EPA-600/3-77 106
September 1977
Ecological Research Series
THE TROPHIC STATUS AND PHOSPHORUS
LOADINGS OF LAKE CHAMPLAIN
Environmental Research Laboratory
Office of Research and Development
U.S. Environmental Protection Agency
Corvallis, Oregon 97330
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RESEARCH REPORTING SERIES
Research reports of the Office of Research and Development, U.S. Environmental
Protection Agency, have been grouped into nine series. These nine broad cate-
gories were established to facilitate further development and application of en-
vironmental technology. Elimination of traditional grouping was consciously
planned to foster technology transfer and a maximum interface in related fields.
The nine series are:
1. Environmental Health Effects Research
2. Environmental Protection Technology
3. Ecological Research
4. Environmental Monitoring
5. Socioeconomic Environmental Studies
6. Scientific and Technical Assessment Reports (STAR)
7. Interagency Energy-Environment Research and Development
8. "Special" Reports
9. Miscellaneous Reports
This report has been assigned to the ECOLOGICAL RESEARCH series. This series
describes research on the effects of pollution on humans, plant and animal spe-
cies, and materials. Problems are assessed for their long- and short-term influ-
ences. Investigations include formation, transport, and pathway studies to deter-
mine the fate of pollutants and their effects. This work provides the technical basis
for setting standards to minimize undesirable changes in living organisms in the
aquatic, terrestrial, and atmospheric environments.
This document is available to the public through the National Technical Informa-
tion Service, Springfield. Virginia 22161.
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EPA-600/3-77-106
September 1977
THE TROPHIC STATUS AND PHOSPHORUS
LOADINGS OF LAKE CHAMPLAIN
by
E. B. Henson
University of Vermont
Burlington, Vermont 05401
and
Gerhard K. Gruendling
State University of New York
Plattsburgh, New York 12901
CC6991931-J
CC6991932-J
Project Officer
Jack H. Gakstatter, Chief
Special Studies Branch
Corvallis Environmental Research Laboratory
Corvallis, Oregon 97330
Published Cooperatively
by
REGION I
U. S. ENVIRONMENTAL PROTECTION AGENCY
J. F. KENNEDY FEDERAL BUILDING
BOSTON, MASSACHUSETTS 02203
and
CORVALLIS ENVIRONMENTAL RESEARCH LABORATORY
OFFICE OF RESEARCH AND DEVELOPMENT
U. S. ENVIRONMENTAL PROTECTION AGENCY
CORVALLIS, OREGON 97330
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DISCLAIMER
This report has been reviewed by the Corvallis Environmental Research Labora-
tory, U. S. Environmental Protection Agency, and approved for publication.
Approval does not signify that the contents necessarily reflect the views and
policies of the U. S. Environmental Protection Agency, nor does mention of
trade names or commercial products constitute endorsement or recommendation
for use.
ii
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FOREWORD
Effective regulatory and enforcement actions by the Environmental Protection
Agency would be virtually impossible without sound scientific data on pollut-
ants and their impact on environmental stability and human health. Responsi-
bility for building this data base has been assigned to EPA's Office of
Research and Development and its 15 major field installations, one of which
is the Corvallis Environmental Research Laboratory (CERL).
The primary mission of the Corvallis Laboratory is research on the effects of
environmental pollutants on terrestrial, freshwater, and marine ecosystems;
the behavior, effects and control of pollutants in lake systems; and the
development of predictive models on the movement of pollutants in the bio-
sphere.
This report summarizes information on the trophic status and phosphorus inputs
to Lake Champlain and suggests the degree of phosphorus control needed in
various portions of the Lake Champlain basin to control cultural eutrophica-
tion.
A. F. Bartsch
Director, CERL
iii
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EXECUTIVE SUMMARY
Information on the trophic status t)f the several basins of Lake Champlain is
summarized, the amounts and distribution of total phosphate-phosphorus loading
into the lake are evaluated, and recommendations for further study are made.
The general objective is to provide Basic background information to assist in
the development of nutrient control policies for the proper management of the
lake. There is a short discussion of the role of phosphorus in the lake eco-
system, how recent thinking is leading to studies of eutrophication models,
and a presentation of estimated historical phosphorus loadings. It is shown
that Lake Champlain is a phosphorus controlled lake.
The morphometric and hydrographic description of the lake and its basin is
given. An Inventory of the 292 tributaries draining into the lake is presen-
ted, and then an explanation of how the lake and its drainage basin is parti-
tioned into 12 distinct hydrographic units to be treated as components of the
total watershed. A mass water transport model is presented to illustrate the
mass water movements through the lake basin involving an annual flow of
nearly 10,000 X 106 m3/yr. This is followed by a short discussion of the
demographic and land use patterns found in the entire drainage basin.
A limnological overview of Lake Champlain summarizes some of the physical,
chemical, and biological conditions of each region of the lake. Ranges and
average values for basic parameters such as Secchi disc readings, dissolved
oxygen, pH, alkalinity, cation concentrations, chlorophyll concentrations,
nitrogen and phosphorus concentrations are tabulated. Observations on the
biological indices of phytoplankton, zooplankton, and benthos are included.
Evidence that accelerated eutrophication is taking place in Lake Champlain
is discussed. Aside from visual observations of an increasing amount of
Cladophora growth along the shores, increasing turbidity, increasing evidence
of aquatic weed growth in shallow regions of the lake, beach closings because
of bacterial contamination, and specific toxins reported found in the water,
there have been some documented non-visual changes in the lake over a fairly
short period of time. Diatom sequence analyses of sediment core samples
indicate an increase in the relative abundance of the mesotrophic-eutrophic
diatom species in the more recent sediments. There are indications that
there have been significant changes in the phytopl ankton populations in the
lake in recent years, with members of the blue-green algae becoming more
important. The Secchi disc readings have declined in the past decade, as has
also the dissolved oxygen concentration of the deeper waters of the lake.
There has also been a trend for an increase in the total dissolved solids in
the lake, and the concentration of dissolved oxygen in the epilimnion during
the early summer. All of these symptoms lead to the conclusion that the lake
is in fact deteriorating.
iv
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In Section 6 there is a detailed discussion of the loadings, transport, and
budgets of phosphorus. Previous studies are reviewed, and estimates indicate
that background, or natural loading is significant. Based primarily on a
previous study of material inputs into the lake, phosphorus loadings were
calculated for each region of the lake. From these estimates the total load-
ing of total PO^-P amounts to 748 metric tonnes per year, with 90% of this
being derived from surface drainage, and 5% from waste treatment plants dis-
charging directly into the lake. Only about 20% of this loading is discharged
through the lake outlet, which means that about 80% of the loading, or nearly
600 metric tonnes are retained in the lake per year.
The 1976 Vollenwefder model was applied to the data presented for each region
of the lake. First, calculations were made for the critical concentrations
of PO^-P,(P)cp,given the input into the equation the calculated loading of
total phosphorus from each district. In this analysis, a critical concentra-
tion of phosphorus (P)c of 10 yg/1 or less would suggest oligotrophy, and 20
yg/1 or more would suggest eutrophy. Secondly, the same equation was used by
calculating for the critical loading (Lc) with the given values of (P)c of
10, 15, 20 and 30. The resulting analyses indicated that, for Lake Champlain
as a whole, the value of (P)c amounted to 31.5 ug/1, indicating a very high
level of phosphorus loading. For the 12 regions of the lake, the calculated
crttical P concentrations ranged between 7 and 48 yg/1, with 5 of the 12 dis-
tricts having a (P)c value above 30 yg/1, and only four of the regions below
the eutrophic level of (P)c-20 yg/1.
For the lake as a whole, the phosphorus loading would have to be reduced by
68% to bring the loading down to the (P)10 level (oligotrophic), 53% down to
the (P)15 (mesotrophic) level, and 37% to the base of the eutrophic level.
The percent reductions vary for the 12 lake regions.
The individuality of phosphorus loading from each region discussed in the
previous section is elaborated in Section 7 of the Report. Point source
loadings are inventoried for the streams draining each region of the drainage
basin. Some districts are rural and have less than 25% contribution of phos-
phorus from point sources while some of the urbanized districts have up to
80% of the phosphorus derived from point sources. For the entire lake, 42%
of the phosphorus loading is from point sources.
In some of the regions of the lake high phosphorus loadings are not expressed
in the usual eutrophic conditions. Missisquoi Bay retains only 5% of the
entering load, and some of this goes into a very large fish population, and
some is being utilized in building up a large area of emergent plant growth.
St. Albans Bay reflects the concentrated and local loading in that area, with
excessive weed growth that has been chemically treated for more than a decade.
In some instances it is not known how much of the estimated stream loading
actually reaches the lake since the streams flow through extensive wetlands
between the point of sampling and the lake. Because of the high clay turbid-
ity and high phosphorus concentration in the waters of the south end lake,
coupled with the very high retention of phosphorus entering the southern
sector of the main lake, much of the phosphorus in this part of the lake is
probably adsorbed on the suspended particles, and sedimented out.
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General recommendations are that phosphorus input levels should be reduced by
variable amounts, and attempts should be made to obtain a better understanding
of the fate of phosphorus entering the lake; where it goes, and how it is
utilized. Major point source loadings along the contributing streams and
directly into the lake should be reduced by constructing advanced waste treat-
ment plants. Since about two-thirds of the phosphorus loading is derived from
non-point sources, investigations should proceed to evaluate these diffuse
sources to better develop management procedures.
This report was submitted in fulfillment of Purchase Orders CC6991931-J by
Dr. E. B. Henson and CC6991932-J by Dr. Gerhard K. Gruendling under the
sponsorship of the U. S. Environmental Protection Agency.
VI
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CONTENTS
Foreword iii
Executive Summary iv
Figures i*
Tables *
Sections
1. Introduction 1
Phosphorus in the Champlain Basin 3
2. Recommendations for additional study and research 7
3. Geography and hydrography of the basin 9
Hydrography 9
Partitioning of the basin into hydrographic units 11
Mass transport of water through Lake Champlain 14
Human resources in the basin 17
Land use , 22
4. General limnological overview of Lake Champlain 24
The lake as a unit 24
Characteristics of regions of the lake 26
Missisquoi Bay 26
Northeast Arm 31
Malletts Bay 36
South Lake 43
Main Lake 47
5. Recent trends of accelerated eutrophication 54
6. Phosphorus loadings, transport, and budgets in Lake Champlain. . 56
Background information 56
Estimates of total phosphorus loading budgets 57
Evaluation of the different loading estimates 62
Other sources of phosphorus 63
Orthophosphate loading data 64
Resulting assessment of the phosphorus budgets , . 64
Application-of models to the phosphorus data 64
7. Sources of phosphorus in the districts 74
General comments 74
District evaluations 75
Summary 97
vn
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8. Summary of lake - drainage basin Interaction 99
Mfssisquoi Bay 99
Northeast Arm TOO
Malletts Bay 101
South Lake 102
Main Lake 104
9. Current research and management programs related to
eutrophication of Lake Champ!ain 106
Vermont Environmental Conservation Agency 106
University of Vermont 107
New York State Department of Environmental Conservation. . 107
State University of New York at Plattsburgh 107
International Joint Commission 108
New England River Basins Commission 108
10. References 109
11. Appendix
List of Appendices 116
Appendix A - Conversion factors 117
Appendix B - Method for estimating the Champlain Basin
population, 1810 - 1870 118
Appendix C - Inventory of tributaries 121
Appendix D - Primary data on median total phosphorus
concentrations of tributaries and loading
calculations 129
Appendix E - Point source inventory 132
viii
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FIGURES
Number Page
1 Orientation map of Lake Champlain 2
2 Phosphorus loadings into Lake Champlain 1810-1970 5
3 Map of Lake Champlain drainage basin 10
4 Water transport patterns in Lake Champlain 15
5 Champlain mass transport water budget model, schematic 16
6 Schematic phosphorus mass transport model 69
7 District A map (Missisquoi) 76
8 District B map (St. Albans) 79
9 District C map (Lamoille) 81
10 District D map (Winooski) 83
11 District F map (Otter Creek) 85
12 District S map (Poultney River sub-basin) 87
13 District S map (Metawee River sub-basin) 88
14 District S map (Lake George sub-basin) 89
15 District M map (Port Henry) 91
16 District L map (Bouquet) 92
17 District K map (Ausable-Saranac) 94
18 District J map (Chazy) 96
IX
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TABLES
Number Page
1 Morphometric values for subdivisions of the Champ!ain
drainage basin 13
2 Mathematical formulation of the mass transport water
budget 18
3 Calculations for the water mass transport model for the
subdivisions of the Lake Champlain drainage 19
4 Population estimates for each district of Lake Champlain
drainage basin 21
5 Generalized use of the land of the Champlain Basin, 1970 22
6 Morphometric features of the major water masses of Lake
Champlain 27
7 Summary of the physical and chemical characteristics of
Mfsslsquoi Bay 28
8 Summary of the biological characteristics of Missisquoi Bay. ... 30
9 Summary of the physical and chemical characteristics of the
Northeast Arm 33
10 Summary of the biological characteristics of the Northeast Arm . . 34
11 Summary of the physical and chemical characteristics of Inner
St. Albans Bay 37
12 Summary of the biological characteristics of Inner St. Albans
Bay 38
13 Summary of the physical and chemical characteristics of Outer
Malletts Bay 41
14 Summary of the biological characteristics of Outer Mallets Bay . . 42
15 Summary of the physical and chemical characteristics of South
Lake Champlain 45
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Number paqe
16 Summary of the biological characteristics of South Lake
Champlain 45
17 Summary of the physical and chemical characteristics of the
Main Lake 50
18 Summary of selected parameters indicative of trophic
conditions in the embayment areas and main portions of
Lake Champlain 51
19 Summary of biological characteristics of the Main Lake 52
20 Comparison of phosphorus input values 58
21 EPA estimates of total phosphorus loading into Lake Champlain . . 59
22 Estimated loadings of reactive phosphorus to Lake Champlain ... 65
23 Summarized phosphorus budgets of Lake Champlain 66
24 Values for total phosphorus loadings into the hydrographic
regtons of Lake Champlain 67
25 Solution of the mass transport-total phosphorus model 70
26 Summary of specific critical loadings of total phosphorus
for regions of Lake Champlain 71
27 Necessary reductions of phosphorus loading to Lake Champlain. . . 73
28 Summary of point source phosphorus loadings in each District. . . 77
29 Summary of potential effect of nutrient control policies on
the reduction of phosphorus on Regions of Lake Champlain . . 98
XI
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SECTION 1
INTRODUCTION
As the Champlain basin became more populated, the phosphorus input of
Lake Champlain increased excessively. Phosphorus has a demonstrated effect
on the deterioration of a lake but it can be controlled significantly. In
reviewing the history of eutrophication of the Great Lakes, it is well docu-
mented that even very large, clear, and clean lakes can become seriously
deteriorated in a relatively short time due to cultural influences; and these
Great Lakes give warning that other large, deep, oligotrophic lakes are vul-
nerable to the same influences.
Lake Champlain is the largest of the deep cold-water and near-oligo-
trophic lakes in the United States other than the Great Lakes. Though the
main deeper part of Lake Champlain is considered to be somewhere in the
oligotrophic-mesotrophic range; the lake does exhibit a number of warning
symptoms such as Cladophora growths along portions of the shoreline, oxygen
deficits in some of the bays, heavy plankton blooms, and abundant bottom weed
beds. In the main lake, warnings are shown by the trend toward reduced oxygen
concentration in sub-surface waters and very high oxygen values in the upper
waters in the springtime. The evidence leads to the conclusion that the lake
is undergoing rapidly deteriorating changes in our own time, and some expedi-
ent remedial action must be taken.
It has been demonstrated that the lake is in fact a phosphorus limited
lake (EPA, 1974; Gruendling, 1976a) and therefore policy development, legis-
lation, and proper management are vital in reducing and controlling the
quantity of phosphorus entering the lake. However, any information about the
phosphorus loadings, the fate of phosphorus in the lake, and the phosphorus
budgets in general, if available, is scattered, fragmentary, and insuffi-
ciently coherent for the Agencies to develop an appropriate strategy for the
control of phosphorus in the basin.
The two authors have been asked to examine the status of the nutrients in
the lake, with special emphasis on phosphorus. Dr. Henson has taken the
responsibility of examining the matter of phosphorus loadings, and transport
within the lake, while Dr. Gruendling has examined the trophic conditions
within the lake considering a vast array of indicators of trophic status.
The section on "Interaction" was written jointly.
The authors endorse the decision to initiate protective management of the
lake. Both authors have had scientific experience on the lake and are abun-
dantly aware of impending changes that are taking place. For readers of this
document who are unfamiliar with the geography of the Champlain Valley, we
wish to point out in Figure 1 that Lake Champlain is the recreational hub for
1
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IHIITIC OCEAN
Figure 1. Orientation map of the Lake Champlain basin showing the proximity
to large urbanized areas: (1) Montreal, Canada; (2) Syracuse,
N.Y.; (3) Albany, N.Y.; (4) Boston, Mass.; (5) New York City. The
concentric circles represent distances of 100 and 200 miles from
Burlington, Vt., located on the middle of the eastern shore of
Lake Champlain.
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a number of large metropolitan areas. The pressure from expanding popu-
lations from these not-so-remote urban areas are being felt in the Champlain
Valley in terms of influx of tourtsts, boaters, skiers, and escapees. This
also has an impact on the increasing amounts of phosphorus imported into the
basin.
PHOSPHORUS IN THE CHAMPLAIN BASIN
The Ecological Need For Phosphorus
Since phosphorus is the primary topic of this document, a few words are
in order to explain why this element assumes such an important position.
Phosphorus is an essential component for all living things; however, exces-
sive amounts are disruptive. The chemical bondage of phosphorus provides the
necessary energy for biological processes, and it can be looked on as the
battery for all biological activities. A plant or animal body needs a large
supply of this element in order to function, and this amounts to approxi-
mately 0.2 mg for every 100 mg of tissue. When one multiplies this by the
total weight of algae, zooplankton, and fish in a lake, the total amount of
phosphorus in the biosphere can become relatively large.
