OPEN WATER ONrt STA 14 A
55 UISCONSIN
LAKE MICHIGAN
21AIS
2
2111202
OU19 FEET
DEPTH
DATE
FROM
TO
73/09/18
71/02/20
71/02/20
TIME
OF
DAY
OEpTH
FEET
0007
0007
0020
00671
pHOS-DIS
ORTHO
MG/L P
0.005
O.OUS
0.011
00665
PHOS-TOT
MQ/L p
0.046
0.005
0.053
Q0605
ORG N
N
MG/L
0.000
1 .600
0.800
DQ618
N03-N
DISS
MG/L
0.02
0.04
0.10
00613
N02-N
OISS
MG/L
0.002
0.005
0.010
00610
NH3-N
TOTAL
MG/L
0.095
0.058
U.609
3221 1
CHLRPHYL
A US/L
CORRECTU
7.UU
9.7U
32214
PHEORHTN
A
UG/L
S.OU
O.OU
-------
STORE! RETRIEVAL DATE 75/06/06
72Q28 72Q29
DATE TIME DEPTH AZIMUTH DISTANCE
FROM OF FR SOUTH FR SOUTH
TO DAY FEET DEGKEES FEET
7M/02/20
7M/02/20
71/02/20
71/02/20
71/02/20
71/02/20
71/02/20
71/02/20
71/02/20
0003
0005
0006
0010
0012
0019
0020
0026
0027
315.0
315.0
1000.0
1000.0
315.0 1000.0
315.0 HOQO.O
053030
-------
STORET RETRIEVAL DATE 75/06/06
153U01 1290AC153001
11 10 51.0 087 SI 56.0
GREEN BAY OPEN »ATER ONR STA I6C
55 WISCONSIN
LAKE MICHIGAN
21». IS 2111202
DATE
FROM
TO
71/02/20
71/02/20
71/02/20
71/02/20
71/02/20
71/02/20
71/02/20
71/02/20
71/02/20
71/02/20
71/02/20
71/02/20
71/02/20
71/02/20
71/02/20
71/02/20
71/02/20
TIME DEpTH
OF
OAr FEET
0002
0003
U001
0005
0006
U007
0010
001 I
0012
0013
0019
0020
0021
0026
0028
0029
0030
72028
AZIMUTH
FR SOUTH
DEGREES
315.0
315.0
315.0
315.0
315.0
315.0
315.0
315.0
315.0
315.0
315.0
315.0
72029
DISTANCE
FR SOUTH
FEET
5000. G
2500.0
10000.0
SUOO.O
5000.0
10000.0
2SOO.O
10000. U
5000.0
2500.0
5000.0
10000.0
0001 0
AATER
TEMP
CENT
0.0
U.O
U.U
0.0
0.0
u.o
0.0
u.o
u.o
0.1
0. 1
u.o
0.0
1 .0
1 .U
1 .0
1.0
2
00299 00078
DO TRANSP
PROSE SECCHI
MG/L METERS
1 1 .5
9.2
9.5
12.2
a. 8
6.8
5.6
9.3
5.7
6.6
5.8
3.8
1.5
1 .7
.1.6
2.6
3.1
UU22 FEET
00310 00312 OU
BOD tlOD CHLO
5 DAY 6 DAY C
MG/L MG/L MG
9.0
13.5
DEPTH
00530
RESIDUE
TUT NFLT
MG/L
13
19
61
1S3U01 129UAC153U01
11 1l> bl.O 087 51 56.U
GRtEN BAY OPtN OATtR DNR STA 1
b5 OISCONSIN
LAKt rilCHlfaAN
2 1 1 I b
2
DATE TIME
FROM OF
TO DAY
71/02/20
71/02/20
DEPTH
FEET
0007
0026
00671
pHOS-OI S
ONTHO
M&/L P
0.003
0.012
00665
PHOb-TflT
MG/L p
0.011
0.096
00605
URG N
N
MG/L
0.300
0.300
00618
N03-N
D1SS
Mfa/L
0.09
O.U9
00613
N02-N
UISS
MG/L
0.013
U.OI9
U06 10
NH3-N
TOTAL
MG/L
0.217
0.711
21 1 12U2
OU22 FEET
DEPTH
32211 32218
CHLRPHYL PHEOPHTN
A U6/L A
CORRECTD UG/L
-------
STORET RETRIEVAL DATE 75/06/06
72028 72029
DATE TIME DEPTH AZIMUTH DISTANCE
FROM OF FR SOUTH FR SOUTH
TO DAr FEET DEGREES FEET
73/09/18
73/09/18
73/09/18
71/05/20
71/05/20
71/05/20
71/06/03
71/06/03
71/06/03
71/07/09
71/07/09
71/07/09
71/07/09
71/08/12
71/08/12
71/08/12
71/08/12
71/09/01
71/09/01
71/09/01
0003
0007
0010
0003
0007
0013
U003
0007
0013
0003
0007
0010
0016
0003
0007
0013
0016
0003
0007
0010
053031 1290ACU53031
11 36 13.0 087 58 21.0
GREEN bAY OPEN *ATER ONK STA 17
55 WISCONSIN
LAKE MICHIGAN
00010
AATER
TEMP
CENT
11.5
11.0
1 1 .0
1 1.0
1 1 .0
13.5
13.5
21.0
21 .0
16.0
19.0
19.0
19.0
17.0
18.0
00299
DO
PROBE
MG/L
10.2
10.0
1 1 .2
1 1.2
11.2
10.6
10.7
a. 3
7.8
1.3
7.9
7.9
7.7
1.7
9.3
00078 U0310
TRANSP BOD
SECCHI 5 UAY
METERS MG/L
1.0
1 .2
1 .6
1 .8
1.
1 .8
3.
1 .b
2111202
OUU9 FEET OLKTH
00312 OU910 00530
&QO CHLORIDE RESIDUE
6 UAr CL TUT NFLT
MG/L Md/L MG/L
11
H.b 11 11
8.6 9 2
5.3
17.0
7.3
00671
DATE TIME DEpTw pHOS-DIS
FROM OF OKTHO
TO DAY FEET MG/L P
73/09/18
71/05/20
71/06/03
71/07/09
71/08/12
71/09/01
0007
0007
OU07
0007
0007
0007
O.U03
O.OOH
O.OU8
o.oos
0.011
0.011
OS3031 129UACUS3U31
It 36 H3.0 087 5tt 21.0
GREEK bAY OPEN WATER UNk bTA \^
55
LAKE MICHIGAN
21AIS
0066C,
PHOS-TOT
MG/L p
0.033
0.019
U.U&U
0.011
0.033
U.056
00605
URG N
N
MG/L
0.200
0.100
1 .QUO
U.300
0.600
0. 100
00618
N03-N
OISS
MG/L
a. 01
0.09
O.U6
0.03
O.U6
0.09
2
00613
N02-N
OISS
MG/L
0.002
0.011
0.003
U.001
U.Gil
U.003
OU610
NH3-N
TOTAL
MG/L
0.133
U.2bU
u.ulu
0.010
U.U1UK
U.U6U
21 1
UU09
3221 1
CMLKPHYL
A UG/L
COKRECTD
Ib.UU
1 .5U
9.30
10. 1U
U.8U
lu. iu
12U2
FEtT DEI
32218
PHtUPhTN
A
UG/L
l.UQ
1 ,BU
2.UU
2b.OU
19. 2U
-------
5TORET RETRIEVAL DATE 75/06/04
053032 1290ACUS303^
Ml 38 10*0 087 67 39.0
GREEN 8A< OPEN WATER DNR STA IB
55 »ISCONSIN
LAKE MICHIGAN
DATE
FROM
TO
73/09/18
73/09/18
73/09/18
73/09/18
71/02/18
71/02/18
71/05/20
71/05/20
71/05/20
71/05/20
71/06/03
71/06/03
71/06/03
71/06/03
71/07/09
71/07/09
71/07/09
71/07/09
71/08/12
71/08/12
71/08/12
71/08/12
71/09/01
71/09/01
71/09/01
72028 72029
TIME DEpTH AZIMUTH DISTANCE
OF FR SOUTH FR SOUTH
DAY FEET DEGREES FEET
0003
0007
0010
0020
0003
0011
0003
0007
0010
0020
0003
OU07
0010
0016
0003
QOU7
U010
0016
0003
0007
0010
0016
0003
0007
0013
00010
WATER
TEMP
CENT
11.5
11.3
11.0
1. 1
2.0
10. 0
1U.O
10.0
IU.O
13.0
13.0
13.0
21. b
21.0
16.0
20.0
20.0
19.0
19.0
17.0
21»1S 2111202
2 Q(J16 FEET
00299 00078 00310 00312 OU
DO TR/tNSP 800 800 CHLO,
PROBE SECCHI 5 OAY 6 OAY C
MG/L METERS MG/L MG/L He,
9.8 1.3
9.1
9.0
18. 5
16.2
11.3 1 .b
11.3 3.7
11 .b
1 1 .0
10.1 1.8
8.6
10.5
10.1
8.6 1.5
3.3
8.2
b.3
'.5 0.9
1.9
7.3
6.8
8.8 1 ,t
1.1
8.1
DEPTH
OOS3Q
RESIDUE
TOT NFLT
MG/L
11
10
053U32 129UACOS3U32
11 38 10.0 087 57 39.0
GREEN SAT OPEN *ATER OHH STA l
55 *ISCONSIN
LAKE MICHIGAN
21V.1S 2II12Q2
2 OU16 Hit DtPTH
DATE
FROM
TO
73/09/18
71/05/20
71/06/03
71/07/09
71/08/12
71/09/01
TIME DEpTH
OF
DAY FEET
0007
0007
0007
0007
0007
0007
U067I
PH05-DIS
ORTHO
MG/L P
0.001
0.006
0.010
OV006
0.005
0.011
0066S
PHOS-ToT
MS/L P
0.029
0.032
O.U50
0.010
0.037
0.018
00605
ORG N
N
MG/L
0.200
U.100K
0.800
0.300
0.700
0.300
00618
N03-N
DISb.