In contrast, the amount of phosphorus available to the algae (the primary
producers) in the lake, is relatively small, on the order of 0.01 mg/1000
grams compared to the 2 mg/1000 grams in the plant or animal. The demand is
great, the supply is small for phosphorus. For the other essential elements,
there is a greater supply. Therefore, phosphorus becomes the critical ele-
ment. Under normal conditions the utilization is in balance with the input
of phosphorus. Excessive amounts of phosphorus added to the system become
disruptive.
Phosphorus Loading Models
Because of the growing awareness of the role of phosphorus in the eutro-
phication of lakes, there has been in the last decade a considerable amount
of research into the practical applications of lake response to various
doses of phosphorus. This has culminated in certain mathematical models that
are intended to provide guidelines for possible control. The conclusion of
this work is that the mean depth of a lake, the rate at which the water and
phosphorus are carried through the lake, and the amount of nutrient added to
the lake per unit time, are the essential parameters that control the trophic
state of the lake. From these studies, Vollenweider (1976) has derived an
equation where one can predict with fairly good probability, the trophic
status of a lake having measures of the essential parameters. These concepts
are here applied to data from Lake Champlain. In the Vollenweider model,
there is a formula that intends to state whether the loading into a lake is
"dangerous" or not. It also can be used to determine whether the loading
places the lake in a eutrophic, oligotrophic, or mesotrophic condition. The
authors are of the opinion that it is premature at this time to take the
numeric values from the model as absolute; but the model, after empirical
testing with a fairly large number of world wide lakes, certainly demon-
strates the relative influence of estimated phosphorus loading on a lake. In
this respect, the value of this model should not be underestimated.
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Background And Historical Phosphorus Loadings
There are no data available on the historical phosphorus loadings of Lake
Champlain; but tt would be desirable, in terms of contemporary perspective,
to have evaluations showing how much phosphorus had been entering the lake
before the basin was heavily populated and how ft then changed in the past
150 years.
To have some speculative evaluations of this information, we have made
some approximations of these matters. In Section 6 we have made an estimate
of what the natural "background" loading would have been were there no human
inhabitants in the basin. This estimate was not corrected for phosphorus
input from the contemporary atmosphere, but it does provide an order of mag-
nitude when phosphate loading control is discussed. It has been estimated
that the "natural" background loading amounts to 128,763 kg/yr.
In Section 6 the phosphorus loading is also estimated on the basis of
population in each subdrainage basin and a loading estimate was derived that
was on the same order of magnitude as several other estimates. Using the
same technique, we have estimated the phosphorus loading for the period
between 1810 and 1970.
The literature (Vollenweider, 1968; Patalas, 1972) suggests that the
average person contributed between 1.5 and 1.7 kg of phosphorus annually to
the environment, and this includes the normal use of fertilizer and other
demophoric additives (Wetzel, 1975). Patalas used the higher value because
of the higher P utilization in modern society. For the purpose here, we will
use the more conservative value of 1.5 kg/C/yr. The question of how much of
this phosphorus enters the lake cannot be answered at present. Some of it
obviously becomes intrapped in the terrestrial biosphere; but our contempo-
rary loading data matches very closely with present population estimates.
A refined model might use a sliding scale of capita loading, but for the
present we will simply estimate that all of the culturally derived phosphorus
eventually reaches the lake.
Estimates, accordingly, have been made of the total population in the
Champlain basin for each year, from 1810 through 1970 (Appendix B). These
population values were then multiplied by 1.5 to derive the estimated phos-
phorus loading into the lake in kg/yr, and these data are presented graphi-
cally in Figure 2.
From Figure 2 it can be observed that there has been a general increase
in the phosphorus loading from the beginning, with decreasing and increasing
rates reflecting the general economic conditions of the area at the time.
The rate of loading Increase was about the same in the periods 1820-1850,
1900-1920, and 1940-1970. The dashed horizontal line at 128,763 kg/yr marks
the estimated background loading to the lake. It is interesting to note
that the cultural curve Intersects the edaphic plot at the beginning, in the
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700_
600 ~
P 200
HM
100 -
50 -
0
JL
I I I I I I I I
J L
' I
I I
-loadingg —
Eutrophic range
Mesotrophic range
Oligotrophic range
e
1975 estimated loading
(P)-30
(P)-20
Background
20 30 40 50 60 70 80 90 10 20 30 40 50 60 70 80
1900
Years
Figure 2. Historical estimates of loadings of phosphorus into Lake Champlain, 1810-1975,
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year 1810* which would presumably be the time that the cultural influence
began to dominate over the natural edaphic loading balance.
Figure 2 also shows three horizontal guidelines labeled (P) = 10, 20,
and 30. As developed fully in Section 5 of this report these are three
levels of loading derived from the 1976 Vollenweider model; where the (P)-|0
level separates oligotrophy from mesotrophy, (P)2o can be considered the
upper level of the mesotrophic-eutrophic boundary, and (P)3Q represents a 3
severe and unacceptable eutrophic level. Our calculated loading of 747x10
kg/yr is above the (PJ3o level. Considering that shallow peripheral embay-
ments theoretically express the signs of eutrophication earlier than the
main deeper lake, and they are in fact presently expressing this state, the
prognosis is clear; Efforts must be made as soon as possible to reduce the
phosphorus loading into the lake. It is the intent of this document to
assist in this endeavor.
* It ts assumed that since the population diverts natural waters that already
contain edaphic P for utilization; edaphic P is then incorporated under the
heading of cultural dishcarge.
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SECTION 2
RECOMMENDATIONS FOR ADDITIONAL STUDY AND RESEARCH
1. Since the State of Vermont will be instituting point-source phosphorus
control at the major discharge facilities into St. Albans Bay, Shelburne Bay,
and Burlington Bay, a study should be implemented to determine the response
of these areas and their tributaries to this management practice. The study
should be designed to determine the water quality conditions in the tribu-
taries and the receiving waters before and after the implementation of the
nutrient control. The sampling program must be comprehensive and frequent
enough to provide meaningful data. The water quality parameters that should
be measured in the receiving waters are dissolved oxygen, total and dissolved
phosphorus, biological oxygen demand, and plankton biomass and productivity
estimates. Nutrient content of the tributaries should also be measured.
2. It is anticipated that in the near future the State of Vermont will
institute a ban on phosphate detergents. A study should be developed to
examine the success of this management program. Changes in phosphorus levels
before and after the detergent ban should be monitored at point sources, in
point source and non-point source segments of a tributary, and in the
receiving body. Results from these test areas could then be applied to other
tributaries in the basin.
3. Cumberland Bay, Northwest Bay and the region near Port Henry are areas of
water quality impairment and significant nutrient loading in New York State.
Since these areas have significant point-source loadings, it is concluded
that the existing controls are possibly ineffective. A review should be made
of the effectiveness of present nutrient controls in New York portion of Lake
Champlain and a determination of the cost and net benefit of upgrading these
point source controls.
4. The amount of phosphorus loading to the lake has been estimated using
limited nutrient data and based on the normalized flow of the tributaries.
Additional studies are needed to develop and refine a model for estimating
phosphorus from selected streams utilizing a minimum of sampling. With good
gaging and monitoring, using U.S.G.S. procedures for collecting water quality
samples, and a communication system for announcing significant flow data,
loading estimates could be developed on an event basis and adequately
measured by taking as few.as 20-25 water samples/year. This refined model
could then be used as a basis for future point and non-point loading and
response studies that will be needed in order to evaluate various management
practices.
5. Utilizing the present phosphorus loading estimates or the future refined
estimates, it is presently not possible to accurately predict the impact of
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specific phosphorus loading on the lake or determine the possible effects of
reducing phosphorus loadings. In order to predict these effects, it is nec-
essary to understand the fate of phosphorus once it enters the lake. A study
should be initiated to investigate the amount of phosphorus being incorpo-
rated into productivity, the amount being lost to the sediments, and the rate
of phosphorus recycling in the lake.
6. It is important to understand the potential impact of the heavy phos-
phorus loading from the south lake upon the main lake north of Crown Point,
New York. The hypothesis that phosphorus is being lost to the sediments by
absorption to clay particles in the main lake should be tested. It should
also be determined if there is any accumulation of phosphorus in the sedi-
ments of the region. Such a study would help in determining whether phos-
phorus control in the south lake is a necessary management practice.
7. In order to determine how far up the drainage basin to apply nutrient
controls, it is necessary to determine the phosphorus transport loss down-
stream from point and non-point sources in the tributaries. Such a study
should be initiated for a few sample areas in the Lake Champlain Drainage.
8. The in-lake monitoring program should be extended to gather data from
each of the 13 drainage regions in order to improve the phosphorus trans-
port model for the lake. The minimal data needed are total phosphorus, dis-
solved phosphorus, nitrogen, and chlorophyll A values collected during the
spring turnover period. It is recommended that this monitoring program be
expanded to a year-round basis.
9. The problem of the severe oxygen depletion in the hypolimnion of Mallets
Bay should be studied further. There is a need to define the actual cause(s)
of the depletion condition. Possible sources of BOD entering via the
Lamoille River and the in-lake contribution of organic matter should be
investigated. Once the cause of the problem has been determined, a manage-
ment strategy should be developed to help alleviate the source of the prob-
lem.
8
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SECTION 3
GEOGRAPHY AND HYDROGRAPHY OF THE BASIN
DESCRIPTION OF LAKE CHAMPLAIN
Lake Champ!ain (Figure 3) occupies a large north-south valley that extends
from the St. Lawrence River, near Montreal, Quebec, to New York City. The
elevation of the lake is +_ 29 meters (95 feet) A.T.; it has a maximum depth
of 122 meters (400 ft.), and therefore occupies a cryptodepression of some 91
meters. The lake drains to the north through the Richelieu River into the
St. Lawrence River at Sorel, Quebec. The total lake area is 1,269.1 Km2 (490
sq. mi.), including a number of large and small islands. The water surface
is 1,130.2 Km2 (436.4 Mi2). The land drainage is 19,881.08 Km2 (7,676.1 Mi2)
so that the ratio of drainage area to lake area is 17.8 : 1. The Adirondack
Mountains rise precipitously close to the western side of the lake, and the
lake itself is in the rain shadow influence of the mountains. The eastern
basin is a broad plain with the Green Mountains of Vermont located about 32
km to the east of the lake. The southern portion of the lake is narrow and
shallow, and water connection is made at the southern end to the Hudson River
through the Hudson-Champlain Canal. The volume of the lake is estimated to
be 25,802.074 X 106 m3 (912 X 109 Ft3) (Hunt et a]_., 1972).
HYDROGRAPHY
Precipitation
Precipitation is the source of the waters of Lake Champlain, and there is
a relationship between the amount of precipitation and the loading of the
nutrients. About 9% of the water enters the lake directly, but the remaining
91% enters the lake after moving through and over the approximately 8000
square miles of drainage basin (Henson and Potash, 1969; Henson and Vibber,
1969). On its way to the lake the water picks up much dissolved and partic-
ulate material.
The Champlain Valley has the lowest amount of precipitation of anywhere
in all of New England or New York State. The lowest mean annual precipita-
tion in this sector of the United States is near the mouth of the Bouquet
River. This is attributed to the fact that the lake is in the rain shadow of
the Adirondack Mountain range to the west.
Precipitation generally increases with altitude in the Champlain Valley,
and generally more on the eastern side of the lake than on the west (Ingram
and Wiggins, 1968). At Burlington, at an elevation of approximately 800
feet, the mean annual precipitation is between 30-35 inches annually. On the
top of Mt. Mansfield it is approximately 45 inches. Fillin (1970) estimated
-------
Figure 3. Map of Lake Champlain and its drainage basin illustrating the sub-
divisions into the major watershed Districts and lake Regions.
Morphometric values for these subdivisions are to be found in
Table 1 and more detailed presentation is found in Figures ' - 18.
Subdivisions are: (S) Missiquoi, (B) St. Albans, (C) Lamoille-
Malletts Bay, (D) Winooski-Burlington, (D) Charlotte, (F) Otter
Creek-Vergennes, (S) South End Lake, including Poultney, Matawee,
and Lake George Subdistricts, (M) Port Henry, (L) Bouquet,
(K) Ausable-Saranac, and (J) Chazy.
10
-------
that 24% of the precipitation fell below 1000 ft; 55% between the 1000 ft and
2000 ft contours, and 21% above the 2000 ft level in the Missisquoi River
basin.
Stream Discharge
Most of the larger tributaries of the lake have been gaged (U.S.G.S. -
1973, 1974). In 1968 a number of the critical stations in New York were dis-
continued after many years of valuable service. The location of many of
these gaging stations are not located near the mouths of the streams. Only
two of the small valley streams (Stone Bridge Brook and Salmon Creek) have
been gaged, and both have recently been discontinued. There is a sound need
for augmenting the stream discharge monitoring in the Champlain basin to
eventually obtain a better estimate of the nutrient loading to the lake.
Lake Levels
After a period of extreme low lake levels in the 1963-1968 period, there
followed a very wet period in the 1970's when the lake attained all time
highs for several years. A report on the statistics of lake levels has been
offered by Downer (1971) and Gillespie 0976). The International Joint Com-
mission is presently investigating the problems concommitant with the high
lake levels, and the possibility of lake level regulation. Such regulation
could exert some influence on the nutrient status of parts of the lake.
The Lake Outlet
The outlet for the lake is the Richelieu River that drains north from
Rouses Point, N. Y., to Sorel, Quebec (Fig. 1), and it there empties into the
St. Lawrence River. The water depth is approximately 20 feet at Rouses
Point, but the sill depth is a ledge at an elevation of 92 feet at Chambly,
Quebec.
The maximum mean daily discharges of the Richelieu since 1938 have ranged
from 13,300 (1965) to 43,700 cfs (1947) whereas the minimum range extends
from 1,410 (1941) to 5,410 cfs (1945). The mean discharge (at 96 ft. lake
level at Rouses Point) is about 10,500 cfs (Fischer, 1976).
Good discharge data are not available for Lake Champlain. Though the
level is monitored at Rouses Point, this is not reportably converted to
flow units. Most of the flow data are derived from Chambly, Quebec, many
miles downstream. There may be 1000 cfs separating these two localities.
PARTITIONING OF THE BASIN INTO HYDROGRAPHIC UNITS
Inventory of the Tributary Streams
An inventory was made of all of the tributaries that drain directly into
Lake Champlain. Utilizing copies of the contourless drainage maps used by
the EPA for the STORET facilities, topographic maps of the U.S.A. and Canada,
the lake charts, information from the New York State Conservation report of
1928, and actual field visits, we have listed each stream entrance to the
11
-------
lake.
The arrangement of this list follows the procedures for identifying
streams in the STORET MANUAL. Beginning on the east side of the Richelieu
portion of the lake at the Canadian border across from Rouses Point, the
shoreline is followed proceeding down Alburg Tongue, around the islands, up
into and around Missisquoi Bay, and on down the east side of the lake to the
Hudson-Champlain Canal. These streams are coded with odd numbers in agreement
with the STORET numbers. A total of 156 outlets were listed from the eastern
side. On the western side, beginning at the Canadian border above Rouses
Point, N. Y., the shoreline was followed in a similar manner, and each outlet
was given an even code number.
A total of 292 streams and subwatersheds were thus inventoried. South
Bay was counted as a single point source, and counting the 23 brooks that
drain into this bay, the total number of tributaries draining into the lake
is 315. Those 34 streams with drainage areas exceeding 10 sq. miles (Appen-
dix C) drain 97% of the entire watershed. The remaining 158 tributaries are
small but could be of local significance. The four largest rivers are in Ver-
mont, and together they drain about half of the total Champlain basin.
Partitioning the Lake Basin into Hydrographic Units
Lake Champlain is geologically divisible into a number of distinct basins
that contain waters of individual character (Potash ejt a]_., 1969). The narrow
southern part of the lake, Missisquoi, and Nalletts Bay, and the body of water
to the east of the islands are physiographically distinct. The main lake
forms a large unit, and this also could be subdivided. We have divided the
lake into a number of physiographic Regions adjacent to, and influenced by,
the discharges being received from the associated Districts of the watershed
(Figure 3).
The areas of the District watersheds were calculated as a working base.
Some minor (up to 3%) discrepancies occured when our figures were compared
with calculations made by others. These inconsistencies are generated by
problems in locating the divide on the maps, especially in the flat lands.
Table 1 summarizes the information about these areas. Two-thirds of the
Champlain watershed lies east of the lake, and one-third is to the west. The
ratio of the areas of drainage basin to lake area is about 18:1 for the entire
Lake Champlain, but within District and Region boundaries the ratio varies
between 0.3:1 (H) to 54:1 for the south end.
Most Districts are drained either by a single major tributary, or two
somewhat equally sized basins. The Islands District (H) is poorly repre-
sented by stream discharges, and District M is drained predominantly by con-
sequential streams. Though about BQ% of District S is drained by three
streams (Poultney, Ticonderoga, and Metawee), we have considered the South End
Lake as a tributary. Drainage from the small District E (9. sq. mi.) is domi-
nated by Holmes Creek which was frequently dry, yielding little data. The
drainage from the other districts can be monitored for 60-96% of tts area by
sampling no more than two streams per District.
12
-------
Table 1. VALUES FOR AREAS, VOLUMES, AND OTHER STATISTICAL INFORMATION FOR THE REGIONS AND DISTRICTS OF
THE CHAMPLAIN DRAINAGE BASIN.
a
Region, Region
District Area (km2
A
B
C
D
E
F
H
J
K
L
M
S
TOTAL
77.50
134.23
54.20
117.22
63.77
48.69
271.92
114.92
78.39
63.77
48.69
56.90
1,130.20
A
District
) Area (km2)
2,963.96
191.17
2,032.29
3,009.08
23.99
2,934.87
87.85
1,029.50
3,548.42
744.57
242.09
3,073.25
19,881.08
vr
Water
Volume (m3 x 106
220.444
1,730.930
699.319
3,019.146
3,545.902
1,193.963
4,502.458
939.019
5,055.552
3,545.902
1,193.963
155.575
25,802.074
2
Mean Ratio of areas
) Depth (m) Pi str/ region
2.8
12.9
12.9
25.8
55.6
24.5
16.6
8.2
64.5
55.6
24.5
2.7
22.8
38.2
1.4
37.5
25.7
0.4
60.3
0.3
9.0
45.3
11.7
5.0
54.0
17.6
% of
No. of drainage
tributaries basin
9
16
15
13
6
26
24
13
32
9
40
89
292
14.8
1.0
10.1
15.0
0.1
14.6
0.4
5.1
17.7
3.7
1.2
15.3
99.0
K
(cfs/sq. mi.)
1.3
1.1
1.4
1.4
1.1
1.3
1.1
1.15
1.1
1.15
1.2
1.2
-------
MASS TRANSPORT OF WATER THROUGH LAKE CHAMPLAIN
Some knowledge of the basic movements of the waters of Lake Champlain is
essential for evaluating the effects of nutrient loadings and dispersal. We
speak here of long-term transport rather than short-term displacements caused
by winds or seiche activity, or local current patterns. Over the past decade
we have made observations of water movements of the lake, allowing us to
derive a general description of these transports; and from this, a mathemati-
cal model can be constructed so that variables can be treated in future
studies.
This circulation pattern is shown in Figure 4. Three tributaries can be
considered as headwaters. -The South end lake contributes about 41 m3/sec.
into the southern part of the lake, and the lake then receives drainage from
the adjacent Districts as it moves northerly down the lake. Regions A and C
are also terminal in that water received is in excess to the receiving basin
volume resulting in a net outflow to other parts of the lake. The flow from
Missisquoi flows south and then splits, some of the water flows directly
south through the Alburg Passage between Alburg Tongue and North Hero Island,
while the remainder moves into the northern part of the northeast arm of the
lake. The prevailing southerly winds carry some of this water into Maquam
Bay. Discharge into Malletts Bay (31 rnVsec.) can escape by a small portal
under the Sandbar Bridge into the northeast arm, or by two portals in the
railroad embankment to the main lake. Sundberg (1972) found that most of the
water left the bay through the two portals to the west, and the study of Myer
et al. (1976) makes some interesting observations regarding this. Our obser-
vations have indicated that most of the time the water in the northeast arm
flows westwardly through the Gut into the main lake, and these have been con-
firmed in winter by LANDSAT imagery and field observations. The only evi-
dence of general flow eastwardly from the main lake into the northeast arm is
when the lake level is well below normal, causing main lake water to flow
to the lower level, Myer et a]_. 0976) has reported that seiche activity can
induce temporary reverse flows through to the northeast arm.
As the water flows from these three origins, the water will flow from
Region to Region and be augmented by discharge from the adjacent Districts,
and finally be discharged through the Richelieu River in Region 0. The lake
also gains water by precipitation directly onto the lake, and water is lost
by evaporation. Precipitation onto the lake for each region was determined
by drawing isohyets through the mean annual precipitation for eleven stations
(1971 data), and examining the patterns existing over the lake regions (Henson
and Vibber, 1969; Henson and Potash, 1969; 1973; Potash and Henson, 1974).
These precipitation values should be updated.
The schematic diagram in Figure 5 is a representation of the water trans-
port pattern in Lake Charaplain and will serve as a basis for developing a
mathematical model. We assume that the water delivered to a Region from
several sources is mixed before proceeding to the next Region. For the model
we have assumed that half of the water from Region A goes to each of Regions
H and B; and that 75% of the water from Region C moves to H and 25% to Region
B. The configuration of the Regions in the broad lake is complex, but by
extending Region H south of the islands to Colchester Point, half of D flows
14
-------
Figure 4. Net annual water transport patterns in Lake Champlain. Headwater
influents are Missisquoi River (A), Lamoille River (C), and the
South End Lake (S). Arrows indicate net movement.
15
-------
Pfgure 5. Schematic model of net annual mass water transport in Lake Cham-
plain. Square figures depict the relative areas of the several
Districts, or drainage basins. The circles deptct the relative
areas of the lake Regions, and the arrow widths depict the
relative amounts of mean annual net water transport.
16
-------
to H, and half to K. Regions K and D each receive half of the discharge from
EL.
The basic format for this model is given below and displayed for each
District in Table 2.
Zlr + Ai6i X 10* + PH - EH + Zn.
where i = a designated District (D) or Region (r)
Ai = Area of District i in km2
Z1 = Constant of 31.5569 X District discharge as m3/m2 Of land area.
Pri = Precipitation directly onto a Region as m3/Km2 X 106
Eri = Evaporation from a Region as m3/Km2 X 106
*ri = ^ater inPut to a Region from an adjacent Region
The solution for this water transport model is set out in Table 3.
According to this run, the net water balance for Lake Champlain is 8,712.5 X
106 m3/year. This is equal to 9,750 cfs, about 7% below the normal discharge
figures. The model does include significant variables (District discharges,
regional precipitation, and evaporation) that could be handled easily with
computer manipulation as better data become available. It should be noted
that the water balance within each Region can be modeled as subroutines.
The last two columns in Table 3 are of special interest as they relate to
the transport of nutrients in the lake. The residence time (Tw) is the time
(years) the water theoretically remains in the basin before being removed.
The longer the residence time, the longer the nutrients have the opportunity
to become a part of the ecosystem of the Region. These values are annual
means, and during Spring melt-off, the value has less meaning. The last col-
umn, pw (flushing rate) is an index of the rate at which water is being
replaced in the Region basin, the inverse of residence time. In effect, the
flow-through rate tells us, using Region A as an example, that the water
coming into Region A per year would fill the basin more than six times.
Those Regions with high flushing rates (Regions J, S, A) would serve
mainly to transport the nutrients elsewhere and full expression of eutrophica-
tion would be translocated and delayed. Those Regions with high residence
times (Regions EL, B, H) are areas where the water input is relatively low
compared with the water volume of the Region, and where a build-up of nutri-
ents might be expected.
HUMAN RESOURCES IN THE BASIN
The number of people living in the basin, how they live and how they are
distributed in the basin, will have a distinct impact on the condition of the
lake. The population is not static and mention will be made of long- and
short-term changes.
17
-------
TABLE 2. MATHEMATICAL FORMULATION OF THE MASS TRANSPORT WATER BUDGET MODEL
District _ Equation
A AA6A X 10* + Pa - E, * D
a , a
C AC6CX.106+PC-EC=DC
B CVB X 10G + Pb - Eb ) + PDa+ PDC = Db
S As6s X 106 4 Ps - £s = Ds
FM (A^ X 10* + Pf - Ef) + (A^ X 106 + Pm - Ej * DS = Dfm
EL (AE6E x io6 + pe- Ee) + (A^ x io6 + PJ-EJ + ofrn = oel
D (ApaD X 106 + Pd- Ed) + PDel + Dd
K (AK<5K X 106 + PR - Ek) + pDel + pDd + Dk
H (^^ X 106 + Ph - Eh) + PDa + Db + PDC + PDd = Dh
J CAj<5j X TO* + PJ - EJ) + DR + Dk = Dj (outlet)
Where:
A is District area (km2)
5 is discharge coefficient (n^/sec. X 31.5569)*
Pr is precipitation onto a Region
Er is evaporation from a Region
Dr is excess water, or outflow from a Region
AD60 is water input from land drainage (District)
= K from Table 1 X 0.0109332, the conversion from cfs/sq. mi. to (Appen
dix A) mvsec/kro X 31.5569, the integer of the number of seconds/year.
18
-------
TABLE 3. WATER MASS TRANSPORT CALCULATIONS FOR THE SUBDIVISIONS OF THE LAKE CHAMPLAIN DRAINAGE.
VALUES IN CUBIC METERS X 106/YR UNLESS OTHERWISE INDICATED.
Di
A
C
B
S
F
M
FM
E
L
EL
D
K
H
J
strict/Location
(Missisquoi)
(Malletts -
Lamoille)
(St. Albans)
(South End)
(Otter Creek)
(Port Henry)
(Charlotte,
Vt.)
(Bouquet R.)
(Burlington -
Winooski)
(Ausable -
Plattsburgh)
(Grand Isle)
(Chazy -
Rouses pt.)
6i
0.44852
0.48303
0.37952
0.41402
0.44852
0.41402
-
0.37952
0.39677
-
0.48303
0.37952
0.37952
0.39677
Val
V
71.8
44.8
110.9
54.9
45.8
45.8
-
56.7
55.9
-
99.7
64.8
217.5
91.9
lues X 10b =
Er
58.1
40.6
100.7
43.2
36.7
36.5
-
53.6
53.6
-
105.7
63.0
204.1
86.3
tn^/year
'r
1343.10
985.86
82.75
1284.09
1325.45
109.53
1434.98
12.20
297.72
309.92
1477.48
1348.50
46.74
414.07
Qy
1343.10
985.86
1000.77
1284.09
1967.50
751.575
2719.08
1371.74
1657.26
3028.99
2991.98
4358.98
3954.45
8727.50
Qy (as
nr/sec)
42.56
31.24
31.71
40.69
62.35
23.82
86.16
43.47
52.52
95.99
93.86
137.66
124.84
276.09
tw
(yea rs )
0.164
0.709
1.730
0.121
0.607
1.589
0.878
2.585
2.140
2.341
1.003
1.160
1.139
0.108
pw
Exchanges/
year
6.098
1.410
0.578
8.254
1.647
0.629
1.140
0.387
0.467
0.427
0.991
0.862
0.878
9.278
* The mean outflow
10,500 cfs given
for the outlet discharge.
cfs, about 7.0% less than a mean of
-------
The historical record of human habitation in the Champlain basin shows
trends that indicate that outside forces are very influential; the basin can-
not remain provincial. The transition patterns of transportation from rail-
road and steamboat to interstate highways and aircraft; the dynamics of metro-
politan growth in the urban perimeters of Montreal, Boston, New York City, and
Albany; and the changing economic and employment patterns; all contribute to
changes in basin population. Some towns in the basin have lost population,
and others have gained (Fischer, 1976). Some short-term population changes
that can become traumatic are related to recreation. During the summers there
is a general increase in the population in the basin for water-related endeav-
ors, with increased boating and occupation of summer dwellings along the lake
shores. There is also the increased use of water during the summer months for
watering lawns and gardens and swimming pools, and this modifies the waters
flowing into the lake. During the winter months, following the introduction
of snow, the mountain areas receive an influx of skiers and their followers.
Some ski resorts may entertain more people in one day than residents in the
entire town. The Winter Olympics in Lake Placid in 1980 is expected to draw
35,000 to 60,000 persons per day.
The total population in the basin has been increasing on an average of
1.3% per year during the past 10 years. The populations for the individual
districts of the basin were estimated by adding the populations in all towns
wholly within a District and then estimating the percentage of those towns
along the outer margins (Table 4). The total basin population of 438,255 is
within 2% of that given by Fischer (1976) in the Champlain Planning Guide
(This estimate was computed independently [Appendix BJ before the Planning
Guide was released).
Three hydrographic Districts have population densities of more than TOO/
square mile. About a fourth of the population lives in cities with popula-
tions of 10,000 or more (three of these cities are in District D). Cowans-
vine, Quebec is the only Canadian City represented in this category. An
additional 40,000 inhabit villages of from 3,000 to 10,000 in population.
These figures indicate that about a third of the basin population lives in
developed communities, and about two-thirds live in small rural coraminities,
most situated on water-courses or on farms.
In the Champlain Basin Planning Guide, Fischer (1976) points out that east
of the lake there has been a trend in realization of the population, that
even though the larger communities are also growing in numbers, the percentage
of rural inhabitants is increasing at a greater rate (This is in contrast to
national trends). Below are tabulated the percentages of the 1970 populations
of the Towns bordering the lake as to urban and rural (From Table IV-6 in the
Planning Guide):
State Urban Rural
Vermont
New York
Quebec
20
-------
TABLE 4. POPULATION ESTIMATES FOR EACH DISTRICT OF THE LAKE CHAMPLAIN
DRAINAGE BASIN, INCLUDING THE PORTION IN CANADA*.
District
A
B
C
D
E
F
H
J
K
L
M
s**
Total s
Population
56,678
13,279
32,853
131,674
733
57,472
3,574
19,861
77,094
4,155
6,645
34,237
438,255
Percent
12.99
3.03
7.50
30.05
0.17
13.11
0.82
4.53
17.59
0.95
1.52
7.81
100.00
Number/ sq. mile
50.86
179.91
41.87
113.33
79.16
50.72
105.43
49.96
56.27
14.45
71.09
28.85
Average 57.09
* Data based on the 1970 Census Bureau Reports, and 1971 census data for
Canada. Estimates were made by adding the populations of all the Towns
completely within a District, and estimating the percentage of the popula-
tion of border towns.
** Not including the three towns along the north shore of Lake George.
21
-------
A pertinent comment in the Planning Guide is that, though there is a shift
of the population into the rural scene, this move is not all the way to the
farm, but the trend is the suburbanization of the small villages in commuting
distance to the larger communities. In terms of nutrient loading to the lake,
this trend can be read to mean that the point source loading will tend to
cluster in denser packets in the future, putting pressure on the assimilative
capacity of the waters receiving the wastewater.
We see from the above table that of the population on the western side of
the lake, only about 14% of the population is rural. The specific strategy to
control nutrients from New York will have to be different from the strategy
developed for the eastern side of the lake.
LAND USE
The pattern of generalized land use in the U. S. sector of the Champlain
basin is given in Table 5 with the information from Table V-6 of the Planning
Guide (Fischer, 1976). About 70% of the land is under shrub and forest, 9% as
waters and wetlands, and about 4% covered by urbanization. The percentage of
built-up areas is much higher in Vermont than in New York (despite the fact
that 86% of New York population is urban). Agriculture, which includes
orchards, cropland and pasture (19%) is a far more common use of land in Ver-
mont than in New York. A fourth of the land in Vermont is agricultural, and
most of this is cropland. According to another set of statistics (Planning
Guide, Table V-7), between the years 1980 and 2020, cropland and pasture in
the basin are projected to decrease 11.5% (from 22% to 10.5%), non-farm forest
lands to increase 10.2%, and urbanization to increase from 1.9 to 2.6%.
TABLE 5. GENERALIZED USE OF THE LAND OF THE CHAMPLAIN BASIN, 1970 IN NEW YORK
AND VERMONT. DATA FROM FISCHER, 1976.
PERCENT OF TOTAL LAND IN BASIN
Land use N. Y. Vermont Totals
Forests and shrubs
Water and wetlands
Public and semi public
Agriculture*
Build-up (urban)
78.2
9.3
1.1
9.8
1.6
60.9
8.7
0.9
24.5
5.0
67.7
8.9
1.0
18.8
3.6
Totals 100.0 100.0 1QQ.Q
* Agriculture includes orchards, croplands and pasture.
22
-------
Agriculture
The role of agriculture in lake eutrophication is a complex one, and will
not be examined in any detail here, but because of use the industry makes of
phosphorus, some comments are in order. The character of the Vermont popula-
tion has changed over the years. There once were more cows in Vermont than
people. The agricultural trends have been that (1) the population of cows has
decreased 27% in the past 20 years with the 1970 population standing at
193,956 bovines; and (2) the number of herds has decreased 60%, though the
herd size has increased (Little, 1971). This trend should increase point
source loading with increased concentration of cows, and reduce diffuse
loading. The Missisquoi District leads the State in cow population, and
Addison County (District F) ranks second (Tremblay, 1967). In 1970, the farm
animals contributed slightly more than 3-4 million tons of wet manure. Wet
manure is about 75-79% water; and a ton of wet manure contains 2-3 Ibs. of
P2®s> or 0.052% phosphorus. Thus, the annual wet manure crop in Vermont
amounts to 1,571 tons, or 1.425 X 106 kg phosphorus per year. Although this
figure represents the entire State, most of the dairys of the State are found
in the Champlain basin. This is almost double the entire Lake Champlain
loading. Considering the load emanating from the two dairy Districts (A and
F), the phosphorus originating from manure contributes a sizable portion of
the total estimated loading (not including cleaning operations). Over the
years the dairy industry would tend to increase the phosphorus export from t.hs>
land as non-point loading because of long-term accumulations. The manure
problem could become acute in small watersheds because of the trend of the
bovine sources to be concentrated into smaller geographical units.
In addition to the manure, more than 3.0 X 106 kg of fertilizer phosphorus
are applied to the croplands in Vermont annually (Little, 1971), more than
twice the manure production.
23
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SECTION 4
GENERAL LIMNOLOGICAL OVERVIEW OF LAKE CHAMPLAIN
THE LAKE AS A UNIT
Lake Champ!ain is one of the largest lakes In the United States (1,130 km2
surface area}. It does not consist of one morphoroetric basin, but is divided
by peninsulas, islands, and railroad and highway causeways into a number of
distinct water basins. Physical, chemical, and biological data indicate that
the lake can be divided into five general water masses. These areas include:
the "south lake" (Whitehall, N.Y. to Crown Point, N.Y.), the "main lake"
(Crown Point, N.Y. following the main channel to Rouses Point, N.Y.), Mallets
Bay (Vermont), the "northeast arm" (Sandbar Bridge, Milton, Vt. to Alburg,
Vt.), and Missisquoi Bay (Vermont and Quebec, Canada).
Because there are a number of distinct water masses in Lake Champlain, it
is not possible to discuss any specific characteristics of the whole water
body. Therefore, throughout this report, each of these indicated areas will
be discussed individually as to their physical, chemical, and biological char-
acteristics. There are, however, a few general comments that are applicable
to the majority of Lake Champlain and which set the background for the speci-
fic water mass descriptions.
Wind induced wave action and water column turbulence play an important
role in determining the limnological conditions of Lake Champlain. The lake
basin has a north-south orientation and the prevailing winds are generally
strong and from the south.
Thus, large open regions of the main lake and the northeast arm are mixed
to considerable depths and exposed embayment areas such as Missisquoi, Cumber-
land, Monty, King's, and outer St. Albans bay are mixed constantly or only
stratify for short periods. Areas of the lake that are protected from the
prevailing winds, such as Shelbume, Willsboro, and Malletts bays, tend to
thermally stratify for extended periods (Potash & Henson, 1966: Potash, Sund-
berg & Henson, 1969; and Gruendling, 1976a).
There is evidence that Lake Champlain has strong internal and surface
seiche activity and strong surface and subsurface currents. These phenomena
play important roles in current generation, vertical mixing, the flushing
action (retention time) of basins, and water movement between the various
water masses. These in turn influence the distribution and retention times of
nutrients throughout the lake (Myer, Larson, Cole and Hulburt, 1976).