MG/L
0.01
0.10
0.06
0.03
0.06
O.U7
00613
N02-N
DISs
MG/L
0.002
0.01 1
0.002
O.OU1
0.006
0.002
U0610 32211 32218
NH3-N C>1LRPHYL PHEoPnTN
TOTAL A'UG/L A
Mfa/L COKRECTU UG/L
O.ilb 10. OU 5.0U
U.26C1
U.CI3U
0.03U
O.UIUK
U.01U
-------
STORET RETRIEVAL DATE 75/06/06
72028 72029
DATE TIME DEPTH AZIMUTH DISTANCE
FROM OF FR SOUTH FR SOUTH
TO DAY FEET DEGREES FEET
73/09/18
73/09/18
73/09/18
73/09/lB
71/06/03
7H/06/03
71/04/03
71/07/09
71/07/09
71/07/09
71/08/12
71/08/12
71/08/12
71/09/01
71/09/01
0003
0007
0010
0013
0003
0010
0016
0003
OQ07
0013
0003
0007
0013
0003
0010
11.3
053Q33 1290ACQ53033
11 38 26.0 087 59 07*0
GREEN BAY OPEN WATER DNR STA 19
55 WISCONSIN
LAKE MICHIGAN
21WIS
OOQlO
fcATER
TEMP
CENT
00299
DO
PROBE
MG/L
2
00078
TRANSP
SECCHI
METERS
00310
BOD
5 DAY
MG/L
21 1 1202
0013 FEET
00312 00
BOD CHLO
6 DAY C
MG/L MG
DEPTH
0053Q
RESIDUE
TOT NFUT
MG/L
9.6
11.0
13. 5
11.0
11.0
11.0
21 .0
21.0
16.5
21.0
21 .0
20.0
19.0
18.0
9
9
10
1U
1U
8
H
3
8
a
7
9
9
.6
.3
.1
.5
.6
.1
.1
.8
.8
.7
.7
.1
.1
1 .0
1 .5
1.5
1 .0
1.3
0067)
DATE TIME DEpTH pHOS-DIS
FROM OF ORTHO
TO DAY FEET M6/L P
73/09/18
0007
O.OQ5
OB3033 1290AC053033
11 36 26.0 087 59 07.0
GREEN BAY OPEN WATER DNK STA 19
55 WISCONSIN
LAKE MICHIGAN
21*15
00665
PHOS-TOT
M6/L P
0.032
00605
ORG N
N
MG/L
0.300
00618
N03-N
DISS
MG/L
0.01
2
OQ6J3
N02-N
DISS
MG/L
0.003
00610
NH3-N
TOTAL
,MG/L
0.133
21 1
OU1 3
32211
CHLRPHYL
A UG/L
CORRECTD
15.00
1202
FEET UE)
322)8
PHEoPhTN
A
UG/L
2. QO
-------
STORE! RETRIEVAL DATE 75/06/06
053031 1290AC053031
11 37 11.0 087 59 21.0
GREEN BAY OPEN WATER ONR STA 21
55 WISCONSIN
LAKE MICHIGAN
DATE TIME
FROM OF
TO DAY
73/09/18
73/09/18
73/09/18
71/06/03
71/06/03
71/07/09
71/07/09
71/08/12
71/08/12
71/08/12
71/09/01
71/09/01
0003
U007
0010
0003
0010
0003
0010
0003
0007
0013
0003
0010
72028 72029
lEpTH AZIMUTH DISTANCE
FR SOUTH FR SOUTH
'EET DEGREES FEET
0003
0007
0010
0003
0010
0003
0010
0003
0007
0013
0003
0010
00010
WATER
TEMP
CENT
11.5
11.5
13.0
13.0
21.0
20.0
21 .0
20.5
19.5
18.0
17.0
00299
DO
PROBE
MG/L
10.0
10.0
1 1 .0
10.8
7.3
6.1
8.6
8.3
6.8
9.1
8.3
21KIS
2
00078 00310
TRANSP BOD
SECCHI 5 DAY
METERS MG/L
0.9
1.5
1.5
0.8
1.2
21 1 1202
0009 FEET
Q0312 00
BOD CHLO
6 DAY C
MG/L MG
DEPTH
0053Q
RESIDUE
TUT NFLT
MG/L
20
u
u
00
I
053031 1290AC053031
11 37 11.0 087 59 21.0
GREEN BAY OPEN WATER DNR STA 21
55 WISCONSIN
LAKE MICHIGAN
DATE
FROM
TO
73/09/18
2 I * 1 S
2
TIME
OF
DAY
DEpTH
FEET
0007
00671
pHOS-DIS
OKTHO
MG/L P
0.005
0066S
PHOS-TOT
MG/L p
0.010
00605
ORG N
N
MG/L
0.1QO
00618
N03-N
DISS
MG/L
0.01
00613
N02-N
OISS
MG/L
0.003
00610
NH3-N
TOTAL
MG/L
0.115
21 1
0009
32211
CHLRPHYL
A UG/L
CORRECTD
18.00
1202
FEET DEI
32218
PHEOPHTN
A
U6/L
1.00
-------
STORET RETRIEVAL DATE 75/06/06
72028 72029
DATE TIME OEpTH AZIMUTH DISTANCE
FROM OF FR SOUTH FR SOUTH
TO DAY FEET DEGREES FEET
73/09/18
73/09/18
73/09/18
71/05/20
71/05/20
71/06/01
71/06/01
71/07/09
71/07/09
71/08/12
71/08/12
71/08/12
71/09/01
71/09/01
0003
0007
0010
0003
0013
0003
0013
0003
0010
0003
0007
0010
0003
0010
13.7
1)33006 1290AC133006
11 11 11.0 087 58 29.0
GREEN BAY OPEN *AT£R DNR STA 23
55 WISCONSIN
LAKE MICHIGAN
2 Hi I b
00010
LATER
TEMP
CENT
00299
DO
PROBE
MG/L
2
00078
TRANSP
SECCH1
METERS
00310
BOD
5 DAY
MG/L
21 I 1202
OU06 FEET
00312 00
BOO CHLO
6 DAY C
MG/L MG
DEPTH
OUB30
RESIDUE
TOT NFLT
MG/L
9.6
1 .2
13.7
10.0
9.5
13.5
13.0
19.0
18.0
22.0
22.0
22.0
18.0
17.0
9.1
12.2
1 1.6
10.2
10.2
6.8
5.1
9.1
9.3
9.3
9.3
9.7
1 .8
1 .9
1 .8
0.9
1 .5
00671
DATE TIME DEPTH pHOS-DIS PHOS-ToT
FROM OF ORTHO
TO DAY FEET MG/L P MG/L p
to
I
"433006 1290AC133006
11 11 11.0 087 58 29.U
GREEN BAY OPEN WATER DNR STA 23
55 WISCONSIN
LAKE MICHIGAN
00605
ORG N
N
MG/L
00618
NO3-N
DISS
MG/L
21A1S
2
00613
N02-N
DISS
MG/L
00610
NM3-N
TOTAL
MG/L
21 1 1202
0006 FEET DEI
32211 32218
CHLRPHYL PHEOPHTN
A UG/L A
CORRECTD UG/L
73/09/18
0007
0.007
0.031
0.600
0.03
0.001
0.027
13.OU
1.00
-------
STORET RETRIEVAL DATE 75/06/06
72028 72029
DATE TIME DEpTH AZIMUTH DISTANCE
FROM OF FR SOUTH FR SOUTH
TO DAY FEET DEGREES FEET
73/09/18
73/09/18
73/09/18
73/09/18
71/02/18
74/02/18
71/05/20
71/05/20
71/05/20
71/05/20
71/06/01
71/06/01
71/06/01
71/06/01
71/07/09
71/07/09
71/07/09
71/07/09
71/08/12
71/08/12
71/08/12
71/08/12
71/08/12
71/09/01
71/09/01
71/09/01
71/09/01
0003
0007
0010
0020
0007
0016
0003
0007
0010
0020
0003
0007
001 1
0023
0003
0007
0010
0020
0003
0007
0013
0016
0020
0003
0007
0010
0023
133007 1290AC13300/
Ml 11 06.0 087 56 05'Q
GREEN 6Ar OPtN HATER UNR STA 21
55 WISCONSIN
LAKE MICHIGAN
00010
HATER
TEMP
CENT
11.0
11.0
11. 0'
1 .1
1 .1
9.0
9.0
8.S
8.0
12.0
12.0
12.0
21 .0
20.0
1 1 .0
19.0
19.0
19.0
18.0
15.0
19.0
17.0
17.0
21*15
2
00299 00078 00310
DO TRANSP BOD
PROBE SECCHI 5 DAY
MG/L METERS MG/L
9.5 1 .2
9.5
9.5
18.6 1 .8
18.6
11.8 1.8
1 1 .8
1 1 .8
12.0
10. 1 1 .9
1U.3
10. 1
8.8 1 .6
1.5
8.1
5.8
8.3 1.5
8.3 5.3
7.9
7.1
5.2
8.2 1 .6
1.1
7.8
7.6
21 1 12U2
LlOlV FEET
00312 OU'
tiOD CHLUI
6 DAY LI
MG/L Hu
3.7
00530
KLSlDUE
TUT NFLT
MG/L
133007 1290AC133007
11 tl 06.0 087 56 05.0
GREEN BAY OPtN *ATER ONK STA 2
Bb D1SCUN5IN
LAKE MICHIGAN
21« IS
2
DATE TIME
FROM OF
TO DAY
73/09/18
71/02/18
71/05/20
71/06/01
71/07/09
71/08/12
71/09/01
DEPTH
FEET
0007
0007
0007
0007
0007
0007
0007
00671
PHOS-DIS
ORTHO
MG/L P
0.005
0.001
0.006
0.005
0.012
0.006
O.U1 1
0066H
PHOS-TOT
MG/L P
0.031
0.011
0.037
0.050
0.011
0.018
0.033
00605
uRG N
N
MG/L
0.200
0.100
0.100
0.300
0.300
0.600
0.300
00618
N03-N
U1SS
MG/L
0.03
0.02
0. 10
0.01
O.U3
0.07
0.06
00^13
N02-N
DISS
MG/L
0.003
0.007
0.012
0.007
0.001
O.OOS
0.002
00610
NH3-N
TOTAL
MG/L
0.020
0.131
0.180
0.060
0.010
0.010K
0.010
21 1
0019
3221.1
CHLRPHYL
A UG/L
COKRECTC
15.00
9.90
5.70
6.7U
0.00
16.70
12U2
FEtT DtpTH
32218
PHEOPHTN
A
UG/L
1 .00
2.30
3.80
31.80
0.00
-------
STORET RETRIEVAL DATE 75/06/04
DATE
FROM
TO
73/09/18
73/09/18
71/05/20
71/05/20
71/06/01
71/06/01
71/07/09
71/08/13
71/08/ 13
71/09/05
71/09/05
TIME DEpTH
OF
DAY FEET
0003
0007
0003
0010
0003
0007
0003
0003
0013
0003
0010
72028
AZIMUTH
FR SOUTH
DEGREES
433008 1290AC
-------
STORE! RETRIEVAL DATE 75/06/06
DATE
FROM
TO
73/09/18
73/09/18
73/09/18
73/09/18
7i/09/18
71/02/20
71/02/20
71/02/20
71/02/20
71/02/20
71/02/20
71/02/20
71/02/20
71/02/20
71/05/20
71/05/20
71/05/20
71/05/20
71/05/20
71/06/01
71/06/01
71/06/01
71/06/01
71/06/01
71/07/09
71/07/09
71/07/09
71/07/09
71/07/09
71/07/09
71/08/13
71/08/13
71/08/13
71/08/13
71/08/13
71/08/13
71/09/05
71/09/05
71/09/05
71/09/05
72028 72029
TIME DEpTH AZIMUTH DISTANCE
OF FR SOUTH FR SOUTH
DAY FEET DEGREES FEET
0003
0007
0010
0020
0030
0003 315.0 5000.0
0006
0010 315.0 5000.0
0012
0020 315.0 5000.0
0025
0030 315.0 5000.0
0033
0036 315.0 5000.0
0003
0007
0010
0020
0039
0003
0007
0013
0023
0033
0003
0007
0010
0020
0026
0033
0003
0007
0013
0026
0030
0033
0003
0007
0013
0033
00010
,.ATER
TEMP
CENT
15.0
15.0
15.0
15.0
0.0
0.0
0.0
0. 1
0.3
0. 1
1 .0
1 .2
1 .0
8.0
8.0
8.0
7.0
7.0
12.0
1 1 .5
1 1.5
9.0
22.0
20.0
19.0
15.0
12.0
19.0
19.0
19.0
11.0
1 1.0
17.0
17.0
17.0
00299
DO
PROBE
Mfa/L
9.2
9.2
9.0
8.8
12.8
12.1
12.8
1 1.1
10. 7
8.1
9.5
3.9
7.7
12.5
12.5
12.1
12.0
12.5
1U.3
10.2
9.8
6.6
8.7
8.5
8.0
6.2
5.6
8.6
8.1
8.1
3.5
2.2
9.9
10.0
9.8
133009 129UAC133009
11 12 t6.0 087 51 OQ.0
GREEN BAY OPEN WATEK DNK STA 26
SS IUSCONSIN
LAKE MICHIGAN
21ft IS 2111202
2 0029 FEET DEPTH
378 00310 00312 Ou?<<0 00&3Q
MSP BOD BOD CHLORIDE RtSlDUE
CHI 5 DAY 6 DAY CL TUT NFLT
ERS Mfa/L MG/L M(j/L M6/L
1 .3
1 .7
2. 1
1 .8
1 .9
1. 1
10
3.3
3.7
5.3
1. 1
3.3
1.5
13
0. 1
6
0.1
18
0.1
O.IK
5
57
-------
STORET RETRIEVAL DATE 75/06/06
433009 1290AC133009
11 12 16.0 087 51 OOiO
GREEN BAY OPEN MATER ONR STA 26
SB AISCUNSIN
LAKE MICHIGAN
DATE
FROM
TO
73/09/18
71/05/20
71/06/OH
71/06/01
71/07/09
71/07/09
71/08/13
71/08/13
71/09/05
71/09/05
00671
TIME DEPTH pHOS-DIS
OF OKTHO
DAY FEET MG/L P
0007
0007
0007
0033
0007
0033
0007
0033
0007
0033
0.006
0.006
0.008
0.010
0.010
0.01 1
0.011
0.010
0.005
0.006
21»IS
00665
PHOS-TOT
MG/L p
0.037
0.050
0.060
0.080
0.013
"0.019
0.011
0.011
0.022
0.331
00605
ORG N
N
MG/L
0.500
U.2QO
0. 100
0.800
0. 100K
Q.5QO
0.300
0..100
0.7QO
1 .000
00618
N03-N
DISS
MG/L
0.03
0.13
0.03
0.07
0.005
0.51
0.17
0.63
0.02
0.08
2
00613
N02-N
DISS
MG/L
0.002
0.015
0.008
O.OQ8
0.005
0.038
0.003
0.011
0.006
0.008
00610
NH3-N
TOTAL
MG/L
0.081
0.210
0.050
0.110
0.010K
0.010
0.010K
O.OIOK
0.010
0.080
2111202
0029 FEET
DEPTH
32211 32218
CHLRPHYL PHEOPHTN
A UG/L A
CORRECTO UG/L
11.00
1 .00
SS
u>
-------
STORE! RETRIEVAL DATE 75/06/06
153002 1290ACI53002
11 HI 12.0 087 18 30-0
GREEN BAY OPEN WATER DNK STA 26A
55 WISCONSIN
LAKE MICHIGAN
DATE
FROM
TO
71/02/20
71/02/20
71/02/20
71/02/20
71/02/20
71/02/20
71/02/20
71/02/20
TIME DEPTH
OF
DAY FEET
0005
0006
0010
0012
0020
0021
0031
0033
72028
AZIMUTH
FR SOUTH
DEGREES
135.0
13B.O
135.0
135.0
72029
DISTANCE
FR SOUTH
FEET
5000.0
5000.0
5000.0
5000.0
00010
WATER
TEMP
CENT
0.1
0.3
0. 1
0.1
0.0
1.2
1.2
21*IS
2
00299 00078 00310
DO TRANSP SOD
PR08E SECCHI 5 DAY
MG/L METERS MG/L
13.3
1 1 .8
12.8
11.2
9.3
7.6
3.3
1.7
211 1202
0029 FEET
00312 OU
BOD CHLO
6 DAY C
Mfa/L Mfa
DLPTH
RESIDUE
TUT NFLT
MG/L
-------
STORE! RETRIEVAL CUE 75/06/06
72028 72029
0«TE TIME DEPTH AZIMUTH DISTANCE
FROM OF FR SOUTH FR SOUTH
TO DAY FEET DEGREES FEET
73/09/18
73/09/18
73/09/18
71/02/20
71/02/20
71/02/20
71/02/20
71/05/20
71/US/20
71/05/20
71/05/20
71/06/01
71/04/01
71/06/01
71/06/01
71/07/09
71/07/09
71/07/09
71/07/09
71/08/13
71/08/13
71/08/13
71/08/13
71/08/13
71/09/05
71/09/05
71/09/05
71/09/OS
0003
OU07
0013
0003
UQ10
0020
0026
UUOJ
U007
0010
0016
0003
0007
0010
0020
0003
0007
0(110
0023
0003
0007
0010
0023
0026
1300)
0007
0010
0025
053035 1290AC053CI3S
11 10 26.0 087 1b 32.0
GREEN BAT OPEN HATER ONR STA 27
55 WISCONSIN
LAKE MICHIGAN
oaoio
HATER
TEMP
CENT
15.5
15,5
0.3
0.5
U.8
1 . 1
».3
9.3
9.0
9.0
11.5
11.0
1 1.0
21.0
23.0
20. U
20.0
2U.O
17.0
16. 0
18. 0
17. U
00299
DO
PROBE
MG/L
9.1
9.6
12.1
12.0
3. 1
3.2
11.6
12.5
1 1 .2
1 1 -b
1U.2
10. 1
9.9
9.7
*•!
U. 1
a. i
7.6
5.8
9.6
9.6
7.1
2IKIS 2-1 1 1202
2 OU22 FEET
00076 00310 00312 00
TRANSP BOD BOO CHLO
SECCH1 5 WAY 6 DAY C
METERS MG/L MG/L MG
1 .5
1 .2
1.5
1 .3
5.3
0.9
6.5
6.1
1 .8
5.3
S.7
1 .8
1.9
3.3
DEPTH
00530
RESIDUE
TOT NFLT
5
IS
1U
ID
9
9
9
6
053035 1290AC053U3b
11 1U 26.0 087 15 32.0
GREEN bAY OPEN HATER DNR STA 27
55 HSCUNSIN
LAKE MICHIGAN
DATE TIME
FROM OF
TO DAY
73/09/18
71/05/20
71/06/01
71/06/01
71/07/09
71/07/09
71/08/13
71/08/13
71/09/05
71/09/05
DEPTH
FEET
0007
0007
0007
Q020
Q007
0023
0007
0026
U007
0025
00671
pHOS-DIS
ORTHO
MG/L P
0.006
0.007
O.UI 1
0.01 1
0.011
0.021
0.007
0.008
0.007
0066S
PHOS-ToT
MG/L P
0.030
0.092
0.090
0.055
U.OSI
0.023
0.028
0.031
U.010
00605
ORG N
N
MG/L
0.7QO
0.30U
0.200
0.5UO
0.300
0.300
O.bOO
O.bOO
D.IOOK
QU618
N03-N
DIS5
MG/L
0.03
U.17
0.01
0.02
0.02
o.oi
0.02
0.03
0.08
2I«IS
2
00613
N02-N
OISS
MG/L
0*001
0.015
0.01U
0.006
0.005
0.001
0.001K
0.006
u.009
00610
NH3-N
TOTAL
MG/L
0.067
U.21U
0.030
U.U2U
U.U1U
O.U3U
0.010K
0.06U
0.150
-------
STORET RETRIEVAL DATE 75/04/06
153003 1290ACIS3003
14 11 31.0 087 19 12.U
GREEN BAY OPEN WATER ONK STA 27A
SB WISCONSIN
LAKE MICHIGAN
21MS
2
DATE
FROM
TO
71/02/20
71/02/20
71/02/20
71/02/20
72Q28 72029
TIME DEpTH AZIMUTH DISTANCE
OF FR SOUTH FR SOUTH
DAy FEET DEGREES FtET
0007
0010
0020
0034
00010
AATER
TEMP
CENT
0.0
0. 1
0.1
1 .0
00299 OOQ76
DO TRANSP
PROBE SECCHI
MG/L METERb
13.2
13.0
12.2
6.7
00310
BOD
5 DAY
MG/L
2.0
9.8
21 1 1202
0036 FEET
00312 00
BOD CHLO
6 DAY C
MG/L MG
DEPTH
10
00530
RESIDUE
TOT NFLT
MG/L
0.5
lb30Cl3 1290AC153003
11 11 31.0 087 19 12.0
GREEN BAY OPEN HATER DNK STA 27A
55 M1SCUNS1N
LAKE MICHIGAN
DATE
FROM
TO
71/02/20
71/02/20
00671
TIME DEPTH PHOS-DIS
OF OKTHO
DAY FEET MG/L P
0007
0036
0.002
0.005
2 1 ft 1 S
2
OOA6R
PHOS-ToT
MG/L p
0.0(17
0.. 005
00605
ORG N
N
MG/L
0.3QO
U.5QO
00618
N03-N
DISS
MG/L
0.01
o.oi
00*13
N02-N
OISS
MG/L
0 .005
0.007
00610
NH3-N
TOTAL
MG/L
O.OB1
0.079
21112U2
OU36 FEET
DEPTH
32211 32218
CHLRPHYL PHEOPhTN
A UG/L A
CORRECTS UG/L
-------
STORET RETRIEVAL DATE 75/04/06
72028 72029
DATE TIME DEpTH AZIMUTH DISTANCE
FROM OF FR SOUTH FR SOUTH
TO DAY FEET DEGREES FEET
71/02/20
71/02/20
71/02/20
71/02/20
0003
0010
0020
0033
D0010
nATER
TErIP
CENT
0.1
0.2
0.3
1 .2
00299
DO
PROBE
MG/L
13.3
13.1
12.2
1.7
153U01 1290AC1S3001
11 13 21.0 087 16 16.0
dKEEN BAY OPEN WATER ONR STA 27B
55 WISCONSIN
LAKE MICHIGAN
2 1 (. I S>
2
21 1 12U2
OU29 FEET
DEPTH
00076 00310 00312
TRANSP BOD BOO
SECCHI 5 DAY 6 HAY
METERS MG/L M6/L
00910 005.11J
CHLORIDE RESIDUE
CL TUT NFLT
MG/L MG/L
72028 72029
DATE TIME DEPTH AZIMUTH DISTANCE
FROM OF FR SOUTH FR SOUTH
TO DAY FEET DEGREES FEET
71/02/20
71/02/20
71/02/20
0007
0012
002*
153005 l290ACIS300b
11 12 35.0 OB7 11 12.0
GREEN BAY OPEN WATER DNK STA 27C
55 WISCONSIN
LAKE MICHIGAN
21V IS
00010
nATER
TEMP
CENT
0.0
u.o
.1.1
00299
DO
PROBE
MG/L
12.6
12.2
1.0
2
0007B
TRANSP
SECCHI
METERS
U031Q
BOO
5 DAY
MG/L
2.0
1.9
21 1 1202
OU22 FEET
U0312 Uu
BOD CHLO
6 DAY C
MG/L MG
00530
RESIDUE
TOT NFLT
MG/L
5
8
153005 1290ACT53005
11 12 35.0 087 11 12-0
GREEN BAY OPEN WATER DNR STA 27C
55 WISCONSIN
LAKE MICHIGAN
21IIIS
2
DATE
FROM
TO
71/02/20
71/02/20
TIME DEpTM
OF
DAY FEET
0007
QU26
00671
pHOS-DIS
OKTHO
MG/L P
0.003
0.008
00666
PHOS-TOT
MG/L P
0.002
0.031
00605
ORG N
N
MG/L
0.300
0.200
00618
N03-N
DISS
MG/L
0.02
0.06
00613
N02-N
DISS
MG/L
0.01U
0.012
006IU
NH3-N
TOTAL
MG/L
0.021
0.501
2111202
0022 FtLT
DEPTH
32211 32210
CHLRPHYL PMEOPHTN
A UG/L A
COKRECTO UG/L
-------
STORET RETRIEVAL DATE 75/06/04
133010 1290AC133010
11 19 20.0 087 51 26*0
GREEN BAY STUDY ONR STA 28
S5 *ISCONSIN
LAKE MICHIGAN
72Q28 72029
DATE TIME DEpTH AZIMUTH DISTANCE
FROM OF FR SOUTH FR SOUTH
TO D*Y FEET DE6REES FEET
71/05/22
71/05/22
71/06/01
71/06/01
71/07/09
71/07/09
71/08/13
71/08/13
71/09/05
71/09/05
0003
0007
0003
0007
0003
0007
0003
0007
0003
0007
QOOlO 00299
1.ATER DO
TEMP PRObE
CENT MG/L
21*15
2
00078
TRANSP
SECCHI
METERS
21 1 1202
0006 FEET DEPTH
OU310
BOD
5 DAY
M(a/L
00312
BOD
6 DAY
M6/L
OU91Q OOS3Q
CHLORIDE RESIDUE
CL TOT NFLT
MG/L
MG/L
IB
16
18
,16
22
16
23
21
17
.0
.0
.0
.0
.0
.0
.0
.5
.0
6
6
6
5
5
5
5
1
a
.9
.1
• 2
.1
.8
• 2
.5
• 1
.9
0.
0.
0.
0.