The maximum and minimum water temperatures and the vertical temperature
regimes in Lake Champlain vary considerable geographically. The main lake
24
-------
from Rouses Point, N.Y. to Port Douglas, N.Y. has colder surface and bottom
temperatures than the southern portion of the main lake, Malletts Bay, the
northeast arm, Missisquoi Bay and the south lake (Henson & Potash, 1966;
Gruendling, 1976a).
Data from numerous sources indicate that there are significantly different
chemical characteristics in the various drainage basins and water masses of
Lake Champlain. Potash, Henson, & Sundberg (1969) have identified five major
water masses according to cation concentrations. Studies on the distribution
of major plant nutrients indicate that there are significant geographical dif-
ferences in concentrations of total, particulate, and dissolved phosphate;
total and nitrate nitrogen; and silicate (Gruendling & Malanchuk, 1974;
U.S.E.P.A., 1974).
Total cation concentrations decrease from the south lake to the outlet at
Rouses Point, N.Y. This gradient is unlike most lakes which pick up cations
as the water moves through the basin (Henson & Potash, 1966). Dilution from
New York rivers, which contribute water low in cations, and ground water aug-
mentation are two possible explanations for this phenomenon (Henson & Potash,
1976; Hunt, 1971).
The waters in most areas of Lake Champlain are well suppled with dissolved
oxygen. The surface waters are generally near saturation and the oxygen sat-
uration levels in the bottom waters rarely fall below 65 per cent. Malletts
Bay is the major exception to this pattern. It has severe dissolved oxygen
depletion in the hypolimnion during the summer and early fall (Potash &
Henson, 1966; Potash, Sundberg, & Henson, 1969).
Studies of phytoplankton populations classify Lake Champlain as a diatom
lake with a few species of bluegreen algae becoming dominant in late summer
and fall (Muenscher, 1930; Gruendling, 1976a). An evaluation of the seasonal
dynamics of phytoplankton in the various water masses indicate basic quali-
tative, quantitative, and temporal differences between embayments and the
deep water stations and differences among the main lake, the northeast arm,
Mallets Bay, and the south lake (Gruendling, 1976a). There is also some evi-
dence that there are significant differences in the abundance of the filamen-
tous green alga Cladaphora glomerata growing on the rocky shoreline areas. It
appears to be abundant in Shelburne Bay, but with only trace amounts in
Malletts Bay and the northeast arm area (Mercer, 1972). The New York shore and
the extreme north and south shores of Vermont have not been examined for
Cladophora however.
The zooplankton populations in Lake Champlain have not been completely
surveyed and analysed, but it appears that the species composition is similar
throughout most of the lake, except in the south lake. However, there are
temporal and quantitative differences in zooplankton among the various water
masses. The total copepod component generally outnumbers the cladoceran com-
ponent throughout the year in all regions investigated. The cyclopoid
copepods comprise the major portions of the copepod community (Legge, 1969;
Sage, 1969; Gruendling & Luguri, 1974; Page!, 1975). A taxonomic discrepancy
presently exists for the oligo-eutrophic indicator Eubosmina coregonii and the
eutrophic indicator Bosmina longirostris in the lake. Some studies record the
25
-------
presence of only Eubosmina while others only Bosmina. Recent studies by
Kantor (per. coran.) seen to indicate the presence of both species.
The benthic invertebrate fauna of Lake Champlain must be scrutinized very
carefully, for it may not only reflect differences in trophic conditions of
the water masses, but also differences in sediments, water depth, aquatic
plant growth, and organic waste materials. The sediment type varies greatly
throughout the embayment areas and becomes more uniform in the deep profundal
areas of the lake. Each bay region has significantly different benthic popu-
lations, which also differ from the deep water areas. They are generally
dominated by populations of Chironomidae and Mollusca. In the profundal
regions, the Oligochaeta are dominant, comprising from sixty to ninety per
cent of the benthic invertebrate community (Pagel, 1969; Pantas, 1966; Wade,
1976). The south lake has been receiving considerable amounts of effluent
from pulp and paper manufacturing which has significantly influenced the ben-
thic populations in this region (Page!, 1975). In general, the benthic fauna
of Lake Champlain is unique when compared with the Great Lakes.
CHARACTERISTICS OF REGIONS OF THE LAKE
Hissisquoi Bay
Missisquoi Bay, Vermont and Quebec, is located in the extreme northeast
portion of Lake Champlain and receives little influence from other water
masses in the lake. It is situated within drainage basin (A) of this report
and has major inputs from the Missisquoi, Rock, and Pike Rivers (Henson &
Potash, 1976). Table 6 summarizes the morphemetrie features of Missisquoi
Bay.
The current patterns of the bay are still under investigation. There is
evidence that a significant amount of the water flows south through the Alburg
Passage into the main lake; however, some of the water also flows into the
northeast arm near Maquam Bay (Myer, Larson, Cole & Hulburt, 1976; Henson &
Potash, 1974a).
There is no permanent sunnier thermal stratification in Missisquoi Bay due
to its shallow depth and high wind activity. There are indications that the
wind velocities and duration are substantially higher in the region than those
measured at Burlington, Vermont. The bay may stratify on a temporary basis
during warm, calm periods (Potash, Sundberg & Henson, 1969; Henson & Potash,
1974a; Vermont Water Resources Dept., 1976).
Table 7 summarizes the physical and chemical parameters for Missisquoi
Bay. The dissolved oxygen pattern appears to be affected locally by the
incoming rivers. There is oxygen deficient water entering from the Pike River
(approx. 20% oxygen deficit) and the Missisquoi River (approx. 10% oxygen
deficit), while there is oxygen saturated water entering from the Rock River.
The general condition in the bay is for some oxygen deficit (approx. 5-20%)
throughout the year (Henson & Potash, 1974a; Vermont Water Resources Dept.,
1976).
The relative total cation concentrations are some of the lowest values
26
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IX)
TABLE 6. BASIC MORPHOMETRIC FEATURES OF THE MAJOR WATER MASSES OF LAKE CHAMPLAIN,
VERMONT, NEW YORK, AND QUEBEC.
Water Mass
Missisquoi Bay
Northeast Arm
MalleUs Bay
South Lake
Main Lake
Surface Area
(km2)
77.5
268.5
54.2
56.9
682.5
Volume
(X 106m3)
220.4
3,450.0
699.3
155.5
21,000.0
Maximum Depth
(m)
4.0
49.0
32.0
'M.O
122.0
Mean Depth
(m)
2.8
12.8
12.9
2.7
30.8
Approximate
Retention Time
(years)
0.3
0.96
0.6
0.12
2.5 - 3.0
-------
TABLE 7. SUMMARY OF THE PHYSICAL AND CHEMICAL CHARACTERISTICS OF
MISSISQUOI BAY, LAKE CHAMPLAIN*.
Parameter
Secchi Disc (m)
Conductivity (micromho)
pH (standard units)
Range
0.7-2.3
78-124
7.1-8.1
Total Alkalinity (mg/1) 21.0-31.0
Total Phosphate-P (rag/1)
Participate Phosphate-P (mg/1)
Dissolved Phosphate-P (rag/1) .
N02 & N03 - N Crag/1) (sunnier)
N02 & N03 - N (rag/1) (winter)
NH3-N (mg/1)
K* Ong/D
Na+ (mg/1)
Mg+* (mg/1)
Ca++ (mg/1 )
Oxygen Saturation - Surface (%)
Oxygen Saturation - Bottom (%)
01 6-. 19
-
007-.023
.20-. 63
-
004-.63
82-107
82-96
Mean
1.6
94.3
7.6
26.7
.050
-
.015
.32
-
.026
1.03
3.24
2.68
11.34
93
92
Trophic Status
eutrophic
-
-
-
eutrophic
eutrophic
eutrophi c
-
eutrophic
V*
-
-
-
-
mesotrophic
Reference
28,
62,
74
62
74
74
74
74
62
62
62
62
74
74
74
74
* All values are from the surface waters except where indicated. The num-
bered references are the data sources used, and correspond to those listed
in the bibliography.
28
-------
found in Lake Champlain. They are similar to concentrations, found in Malletts
Bay and are approximately 25-30% lower than the main lake. In comparison with
cation concentrations in the Great Lakes, Missisquoi Bay has calcium and mag-
nesium values similar to Lake Superior and potassium and sodium concentrations
similar to Lake Michigan (Potash, Sundberg & Henson, 1969).
The phosphorus and nitrogen concentrations are some of the highest in Lake
Champlain, except for the south lake (Vermont Water Resources Dept., 1976).
Total phosphate, dissolved phosphate, and total inorganic nitrogen values com-
pare favorably with the values found in western Lake Erie and should be con-
sidered at a eutrophic level. The high phosphorus and nitrogen values coupled
with the low cation and alkalinity concentrations suggest that Missisquoi Bay
is probably receiving significant loading from man-made sources.
The secchi disc readings range from 0.75-2.3 meters, indicating that
Missisquoi Bay is a rather turbid body of water. Low readings are due to both
phytoplankton and sediment particulate matter in the water column (Henson &
Potash, 1974a; Vermont Water Resources Dept., 1976).
Table 8 summarized the biological parameters for Missisquoi Bay. There
are very little published data available on phytoplankton populations, primary
productivity, and zooplankton populations for the region. The only phyto-
plankton data available on Missisquoi Bay were collected in 1966-67. From
these data, it is apparent that the algal community throughout the year is
Quite different from other regions of the lake. Diatoms are almost always the
dominant group with Melosira italica, Asterionella formosa, Diatoma sp. and
Stephanodiscus sp. being the most important species. Occasionally, Dinobryon
bavaricum and D. divergens are abundant. The most striking difference between
Missisquoi Bay and other regions of the lake is the lack of significant popu-
lations of bluegreen algae. Aphanothece sp. and Anabaena flos-agua occasion-
ally reach moderate population densities. In general, the phytoplankton com-
munity is mesotrophic (Philip Cook, personal communication). Only two chloro-
phyll values are available. They indicate a moderate amount of phytoplankton
biomass present in the summer (Vermont Water Resources Dept., 1976).
The oligochaete and other benthic populations were sampled in 1966, 1974,
and 1975. Wide year to year variations in benthic organism numbers have been
found, however there are generally equal percentages of Sphaeridae, Gastro-
poda, Oligochaeta, and Chironomidae present. Among the oligochaetes, Pelos-
colex ferox, immature capilliform specimens, Aulodrilus americanus, and
Potamothrix vejdovskyi are the most abundant. These populations are character-
istic of shallow mesotrophic to eutrophic areas in the Great Lakes and other
regions (Pagel, 1969; Wade, 1976).
Presently, the trophic status of Missisquoi Bay can be classified as late
mesotrophic to eutrophic based on phosphorus and nitrogen concentrations and
benthic invertebrate populations. More data are needed on the plankton and
aquatic plant components to verify this assessment however. It appears that
the shallow depth with subsequent mixing and the short retention time of the
bay do not allow for the development of certain eutrophic characteristics.
For example, dissolved oxygen concentrations do not reflect the amount of
plant nutrients available in the region.
29
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TABLE 8. SUMMARY OF THE BIOLOGICAL CHARACTERISTICS OF MISSISQUOI BAY,
LAKE CHAMPLAIN.
Parameter Range Mean Trophic Status Reference*
Phytoplankton Biomass (rag/I) -
Chlorophyll A (jig/1) **7.0-14.0 **10.0 eutrophic 74
P.A.A.P. Final Biomass (mg/1) -
P.A.A.P. Limiting Factor
Dominant Phytoplankton
(Diatoms)
Melosira jtalica
'Asterionella formesa
Diatproa spT"
Stephanodiscus sp.
(Bluegreens)
Aphanothece sp.
Anabaena fTos-aqua
(Golden-Browns)
Dinobryon bavaricum
Dinobryon divergens
Dominant Zooplankton
Dominant Benthic Invertebrates
(Oligochaeta)
Peloscolex ferox meso-eutrophic 51, 77
Aul odri 1 us" americana
Immature capilliforms
(Chironomidae)
Chaoboris punctipennis
* The numbered references are the data sources used andcorrespond to those
listed in the bibliography.
** Only 2 values.
30
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Northeast Arm - Main Portion
The northeast arm of Lake Champlain is located within drainage basin (B)
and a portion of (H) of this report, between Sandbar Bridge, Milton, Vermont
and Swanton, Vermont. The area is isolated from other sections of the lake
by railroad and road fills and by large islands. Thus there are only four
narrow connections available for water exchange; a culvert to Malletts Bay, a
small passage to Missisquoi Bay, the Alburg Passage to the main lake, and a
highway and railroad bridge opening through the Gut to the main lake. There
are no major tributaries entering the region, although a few small streams
contribute significant phosphorus loading. The morphometric features are sum-
marized in Table 6 (Potash, Sundberg, & Henson, 1969; Henson & Potash, 1976).
In the following discussion, the data collected by the U. S. Environmental
Protection Agency during 1972 will be used sparingly. It was felt that the
sampling station was not representative of the northeast arm area since it was
located in quite shallow water and close to St. Albans Bay, which probably
significantly influenced the chemical constituents (U.S.E.P.A., 1974). Also,
since the characteristics of St. Albans Bay are substantially different from
the rest of the northeast arm, a separate section discussing its features is
included.
The deeper portions of the northeast arm are thermally stratified during
the summer with an average epilimnion thickness of about 12.0 meters and a
maximum of 20.0 meters. Maximum surface and hypolimnial temperatures are sig-
nificantly higher than in other areas of the lake (Henson & Potash, 1966;
Potash, Sundberg & Henson, 1969; Gruendling, 1976a).
Table 9 summarizes the physical and chemical characteristics of the north-
east arm. The surface waters are well oxygenated throughout the year. How-
ever, bottom waters show considerable oxygen deficit during the summer strati-
fication period. Minimum values in the hypolimnion generally range from 45-
48% saturation. Moderate algal productivity, relatively small hypolimnial
volume, and warmer bottom temperatures, probably account for this oxygen defi-
cit (Henson & Potash, 1966; Potash, Sundberg & Henson, 1969).
Major cation concentrations in the northeast arm are very similar to
Malletts Bay and Missisquoi Bay and only slightly less than the main lake.
Potassium concentrations are an exception, exhibiting the highest concentra-
tions found in the lake. Cation values are similar to oligotrophic Lake
Superior and oligo-mesotrophic Lake Huron. Total alkalinity is also substan-
tially lower than the main lake (Henson, Potash & Sundberg, 1966; Potash,
Sundberg & Henson, 1969).
The particulate phosphorus values average slightly higher than most sta-
tions on Lake Champ!ain, except for a few enriched embayment areas and the
south lake. These values, however, are in the mesotrophic range. Total
nitrate-nitrogen values ranged from 40-80% lower than values observed in other
portions of the lake. This trend continues during the winter when phytoplank-
31
-------
ton are low and can not be solely attributed to phytoplankton uptake during
the rest of the year. Values for Inorganic nitrogen are lower throughout
most of the northeast arm than the Great Lakes and mist be considered In the
oUgotrophlc to mesotrophlc range (Gruendllng & Malanchuk, 1974).
The secchl disc values are the highest found anywhere 1n Lake Champlaln.
The mean values for three stations within the region during the summer and
fall are Indicative of early mesotrophlc situations. The phytoplankton data
support this contention (Gruendllng, 1976b).
Table 10 summarizes the biological parameters for the northeast arm.
Studies on the seasonal and geographical distribution of phytoplankton popula-
tions Indicate some qualitative and quantitative differences between the
northeast arm and other areas. Algal populations are generally lower through-
out the growing season In the northeast region. This Is supported by rela-
tively lower chlorophyll A and phytoplankton biomass values, both of which are
In the oligo-mesotrophic range. Qualitative differences are reflected in the
relative dominance of phytoplankton species. Fragi 1 aria crotonenses, F.
capucina. and Synedra ulna are the most abundant diatoms.Helqsira isTandica,
a diatom that reaches relatively high numbers in other areas of the lake, is
a minor constituent in the northeast arm. Among the bluegreen algae, the
three major Anabaena species are found in lower numbers than elsewhere. The
florfstic composition and the population numbers of phytoplankton in the
region are indicative of mesotrophic conditions (Gruendling, 1976a;
Gruendling, 1976b). The P.A.A.P. algal bioassays conducted in the northeast
arm demonstrate that phosphorus is the limiting factor to algal growth. Final
control yields of Selenastrum are indicative of mesotrophic areas (U.S.E.P.A.,
1974; Gruendling, 1976b).
The composition of the zooplankton fauna of the northeast arm region is
very similar to other areas of the lake. The copepods dominate the community
throughout most of the year, comprising 53-85% of the total microcrustacea.
Cyclops bicuspidatus thomasi is generally the predominant species except
during the fall when the three species of Diaptomus sp. become dominant. The
cladoceran fauna is dominated by Daphnia galeata mendotae (comprising approxi-
mately 41-85% of the cladoceran community) and theTBosmina-Eubosmina complex
which comprises from 10-57X throughout the year. The total copepod numbers
(maximum - 1.18 x 106/m*; mean - 0.63 x 106/ro2) are slightly lower than other
deep portions of the lake but higher than most bay regions. The total clado-
ceran numbers (maximum - 0.71 x 106/ro2; mean = 0.28 x 106/m2) are slightly
higher than other areas of Lake Champlain.
The general chemical and biological characteristics of the deeper portions
of the northeast arm indicate early mesotrophic conditions. Although there
are little data available, the shallow bay areas (Maquam Bay, Keeler Bay,
Laparo Bay, Gary Bay, and the Gut) tend to have late mesotrophic to eutrophic
conditions. St. Albans Bay is classified as eutrophic.
Northeast Arm - St. Albans Bay
St. Albans Bay has been selected for separate treatment in this report due
to the occurrence of limnological conditions that are extremely different from
32
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TABLE 9. SUMMARY OF THE PHYSICAL AND CHEMICAL CHARACTERISTICS OF
NORTHEAST ARM, LAKE CHAMPLAIN*.
Parameter
Secchi Disc (ra)
Conductivity (micromho)
pH (standard units)
Total Alkalinity (mg/1)
Total Phosphate-P (rag/1)
Particulate Phosphate-P (rag/1)
Dissolved Phosphate-P (mg/1)
N02 & N03-N (mg/1) (summer)
N02 & N03-N (mg/1) (winter)
NH3-N (mg/1)
K+ (mg/1)
Na* (mg/1)
Mg++ (mg/1 )
Ca** (mg/1)
Oxygen Saturation-Surface (%)
Oxygen Saturation- Bottom (%)
Range
4.5-6.5
**130-132
7.5-8.2
-
t
.006-. 02
t
-
-
t
108-89
100-45
Mean
5.5
**131
7.8
30.8
-
.011
-
.014
.033
-
**1.2
**3.0
**2.9
**13.2
-
-
Trophic Status Reference
mesotrophic 21
14
14
31
14
mesotrophic 24
14
oligo-mesotrophic 24
oligo-mesotrophic 24
14
62
62
62
62
14, 62
meso-eutrophic 14, 62
* All values are from the surface waters except where indicated. The num-
bered references are the data sources used, and correspond to those listed
in the bibliography.
** Median value.
t Samples taken from a station near St. Albans Bay which is more eutrophic
than Northeast Arm in genera-1 (see text for explanation).
33
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TABLE 10. SUMMARY OF THE BIOLOGICAL CHARACTERISTICS OF NORTHEAST ARM,
LAKE CHAMPLAIN.
Parameter Range Mean Trophic Status Reference*
Phytoplankton Biomass (rog/1) .15-.66 .50 oligo-mesotrophic 21
Chlorophyll A (ug/1) 1.5-6.5 3.5 oligo-mesotrophic 21
P.A.A.P. Final Biomass (mg/1) -
P.A.A.P. Limiting Factor - Phosphorus 14, 19
Dominant Phytoplankton max. cells x 105/1 20, 21
Fragilaria crotonensis 4.83
Synedra uTna .55 mesotrophic
Anabaena~crrci nali s 3.69
Anabaena flos-aqua~ 1.24
Dominant Zooplankton 23
(Copepods)
Cyclops bicuspidatus thomasi
Hesocyclops edax
Diaptomus oregonensis
Diaptomus minutus
Diaptomus sicilis
(Cladocerans)
Daphnia ge
Eubosroina coregom-Bosmina longirostris
Dominant Benthic Invertebrates
Daphnia galeata roendotae
jbc
* The numbered references are the data sources used and correspond to those
listed in the bibliography.
34
-------
other areas of the northeast arm. St. Albans Bay is divided into two general
areas; the inner bay with a maximum depth of approximately 6.0 meters and the
outer bay with a maximum depth of 10.0 meters. There appears to be a gradi-
ent of chemical conditions, especially the concentrations of phosphorus and
nitrogen, from the inner bay to the outer bay area. This is primarily a
result of the heavy nutrient loading from the City of St. Albans, Vermont
sewage treatment facility entering via Stevens Brook. Stevens Brook has the
highest total phosphorus concentration of any tributary entering Lake Cham-
plain (Henson & Potash, 1976).
Due to the shallowness of the bay region, the water column seldom strati-
fies for any length of time. Throughout the majority of the season the bay
is isothermal (Gruendling, 1976a; Vermont Water Resources Dept., 1976).
Table 11 summarizes the physical and chemical characteristics of inner St.
Albans Bay. The dissolved oxygen concentrations in the bay seldom show any
oxygen deficit. During the summer and early fall, surface water dissolved
oxygen values are generally supersaturated, while the bottom waters are only
slightly less than saturated. The lack of a significant oxygen deficit in
the bottom water is probably due to the well mixed conditions and active
photosynthesis throughout the water column. Trends in oxygen values since
1966 demonstrate increasing oxygen saturation values in the surface water,
thus indicating increasing productivity (Henson & Potash, 1974b; Vermont.
Water Resources Dept., 1976).
The dissolved and total phosphate concentrations are high. The values are
the highest recorded for the lake, except for the south lake and Missisquoi
Bay, and are two-three times the average values for other areas of the north-
east arm. They fall well within the eutrophic range (Vermont Water Resources
Dept., 1976). Phosphorus has been determined to be the chief limiting factor
to algal growth in St. Albans Bay (U.S.E.P.A., 1974; Gruendling, 1976b).
Corlis and Hunt (1973) have compared the phosphorus content of the sedi-
ments in St. Albans Bay with that of an adjacent area, Lapan Bay. The con-
centrations of phosphorus ranged from 513-1576 p.p.m. (mean = 983) in St.
Albans Bay, while in the relatively unpolluted Lapan Bay the values ranged
from 298-760 p.p.m. (mean = 535). The maximum concentrations in St. Albans
Bay were found near the mouth of Stevens Brook and in the deeper parts of the
bay and are associated with high organic content sediments. It is believed
that continued buildup of phopshorus in the sediments may make future res-
toration of the bay difficult (Corliss & Hunt, 1973).
The Secchi disc transparencies are the lowest recorded summer values for
Lake Champ!ain, except for the south lake. The present values are indicative
of eutrophic conditions. Secchi disc values have recently declined, with the
summer range in 1966 being 2.0 - 4.0 meters and the summer mean during 1974
being 1.25 - 2.25 meters. The majority of this reduced transparency is
believed to be due to increases in phytoplankton growth (Henson & Potash,
1974b; Vermont Water Resources Dept., 1976).
Although algal blooms and aquatic weed growth have been considered serious
problems for inner St. Albans Bay in recent years, there are little detailed
35
-------
quantitative data available on the subject. Table 12 is a summary of the bio-
logical characteristics of the area. Studies on phytoplankton tn the outer
St. Albans Bay, an area that is less nutrient rich than the inner bay, indi-
cate a mesotrophic-eutrophic flora with algal bionjass and chlorophyll A values
also suggesting the same trophic classification (Gruendling, 1976a;
Gruendling, 1976b). There are Indications that the inner bay has significant-
ly higher algal populations however (Vermont Water Resources, Dept., pers.
comm.).
In order to control some of the algal blooms in inner St. Albans Bay,
50,000 pounds of copper sulphate have been applied over the past nine years
(Burlham, 1974). This has apparently lead to the increase in rooted aquatic
weed growth, which, in turn, is believed to have affected fish populations of
the area (Anderson, 1974). The Vermont Water Resources Department considers
the extensive growth of the rooted aquatic plants to be the largest eutrophi-
cation problem of the inner bay area. The european milfoil, Myriophyllum
spicatum, in addition to other plants, form dense beds around the perimeter
of the bay and interfere extensively with recreational activities (Vermont
Water Resources Dept., pers. comm.).
The zooplankton fauna and seasonal dynamics in outer St. Albans Bay is
very similar to those observed in other sections of the northeast arm. The
copepods comprise 38-94% of the total fauna throughout the year, while the
cladocerans comprise from 6-62%. Cyclops bicuspidatus thoroasi is the most
abundant copepod followed by Diaptomus oregonensis and Uiaptomus minutus.
The Bosmina-Eubosmina complex and Daphma gal eat a mendotae generally comprise
nearly all of the cladoceran biomass. The total numbers of copepods (maximum
= 0.39 x 106/m2; mean = 0.15 x lOVm2) and cladocerans (maximum = 0.19 x 106/
m2; mean 0.12 x 106/m2) are lower than other parts of the northeast arm but
similar to some of the other bay regions of the lake.
The general distribution and population trends of benthic invertebrates
reflect both the effects of increased eutrophication and the treatments with
copper sulphate. In the regions where copper sulphate treatments have been
the heaviest, there has been a reduction in gastropods and a six-fold increase
in "copper-tolerant" chironoroids. The oligochaete population numbers through-
out the bay are lower than expected for the highly organic sediments, possibly
a copper sulphate influence. However, the dominant types of oligochaetes have
changed from mesotrophic forms (Peloscolex ferox) which were dominant in 1966
to strongly eutrophic species (LiiDnodnlus hoffmeisteri and others) in 1974
(Pagel, 1969; Wade, 1976a).
In summary, all indicators point to St. Albans Bay being a eutrophic body
of water. Trends in the past ten years also indicate that the problem is
accelerating. It is generally believed that the major cause of the accelera-
ting eutrophication is the significant phosphorus loading from the sewage
facility in St. Albans, Vermont.
Malletts Bay
Malletts Bay, Vermont is an area of Lake Champlain that is almost com-
pletely isolated from the main lake and the northeast arm by railroad and
36
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TABLE 11. SUMMARY OF THE PHYSICAL AND CHEMICAL CHARACTERISTICS OF
INNER ST. ALBANS BAY, LAKE CHAMPLAIN*.
Parameter
Seech i Disc (m)
Conductivity (micromho)
pH (standard units)
Total Al kal i n i ty (mg/ 1 )
Total Phosphate-P (mg/1)
Particulate Phosphate-P (mg/V
Dissolved Phosphate-P (mg/1)
N02 & N03-N (rag/1 ) (summer)
Range
2.0-3.0
100-165
7.5-9.3
35-43
.022-. 066
)
.008-. 036
-
Mean
2.4
136
8.1
39.1
.037
-
.015
-
Trophic Status
eutrophic
-
-
-
eutrophic
-
eutrophic
-
Reference
74
74
74
74
74
74
N02 & N03-N (mg/1) (winter)
NH3-N (mg/1)
K+ (mg/1)
Na+ (mg/1)
++
.004-. 06
.023
Mg
Ca""" (iug/1)
Oxygen Saturation-Surface (%) 90-110
Oxygen Saturation-Bottom (56) 80-103
mesotrophic
74
74
74
* All values are from the surface waters except where indicated. The numbered
references are the data sources used, and correspond to those listed in the
bibliography.
37
-------
TABLE 12. SUMMARY OF THE BIOLOGICAL CHARACTERISTICS OF
INNER ST. ALBANS BAY, LAKE CHAMPLAIN*.
Parameter Range Mean Trophic Status Reference
Phytoplankton Biomass (rag/1) **.18-2.1 **1.0 raeso-eutrophic 21
Chlorophyll A (yg/1) **4,1-12.6 **6.7 raeso-eutrophic 21
P.A.A. P. Final Biomass (rog/1) -
P.A.A.P. Limiting Factor - phosphorus 19, 74
Dominant Phytoplankton - max. cells x 105/1
** (Diatoms) 20, 21
Fragi1iana crotonensis ** 5.64
Helosira islandica.97 meso-eutrophic
(Bluegreens)
Anabaena flos-agua 30.39
Anabaena circinalis 23.35
Dominant Zooplankton 23
** (Copepods)
Cyclops bicuspidatus thomasi
Hesocyclops edax
Diaptomus oregonensis
Diaptomus ml nutus
(Cladocerans)
Eubosmina coregoni-Bosroina longirostris
Daphnia galeata mendotae
Dominant Benthic Invertebrates
(Oligochaeta) 77
Lironodrilus hoffmeisteri eutrophic
11 yodri 1 us~templ etoni eutrophic
Tubifex tubTFixmesotrophic
* "Tie numbered references are the data sources used and correspond to those
listed in the bibliography.
** Measurements taken in Outer St. Albans Bay only.
38
-------
highway fills. As a result, conditions in the bay are often quite different
than they are in the open portions of the lake. There is evidence that
seiche activity in these open portions have some influence on Malletts Bay in
terms of mass water movement through the openings in the causeway barriers
(Myer, Larson, Cole & Hulbert, 1976). Studies are presently being completed
to quantify these phenomena (Myer, pers. comm.).
The Malletts Bay area actually consists of two areas; a small shallow
inner bay and a larger, deeper outer bay. Most of the research has been con-
ducted on the outer bay and the discussion that follows concentrates on this
area.
Malletts Bay is located in drainage basin (C) of this report. The Lamoille
River, the major tributary of the drainage basin, has significant influences
upon the limnological characteristics of the bay. This river contributes the
second largest discharge of tributaries entering Lake Champlain, it ranks
sixth in terms of phopshorus loading, and discharges large amounts of BOD
to the Malletts Bay area (Gregg, 1974; Henson & Potash, 1976). Table 6 sum-
marized the morphometric features of Malletts Bay.
Malletts Bay generally exhibits strong thermal stratification from early
July through early October. Maximum surface temperatures range from 22.0 -
24.0° C in the summer, while hypolimnial temperatures range from 9.0 - 10.0° C.
The major reason for such a long period of stratification is the lack of
strong winds and other mechanisms for vertical water movement due to the pro-
tected nature of the basin (Potash & Henson, 1966; Potash, Sundberg & Henson,
1969; Gregg, 1970; Gruendling, 1976a).
Table 13 summarizes the physical and chemical characteristics of Outer
Malletts Bay. As a result of the strong thermal stratification, the in-lake
productivity, and the organic matter entering via the Lamoille River, the
hypolimnion of the outer bay exhibits severe oxygen depletion during the sum-
mer and early fall. The bay has had oxygen depletion each year since 1964
with minimum values reaching as low as 3.0% saturation (0.1-0.2 mg/1 oxygen).
An illustration of the localized nature of the severe oxygen depletion in
Malletts Bay is that summer bottom water values in the main lake just west of
the railroad fill are not below 75% saturation and values in the northeast arm
north of the causeway are not below 50% saturation. Oxygen values close to
saturation reoccur following turnover in the fall. There are also indications
that oxygen values during ice cover dropped below 50% saturation at 25.0
meters and below 15% (1.0 mg/1 oxygen) near the bottom. No severe oxygen
depletion in the hypolimnion has been demonstrated for inner Malletts Bay
(Potash & Henson, 1966; Potash, Sundberg & Henson, 1968; Potash, Sundberg &
Henson, 1969; Gregg, 1970).
Epilimnetic oxygen values are generally above 90% saturation throughout
the year. The only significant oxygen deficits in the epilimnion occur during
fall turnover and at times when unusually high winds induce a vertical dis-
placement of the epilimnion-metalimnion boundary. Under these displacement
conditions, epilimnial water is exposed to the reduced organic sediments and
a significant drop in the dissolved oxygen occurs (Potash & Henson, 1966;
Potash, Sundberg & Henson, 1968; Potash, Sundberg & Henson, 1969).
39
-------
Cation concentrations in Malletts Bay tend to be lower than most other
areas of the lake. This is possibly due to the short retention time of the
basin. Calcium and magnesium values compare favorably with Lake Superior
values and potassium and sodium concentrations are similar to Lakes Huron and
Michigan (Henson, Potash & Sundberg & Henson, 1969).
Phosphorus and nitrogen values appear to support the trends of low nutrient
levels as demonstrated by the cation concentrations. Total, particulate, and
dissolved phosphorus concentrations are low, even though there is high phos-
phorus input entering from the Lamoille River. This possibly reflects the
short retention time of the water mass and/or loss of phosphorus to the sedi-
ments. Phosphorus levels are lower than levels for other areas of Lake Cham-
plain. Values are similar to phosphorus concentrations in Lake Michigan and
the eastern basin of Lake Erie and are considered to be in the early mesotro-
phic range. Mean winter values for nitrate nitrogen are slightly lower than
other areas of the lake, except the northeast arm. Mean summer values in the
surface waters are higher than other areas, indicating a lack of biological
uptake during this period. The range of nitrate nitrogen concentrations are
similar to the open waters of Lake Ontario and are considered to be at meso-
trophic levels (Gruendling & Malanchuk, 1974; U.S.E.P.A., 1974).
The Secchi disc readings are among the highest for Lake Champlain, except
for the deeper portions of the northeast arm. The range of values and mean
summer and fall values are within the mesotrophic range (U.S.E.P.A., 1974,
Gruendling, 1976b).
Table 14 summarizes the biological characteristics of outer Malletts Bay.
The phytoplankton data present somewhat of a confusing picture as to the tro~
phic status of Malletts Bay. The calculated phytoplankton biomass values from
May-October 1970 and 1974 are low and are similar to Lake Huron, thus indica-
ting an oligotrophic condition. Chlorophyll A concentrations for the summer
and fall period are some of the highest determined for the lake and fall
within the mid-mesptrophic range. The dominant phytoplankton species are
somewhat different than other areas of Lake Champlain. The most striking
difference is the lack of appreciable numbers of bluegreen algae. The area
ts dominated by diatoms (Fragilaria crotonensis, Synedra ulna, Tabellaria
fenestrata) at all times of the year and has basically a mesotrophic flora.
The tenthic green alga, Cladophora glomerata, which is so abundant in eutro-
phic situations such as Lake Erie, is extremely sparce on the rocky shores of
Malletts Bay (Gruendling, 1976a; Gruendling, 1976b; U.S.E.P.A., 1974; Mercer,
1972).
The composition of the zooplankton fauna is not significantly different
than other areas of the lake. During the winter and spring, the copepods
comprise about 95% of the crustacean zooplankton, of which a major portion
are the cyclopoid copepods (Cyclops bicuspidatus thomasi dominant). During
the summer and early fall, there are significant increases in the cladoceran
populations; primarily the Bosmina-Eubosomina complex, Daphnia galeata men-
do tae, and Daphnia retrocurva. However, the copepods still comprise a major-
ity of the zooplankton community in the summer. Both the maximum (0.63 x 106
organisms/m2) and the mean (.014 x 106 organisms/m2) numbers of total copepods
tn Malletts Bay are slightly less than other areas of the lake except some of
40
-------
TABLE 13. SUMMARY OF THE PHYSICAL AND CHEMICAL CHARACTERISTICS OF
OUTER MALLETTS BAY, LAKE CHAMPLAIN*.
Parameter
Secchi Disc (m)
Conductivity (micromho)
pH (standard units)
Total Alkalinity (mg/1)
Total Phosphate-P (mg/1)
Particulate Phosphate-P
(mg/1 )
Dissolved Phosphate-P (mg/1)
N02 & N03-N (mg/1) (summer)
N02 & N03-N (mg/1) (winter)
NH3-N (mg/1)
K+ (mg/1 )
+
Na (mg/1 )
Mg++ (.rag/1 )
Ca"1"1" (mg/1 )
Oxygen Saturation-Surface (%)
Oxygen Saturation-Bottom (%}
Range
3.7-6.5
100-123
6.4-7.4
-
.007 -.021
.006-. 01 3
.005-. 01 3
-
-
.030-. 070
86-100
3-90
Mean
4.4
106
7.0
27.6
.012
.010
.009
.095
.149
.047
.092
2.86
2.53
12.30
-
-
Tropjvic Status
mesotrophic
-
-
-
ol igo-mesotrophic
mesotrophic
mesotrophic
mesotrophic
mesotrophic
mesotrophic
-
-
-
-
-
eutrophic
Reference
21
14
14
62
14
24
14
24
24
14
62
62
62
62
60, 61
60, 61
* All values are from the surface waters except where indicated. The numbered
references are the data sources used, and correspond to those listed in this
bibliography.