1 •
8
9
9
9
2
8
1
9
5
6
.0
. 1
.8
.3
.5
8
9
9
10
10
17
6
9
11
20
2 1 K I S
2
DATE TIME
FROM OF
TO DAY
71/05/22
71/06/01
71/07/09
71/08/13
71/09/05
DEPTH
FEET
0007
0007
0007
0007
0007
00671
PHOS-D1S
ORTHO
MG/L p
0.011
0.030
0.012
o.oza
0.018
Q066<;
PHOS-TOT
MG/L p
0,090
0. 100
0.103
0.061
0.162
Q0605
ORG N
N
MG/L
0.200
0.6QO
0.700
0.6UO
0.700
0061B
N03-N
DISS
MG/L
0.05
0.11
0.20
0.08
0.11
00613
N02-N
OISS
MG/L
0.011
0.031
0.016
0.023
0.022
00610
NH3-N
TOTAL
MG/L
0.010
0. 150
O.Q3U
0.010K
0.310
133010 129UAC13301U
It 19 20.0 087 SI 26.0
GREEN BAY STUDY ONR STA 28
55 WISCONSIN
LAKE MICHIGAN
2111202
OUU6 FEET.
DEPTH
32211 322lB
CHLRPHYL PHEUPHTN
A UG/L A
CORRECTD UG/L
-------
STORET RETRIEVAL DATE 75/06/04
133011 1290AC13301I
11 18 15.0 087 52 11.0
GREEN BAY OPEN WATER OUR STA 29
55 WISCONSIN
LAKE MICHIGAN
DATE
FROM
TO
73/09/18
73/09/18
73/09/U
71/05/22
71/05/22
71/05/22
71/05/22
71/06/01
71/06/01
71/06/01
71/06/01
71/07/09
71/07/09
71/07/09
71/08/13
71/06/13
71/08/13
71/09/05
71/09/05
71/09/05
TIME DEpTH
OF
0X1 FEET
0003
0007
0010
0003
0007
0010
0016
0003
0007
0010
0016
0003
0007
0010
0003
0007
0010
0003
0007
0010
72028 72Q29
AZIMUTH DISTANCE
FR SOOTH FH SOUTH
DEGREES FEET
00010
(,ATER
TEMP
CENT
13.2
13.2
12.0
12.0
10.5
10.0
11.0
13.0
12. S
17. S
13.0
19.0
16.5
17.0
00299
DO
PROBE
MG/L
10.2
1U.2
i i.a
12.2
12.2
12.2
10.1
10.1
10. S
7.6
6.2
8.1
5.9
10.8
21AIS
2
00078
TRANSP
SECCHI
METERS
1.5
1 .9
2. 1
1 .5
1 .3
1 .6
00310
BOD
5 DAY
MG/L
8.0
1.1
5.7
5.3
2111202
0013 FEET DEPTH
00312 OLI91Q 0053Q
BOD CHLORIDE RESIDUE
6 DAY (.L TOT NFLT
MG/L MG/L MG/L
17
10
12
133U11 1290AC133UI1
Ml 18 IS.U OB7 52 11.U
GHEEN BAY OPEN WATER DNK STA 29
bS WISCONSIN
LAKt MICHIGAN
DATE
FROM
TO
73/09/18
71/05/22
71/06/01
71/07/09
71/08/13
71/09/05
TIME DEPTH
OF
DAY FEET
0007
0007
0007
0007
0007
0007
00671
pHOS-OIS
ORTHO
MG/L P
0.003
0.001
0.010
0.007
0.003
O.UQ9
0066S
PHOS-TOT
M6/L p
0.027
0.020
0,0*0
0.051
0.018
0.029
U06U&
ORS N
N
MG/L
0.200
0.2QU
0.200
0.100
0.100
0.100K
00618
N03-N
DISS
MG/L
U.01
0>01
O.UJ
0.02
0.12
0.02
2 1 .. 1 S
2
00613
N02-N
DISS
MG/L
0.001
O.OQ2
0.010
0.001K
O.OU9
0.007
21 1 12U2
OU610
NH3-N
TOTAL
M(,/L
u.UBB
0.010
O.OIOK
0.010K
O.OIOK
0.080
Uul3
3221 1
CHLRPHYL
A U6/L
CORRECTB
6.UU
FEET UEPTH
32218
PrtEopnTN
A
UG/L
b.JU
-------
STORET RETRIEVAL DATE 75/04/06
72028 72Q29
DATE TIME DEPTH AZIMUTH DISTANCE
FROM OF FR SOUTH FR SOuTH
TO DAr FEET DEGREES FEET
73/09/18
73/09/18
73/09/18
73/09/18
73/09/18
71/05/22
71/05/22
71/05/22
71/06/01
71/06/01
71/06/01
71/06/01
71/06/01
71/07/09
71/07/09
71/07/09
71/08/13
71/08/13
71/08/13
71/08/13
71/09/05
71/09/05
71/09/05
71/09/05
71/09/05
0003
0007
0010
0020
0030
0003
0013
0030
0003
0010
0020
0030
0013
0003
0010
0016
0003
0010
0016
0020
0003
0010
0023
0033
0013
133012 1290AC1330I*
IM 17 01.U 067 SO 12.U
GREEN BAT OPEN DATED DNR STA 30
55 XiSCONSIN
LAKE MICHIGAN
ooulo
ATER
TEMP
CENT
11.5
11.5
11.5
11.5
1 1.0
7.5
6.0
12.0
1 1 .5
1 1 .0
1 1 .0
6.0
20.0
18.5
13.5
20.0
19.0
17.5
13.0
17.0
17.0
17.0
17.0
17.0
OU299
DO
PROdE
M(a/L
8.1
8.1
8.1
8.3
12.2
12.3
12.0
1 1 .2
1 1 .2
10.6
10.1
8.2
8.3
8.2
7.2
8.8
8.0
6. 1
1.9
9.7
9.6
8.7
1.9
1.6
2 1 1> 1 S
2
00078 OU3 1 0
TRANSP BOD
SECCHI 5 DAT
METERS MG/L
1 .6
1 .6
2. 1
1 .8
1 .5
1 .9
21 1 1202
0029 FEET OEpTH
00312 00*10 OOS3Q
BOD CHLORIDE RtSIUUE
6 DAT CL TUT NFLT
MG/L M(,/L MG/L
18
00671
DATE TIME DEpTH pHOS-DIS
FROM OF ORTHO
TO DAY FEET MG/L P
73/09/18
0007
0.003
0.023
133012 1290AC1J3UI2
11 17 Ul.U 087 SO 12.D
GRtEN BAT OPEN *ATER bNK SIA JQ
55 A1SCUNSIN
LAKE MICHIGAN
21015
0066C,
PHOS-TOT
MG/L p
00605
ORG N
N
MG/L
0061B
N03-N
DISS
MG/L
2
00613
N02-N
DISS
MG/L
00610
NH3-N
TOTAL
MG/L
21 1
0029
3221 1
CHLRPHTL
A UG/L
CORRECTO
1202
FEET DEPTH
32218
PHEOPHlN
A
Uu/L
0.100
0.03
0.001
0. I 18
1.UO
-------
STORET RETRIEVAL DATE 75/06/06
DATE TIME
FROM OF
TO DAY
73/09/18
73/09/18
73/09/18
73/09/18
71/02/20
71/02/20
71/02/20
71/02/20
71/02/20
71/05/22
71/05/22
71/05/22
71/05/22
71/05/22
71/05/22
71/06/01
71/06/01
71/06/01
71/06/01
71/06/01
71/06/01
71/07/09
71/07/09
71/07/09
71/07/09
71/08/ 13
71/08/ 13
71/08/1 3
71/08/1 3
71/08/1 3
71/08/15
71/08/13
71/08/13
71/09/05
71/09/05
71/09/05
71/09/05
DEPTH
FEET
0003
0007
0023
0039
0003
0007
0010
0023
0039
0003
0007
0013
0030
OU33
0013
0003
0007
0010
0020
0030
0039
0003
OU07
0026
0039
0003
0007
0016
0033
0036
0039
0013
0016
0003
0007
0022
00^9
72028 72029
AZIMUTH DISTANCE
FR SOOTH FR SOUTH
DEGREES FEET
153006 1290AC153006
Ml 15 30.0 087 17 35.0
GREEN BAY UPEN HATER DNR STA 3)
55 WISCONSIN
LAKE MICHIGAN
000)0
AATER
TEMP
CENT
15.0
1S.O
Ib.U
0.0
0. 1
0.3
0.7
a.s
a. s
7.5
7.0
6.5
6.0
12.11
1 1 .5
1 l.S
1 1.5
e.o
21 .0
18.0
12.0
20.0
20.0
18. 0
12.0
11.0
1 1 .0
11.0
17.0
17.0
15.0
00299
DO
PROBE
M&/L
8.3
8.3
8.0
13.0
12.8
1 1.2
10.2
12.1
12. 1
12.5
12.2
12" U
11.8
10.6
10.1
10.2
9.9
9.0
a. 7
7.5
6.1
9.0
8.1
7.1
1.6
1.5
1.8
1.8
9.6
9.2
8.3
21MS
2
00078 00310
TRANSP BOD
SECCHl 5 DAY
METERS M&/L
1 .5
2.3
8.6
7.1
1 .6
3.6
3.3
1.8
3.7
2.9
1 .6
1.5
3.3
1 .9
2.9
1.5
21 1 1202
OU39 FEET DEPTH
00312 00910 0053Q
80D CHLORIDE RESIDUE
6 DAY CL TOT NFLT
H&/L Mfa/L M&/L
13
0.1
3
5
11
1
1
7
18
-------
STORET RETRIEVAL DATE 75/06/06
00671
DATE TIME DEPTH pHOS-DIS
FROM OF ORTHO
TO DAY FEET MG/L P
73/09/18
71/02/20
71/05/22
71/05/22
71/06/04
71/06/01
71/07/09
71/07/09
71/08/13
71/08/13
71/09/05
71/09/05
0007
0007
0007
0033
OQ07
0039
0007
0039
0007
0016
0007
0019
0.003
0.006
0.001
0.005
0.012
0.009
0.005
0.003
0.010
0.010
0.008
0.006
153006 1290AC153006
11 1b 30.0 087 17 35.0
GREEN BAY OPEN WATER DNR STA 31
5b WISCONSIN
LAKE MICHIGAN
21W1S
0066%
PHOS-TOT
MG/L P
0.031
0.006
0.017
0.017
U.060
0.070
0.018
0.011
0.018
U.02I
0.01H
0. 135
00605
ORG N
N
MG/L
0.000
0. 100K
0.200
0.3QO
0.300
0.200
0.100
0.500
O.BQO
0.200
0.200
0. 100
00618
N03-N
DISS
MG/L
0.01
0.003
0.17
0.21
0.06
0.17
0.03
0.50
0.06
1 .02
0.07
0.16
2
00613
N02-N
DISS
MG/L
0.003
0.010
0.005
0.005
0.011
0.011
0.003
O.U37
0.007
0.01 1
0.011
0.019
00610
NH3-N
TOTAL
MG/L
0.118
0.109
0.150
U.030
Q.010K
0.050
0.010K
U.030
0.010K
U.OIOK
0.060
0.06U
211
0039
3221 1
CHLRPHYL
A UG/L
CORRECTO
3.00
1.50
5.10
1.30
1.20
10.80
1202
FEET OE
32218
PHEOPHTN
A
UG/L
3.30
3.10
8.10
1 .60
-------
STORET RETRIEVAL DATE 75/04/06
72028
DATE TIME DEpTH AZIMUTH
FROM OF FR SOUTH
TO DAY FEET DEGREES
71/02/20
71/02/20
71/02/20
71/02/-20
71/02/20
0007
0010
0020
0030
0039
153007 1290AC153007
11 11 17*0 OB7 15 11>0
GREEN BAY OPEN WATER DNR STA 31A
55 WISCONSIN
LAKE MICHIGAN
ziius
72029
DISTANCE
FR SOUTH
FEET
00010
HATER
TEMP
CENT
0.0
0. 1
0. 1
0.7
1 . 1
2
00299 00078
DO TRANSP
PROBE SECCHI
MG/L METERS
12.7
12.6
12.1
9.2
5.6
21!