41
-------
TABLE 14. SUMMARY OF THE BIOLOGICAL CHARACTERISTICS OF
OUTER HALLETTS BAY, LAKE CHAMPLAIN*.
Parameter
Range
Mean Trophic Status Reference
Phytoplankton Biomass (rag/1) .24-1.33 .69
Chlorophyll A (yg/1) 3.4-11.4 6.2
P.A.A.P. Final Biomass (mg/1)
P.A.A.P. Limiting Factor - Phosphorus
Dominant Phytoplankton max. cells x 10S/1
(Diatoms)
Fragilaria crotonensis 32.56
Tabellaria fenestrata 2.30
Synedra uTna 1.41
(Bluegreens)
Anabaena circinalis 1.89
Dominant Zooplankton
(Copepods)
Cyclops bicuspidatus thomasi
Piapterous minutus
Diaptomus sicilis
Mesocyclops edax
(Cladocerans)
Daphnia galeata mendotae
Daphma retrocurva
Eubosimna coregom'-Bosmina longirostris
Dominant Benthic invertebrates
(Oligochaeta)
Limnodrilus sp.
Potamothrix vejdovskyi
(Diptera)
ChironiBnus anthracinus
(Isopoda)
Ascellus internedius
oligotrophic
mesotrophic
oligo-mesotrophic
21
21
14, 19
20, 21
18, 23
54, 77
eutrophic
eutrophic
meso-eutrophic
mesotrophic
* The numbered references are the data sources used and correspond to those
listed in the bibliography.
42
-------
the shallow bay regions. Cladoceran populations (maximum = 0.24 x 106/m2;
mean = 0.14 x 106/nr*) are also lower than most areas of the lake (Sage, 1969;
Gruendling & Luguri, 1974).
The benthic invertebrate populations in Malletts Bay are typical of deep
water lakes of the glaciated region of North America. It appears as though
the populations reflect the dissolved oxygen conditions occurring in the
lower waters. The inner bay (no significant oxygen deficit) is dominated by
a number of mesotrophic chironomid species with some oligochaete species also
being important. Approximately 97% of the oligochaete component consists of
immature capilliform specimens. The outer bay (severe oxygen depletion) is
dominated by the oligochaetes, Limnodrilus sp. and Potamothrix vejdovskyi,
both of which are abundant in eutrophic situations. The seasonal population
dynamics of the isopod Asellus intermedius and the chironomid Chironomus
anthracinus also reflect the changes in the dissolved oxygen conditions in
the hypolimnion. Both species increase in number at deep stations only after
completion of fall turnover. These population increases are a result of
migration from well oxygenated shallow water areas (Pantas, 1966; Wade,
1976a).
The general trophic status of Malletts Bay is a paradoxical situation.
Characteristics such as severe oxygen depletion of the hypolimnion and the
benthic invertebrate populations indicate that eutrophic conditions are
present. On the other hand, the transparency of the water, most of the chenh
ical data, and the phytoplankton data, indicate that the area is probably in
an early mesotrophic state. The oxygen characteristics are probably due to
the high BOD loading from the Lamoille River and not solely due to nutri-
ent loading. The invertebrate populations subsequently respond to the oxygen
conditions. Considering these data, Malletts Bay should be classified as
early mesotrophic (Gregg, 1970).
South Lake
South Lake Champlain, Vermont and New York, is that portion of the lake
from the Crown Point Bridge south to Whitehall, N.Y.. It is located within
drainage basin (S) of this report and is comprised of drainage areas (G) in
Vermont and (N) in New York. It receives major inputs from the Barge Canal-
Poultney River System, Putnam Creek, East Creek, Mill Creek, Ticonderoga
Creek, and the International Paper Company outfall north of Ticonderoga, N.Y.
It ranks fifth in the amount of phosphorus loading and has an exceptionally
high theoretical phosphorus concentration (Henson & Potash, 1976). Table 6
sunmarizes the morphometric features of the region.
Summer thermal stratification is generally not pronounced throughout most
of the south basin. The shallow depth, long, narrow surface area to generate
turbulence, and the frequent barge traffic probably all contribute to peri-
odic mixing of the water column. In the deeper northern parts of the region,
some thermal stratification does occur. The south lake is considered one of
the "warm" regions of Lake Champlain, with maximum summer temperatures 2.0-
4.0° C higher than the main lake (Henson & Potash, 1966; Henson, Potash &
Sundberg, 1966; Potash, Sundberg & Henson, 1969).
43
-------
Table 15 is a summary of the physical and chemical features of the south
lake. Dissolved oxygen concentrations in the surface and bottom waters have
a wide range of values throughout the region. Oxygen values near or above
saturation occur in algal growth areas and low values in localized areas
receiving organic pollution. In general, there is no significant oxygen
depletion in the lower waters for any appreciable length of time. However,
generalizations about the limnological characteristics of the south lake are
difficult to make since the overall conditions are complicated by major
inputs from past and present pulp and paper operations. Areas in the vicin-
ity of Ticonderoga Bay and the "effluent diffuser" of the International
Paper Company have limnological conditions quite different from other south
lake areas (Potash, Sundberg & Henson, 1969; Pagel, 1969; U.S.E.P.A., 1974;
Page!, 1975).
Median values for the concentration of major cations are significantly
higher (50-60%) than other areas of the lake, although when compared to the
Great Lakes, the values are similar to the low nutrient lakes of Huron and
Michigan. Total alkalinity values are also significantly higher in the south
lake. It has been noted that there are great fluctuations in concentrations
of ions, 50% or more, between sampling periods in the region. These periodic
variations may be due to increased short-term runoff in a lake basin of very
small volume (Henson, Potash & Sundberg, 1966; Potash, Sundberg, Henson,
1969).
Nitrogen and phosphorus are abundant throughout the south lake region,
with values averaging higher than any other areas of Lake Champlain. Values
for total and dissolved phosphorus and inorganic nitrogen compare favorably
with those for the western basin of Lake Erie and fall well within the eutro-
phic range. The nutrient rich water of the south lake has the potential of
significantly influencing the water mass in the main lake north of Crown
Point, N.Y. Extension of high nutrient water into this area of the lake may
result in accelerating eutrophication problems. There have already been
reports of extensive algal blooms just north of Crown Point Bridge and in the
Port Henry, N.Y. area (Beak Associates, 1972; U.S.E.P.A., 1974; Pagel, 1975).
The secchi disc values for the south lake are the lowest found in Lake
Champlain (0.7-1.3 meters) and fall within the eutrophic range. However, the
turbidity found in this region is caused primarily by suspended clay parti-
cles and only occasionally due to substantial algal growth (U.S.E.P.A., 1974).
Table 16 is a summary of the biological features of the south lake. There
have been no detailed seasonal studies made of phytoplankton populations.
Preliminary reports, however, indicate that there have been blooms of
Aphanizomenon sp. and Melosira sp. in the region. A limited number of chlo-
rophyll A measurements and P.A.A.P. control yields indicate that the phyto-
plankton biomass is not extremely high and it can be categorized as mesotro-
phic to eutrophic. It appears that, because of high nutrients and elevated
summer temperatures, the potential for extensive algal blooms (especially
bluegreen algal blooms) exists in the south lake. However, due to the
extremely high turbidity, phytoplankton productivity is suppressed fBeak
Associates, 1972; Wood, 1972; U.S.E.P.A., 1974).
44
-------
TABLE 15. SUMMARY OF THE PHYSICAL AND CHEMICAL CHARACTERISTICS OF
SOUTH LAKE, LAKE CHAMPLAIN*.
Parameter
Secchi Disc (ID)
Conductivity (Tiricromho)
pH (standard units)
Total Alkalinity (mg/1)
Total Phosphate-P (rag/1)
Particulate Phosphate-P (mg/1)
Dissolved Phosphate-P (mg/1)
N02 & N03-N (mg/1 ) (summer)
N02 & N03-N (mg/1) (winter)
NH3-N (mg/1)
K+ (mg/1)
Na+ (mg/1)
Mg""" (rag/I )
Ca** (rag/1)
Oxygen Saturation-Surface (%)
Oxygen Saturation-Bottom (%)
Range
.07-1.3
90-245
6.8-8.3
-
.012-. 188
.04-. 34
-
.006-. 071
.005-. 14
.01-. 44
-
.01-. 22
-
-
-
-
36-98
20-100
Mean
0.7
188
-
**67.4
.050
.11
-
.020
.045
.158
-
.098
**1.2
**5.1
**5.8
**24.4
-
-
Trophic Status
eutrophic
-
-
-
eutrophic
eutrophic
-
eutrophic
eutrophic
mesotrophic
-
mesotrophic
-
-
-
-
meso-eutrophic
Reference
14
14
52
62
14
52
14
52
14
14
62
62
62
62
52
52
* All values are from the surface waters except where indicated. The numbered
references are the data sources used, and correspond to those listed in the
bibliography.
** Median value.
45
-------
TABLE 16. SUMMARY OF THE BIOLOGICAL CHARACTERISTICS OF
SOUTH LAKE, LAKE CHAMPLAIN.
Parameter
Range
Mean Trophic Status Reference*
Phytoplankton Biomass (ms/1)
Chlorophyll A (yg/1) 1.5-30.2
P.A.A.P. Final Biomass (rag/1) 0.2-8.0
P.A.A.P. Limiting Factor - phosphorus
Dominant Phytoplankton
(Diatoms)
Melosira granulata
(Bluegreens)
Aphanizoraenon sp.
(Flagellates)
**0chromonas acuta
Dominant Zooplankton
(Copepods)
Hacrocyclops albidus
Mesocyclops edax
Cyclops vernal is
(Cladocerans)
Si da crystal!ina
Daphma retrocurva
Dominant Benthic Invertebrates
(Diptera)
Chironomus tentans
Cryptochironomus fluvus
Chapborus punctipenm's
Coelotanypus concinnus
(Oligochaeta)
Limnodrilus hoffroeisteri
10.1
1.9
Peloscolex ferox
PotanpthrTx vejdovskyi
meso-eutrophic 14
eutrophic 8, 14
8, 14
eutrophic
eutrophic
8, 14
8, 14
80
52
52, 77
meso-eutrophic
* The numbered references are the data sources used and correspond to those
listed in the bibliography.
** Examined only in October, 1972.
46
-------
The zooplankton populations in the south lake are quite different from
other areas of the lake. Most of the organisms are characteristic of shallow
water environments. There are no quantitative data presently available on
the zooplankton communities in the south lake (Page!, 1975).
The benthic invertebrate community is generally dominated by chironomids
and oligochaetes. The oligochaetes, in particular, increase in abundance in
areas of high organic pollution. In assessing the benthic populations in the
south lake, one is faced with the problem of separating the conditions result-
ing from eutrophication and those caused by effluents from pulp and paper
operations. Although the majority of the benthic invertebrate populations are
mesotrophic-eutrophic indicators, there are a number of species present that
are indicative of earlier trophic states (Page!, 1969, Wade, 1976).
The effects of the pulp and paper effluents on the benthic fauna have been
intensively studied. Before the new International Paper Company mill in
Ticonderoga, N.Y. began operations in December, 1970, samples taken at the
effluent diffuser area contained abundant mayflies (Hexagenia limbata) and
significant populations of Amphipoda and Sphaeriidae. Since mill operations
began, the bottom fauna has been significantly altered in the diffuser line
area. Of over fifty benthic species formerly known to inhabit this area, only
eighteen were collected in 1975. Changes in the community structure from 1972
to 1975 have been the loss of most Chironomidae, Sphaeridae, and Ephemeroptera
and a drastic increase in Tubificidae. A pollution tolerant oligochaete, Lim-
nodri1 us hoffmeisteri. had increased to tremendous numbers by 1974. The num-
bers of oligochaetes in this region are from 10-60 times greater than in other
portions of the south lake. The new International Paper Company mill contrib-
utes substantial amounts of phosphorus, suspended solids, and BOD to the
south lake (Pagel, 1975).
A potential eutrophication related problem that has received little atten-
tion in the south lake is the extensive growth of the water chestnut (Trapa
natans) and the yellow floating heart (Nymphyoides peltatum). Both aquatic
plants have been introduced into the United States and in some eutrophic
situations have caused significant degradation of water quality. These two
populations have been increasing in the south lake in recent years and they
present a potential problem for the future (Gruendling & Bogucki, 1975).
The nutrient characteristics of the south lake are definitely Indicative of
eutrophic situations. Primary productivity would be considerably^higher if it
were not for the extremely high turbidity of the water. Limnological charac-
teristics of localized areas are significantly influenced by industrial pol-
lution, which tend to compound the eutrophication related problems.
Main Lake
The main lake is considered that area of Lake Charoplain from Crown Point,
N Y. to Rouses Point, N.Y., excluding the northeast arm, Malletts Bay, and
Missisquoi Bay. It can be subdivided into three regions that have slightly
different limnological characteristics: south basin - Crown Point, N.Y. to
Split Rock Point (drainage basins M and F); central basin - Split Rock Point
to Cumberland Head, N. Y. (drainage basins, D, E, L, K, and part of H); and
47
-------
north basin - Cumberland Head, N. Y. to Rouses Point, N.Y. (drainage basins
J and part of H). There are eighteen major tributaries with drainage basins
of ten square miles or more entering the region. Table 6 summarizes the
morphometric features of the main lake. In general, the south and north
basins are shallower and have significantly smaller volumes than the central
basin (Hunt & Boardman, 1968; Hunt, Boardman & Stein, 1971; Potash, Sundberg
& Henson, 1969; Henson & Potash, 1976).
As was mentioned in the general overview, the thermal regimes in the main
lake are highly variable and are dependent upon depth and the orientation of
the water mass in relation to the prevailing winds. The deeper portions of
the main lake are a typical temperate dimictic lake. Stratification begins
in early June and continues into October or November. Maximum surface tem-
peratures are generally about 23.0° C and hypoliminal temperatures during
the summer average close to 6.0° C (Potash, Sundberg & Henson, 1969; Henson
& Potash, 1976; Gruendling, 1976a).
Table 17 is a summary of the physical and chemical characteristics of the
main lake. Stratified areas of the main lake generally have epilimnial oxy-
gen saturation levels near or above saturation, while hypolironial values
rarely fall below 65% saturation. The minimum bottom water oxygen saturation
values generally range between 70 - 803». Recent evidence from the very deep
stations demonstrate minimum oxygen levels in the metalimnion during the sum-
mer rather than in the hypolimnion. There is also evidence of a gradual
trend toward higher supersaturated values in the epilimnion, thus suggesting
a trend toward accelerating rates of primary production (Potash, Sundberg &
Henson, 1969; Henson & Potash, 1976).
Cation concentrations in the main lake are generally higher than other
areas, except the south lake. Values for cations and total alkalinity are
relatively similar throughout the main lake with only slightly higher values
observed in the southern basin and slightly lower values found in the north-
ern basin. Sodium and potassium concentrations are similar to Lake Michigan,
while calcium and magnesium concentrations most closely resemble values for
Lake Superior (Potash, Sundberg & Henson, 1969: Henson & Potash, 1976).
Phosphorus and nitrogen concentrations for the deep portions of the main
lake are the lowest recorded for Lake Champ!ain, except for Malletts Bay and
the northeast arm (only nitrogen values lower). These levels are similar to
values for the early mesotrophic Great Lakes. The shallow areas of the main
lake, however, have higher phosphorus and nitrogen values. Cumberland Bay,
Burlington Bay (east of the breakwater) and inner Shelburne Bay have signifi-
cantly higher levels of these nutrients than the deep stations. Table 18
compares characteristics of the embayment areas with the main lake. Phos-
phorus and nitrogen concentrations in these bay areas are characteristic of
late mesotrophic to early eutrophic situations. The high nutrient values in
Cumberland Bay result from the major input entering from the Saranac River
and the City of Plattsburgh, N. Y. Sewage Treatment Facility. High values in
inner Burlington and Shelburne Bays are probably due to input from sewage
treatment facilities (Burlington, South Burlington, and Shelburne Fire Dis-
trict) and small tributaries (Potash Brook) (Gruendling & Malanchuk, 1974;
U.S.E.P.A., 1974; Barnett, Poulias & Biggane, 1975; Henson & Potash, 1976).
48
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Secchi disc transparencies for the deep stations are relatively high and
are within the mesotrophic range. There is a trend toward lower Secchi disc
values in the south basin with a gradial increase in transparency northward
toward the outlet at Rouses Point, N.Y. The areas of Cumberland Bay, inner
Burlington Bay, and inner Shelburne Bay have Secchi disc readings substan-
tially.lower than other areas of the central and northern basin of the main
lake. These values are in the late mesotrophic to early eutrophic range
CU.S.E.P.A., 1974; Gruendling, 1976b).
Table 19 summarizes the biological characteristics of the main lake. The
total biomass of phytoplankton populations in the main lake, as determined by
chlorophyll A, dry weight, and total cell count, are the lowest values
recorded for Lake Champlain, except for a few stations in the northeast arm.
These values generally indicate oligotrophic to mesotrophic conditions.
Melosira islandica is dominant in the spring, Fragilaria crotonensis. £.
capucina, Anabaena planktonica, and A. circinalis are abundant in the summer
and fall, and the flagellates (Cryptomonas ovata, C_. erosa, and Rhodomonas
lacustris are periodically abundant throughout the year. The qualitative
and quantitative aspects of the phytoplankton community are indicative of
roesotrophic situations. Although the qualitative components of the phyto-
plankton in the embayment areas are similar to the deep stations, the quan-
titative aspects are quite different. Cumberland Bay, inner Burlington Bay,
and inner Shelburne Bay have significantly higher chlorophyll A, dry weight,
and cell numbers of phytoplankton than the deep areas (see Table VI-13)
(Gruendling, 1976; Gruendling, 1976a).
A number of shoreline areas in Shelburne Bay have high amounts of Clado-
phora glomerata growing on the rock surfaces. This is another indication
of developing eutrophic conditions in the region (Mercer, 1972).