1 1202
OU36 FEET DEPTH
00310
BOD
5 DAY
MG/L
2.5
7.0
00312
BOD
6 DAY
MG/L
00910
CHLORIDE
CL
Mfa/L
8
10
OOS3Q
RESIDUE
TOT NFLT
MG/L
3
7
00671
DATE TIME DEpTM pHOS-DIS
FROM OF ORTHO
TO DAY FEET MG/L P
71/02/20
71/02/20
0007
0039
0.005
0.013
153007 1290AC153007
11 11 17.0 Oti7 15 11.0
GREEN BAY OPEN WATER DNK STA
55 WISCONSIN
LAKE MICHIGAN
21*IS
2
0066^
PHOS-TOT
MG/L p
0.005
0.013
00605
ORG N
N
MG/L
0.500
0.100
00618
N03-N
DlSS
MG/L
0.02
U.01
00613
N02-N
DISS
MG/L
0.012
O.Olb
00610
NH3-N
TOTAL
MG./L
0.063
0. 181
21 1
0036
3221 1
CHLRRHYL
A UG/L
CORRECTD
1202
FEET Dt
32218
PHEOPHTN
•A
UG/L
-------
STORE! RETRIEVAL DATE 75/06/06
153006 1290»C15300b
11 S3 Si.Q 087 13 58.0
GREEN BAY OPEN WATER DNR STA 32
55 *ISCUNSIN
LAKE MICHIGAN
2IMS
2
21112U2
002V FEET
DEPTH
72028 72029
DATE TIME DEpTH AZIMUTH DISTANCE
FROM OF FR SOUTH FR SOUTH
TO DAY FEET DEGREES FEET
73/09/18
73/09/18
73/09/21
71/02/20
71/02/20
71/02/20
71/02/20
71/05/22
71/05/22
71/06/01
71/06/01
71/06/01
71/07/09
71/07/09
71/07/09
71/08/13
71/08/13
71/08/1 3
7-1/08/13
71/08/13
71/09/05
71/09/05
71/09/05
0003
0007
0023
0003
0012
002U
0030
0003
0010
0003
0013
0023
Ou03
0013
0026
0003
0010
0023
0026
0030
0003
0013
OU30
QOOlO
,,ATER
TEMP
CENT
15.5
00299
00
PROBE
MG/L
B.6
15.0
0.0
U.O
0.5
1 .2
10.5
10.0
15.0
11.0
11.0
23.0
22. S
21 .0
21 .U
21 .0
19.0
15.0
11.0
18.0
17.0
17.0
8.6
13.0
12.6
1 1.6
1.5
1 1 .6
1 1 .6
lu.o
9.6
9.5
9.1
9.6
8.2
9.0
a. 7
8.3
3.2
3.2
9.6
9.0
9.2
0007B
THANSP
SECCHI
METERS
I .0
1 .0
0.9
00310 00312 00910 00530
BOO BOD CHLORIDE RLSIOUE
5 DAY 6 DAY CL TUT NFLT
MG/L MG/L MG/L MG/L
12
00671
DATE TIME DEpTH pHOS-DIS
FROM OF OkTHO
TO DAY FEET MG/L P
1S3UDB 129UACIS3008
11 13 SI'0 067 13 58.0
GREEN BAY UPtN HATER OHK STA 32
55 *ISCUNSIN
LAKt MICHIGAN
21A1S
0066=,
PHOS-TOT
MG/L p
OU605
ORG N
N
MG/L
OU618
N03-N
DISS
MG/L
2
00613
N02-N
D1SS
MG/L
UU610
NH3-N
TOTAL
MG/L
21 1 1202
JU29
3221 1
CHLKPHYL
A UG/L
CORRECTS
FEET DEPTH
32218
PHLUPHTN
A
UG/L
73/09/18
0007
0.003
0.021
O.OoO
O.Ob
0.103
7.00
-------
STORET RETRIEVAL DATE 75/06/06
153009 t290AC153UQ9
tt t7 16.0 087 tO S3.0
GREEN BAY OPEN WATER DNK STA 32A
SB WISCONSIN
LAKE MICHIGAN
DATE TIME
FROM OF
TO DAY
7H/02/27
7H/02/27
74/02/27
71/02/27
71/02/27
71/02/27
71/02/27
71/02/27
DEpTH
FEET
0003
0006
OU10
0012
0020
0021
002S
0033
72Q28
AZlMOTH
FR SOUTH
DEGREES
315.0
315.0
315.0
315.0
72Q29 000 10
DISTANCE HATER
FR SOOTH TEMP
FEET CENT
5000.0
BOOO.O
5000.0
5000.0
21VHS
2
00299 00078 00310
DO TRANSp 600
PROflE SECCHI 5 DAY
M6/L METERS M6/L
It. 8
IS. 6
It.b
It. 8
It. 2
8.Q
7.8
t.9
21 1 1202
OU29 FEET
1)0312 00
BOD CHLO
6 DAY C
MG/L Mb
DEPTH
RESIDUE
TUT NFLT
Mfi/L
-------
STORET RETRIEVAL DATE 75/06/06
163010 1290AC153010
HI 18 07.0 087 13 19.0
GREEN SAY OPEN WATER ONK STA 32B
55 WISCONSIN
LAKE MICHIGAN
72028 72029 00010
DATE TIME DEPTH A-ZlMUTH DISTANCE AATER
FROM OF F" SOUTH FR SOUTH TEMP
TO DAY FEET DEGREES FEET CENT
71/02/27
71/02/27
71/02/27
71/02/27
71/02/27
71/02/27
71/02/27
71/02/27
71/02/27
71/02/27
0003
0006
0010
0012
0020
0021
0030
0031
OU39
0013
315.. 0
315.0
315.0
315.0
315.0
5000.0
5000.0
5000.0
5000,0
5000.0
00299
DO
PROBE
Mfa/L
15.2
it.a
11.8
11.2
11.6
11.0
12.u
1 1 .2
6.6
6.1
21IMS
2
2111202
UU1S FEET
DEPTH
00078 00310 00312 009tU 00530
TRAMSP BOO BOO CHLUKIOE RESIDUE
SECCHI $ DAY 6 DAY CL TOT NFLT
METERb M&/L MG/L MG/L MG/L
153U11 1290AC153011
1M Ifa 55.0 087 1b 51.U
GKEEN BAY OPEN WATER UNK STA 32C
S5 WISCONSIN
LAKE MICHIGAN
72028
DATE TIME DEPTH AZIMUTH
FROM OF FR SOUTH
TO DAY FEET DEGREES
71/02/27
71/02/27
71/02/27
71/02/27
71/02/27
0003
0010
0020
0030
0013
2 1 >. I S 2111202
72029
DISTANCE
FR SOUTH
FEET
QOOIO
WATER
TEMP
CENT
00299
00
PROBE
MG/L
15. 1
ib.O
11.0
12.0
7.6
i
0007B
TRANSP
SECCHI
METERS
OU19 FEET
U0310 U0312 Ou
BOD BOD CHLO
5 DAY 6 DAY C
MG/L MG/L Ml,
DEPTH
00530
RESIDUE
TUT NFLT
MG/L
-------
STORET RETRIEVAL DATE 75/06/06
72028
DATE TIME DEPTH AZIMUTH
FROM OF F« SOUTH
TO DAY FEET DEGREES
71/05/22 0003
74/05/22 0007
71/06/01 0003
74/06/04 0007
74/07/08 0003
74/07/08 0007
7H/08/13 0003
71/08/13 0007
74/08/13 0010
71/09/05 0005
74/09/05 0007
133013 4290AC4330I3
14 53 32.0 087 50 07.0
GREEN BAY STUDY DNR STA 33
55 WISCONSIN
LAKE MICHIGAN
21*15 21
72029
DISTANCE
FR SOUTH
FEET
00010
HATER
TEMP
CENT
16.0
11.0
18.0
17.0
27.5
22.0
22.0
16.0
19.0
00299
DO
PROBE
MG/L
1.8
6.8
6.Q
6.0
6.S
1.8
6.0
3.9
8.9
2
00078
TRANSP
SECCHI
METERS
0.7
1.2
1.0
1.2
1.2
QUO.
00310 00312
BOD BOD
5 DAY 6 DAY
MG/L MG/L
6.1
3.6
1.3
S.7
3.3
0006 FEET DEPTH
00940 0053Q
CHLORIDE RESIDUE
CL TOT NFLT
MG/L
MG/L
13
2
2
5
433013 129QAC133013
44 53 32.0 067 50 07*0
GREEN BAY STUDY ONR STA 33
55 WISCONSIN
LAKE MICHIGAN
21*15 211
2 0006
DATE TIME
FROM OF
TO DAY
74/05/22
74/06/01
74/07/08
74/08/13
74/09/05
DEPTH
FEET
0007
0007
0007
0007
0007
00671
pHOS-OIS
ORTHO
MG/L P
0.009
0.005
0.013
0.010
0.012
OQfe6S 00&05
PHOS-TOT
M'G/L p
0.062
0.080
0.046
0.013
0.033
ORG
N
N
MG/L
0
0
3
0
0
.300
.400
• 100
.300
.100
00618
N03-N
DISS
MG/L
0.
0.
1 .
0.
0.
60
64
13
82
86
00613
N02-N
DISS
MG/L
0.032
0.057
0.137
0.007
0.081
00610 32211
NH3-N CHLRPHYL
TOTAL A UG/L
MG/L CORRECTD
0.410
0.1BU
0.15U
0.010K
0.170
1202
FEET DEI
32218
PHEOPHTN
A
UG/L
-------
STORE! RETRIEVAL DATE 75/06/06
72028 72029
DATE TIME DEpTH AZIMUTH DISTANCE
FROM OF pR SOUTH FR SOUTH
TO DAT FEET DEGREES FEET
71/05/22
71/05/22
71/05/22
71/06/01
71/07/09
71/07/0?
71/07/09
71/08/13
71/08/13
71/08/13
71/09/05
71/09/05
71/09/05
0003
UOIO
0023
0001
0003
001U
0023
0003
0010
U016
0003
0010
0020
00010
*ATER
TEMP
CENT
12.5
1 1 .0
7.0
15.5
20.0
13. U
12.5
17.U
13.0
1 I .0
16.0
15.0
15.0
00299
00
PROBE
Mb/I.