The P.A.A.P. algal bioassays conducted throughout the main lake, both in
deep areas and at bay stations, indicate that phosphorus is the limiting
factor to algal growth (Gruendling, 1976b; U.S.E.P.A., 1974).
The zooplankton community in the main lake is typical for deep cold-water
lakes of North America. The total copepod component (Calanoida and Cyclo-
poida) generally outnumbers the Cladocera, except during short periods in
mid-summer and early fall, when species of Daphnia, Chydorus. and Bosmina-
Eubosmina become abundant. Numerically, the cyclopoid copepods are the
major component throughout the year with Cyclops bicuspidatus thomasi being
the most abundant species. The calanoid populations of Diaptomus sicilis.
D minutus, and D. oregonensis reach maximum abundance in August and Septem-
Fer—ThT~species composition of the main lake is not identical to any one
of the Great Lakes, but it closely resembles the zooplankton community of
northern Lake Michigan. The total copepod community is larger in the deep
open portions of the main basin than in other areas of the lake. Maximum
copepod numbers are 3.6 x 106 organisms/m2, while the average during the sum-
mer and fall period is 1.1 x 106 organisms/m2. Cladoceran population numbers
are similar to deep portions of the northeast arm (maximum = 0.59 x 10 /m ;
mean = 0.26 x 106/m2) and generally higher than the bay region in the lake
(Leggi, 1969; Gruendling & Luguri, 1974).
49
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TABLE 17. SUMMARY OF THE PHYSICAL AND CHEMICAL CHARACTERISTICS OF
MAIN LAKE, LAKE CHAMPLAIN*.
Parameter
Secchi Disc (TO)
Conductivity (micromho)
pH (standard units)
Total Alkalinity (rag/1)
Total Phosphate-P (mg/1)
Parti cul ate Phosphate-P
(rag/1)
Dissolved Phosphate-P (rog/1)
N02 & N03-N (rag/1 ) (summer)
N02 & N03-N (mg/1) (winter)
NH3-N (mg/1)
K+ (rog/1)
Na* (rog/1)
Mg** (mg/1)
Ca""" (mg/1)
Oxygen Saturation-Surface (%)
Oxygen Saturation-Bottom (%)
Range
3.0-6.7
100-160
5.8-8.3
.009-. 040
.006-. 01 9
.005-. 01 7
-
-
.010-. 090
83-120
64-91
Mean
4.4
137
7.5
**41.4
.018
.011
.009
.066
.164
.043
**1.13
**3.92
**3.59
**15.81
-
Trophic Status
raesotrophic
-
-
-
mesotrophi c
meso trophic
roesotrophic
mesotrophi c
mesotrophi c
™
-
-
-
-
raesotrophic
Reference
21
14
14
62
14
24
14
24
24
14
62
62
62
62
14, 30
14, 30
* All values are from the surface waters except where indicated. The numbered
references are the data sources used, and correspond to those listed in the
bibliography.
** Median value.
50
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TABLE 18. SUMMARY OF SELECTED PARAMETERS INDICATIVE OF TROPHIC CONDITIONS IN THE EMBAYMENT AREAS
AND THE MAIN PORTIONS OF LAKE CHAMPLAIN*.
Cumberland Bay
Burlington Bay,
Shelburne Bay
Main Lake (4 stations)
Total Secchi Chlorophyll A
Phosphorus Disc (pg/1)
(mg/1 ) (m)
.025 2.9 5.45
.022 3.9 5.80
.020 3.8
.018 4.4 3.74
Maximum No. Maximum No.
Bluegreens Diatoms
(X 106 cells/1) (X 10s cells/1)
1.40 0.90
1.17 0.88
1.15 1.40
0.90 0.35
* Total phosphorus data are mean values taken from U.S.E.P.A. (1974) and Vermont Water Resources Dept.
(1976). Remaining data are monthly means calculated from data collected from May-Qct., 1970 and 1974
by Gruendling (1976a) and Gruendling (1976b).
-------
TABLE 19. SUMMARY OF THE BIOLOGICAL CHARACTERISTICS OF MAIN LAKE,
LAKE CHAMPLAIN.
Parameter
Range Mean
Trophic Status Reference*
Phytoplankton Biomass (mg/1) .23-1.6 .56
Chlorophyll A (ug/1) 2.0-5.8 3.8
P.A.A.P. Final Biomass (mg/1)
P.A.A.P. Limiting Factor - phosphorus
Dominant Phytoplankton - max. cells x 105/1
(Diatoms)
Melosira islandica
fragilaria crotonensis
(Bluegreens)
Anabaena planktonica
Anabaena circinalis
Dominant Zooplankton
3.55
3.19
6.45
5.93
(Copepods)
Cyclops bicuspidatus
Diaptomus sicilis
Diaptomus imnutus
(Cladocerans)
Eubomina Coregoni-Bosnrina longirostris
Daphnia retrocurva
Chydorus~sphaeri cus
Dominant Benthic Invertebrates
(Oligochaeta)
Stylodrilus heringianus
T)eloscolex~vanegatus
Limnodrilus hoffmeisteri
LimnodriluT claparedianus
oligo-mesotrophic
oligo-mesotrophic
mesotrophic
oligotrophic
oligotrophic
eutrophic
eutrophic
21
21
14, 19
20, 21
23, 39
77
* The numbered references are the data sources used and correspond to those
listed in the bibliography.
52
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The two most abundant groups of benthic invertebrates in the profundal
zone are the Oligochaeta (59-90% of the total fauna) and the Sphaeriidae.
There are very low numbers of Chironomidae, Amphipoda, and Hirudinea. The
deep benthic fauna of Lake Champlain are unique when compared with the Great
Lakes. The Great Lakes have substantial numbers of chironomids and the
amphipod, Pontoporela affinis; both of which are insignificant in the main
lake. There are also considerable less organisms per square meter in Lake
Champlain than in most large lakes. For example, the average number of total
benthic organisms/m2 in the main lake is 663 as compared to an average of
approximately 6000 organisms/m2 in Cayuga Lake, N. Y. (Wade, 1976a).
Among the oligochaetes, Stylodrilus heringianus is the most abundant.
This species is generally abundant in oligotrophic areas such as Lake
Superior and Lake Michigan. The oligotrophic indicator Peloscolex variegatus
is also quite abundant in some of the profundal areas. There appears to be a
general decrease of Stylodrilus heringianus and an increase in Limnodrilus
species at the northern stations of the main lake. The overall trend appears
to be an increase in species characteristic of more eutrophic situations at
the northern stations (Wade, 1976).
Only a limited number of the embayment areas of the main lake have been
investigated for benthic invertebrates. For those areas that have been
studied, the general trend is toward more chironomids and less oligochaetes
than the profundal zone. In some areas there is also a trend toward more
eutrophic species of oligochaetes. There is a succession from the mesotro-
phic species Peloscolex ferox and Stylodrilus herinaianus outside the break-
water in Burlington Bay to the eutrophic indicator Limnodrilus hoffmeisteri
in the inner bay. In Shelburne Bay, there is also a trend toward more eutro-
phic species from the outer bay to the inner bay. The inner bay is dominated
by the eutrophic indicator Limnodrilus sp. (Wade, 1976a).
The main portion of Lake Champlain is comprised of a number of water
masses which have different trophic characteristics. The deeper portions of
the southern, main, and northern basins are generally mesotrophic, although
some areas have conditions approaching oligotrophy. Those bay areas (Wills-
boro, Whallon, Corlear, Treadwell, Monty Bays) which do not receive signifi-
cant nutrient inputs have conditions similar to the deep portions of the
region. Other bay areas (Bullwagga, Northwest, Cumberland, Shelburne, Bur-
lington Bays) tend to be more eutrophic.
53
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SECTION 5
RECENT TRENDS OF ACCELERATED EUTROPHICATION
Studies depicting any signs of accelerating eutrophication in Lake Cham-
plain are limited. In some cases, there have been casual visual observations
of water quality deterioration in various embayment areas such as St. Albans
Bay, Shelburne Bay, Cumberland Bay, and Burlington Bay, but there is little
quantitative evidence available to support these observations. Some quanti-
tative data for these regions and the south lake have been discussed previ-
ously in this report.
Some recent investigations demonstrate that Lake Champlain is showing
signs of increased eutrophication. An analysis of the diatom stratigraphy
has shown recent increases in the characteristic mesotrophic-eutrophic
species of diatoms Fragilaria capucina, £. crotonensis, Asterionella formosa,
Melosira Islandica in the main lake. The general shift from oligotropFic
species to more eutrophic species apparently began shortly after 1900 and
more recent sediments contain larger numbers of these indicators (Sherman,
Detailed analyses have been made of the phytoplankton in Lake Champlain,
comparing populations present in the early 1970's with populations recorded
by Muenscher (1930). Although quantitative comparisons with the 1929 data
were difficult to make due to the manner in which th data were collected and
expressed, there are indications that significant changes in phytoplankton
populations have taken place. Bluegreen algal populations are becoming more
abundant and the characteristic eutrophic species of Anabaena flos-aqua, A.
circinalis, A_. pTanktonica, and Apham'zpmenon flos-aqua are becoming more
Important. Also, populations of the oligotrophic species of Dinobryon, which
were very abundant in 1929, are presently very sparse and not very widely
distributed (Gruendling, 1976a).
The only comprehensive physical and chemical data supporting increased
eutrophication trends in Lake Champlain come from a reference station in the
main lake, west of Burlington, Vermont. This station is located in a deep
open area of the lake (approximately 100 meters in depth) and was sampled at
regular intervals from 1965 through 1974. Four general trends in chemical
and physical characteristics of the water mass are apparent. The ten-year
trend has been for slight increases in the conductivity and cation concentra-
tions in the surface waters. However, the conductivity values appear to have
stabilized over the last few years and the cation concentrations have
decreased slightly during the past three years. These changes are difficult
to evaluate and may only be natural variations due to changes in precipita-
tion. The ten-year trend in Secchi disc readings show a decline in trans-
parency during the summer and fall. Values during 1965 ranged from 4.5-6.0
54
-------
meters, while the 1974 values ranged from 2.5-4.5 meters. There has also
been a recent trend toward increasing dissolved oxygen values in the surface
waters above the 100% saturation level and some trend toward decreasing hypo-
limnetic oxygen concentrations. Both the Secchi disc and dissolved oxygen
values suggest increased algal growth over the ten-year period. This trend
can not be substantiated, however, since no data were collected on phyto-
plankton populations (Henson & potash, 1976).
55
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SECTION 6
PHOSPHORUS LOADINGS, TRANSPORT, AND BUDGETS IN LAKE CHAMPLAIN
BACKGROUND INFORMATION
Theoretical Considerations
It is axiomatic in the science of limnology that in any lake system (lake
and drainage basin) there exist a certain amount of materials entering the
lake to establish a dynamic ecosystem. This ecosystem will consist of pri-
mary producers, herbivores, and predators. The dynamics of the system is
such that equilibrium is established according to the energy and materials
entering and leaving the system. With the statement that the system tends
to develop a balance, we have the format of a controlled system that can be
understood.
In our attempt to understand the Lake Champlain ecosystem, we must make
some assumptions, use inadequate data, and over simplify. We take as a prem-
ise that the lake is (1) phosphorus limited (documented by E.P.A., 1974;
Gruendling, 1976a), (2) that increasing amounts of phosphorus to the system
is causing a disbalance to the system, expressed in documented symptoms of
excessive algae growth, large amounts of aquatic weeds, decreased oxygen con-
centrations in certain bottom waters, and a number of additional ramifica-
tions; and (3) that if the phosphorus input is reduced, the lake would
respond by an alleviation of the symptoms, and there would be general
improvement for public benefit.
The mission here is to identify and quantify the role of phosphorus in the
Champlain ecosystem, and to develop information for the formulation of policy
of nutrient control necessary for future lake improvement.
Estimation of Background Phosphorus in the Lake
Before a full assessment can be made on the cultural influence of phos-
phorus input, it would be desirable to have some reasonable estimate of the
general background phosphorus entering the lake if there were no human
inhabitation of the basin. There are obvious limitations in attempting this,
but we should be able to provide some order of magnitude that would be useful
in interpretation. Vollenweider (1968) abandoned this approach, as natural
as it is, because man's complex intervention in nature increasingly tends to
obscure the boundary between natural and modified soil export. This reason
for abandoning the approach is less valid in parts of North America than in
Europe, where civilization has been in existence for more than a thousand
years. The Champlain Valley has been open for settlement for less than 400
years.
56
-------
In examining the phosphorus from soils, Vollenweider (1968) estimated
oligotrophic soils to yield less than 0.02 g/P/yr, and more than 0.05 g/P/yr
per square meter from polytrophic sofls. The conservative value of 0.02 g
applied to the Champlain basin would yield an annual loading of nearly
400,000 kg/yr. This estimate, based on data from "contaminated" soils is
believed to be too high for natural loadings.
A team from Cornell University (Porter, 1975) attempted to measure the
non-human background loading by measuring the concentrations of phosphorus
(biogeochemical total dissolved phosphorus) in streams draining small water-
sheds that contained no homes or farms, and from wells distant from barns,
houses etc. The mean value ranged from 12 and 24 ug/1, with the grand mean
of 107 samples being 15 ug/1, and with a standard deviation of 0.9 yg/1.
Applying this mean value to the Champlain Valley, which is equal to 66 x
TO"1* g/nr of land annually, we derive an estimate for background loading of
128,770 kg/yr or 0.1154 g/m2/yr of lake surface (Table 20). Since the
Increasing amounts of phosphorus in precipitation were not considered in the
Cornell data, this estimate determined for the lake should be considered
maximal.
ESTIMATES OF TOTAL PHOSPHORUS LOADING BUDGETS
There are several methods by which the phosphorus loadings and budgets can
be estimated, and these will be reviewed, applied, and compared in this sec-
tion. Only two studies conducted thus far have attempted to measure the
phosphorus loading into the lake. The Working Paper #154 (E.P.A., 1974),
based on a 13-month sampling program, was the first. The materials input
study of Henson and Potash (1976) reported on five years of sampling from 37
tributaries, but made no attempt to relate the results with the trophic levels
of the lake. These two reports will be reviewed here before further analyses.
The EPA Report of 1974
An evaluation of the total Charaplain phosphorus loading was made by (1)
measuring monthly for 13 rnonths the phosphorus concentrations near the mouths
of 21 key tributaries to the lake, applying these data to the normalized flow
of the streams, and calculating the loading; (2) analysing the populations
being served in each stream by waste treatment facilities, and calculating the
point-source loadings in each stream. By using a cut-off point of 25 miles
from the lake where point sources were of reduced significance, they were
able to estimate the relative amounts of point-source and non point-source
phosphorus being introduced into the lake; (3) the point sources discharging
directly into the lake were analysed and compiled; and (4) the unsampled smal-
ler streams and diffuse drainage into the lake were estimated by using data
from some of the sampled streams that were without point sources, and applying
this rate to the unsampled areas. Contributions to the lake from the atmosphere
were adapted from the literature.
The results of this study are summarized in Table 21 and show an annual
loading of 598.14 metric tonnes of phosphorus, 90% derived from the tribu-
taries, and about 50% of this leaving through the outlet.
57
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TABLE 20. COMPARISON OF ESTIMATED PHOSPHORUS INPUT VALUES AS DERIVED BY
SEVERAL METHODS FROM THE DISTRICTS.
Kg/yr of total phosphorus
District
A
B
C
D
E
F
H
J
K
L
M
S
EL
FM
Total
I
Background
19,420
1,090
14,720
21 ,800
140
19,750
500
6,130
20,200
4,430
1,500
19,090
_
-
128,770
II
Population
90,680
21,250
52,560
210,680
1,170
91 ,960
5,720
31,780
123,350
6,650
10,630
54,780
-
^
701,210
III
Measured
86,920
22,560
41,130
137,480
810
133,740
4,330
52,690
127,930
20,090
18,470
63,620
-
-
709,770
IV
Vollenweider
92,950
26,860
21,800
98,350
-
-
49,530
248,440
119,380
-
-
85,570
151,760
9,160
903,800
I Assuming background leaching amounts to 15 yg/1.
II Assuming a 1.6 kg/P per capita per year.
Ill From Henson and Potash, 1976.
IV Vollenweider, 1976.
58
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TABLE 21. E.P.A.* ESTIMATES OF TOTAL PHOSPHORUS LOADING INTO
LAKE CHAMPLAIN.
kg/yr** gms/m2/yr*** %
I. INPUTS
1. Sampled tributaries 484,810 0.429 81.0
2. Minor tributaries and
diffuse drainage 57,460 0.058 9.6
3. Municipal (8) STP directly
into the lake 34,440 0.030 5.8
4. Industries directly into
the lake 10,930 0.010 1.8
5. Precipitation into the lake 10,500 0.009 1.8
total input . . .598,140 0.529 100.0
II. PHOSPHORUS LOST
1. Through outlet
III. RETENTION
296,070 0.262 49.5
302,070 0.267 50.5
* E.P.A., 1974, Working Paper No. 154; (Table 13, pg. 44)
** Original was expressed in pounds/yr.
*** Over entire area of Lake Champlain.
59
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The Henson-Potash Report (1976)
The strategy behind this Investigation was to sample for total and reac-
tive phosphates (and other parameters) for a five-year period (1970-1975)
at stations located near the mouths of nearly 40 tributaries of the lake.
The central tendency value used was the median, and this was applied for
determining the loading for each stream. Stream discharge estimates were
made by examining the mean annual discharge data for the stations in the
Champlain Valley from the Water Supply Papers of the U. S. Geological Survey,
and with cfs/sq. mile as the unit. From the plotted isopleths, a discharge
index per unit area was derived for each of the Districts in the drainage
basin. The weighted mean concentration for the District was used to estimate
the diffuse input for each District. These diffuse inputs, which include the
smaller unsampled streams in a District, were usually small when compared
with each tributary considered as a point source.
It might be noted that the values for total phosphorus utilized in the
present document are not identical to those presented in the original paper
(Henson & Potash, 1976). Standard reagents were prepared throughout the
1970-1974 sampling season, and blanks were run for each series of analyses.