10.1
I 1 .5
1 1 .8
10.2
8.1
7.5
7.5
7.8
5.0
5.0
IU.6
10.3
9.9
133011 1290AC133011
11 53 15.0 087 IB 56.0
GREEN BAT OPEN WATER ON* STA j
55 WISCONSIN
LAKE MICHIGAN
ZIMS
2
21 I 1202
UQU6 FEET
OLPTH
00078
TRANSP
5ECCHI
METERS
1 .3
I .2
I .6
1.2
00310 00312 00910 OUBJO
BUD BOO CHLuKJDt RESIDUE
5 UAT 6 DAY LL TOT NFLT
Mb/L M6/L Mb/L Mb/L
72028
DATE TIME DEPTH AZIMUTH
FROM OF FR SOUTH
TO DAY FEET DEGREES
71/05/22
71/05/22
71/05/22
71/06/01
71/07/09
71/08/13
71/09/05
71/09/05
0003
001U
0016
QQU3
0003
0003
0003
0007
133015 1290AC1330I5
11 bi 11.U 0»7 "»» 21.0
(SHEEN bAY OPEN HATER DI1K STA 31,*
55 IIISCONSIN
LAKE MICHIGAN
72029
DISTANCE
FR SOUTH
FEET
00010
»ATER
TEMP
'CENT
1 1.5
1 1 .0
10.0
16.0
19.0
18.0
17. U
17.0
00299
DO
PROBE
Mb/L
1 1 .7
1 1 .8
12.2
9.B
8.9
»• I
1 1 .0
1 1.1
21US 211 12U2
2 OUU3 FEET
00076 1)0310 00312 00
TRANSP BOD BOD CHLUl
SECCH1 5 DAY 6 DAY Cl
METERS Mb/L Mb/L Mi,
1 . f
1.2
1 .8
1 .8
1 .6
DEPTH
UUbJQ
RESIDUE
TUT NFLT
MS/L
-------
STORET RETRIEVAL DATE 75/06/06
-.33017 1290AC1330I7
11 52 09.0 OB7 11 28*0
GREEN BAY OPEN WATER ONR STA 35
SB WISCONSIN
LAKE MICHIGAN
21*15 2111202
2 OU1S FEET DEPTH
DATE TIME
FROM OF
TO DAY
71/02/27
71/02/27
71/02/27
71/02/27
71/02/27
71/02/27
71/02/27
71/02/27
71/02/27
71/02/27
71/02/27
71/02/27
71/02/27
71/02/27
71/02/27
71/05/22
71/05/22
71/05/22
71/05/22
71/05/22
71/06/01
71/06/01
71/06/01
71/06/01
71/06/01
71/06/01
71/07/09
71/07/09
71/07/09
71/07/09
71/07/09
71/07/09
71/08/13
71/08/13
71/08/13
71/08/13
71/OB/ 13
71/08/13
71/08/1 3
71/09/05
71/09/05
71/09/05
71/09/05
72028
DEPTH AZIMUTH
FR SOUTH
FEET DEGREES
0005 135.0
0006
0007 135.0
0010 135.0
0011 135.0
0012
0019 135.0
0020 135.0
0021
0029 135.0
0030 135.0
0031
0013 135.0
0011 135.0
001S
0003
0007
0020
0033
0039
0003
0007
0010
OU20
0030
0013
0003
0007
0016
0033
0039
0016
0003
0007
0013
0026
0030
0033
0016
0003
0007
0023
0019
72029
DISTANCE
FR SOUTH
FEET
5000.0
10000.0
5000.0
10000.0
10000.0
5000.0
10000.0
5000.0
5UOO.O
10000.0
000 1 0
nATEK
TEMP
CENT
9.0
9.0
6.5
6.0
5.0
12.0
12.0
1 1 .0
8.0
7.0
21 .0
19.0
15.5
11.0
11.0
19.5
19.0
16.0
11.0
10.5
9.8
17.0
17.0
15.0
U0299 00078 00310 00312
00 TRANSP SOD BOD
PROBE SECCH1 5 DAY 6 DAY
M6/L METERS Mb/L MG/L
15.8
lb.9
11.6
15.2
11.2
15.5
13.2
13. 0
11.0
11.6
12.2
12.6
9.0
8.8
12.2
12.2 1.9
12.2 5.3
12.2
12. U 1.1
1 1 .8
10.9 2.5
2.0
10.8
1U.8
1 l.U
10.2 1 .6
B.B 1.8
1. 1
a. 3
7.5
7.1
7.8 7.8
9.1 2.1
t.b
D.8
7.1
1.8
1.8
5.0 3.3
9.2 1.9
3./
9.7
9.7 2.5
00910 0053Q
CMLUKIOE RESIDUE
CL TUT NFcT
Mi/L MS/L
7 t
7 7
8 0.1
6 0.1
8 . b
8 5
8 0.1
7 5
8 6
7 I
-------
STORET RETRIEVAL DATE 75/06/06
DATE
FROM
TO
71/05/22
71/05/22
71/06/01
71/06/01
71/07/09
71/07/09
71/08/13
71/08/13
71/09/05
71/09/05
00671
TIME DEPTH pHOS-OIS
OF ORTHO
DAY FEET MG/L p
0007
0033
0007
0013
0007
0016
0007
0016
0007
0019
0.009
0.009
0.005
0.003
0.005
0.010
0.003
0.012
0.007
0.003
211MS
0066S
PHOS-TOT
MG/L p
0.027
0.030
0.040
0.060
0.01Q
0.051
0.037
0.021
0.021
0.020
00605
ORG N
N
MG/L
0.100
0.100
0. 100K
0.200
0. 100K
0.800
0.200
0.200
0.100
O.lOOK
00618
N03-N
DISS
Mfa/L
0.02
0.38
0.01
0.25
0.03
O.S6
0.01
1 .08
0.09
0.91
2
006 13
N02-N
DISS
MG/L
0.003
0.002
0.008
0.013
0.003
0.038
0.002
0.001
0.010
0.020
00610
NH3-N
TOTAL
MG/L
0.000
0.002
0.030
0.010
0.010
0.030
0.010K
0.010K
0.020
0.170
133017 1290AC133017
HI 52 09.0 087 11 28.0
GREEN BAY OPEN WATER DNR STA 35
SS WISCONSIN
LAKE MICHIGAN
21112U2
0015 FEET DEPTH
32211 32218
CHLRPHYL PHEOPHTN
A UG/L A
CORRECTO UG/L
6.20
3*60
9.10
5.90
0.80
1 .10
9.50
S.90
-------
5TORET RETRIEVAL DATE 75/06/06
72028 7202v
DATE TIME DEPTH AZIMUTH DISTANCE
FROM OF FR SOUTH FR SOUTH
TO DAT FEET DEGREES FEET
7M/02/27
7M/02/27
71/02/27
74/02/27
7M/02/27
71/05/22
71/05/22
71/05/22
71/05/22
71/06/01
71/06/01
71/06/01
71/06/04
71/06/04
71/U7/09
71/07/09
71/07/09
71/07/09
74/07/09
74/07/09
74/07/09
74/07/09
71/08/13
71/08/13
71/08/13
71/08/13
74/08/13
71/08/13
71/08/13
74/09/05
71/09/05
71/09/OS
U003
0010
0020
0030
0013
0003
0013
0030
OOM3
0003
0010
0020
OU30
OUM3
0003
0016
OU23
0026
0030
0033
0039
0016
0003
0013
UG3U
0033
U036
0039
0043
0003
0023
0019
153012 1290ACI53U12
MM 50 16.u UH1 Ml 02-U
GREEN bAY OPEN HATER DNR STA 36
55 HISCONSIN
LAKE MICHIGAN
ooo I o
CATER
TEMP
CENT
7.0
6.5
6.0
6.0
1 1 .5
1 1 .0
10.0
10. U
6.U
21 .0
2U.U
19. a
19.0
1 1 .U
9.0
9.0
9.0
20.5
20. a
17.0
10.5
10. 5
lU.b
10.5
1 7.U
17.0
I 7.0
2 1 1. I b
2
00299 0007d 00310
00 TRANSp SOD
PROBE SECCH1 5 UAY
MG/L METERS MG/L
11.6
14.1
12.7
1U.5
6.2
12.3 2.7
12, M
12.0
12.0
11.5 2.7
1 1 .7
1 1 .1
11 .2
10.7
e. a 1.6
8.2
a. 3
8.M
8.5
6.2
6.2
6.2
9.2 1.5
8.9
8.1
1.9
1.9
M.V
1.9
9.9 1.8
9.6
9.8
21 1 12U2
QUbS FtET
00312 Oir
BOD CHLO
6 UAY LI
MG/L Mb
0053Q
RESIDUE
TUT NFLT
MG/L
153013 129UAC1S3013
MM M9 3L.O U87 38 35.0
GKEEN BAY OPEN HATER ONR STA 37
55 nlSCONSlN
LAKE MICHIGAN
72026 72029
DATE TIME DEPTH AZIMUTH DISTANCE
FROM OF FR SOUTH FR SOUTH
TO DAY FEET DEGREES FEET
71/02/27
7M/02/27
71/02/27
74/02/27
0003
0010
0020
0033
21HIS
00010
,,AT£R
TEMP
CENT
OU299
DO
PSOBt
MG/L
13.1
13.1
13. U
9.1
2
00078
TRANSP
SECCHI
METERS
00310
60D
5 UAY
MG/L
211 1202
OU39 FEET
003.12 00
BOO CHLUI
6 DAY LI
MG/L M«
DEPTH
005JQ
RESIDUE
TUT NFLT
MG/L
-------
STORET RETRIEVAL DATE 75/04/06
72028 72029
DATE TIME DEPTH AZIMUTH DISTANCE
FROM OF F« SOUTH FH SOUTH
TO DAY FEET DEGREES FEET
73/09/21
73/09/21
73/09/21
73/09/21
73/09/21
71/05/21
71/05/21
71/05/21
71/06/01
71/06/01
71/06/01
71/06/01
71/07/08
71/07/08
71/07/08
71/07/08
71/07/08
71/07/08
71/08/13
71/08/13
71/08/13
71/08/13
71/09/05
71/09/05
71/09/05
71/09/05
0003
0007
0010
0020
0023
0003
0007
0016
0003
0007
0010
0016
0003
0007
0010
0013
0016
0020
0003
0007
0010
0020
0003
0007
0010
0020
133018 129UAC13301B
11 !>6 Q2.0 087 HI bl.u
GREEN BAY OPEN WATER DNR STA 38
55 WISCONSIN
LAKE MICHIGAN
00010
[,ATER
TEMP
CENT
13. 5
13.6
13.5
13.5
9.0
9.0
7.0
13. 5
13.0
13.0
2U.5
19.0
18.0
15.0
11.9
17.0
15.0
1 1 .0
14.0
15.0
15.0
00299
DO
PROBE
Mta/L
9.6
9.5
9.5
9.1
12.2
12.2
12.2
10. 6
10.5
IU.5
9.1
7.1
8.0
7.6
5.6
10.6
10.6
10.6
21AIS 211 1202
2 0013 FEET
00078 00310 00312 OO'
TRANSp flOD BOD CHLO
SECCHI 5 DAY 6 DAY Ci
METERb Mfa/L Mb/L M<,
1.5
1 .9
3.3
2. 1
2.5
1.9
1.9
1 .9
1.5
1.9
1.1
DEPTH
OOS3Q
RESIDUE
TOT NFLT
M6/L
133018 1290AC1330IB
11 56 02.U OB7 11 51.0
SHEEN BAY OPEN WATER DNR STA 38
55 .11 SCONS IN
LAKt MICHIGAN
DATE
FROM
TO
73/09/21
71/05/21
71/06/01
71/07/08
71/08/ 13
71/09/05
TIME DEpTH
OF
DAY FEET
0007
0007
0007
0007
0007
0007
00671
PHOS-DIS
OKTHO
MG/L P
0.002
O.OU3
0.006
0.006
0.012
0.003
0066S
PHOS-ToT
MG/L P
a. oas
0.017
0.06U
0.021
0.028
U.02B
00605
ORG N
N
MG/L
0. 100
0.200
0.200
1 .700
U.3UU
O.JO UK
00618
N03-N
DISS
MG/L
U.QQi
0.02
0.02
0.02
0. 26
0*28
2 1 ft 1 S
2
0061 3
N 0 2 - N
DISS
MG/L
O.OQO
0.005
0 . DOB
0.008
O.OOIK
0.017
21 1 1202
0013 FEET DE
00610 32211
NH3-N CHLRPHYL
TOTAL A UG/L
MG/L COKRECTU
0.030 9.00
0. 170
a. too
0.210
U.OIOK
0.100
32218
PHEOphlN
A
U4/L
3. 00
-------
STORE! RETRIEVAL DATE 75/06/06
72Q28 72029
DATE TIME OEpTH AZIMUTH DISTANCE
FROM OF FR SOUTH FR SOUTH
TO DAY FEET DEGREES FEET
73/09/2M
73/09/21
73/09/2M
73/09/21
73/09/21
73/09/2M
73/09/21
71/05/21
71/05/21
71/05/21
7M/OS/21
7M/OS/21
7M/06/01
71/06/01
7M/06/OM
7M/06/OM
7M/06/01
71/07/08
71/07/08
71/07/08
71/08/13
71/08/ 13
71/08/13
71/08/13
71/09/U5
71/09/05
71/09/05
0003
0007
0010
0020
0030
0039
OOM9
0003
0010
002U
0030
0013
0003
0010
U020
0030
0013
0003
U023
OUM7
0003
0016
0033
0016
0003
0023
0019
153011 M290ACI530I1
MM 53 38.Q 067 MO 13.U
GREEN BAY OPEN HATER CiNR STA 39
55 KISCUNSIN
LAKE MICHIGAN
00010
HATER
TEMP
CENT
11.0
1M.Q
1M.Q
1M.Q
11. Q
13. S
e.o
7.D
6.0
6.0
6.0
12. S
12.0
10. S
10.0
S.O
20. S
17.0
13.0
19.0
16.0
13.0
10.0
17.0
16.0
16.0
21MS 21 1 1202
2 01)62 FEET
00299 0007B 00310 Q03I2 00
DO TRANSP BOD BOO CMLO
PROBE SECCHI 5 DAY 6 DAY C
MS/L METERS MG/L MG/L Mb
V.8 1.9
9.7
9.7
9.7
9.7
9.6
12.0 2.M
12.0
1 1 .6
1 1 .6
1 1 .8
1 1 '0 2.M
1 1 .2
i i.e
1 1 .6
lu.e
H.B 2.M
/•6
7.M
9.2 2.M
7.9
6.1
6.0
9.2 2. 1
9.6
9-3
DEPTH
OUS30
RESIDUE
TOT NFLT
MG/L
UQ671 0066S
DATE TIME DEpTH pHOS-OIS PHOS-ToT
FROM OF ORTHO
TO DAY FEET MG/L P MG/L p
153011 1290ACIS30I1
MM S3 36.0 087 MU 13.U
GREEN BAY OPEN WATER ONR STA 39
55 H1SCONSIN
LAKE MICHIGAN
00605
ORG N
N
MG/L
00618
N03-N
DISS
MG/L
2 1 « 1 S
2
00613
N02-N
0155
MG/L
0061Q
NH3-N
TOTAL
MG/L
2111202
0062 FEET otPTH
32211 32218
CHLRPHYL PHEOPhTN
A UG/L A
CORRECTO UG/L
0007
0.003
0.0)2
0.100
0.01
-------
STORET RETRIEVAL DATE 75/06/06
72028 72029
DATE TIME DEPTH AZIMUTH DISTANCE
FROM OF FR SOUTH FR SOUTH
TO' DAY FEET DEGREES FEET
73/09/21
73/09/21
73/09/21
73/09/21
73/09/21
73/09/21
73/09/21
71/05/21
71/05/21
71/05/21
71/05/21
71/05/21
71/06/01
71/06/01
71/06/01
71/06/01
71/06/01
71/06/01
71/07/08
71/07/08
71/07/08
71/07/08
71/08/13
71/08/13
71/08/13
71/08/13
71/08/13
71/09/05
71/09/05
71/09/05
7^/09/05
71/09/05
0003
0007
0010
0020
0030
0039
0019
0003
0007
0013
0030
0013
0003
0007
0010
0020
0030
0013
0003
0007
0023
0016
0003
0007
0016
0033
0016
0003
0007
0015
UU30
0019
00010
ftATER
TEMP
CENT
11.5
1H.5
11.5
11.0
11. U
11.0
e.o
8.0
6.3
6.3
6.5
11.0
13.0
12.0
12. U
12. U
22.0
19.0
10.0
19.0
IB. 5
11.5
10.0
17.0
17.0
17.0
16.0
00299
DO
PROBE
MG/L
10.7
9.5
9.1
8.7
8.1
8.3
12.2
12.2
12.0
12. 1
1 1 .5
10.5
10.1
10.8
10.8
10.7
9.8
8.1
7.5
9.1
8.6
6.2
1.3
10.1
9.6
9.2
1.8
153U15 1290AC153015
11 51 1S.O 087 35 55.0
GRtEN BAY OPEN WATER DNR STA 10
55 WISCONSIN
LAKE MICHIGAN
21«IS
2
00078 00310
TRANSP 600
SECCHI 5 DAY
METERS MG/L
I .5
1.9
1 .8
1 .2
2.1
1 .9
2.5
3.3
1.9
3.7
3.3
2.5
21112U2
0052 FEET DEPTH
00312 00910 OQb3Q
BOD CHLORIDE RESIDUE
6 DAY CL TUT NFLT
MG/L M(,/L MG/L
3.3
3.7
5.b
3.1
10
10
9
7
10
B
9
7
9
9
26
1
6
12
-------
STORET RETRIEVAL DATE 75/06/06
U067|
•DATE TIME DEpTH pHOS-DIS
FROM OF OKTHO
TO DAY FEET MG/L P
73/09/21
71/05/21
71/05/21
71/06/01
71/06/01
71/07/08
71/07/08
71/08/13
71/08/13
71/09/05
71/09/05
0007
0007
0013
0007
0013
0007
0016
0007
0016
0007
0019
0.002
0.006
0.020
O.UI2
0.019
O.U09
0.010
0.007
0.007
0.003
0.002
0066s
PHOS-ToT
MG/L P
0.005
0.017
0.021
0.170
0.070
0.017
0.021
0.059
0.017
0.017
0.037
00605
ORG N
N
MG/L
0.100
U.I 00
0.100
1.000
0.200
0.700
1.200
0.300
0.200
0.100K
0. IQOK
00618
N03-N
D1SS
MG/L
0.01
0.11
0.30
0.27
O.U3
U.01
0.36
0.03
1 .05
0.07
0.91
2l»IS
2
00613
N02-N
DISS
MG/L
0.002
0.009
0.009
0.013
0.009
0.006
0.038
0.001
0.001K
0.006
0.029
00610
NH3-N
TOTAL
MG/L
0.016
Q.21U
0. 100
0. 100
0.250
0.000
0.000
U.010K
0.010K
0.120
0.1 10
153015 1290AC15301S
14 51 18.0 087 35 55.0
GREEN BAY OPEN H/ATER DNK STA 1Q
5& WISCONSIN
LAKE MICHIGAN
2111202
0052 FEET DEPTH
32211 322)8
CHLRpHYL PHEOPHTN
A UG/L A
CORRECTD UG/L
5.00
1.00
-------
STORET RETRIEVAL DATE 75/06/06
72Q28
DATE TIME DEPTH AZIMUTH
FROM OF fR SOUTH
TO DAY FEET DEGREES
71/05/21
71/05/21
71/05/21
71/06/01
71/07/08
71/07/08
71/07/08
71/08/13
71/08/13
71/08/13
71/09/05
71/09/05
0003
0007
0010
0007
0003
0007
0010
0003
0007
0010
0003
0007
383003 1290AC383003
11 58 25.0 087 39 15.0
GREEN BAY STUDY DNR STA 11
55 WISCONSIN
LAKE MICHIGAN
/2029
DISTANCE
FR SOUTH
FEET
00010
V.ATER
TEMP
CENT
15.0
15.0
15.0
17.5
25.0
25.0
22.0
17.0
19.0
18.0
00299
DO
PROBE
MG/L
5.7
5.7
6.0
5.2
1.5
1 .7
3.8
5.7
6.1
6.0
2I*IS 2111202
2 0009 FEET
00078 00310 00312 00
TRANSP BOO BOD CHLO
SECCH1 5 DAY 6 DAY C
METERS MG/L MG/L Mb
0.8
7.0
1.0 1.1
1.2
7.1
1.2
1.1
1.2
DEPTH
0053Q
RtSIUUE
TUT NFLT
MG/L
11
1
2
1
5
i
u
383003 1290AC383003
11 58 25.0 087 39 15.U
GREEN BAY STUDY DNR STA 11
55 WISCONSIN
LAKE MICHIGAN
DATE
FROM
TO
71/05/21
71/06/01
71/07/08
71/08/13
71/09/05
00671
TIME DEpTH pHOS-DIS
OF ORTHO
DAY FEET MG/L P
0007
0007
0007
0007
0007
0.005
0.019
0.021
0.005
21*IS
00665
PHOS-TOT
MG/L p
0.026
0.070
0.017
0.032
0.033
00605
CRG N
N
MG/L
O.lOOK
0.100
0.500
0.300
0.300
00618
N03-N
DISS
MG/L
0.03
0.05
0.01
0.13
0.31
2
00613
N02-N
DISS
HG/L
0.018
0.017
0.026
0.001
0.019
00610
NH3-N
TOTAL
MG/L
0.260
0.070
0.020
0.010K
0.017
21 1
000?
32211
CHLRPHYL
A UG/L
CORRECTD
1202
FEET DE
32218
PHEOPHTN
A
UG/L
-------
STORET RETRIEVAL DATE 75/06/06
72028 72029
DATE TIME DEpTN AZIMUTH DISTANCE
FROM OF FR SOUTH FR SOUTH
TO DAY FEET DEGREES FEET
73/09/21
73/09/21
73/09/21
73/09/21
73/09/21
71/05/21
71/05/21
71/05/21
71/05/21
71/06/01
71/06/01
71/06/01
71/06/01
71/06/01
71/07/08
71/07/08
71/07/08
71/08/13
7t/08/13
71/08/13
71/09/05
71/09/05
71/09/05
0003
0007
0010
0020
0030
0003
0013
0030
0013
0003
0010
0020
0030
0015
0003
0017
0030
0003
0016
0030
0003
OQ20
0039
3B3U01 129UAC383001
11 57 QS.O OB7 39 16.0
GKEEN BAT OPEN *ATtR ONR STA 12
Sb KISCONSIN
LAKE MICHIGAN
ooolo
LATER
TEMP
CENT
13. S
13.5
13. S
13.5
7.5
5.0
S.O
S.O
13.0
12.0
6.0
S.O
S.O
2U.O
12. 5
1 1 .0
18. 5
16.0
11. S
17.0
IS. 0
11.0
00299
00
PROgE
Mb/L
9.3
9.3
9.3
9.2
12.2
12.0
11.1
11.2
10. B
10,7
10.2
10.1
10.2
10. S
9.5
7.2
9.1
7.7
6.6
10.2
d.8
7.9
21WIS 2111202
2 OU36 FEET
00078 00310 00312 Ou
TRANSP BOD bOD CHLU
bECCHI 5 UAT 6 DAT C
METERb Mb/L MG/L Mb
2.1
2.5
1 .9
1 .8
1 .6
1 .V
DEPTH
00530
fitSIUUL
TOT MFLT
MG/L
38JOUM 129UAt3B3UU1
11 b7 ub.U C.67 39 16>U
&KE.EN BAT OPtN AATER u(«h bTA s
SB UlSCUNSIN
LAKE MICHIbAN
21Alb
DATE
FROM
TO
/09/2'
TIME
OF
DAY
1
OEpTH
FEET
OOP?
00671
PHOS-DIS
ORTHO
MS/L P
0.002
0066S
PHOS-ToT
M&/L p
0.003
00605
ORG N
N
Mb/L
0. IQO
G061B
N03-N
DISS
Mfa/L
0.03
2
00613
N02-N
OISS
MG/L
0 .Ou 1
U06IQ
NH3-N
TOIAL
MS/L
0.061
21 1
0036
32211
CHLRPHYL
A UG/L
COKKECTL1
1.0U
1202
FtET DE
32218
HHEuphTw
A
Ub/L
i.oo
-------
STORET RETRIEVAL DATE 75/06/06
153016 1290AC153016
11 55 08*0 087 35 37.u
GREEN BAY OPEN WATER UNK STA 13
55 WISCONSIN
LAKE MICHIGAN
72Q28 72029
DATE TIME DEPTH AZIMUTH DISTANCE
FROM OF FR SOUTH FR SOUTH
TO DAY FEET DEGREES FEET
73/09/21
73/09/21
73/09/21
73/09/21
73/09/21
71/05/21
71/05/21
7H/05/21
71/05/21
71/05/21
71/05/21
71/06/01
71/06/01
71/06/01
71/06/OH
71/06/01
71/06/01
71/07/08
71/07/08
71/07/08
71/07/08
71/08/13
71/08/13
71/08/13
71/08/13
71/08/13
71/09/05
71/09/05
71/09/05
71/09/05
0003
0007
0020
0039
OOM9
0003
0007
0013
0030
0013
OOB9
0003
0007
0010
0020
0030
0013
0003
0007
0023
0016
0003
0007
0016
0030
0016
0003
0007
002S
0050
00010
AATEK
TEMP
CENT
00299
iiO
PROBE
M6/L
2H IS
2
0007d
TRANSP
SECCHI
METERS
U0310
SOD
5 DAY
Ma/L
11.0
8.7
11.0
11 .0
13.0
8.0
8.0
6,5
5.0
1.5
1.5
13.0
12. 5
10.0
7.0
6.5
20.0
17.0
12.0
18.0
16.5
12.5
9.0
18.0
16.0
13.0
8
8
a
12
12
12
1 1
1 1
1
1
1
1
1
1
9
7
9
9
8
6
7
9
9
7
• 7
.7
.7
• 2
.2
.2
.8
>8
.8
.2
.2
•3
.2
• 2
.0
.1
.5
.0
.)
.7
.6
.5
.5
.5
2. 1
2.5
2.5
1 .b
2.3
2. 1
2111202
006b KEET DEPTH
00312 00940 00530
BOD CHLORIDE RESIDUE
6 DAY CL TUT NFLT
MS/L MC./L M&/L
2.9
3.7
2.9
2.5
l.b
1.9
U.I
-------
STORET RETRIEVAL DATE 75/06/06
153016 1290AC153016
11 55 08.0 087 3b 37.U
GREEN BAY OPEN WATER DNK STA H3
55 WISCONSIN
LAKE MICHIGAN
DATE
FROM
TO
73/09/21
71/05/21
71/05/21
71/04/01
71/07/08
71/08/13
71/09/05
TIME DEpTM
OF
DAT FEET
0007
0007
0059
0007
0007
0007
0007
00671
pHOS-DIS
ORTHO
MG/L P
0.003
0.012
O.U02
0.012
0.003
0.003
0066s
PHOS-TOT
MG/L p
0.011
0.013
0.016
0.06Q
0.032
0.031
0.025
00605
ORG N
N
MG/L
0. 100
0. 1QU
0.100
O.lQOK
0.700
0.2QO
O.lOOK
OU618
N03-N
DISS
MG/L
0.01
0.27
0.16
0-OlK
0.03
0.1 1
0.19
21W1S
2
00613
N02-N
DISS
MG/L
0.002
0.017
0.018
0.01)6
0.077
O.Q01K
0.011
21 1 1202
0065 FEET BEpTH
00610
NH3-N
TOTAL
MG/'L
0.016
0.230
0. 160
0.120
0.05U
0.010K
0.070
3221 1
CHLHpHYL
A UG/L
COKRECTD
6.00
3.60
6.60
1 1 .70
1.10
32218
pHEOphTN
A
UG/L
1 .00
1.60
1.70
-------
STORE! RETRIEVAL DATE 75/06/06
72028 72029
DATE TIME DEPTH AZIMUTH DISTANCE
FROM OF FR SOUTH FR SOUTH
TO DAY FEET DEGREES FEET
73/09/21
73/09/21
73/09/21
73/09/21
73/09/21
73/09/21
71/05/21
71/05/21
71/05/21
71/05/21
71/06/01
71/06/01
71/06/01
71/06/01
71/06/01
71/07/06
71/07/08
71/07/08
71/08/13
71/08/13
71/08/13
71/08/ 1 3
71/09/05
71/09/05
71/09/05
71/09/05
0003
0007
0010
0020
0030
0039
0003
0013
0030
0013
0003
0010
0020
0030
0013
0003
0023
0016
0003
0016
OU33
0016
0003
0023
0013
0019
Ib3U I 7 429UA1.15301 7
11 53 02.CJ 0«7 32 1 3«U
GREEN BAY OPtu HATER QMK STA Ml
55 H1SCUNSIN
LAKE MICHIGAN
OOQ1U
sATER
TEMP
CENT
11.0
11.0
1 1.U
11. U
11.0
8.5
7.0
6.5
6.0
1 J.O
12.0
12.0
1 1 .5
11. b
21 .0
19. a
1 1 .0
19.5
1 8.0
16.0
16.0
ie.o
1 7.0
16. 0
13.0
OU299
IjQ
PROBL
MG/L
9.2
9. 1
9.U
O.B
b.7
12.2
12.3
12. U
12.1
11.1
11.1
1 1 >2
11.2
ll.U
9.0
8.6
7.9
9.1
6.1
7.9
/.B
10.0
9.1
8.0
7.6
21 . IS 211 1^Q2
2 OU6b fttT
00078 00310 UU312 Ou
TRANSP BOO BOD CMLO
SECCHI 5 UAY 6 DAY C
METERb MG/L MS/L MG
2. 1
7. 1
1 .6
2.1
2.3
1 .8
Oub-10
Rtbiout
TUT NFLT
MG/L
00671
DATE TIME OEpTH pHOS-DIS
FROM OF OKTHO
TO DAY FEET MG/L P
73/09/21 0007
21A1S
2
0066<;
PHOS-ToT
MG/L p
0.012
0060S
ORG N
N
MG/L
0. 100
00618
N 0 J - W
D1SS
MG/L
0.03
00613
N02-N
UISS
MG/L
o.oon
00610
NH3-N
TOTAL
MG/L
0.00
153017 129QAClb3U 1 /
11 S3 02.U 067 32 13.U
GREEN BAY OPEN IIATEx UNN S1A <| 1
SB HISCUnbM
LAKE MICHIGAN
21 I 1202
0065 FEtT utf
32211 32218
CHLKpHYL PHEUPHTN
A UG/L A
COKRECTU Uu/L
5.Ob
. UU
-------
STORE! RETRIEVAL DATE 75/06/06
72028 72029
DATE TIME DEPTH AZIMUTH DISTANCE
FROM OF FR SOUTH FR SOUTH
TO DAY FEET DEGREES FEET
73/09/21
73/09/21
73/09/21
73/09/21
73/09/21
71/06/01
71/06/01
71/06/C1
71/06/01
71/U6/01
71/06/01
71/07/08
71/07/08
71/07/08
71/07/08
71/08/13
71/08/13
71/08/13
71/08/13
71/08/13
71/08/ 13
71/08/13
71/09/05
71/09/05
71/09/05
71/09/05
0003
UOCJ7
0010
0020
0030
0003
0007
0010
OU20
0030
0015
0003
0007
0023
0016
0003
0007
0013
U026
003U
0033
0016
0003
UOU7
0025
0019
153018 1290AC153018
11 53 11.0 U87 25 06.0
GREEN BAY OPEN WATER ONR STA 1
55 WISCONSIN
LAKE MICHIGAN
OOQIO
ATER
TEMP
CENT
11.0
11.0
11.0
1 H.O
12.0
1 1 .5
1 1 .5
1 1 .0
1 1 .0
21 .5
20.0
13.0
IV. 0
18.5
18.0
15.5
13.0
12.0
18. 0
18.0
16.0
00299
DO
PROSE
MG/L
9.1
9.1
9.3
9.2
1 1 .6
11. 5
1 1 .1
1 1 .3
1 1 .2
9.1
8.5
7.5
9.3
8.9
8.2
7.1
5.7
5.7
10. 1
9.8
9.8
21HIS
2
00078 00310
TRANSP BOO
SECCHI 5 DAY
METERS M6/L
2.1
2.3
3.3
2.1
1.5
2. 1
1.9
1.1
1 .6
3.3
3.3
21 1 1202
OU1S FEET DEPTH
00312 00910 OU530
BOD CHLORIDE RESIDUE
6 DAY CL TUT NFLT
MG/L MG/L «G/L
1
B U.I
8 U.I
1.3 7 U.I
3.7 8 1
8 3
6 1
a 3
8 1
153018 1290AC153UIB
11 53 11.0 087 25 U6.0
GREEN BAY OPEN WATER DNR STA -1
55 WISCONSIN
LAKE MICHIGAN
DATE
FROM
TO
73/09/21
71/1)6/01
71/06/01
71/07/08
71/07/08
71/08/13
71/08/13
71/09/05
71/09/05
TIME UEpTH
OF
DAY FEET
0007
0007
U015
0007
0016
QOD7
0016
0007
0019
00671
pHOS-DIS
OKTHO
MG/L p
U.UOl
0.003
0.003
0.006
0.006
O.U12
U.UU3
0.003
O.U02
0066";
PHOS-TOT
MS/L p
0.010
U.OBU
0.080
0.010
0.011
0.011
0.018
0.021
0.017
00605
ORG N
N
MG/L
0.100
0.100K
O.IOUK
0.100
0.500
0.300
U.200
0.100K
0.100K
00618
N03-N
D1SS
MG/L
0.01
U.06
0.32
0.02
0.18
0.01
0.73
0.02
0.30
21( IS
2
00613
N02-N
OISS
MG/L
0.000
0.010
0.012
0.020
0.052
O.OQ1K
0.001
0.006
0.011
21 1 12U2
0061U
NH3-N
TOTAL
Hti/L
0.000
0. 100
o.oso
O.UQU
o.ouo
O.OIUK
0.01UK
0.050
O.ObU
OU1S
32211
CHLHpHYL
A UG/L
CORRECTU
6.00
9.10
5.30
o.uo
3.30
FEET DEPTH
32218
PHEOPHTN
A
UG/L
2.00
U.QU
0.20
9.10
2.bO
-------
-------
TECHNICAL REPORT DATA
(Please read Instructions on the reverse before completing)
1 REPORT NO
EPA-905/9-74-017
3 RECIPIENT'S ACCESSIOWNO.
4. TITLE AND SUBTITLE
Water Pollution Investigation: Lower Green Bay
and Lower Fox River
5. REPORT DATE
June 1975
6. PERFORMING ORGANIZATION CODE
7 AUTHOR(S)
D. J. Patterson, E. Epstein, and J. McEvoy
8. PERFORMING ORGANIZATION REPORT NO
9. PERFORMING OR'ANIZATION NAME AND ADDRESS
Wisconsin Department of Natural Resources
Division of Environmental Standards
Box 450
Madison, Wisconsin 53701
10. PROGRAM ELEMENT NO.
11. CONTRACT/GRANT NO.
EPA No. 68-01-1572
12 SPONSORING AGENCY NAME AND ADDRESS
U.S. Environmental Protection Agency
Enforcement Division, Region V
230 S. Dearborn Street
Chicago, Illinois 60604
13. TYPE OF REPORT AND PERIOD COVERED
Final Report
14. SPONSORING AGENCY CODE
15. SUPPLEMENTARY NOTES
EPA Project Officer: Howard Zar
16. ABSTRACT
The lower third of Green Bay and the Lower Fox River were intensively studied. Seven
surveys of the Bay were carried out between September 1973 and September 1974. Over
40 stations were sampled for 15 different chemical and physical parameters. In
addition, plankton samples were taken and general groupings and counts were made.
Nearly 5,000 data points were generated and inserted into the STORE! system. The
surveys revealed algae blooms over the entire study area. Nitrogen forms showed
fluctuations over 3 orders of magnitude that may be relatable to nitrogen-fixing
algae. Phosphorus concentrations were more stable than nitrogen concentrations,
but appeared to decrease in correspondence to blue-green nitrogen-fixing algae.
Dissolved oxygen concentrations in the Bay were generally acceptable except during
the winter survey. The February survey revealed critical dissolved oxygen levels
over a 50 sq. mile area north of Point Sable.
Computer models of the Lower Fox River and Green Bay were developed and used to
evaluate the effect of the final limits for the present discharge permits at all
point source discharges on the water quality, specifically dissolved oxygen. The
most critical dissolved oxygen case was determined by the model tq.be the summer
low flow and high temperature condition in the river. The final discharge. limit
e to meet fish and aquatic lif
from the present permits was shown to be inadequat
standards with regard to dissolved oxygen (5 mg/1 ) and may even violate the variance
dissolved oxygen standards now in force. A proposed "waste load allocation" to
maintain 5 mg/1 of DO was developed. The WLA calls for a 37% decrease in BOD and
suspended solids from the final discharge levels on the present permits.
KEY WORDS AND DOCUMENT ANALYSIS
DESCRIPTORS
Water Quality
Aquatic Biology
Water Pollution
b.IDENTIFIERS/OPEN ENDED TERMS
Green Bay
Lake Michigan
Great Lakes
Fox River
Chemical Parameters
Biological Parameters
c. COSATI Field/Group
3. DISTRIBUTION STATEMENT
Limited number of copies from U.S. EPA,
Chicago.At cost of publication from NTIS,
5285 Port Royal Rd..Springfield, VA 22161
19 SECURITY CLASS (This Report)
21. NO. OF PAGES
20 SECURITY CLASS {Thispage)
EPA Form 2220-1 (9-73)
ou.S.Government Printing Office: 1975 — 650-478/1101 Region 5-1
------- |