New standards were recently made up to take care of the wide range of dilu-
tions that were required, and this has slightly modified the scope of the
standard curve. Applying this curve has downgraded some of the published
values, expecially the very high values. The results of phosphorus loading
into the lake according to this survey are offered in Table 20 with the raw
data placed in Appendix D. With this account, 30.9% of the phosphorus is
derived from New York, 10.4% from the South Lake, 38% from Vermont south of
Malletts Bay, and 20.7% from the northeast sector. District F (Otter Creek)
contributes 19% of the total input of 709,770 kg/yr, from the drainage basin.
Comparispnj)f^jhejrwo Reports
The EPA total loading estimate of 598,140 kg/yr (Table 21) is somewhat
low compared with the HP estimate of 709,770 kg/yr (Table 20). Some of this
difference can be attributed to the fact that the HP study included a number
of smaller tributaries with high phosphorus concentrations not sampled in the
EPA study. The HP study extended for five years allowing for a better chance
of collecting more of the higher values. EPA assessed the smaller non-point
watersheds at a rate of 106 pounds P/sq. mi., while our data with the same
streams were 72% higher. When the two sets of data from the same streams
sampled during the overlapping year are compared, the magnitude of concentra-
tions overlap (i.e., our lower values are within the range of the higher
values of EPA) so the HP values tend to be higher, but there is no consis-
tency in how much higher. For the present mission these differences are of
little significance. The relative amounts are more important in the develop-
ment of a nutrient control program. We will adopt here the data from the HP
report, not because it is more accurate, but because there are more relative
data available in it.
Loading Estimate by Basin Population
One frequently used method for estimating the amount of phosphorus enter-
60
-------
ing a lake is to count the number of people living in the watershed and mul-
tiply by a factor determined by the mass of phosphorus generated by an aver-
age individual per unit time. The EPA (1974) used a factor of 3.5 pounds
(1.587 kg) per capita per year. For treated waste this value was reduced to
2.5 pounds (1.1340 kg). These values were obtained from Bartsch (1972).
Vollenweider (1968) estimated the per capita genesis of phosphorus to be
between 1.5 and 1.7 kg/yr. Patalas (1972), Patalas and Salki (1973), and
Stewart ejt al_. (1974) each used 1.7 kg/C/yr because of the heavy agricultural
influence.
The populations in the individual Districts (Table 4) were multiplied by
a middle factor of 1.6 kg to derive a set of estimated phosphorus loading
from each District (Table 20). The contribution by this method is 701.2
tonnes/yr.
Estimates by the Patalas Formula
Patalas (1972) and Patalas and Salki (1973) used an equation developed
from Vollenweider's discussion (1968) on estimating phosphorus loading.
This equation:
Esx
Ad Ec- C
Ao Ao
presents the loading in terms of grams of phosphorus per square meter of lake
surface, and applies the factor Es (the soil export), and the population
contribution (ECC/A0). Ad is the area of the drainage basin, and Ag is the
area of the lake. According to this model, the total loading is the summation
of the edaphic plus the human factors.
Theoretically, the above model withstands logical analysis, but in prac-
tice, it tends to inflate the loading. Applying this model to the Champlain
basin, we obtained loading values 2-3 times larger than any other estimate.
The second factor in the equation, the human component, is the mass of phos-
phorus per person entering the lake, divided by the lake area. At the pres-
ent time, the measure of the amount per capita entering a lake is a matter of
subjective judgement. The above authors used a value of 1.7 kg/C/yr because
of the high human influence, and used low to middle values for the soil
export component. When we compared the loadings from this equation using the
second factor alone, it was almost identical to the estimates based on popu-
lation, as discussed above. In other words, the second factor in this equa-
tion presents a reasonable estimate of loading based on population. The
first factor, the edaphic factor is already included in the second factor.
When we consider that the water the population uses has the edaphic phos-
phorus in it, that P is looped in a recycling process and should be removed
from the equation.
Estimates by the 1976 Vollenweider Model
In the latest publication, Vollenweider (1976) presents his equation 11,
61
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which is:
^ x z (
where the critical loading [Li is equal to the specific concentration of
phosphorus in the lake during spring overturn, multiplied by the mean depth
(z), and by a relation of the retention time (t^). This is a non-linear
model, and intends to show that the critical loading is a function of mean
depth and retention time.
In this eutrophication model, IP] is given a value of 10 yg/1 at the
time of Spring overturn to separate oTigotrophic from more enriched waters
(mesotrophic). If we were to substitute into the equation the observed
values of total phosphorus in the lake, we could then calculate for L rather
than the specific, or critical loading.
The solution to this equation, solving for loading, and converting the
values from g/m2/yr to read in terms of kg/yr, are tabulated in Table 20
yielding 904 tonnes/yr, a higher estimate than the others. A better set of
data from the Regions of the lake during early Spring would probably refine
this estimate. The Vollenweider equation requires precise values of phos-
phorus concentration levels.
EVALUATIONS OF THE DIFFERENT LOADING ESTIMATES
The results of these three methods for estimating the loading into Lake
Champlain are compared in Table 20. For the lake as a whole, the estimates
ranged between 701.2 to 903.8 tonnes/year, and averaged 771.60 tonnes. The
range was within 17% of the mean. On the basis of this analysis, the HP
Report is representative, and falls between the other values.
The three assessments presented in Table 20 were made according to three
different approaches. The first evaluation is based completely on the popu-
lation in the basin, and assumes that all of the phosphorus generated by that
population will enter the lake. The second evaluation was based on a five-
year measurement of the loading from a fairly large number of tributaries,
and the third is based on an empirically derived mathematical model associa-
ting the most probable load with the actual concentration of phosphorus found
In the lake. The first estimate used a fairly conservative value of 1.6 kg/
capita. Using the value of 1.7 kg/c would raise the loading value to 745.03
tonnes. The Vollenweider equation demands precise values of the phosphorus
concentrations at the time of spring overturn, and we do not have this infor-
mation. According to the HP assessment, the actual per capita ratio is 1.620
kg/C/yr. Since the measured values presented in the HP Report are of inter-
mediate value, and there is good regional representation, these values will
be used in the further discussion.
62
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OTHER SOURCES OF PHOSPHORUS
Atmospheric Input
The amount of phosphorus entering the lake surface from the atmosphere,
either as dissolved in the precipitation, or as bulk fallout, is variable in
space and time, and based on minimal data in the literature. In a discussion
of this subject, Vollenweider (1968) summarizes that in Europe, atmospheric P
amounts to between 0.02 and 0.05 g/m2/yr. Wetzel (1976) says that the total
amount from this source may amount to as much as 0.1 g/m2/yr. Loehr (1974)
reviewed the world literature on this subject and found that the yield ranged
from 0.005 to 0.1 g/m2/yr.
A recent study of atmospheric inputs in the upper Great Lakes gave a
range of 0.01 to 0.04 g/m2. The average value for southern Lake Huron was
around 0.025 g/m2. Stewart ejt al_. 1974, using melted snow in central New
York State as a basis for estimating annual loading found concentrations to
range between 0.008 and 0.034 mg/1, the higher values being found near Buf-
falo, N. Y., and the average was 0.019 mg/1. Peuchert (1976) determined an
average of 0.08 in East Germany. Aulenbach (1972) derived a figure of 23.85
kilograms per year for Lake George, equal to 0.009 q/m2. For the purpose of
this document, we have used an average of 0.018 g/m /yr.
Bird Populations
There is a certain amount of phosphorus exchange by way of the gull popu-
lations over the lake, but no data are really available that are applicable.
Sanderson (1960) claims that domestic ducks contribute 0.4 kg/P/yr, while
Paloumpis and Starrett (1960) estimate that wild ducks contribute about 0.53
g/m2 to a lake in Illinois, but this could be a high value for a large lake.
Peuchert (1976) suggested that the bird's net input to the ecosystem on the
order of 3 - 24 kg/ha/yr (.03 - 2.4 g/m2). It is possible that the P
exchange is balanced; that what is removed from the lake as food about equals
what is dropped in the lake later. Islands are known to accumulate guano, so
the bird's role may be one of redistribution of the phosphorus, rather than
input.
Municipal Waste Treatment Plants
There are seven municipal waste treatment plants that contribute an esti-
mated 38,850 kg/P/yr directly into the lake, (EPAJ974) and another near
Plattsburg is presently under construction. There is but a single industrial
plant discharging directly into the lake (See Appendix E).
Discharges from Boats and Marinas
The potential problem from this source is not as great today as it was a
few years ago before withholding tanks were required for boats on the lake.
There are still some boats that move into the lake with overboard disposal
systems. There may be local problems at marinas where boat owners wash down
the vessels with detergents.
63
-------
ORTHOPHOSPHATE LOADING DATA
A body of data does exist for loadings of reactive, or soluble phosphorus
(Henson and Potash, 1976). All of the 37 tributaries sampled were transport-
ing reactive phosphates to the lake, though a number of streams had concen-
trations from time to time below detectable limits. The median values ranged
between 0.007 and 0.493 mg/1, with eight tributaties having median values
exceeding 0.05 mg/1.
Examining the sets of data where total and reactive P were measured for
the same sample, we find that the relative amounts of reactive P was small,
ranging from 1.7% for Salmon River to 20.5% for Mill River. Since the first
Vollenweider model (1968) utilized the reactive phosphate, these data have
been analysed for the Districts to derive loading values for the reactive
phosphorus (Table 22). These data were obtained by finding the average per-
cent of the total that was reactive for each District (column 3) and multi-
plying this by the annual load of total phosphorus. This analysis suggests
that about 10% of the phosphorus entering the lake is in the reactive form.
RESULTING ASSESSMENT OF THE PHOSPHORUS BUDGETS
We will now assemble the information available to derive a realistic pic-
ture of the distribution of phosphorus to and within the lake. Table 23 is
an accounting of the phosphorus budgets. Almost 90% of the phosphorus enter-
ing the lake enters from the larger tributaries. About 20% of the 747.5
tonnes entering the lake leaves through the outlet at Rouses Point. There
are some other losses of P, and 'these are mentioned in the table, but at
present we do not have enough data for evaluation. The amount of phosphorus
being retained in the lake concurs with values given in the literature
(Patalas, 1972; Stewart & Markello, 1974).
Table 24 will become a working table, for it provides the data of
Regional loadings that will be used with some of the models later. The point
sources in column 4 are the municipal and industrial waste treatment plants.
Districts D and F each contribute more than 18% of the total loading to the
lake.
APPLICATION OF MODELS TO THE PHOSPHORUS DATA
The 1968 Vollenweider Model
In this model, the impact of phosphorus loads into a lake is a function
of mean depth alone, and requires data for the loading of "total phosphorus
(biochemically active)", and this is interpreted to mean the reactive phos-
phorus. According to this most of the regions are in the oligotrophic range,
mainly because of the major influence of large mean depths. Region A is just
at the dangerous level, but Missisquoi Bay does not exhibit the symptoms of
trophy nearly as much as does Malletts Bay (Region C), which ts below the per-
missible level. Region F receiving the heavy load from Otter Creek is near the
dangerous level, and Region D (Burlington) is just below the permissible. In
subsequent evaluations of the loading problems, Vollenweider has indicated that
64
-------
TABLE 22. ESTIMATED LOADINGS Of REACTIVE CDISSOLVED) PHOSPHORUS TO
LAKE CHAMPLAIN FROM THE DISTRICTS.
District
A
6
C
D
E
F
H
J
K
L
M
S
Total
kg/yr
Total P input
from drainage
86,920
22,560
41,130
110,460
810
133,740
4,280
50,240
127,930
20,090
15,640
63,620
677,420
Avg. prop.
as reactive
.0672
.1438
.1316
.1544
.1015
.1036
.1306
.0958
.0797
.0454
.0652
.1015
.1015
Loading of
reactive
P-kq/yr
5,410
3,240
5,410
17,000
80
13,860
560
4,810
10,200
910
1,020
6,460
9,450
gms/m2 z
.0754 2.8
0.024 12.9
0.759 12.9
0.1455 25.8
0.001 55.6
0.2846 24.5
0.0021 16.6
0.042 8.2
0.130 64.5
0.014 55.6
0.021 24.5
0.011 2.7
0.060 22.8
Trophic*
status
M/E
0
0+
0/M
0
M+
0
0
0
0
0
0
0
* Vollenweider's 1968 model. 0 = oligotrophic; m = mesotrophic; e = eutrophic.
65
-------
TABLE 23. SUWARIZED PHOSPHORUS BUDGETS OF LAKE CHAMPLAIN.
Ka/yr *
I. INPUTS
1. From measured tributaries 649,120 86.8*
2. From unmeasured drainage basin 28,310 3.8*
3. From WTP directly to lake 38,850 5.2
4. Atmospheric input 20,340 2.7
5. Industrial input 10.930 1.5
747,570 100.0
II. PHOSPHORUS LOST:
1. Through outlet 147,860
2. Through fishing ?
3. Sedimentation ?
4. Biologic incorporation ?
147,860 19.8%
III. PHOSPHORUS RETAINED 599,690 80.2%
* Includes 128,763 kg/yr as "background" loading (Table 20), which makes up
17.2% of total input.
66
-------
TABLE 24. VALUES FOR TOTAL PHOSPHORUS LOADINGS INTO THE HYDROGRAPHIC REGIONS OF LAKE CHAMPLAIN,
FROM SURFACE RUN-OFF FROM THE DRAINAGE BASIN, FROM THE ATMOSPHERE, AND FROM POINT SOURCES THAT INCLUDE
INDUSTRIAL OR MUNICIPAL DISCHARGE DIRECTLY INTO THE LAKE (FROM EPA REPORT NO. 154J.
Land drainage
Region kg/yr
A
B
C
D
E
F
H
J
K
L
M
S
Totals:
86,920
22,560
41,130
110,460
810
133,740
4,280
50,240
127,930
20,090
15,640
63,620
677,420
Precipitation
kg/yr
1,390
2,420
980
2,110
1,150
880
4,890
2,070
1,410
1,150
880
1,020
20,350
Point sources Total
kg/yr kg/yr
88,310
24,980
42,110
27,020 139,590
1,960
134,620
540 9,710
2,450 54,760
129,430
21,240
8,830 25,350
10,930 75,570
49,770 747,540
%
11.8
3.3
5.6
18.8
0.3
18.0
1.3
7.3
17.3
2.8
3.4
10.1
gms/m2*
1.14
0.19
0.78
1.19
0.03
2.76
0.04
0.48
1.65
0.33
0.52
1.33
0.66
Theoretic*
ma/1
0.401
0.040
0.060
0.046
0.001
0.113
0.002
0.058
0.026
0.006
0.021
0.486
0.029
Actual*
mg/1
0.050
0.034
0.012
0.024
0.021
0.018
0.021
0.017
0.013
0.021
0.018
0.050
* Column 6 converts the total loading to grams phosphorus per square meter of lake surface in the Region,
and the "theoretical concentration" is the concentration of the water in the Region if the total load
were added to the volume of water in the region. Actual concentrations is based on sampling, data from
several sources.
-------
in lakes where the flushing rate is influential on the trophic impact, this
first model is not very realistic. This notion applies to Lake Champlain.
The Mass Transport Model
The mass transport scheme was adopted earlier to evaluate the water budgets
of the lake, and to trace the major water movements through the lake. The
same scheme is applied now to the phosphorus budgets of the lake. In a com-
parable fashion, the phosphorus enters the headwater Regions A, C, and S. The
actual phosphorus concentration in that Region (Table 24) and the flow leaving
the Region (D of Table 2) were used to obtain a value for the phosphorus in
the Region. The solution of this model is outlined in Table 25 and using this
scheme, the phosphorus retention time is calculated for each Region, a value
needed for later analyses. The model is displayed in Figure 6.
The 1976 Vollenweider Model
As was discussed earlier, this equation was developed after a consider-
able study of both the theoretical aspects of the subject, and by testing it
on a vast array of empirical data from a large number of lakes throughout the
world. The equation is here presented again:
Lc - [P£P x I 1 +Ytw"
where L is the critical loading of a lake in g/m2/yr. The critical loading
is thatclevel where the lake can be oligotrophic, or defined as moderately
ic. The value EP] is the critical concen-
eutrophic, or dangerously eutrophic
tration of total phosphorus at the time of spring overturn, and is expressed
in units of iig/1 or mg/m3. A value of 10 for the critical concentration is
used to separate oligotrophy from mesotrophy. A value of 20 would be
eutrophic, but when the critical concentration attains a value of 30,
experience has shown these lakes to be "highly" eutrophic. The factor z is
the mean depth (meters), and t is the retention time in years.
w
If lake standards of trophy are adopted, then the values gf 10, 20, 30
etc. can be assigned to the critical concentration factor [P]c , and then the
equation can be modified to read:
Ls - (10)
where a is the hydraulic load = z/t.
s w
The critical loading has been determined using these relationships and
these are presented in Table 26. The actual loading for each Region is given
in the second column, and therefore the actual load, and the critical loading
for any lake standard can be compared.
With this analysis, Regions A, B, F, and M, and S are experiencing
68
-------
Figure 6. Schematic model of the net annual mass transport of phosphate-
phosphorus in Lake Champlain. The width of the arrows depict the
relative amounts of PC^-P being transported annually.
69
-------
TABLE 25. SOLUTION OF THE MODEL INDICATING INPUT AND MASS TRANSPORT OF TOTAL PHOSPHORUS INTO AND
THROUGH THE REGIONS OF LAKE CHAMPLAIN*.
Region
A
C
B
S
FM
EL
D
K
H
J
Lake
Champ! ain
District
input
88.310
42.110
24.980
75.570
159.970
23.200
139.590
129.340
9.710
54.760
747.540
Total phosphorus in
Gained
by mass
transport
-
-
44. 594
-
64. 204
48.943
31.804
67.348
120.079
139.200
_
the cycle:
Total
input
tonnes
88.310
42.110
69.574
75.570
224.174
75.143
171.394
196.688
129.789
193.960
-.
Input:
(10.4%)
Outflow
83.272
42.110
34.026
64.204
48.943
63.609
71.088
56.472
82.728
147.858
147.858
747.55 t (52.
= 1,424.71 t
Amount
retained
5.038
30.280
35.548
11.366
175.231
8.534
100.309
140.216
47.061
46.102
599.683
5%); In 1
(100.0%).
retained
5.7
71.9
51.1
15.0
78.2
11.8
58.5
71.3
36.3
23.8
80.2
ake: 529.30 t
Mass of
P in region
13.668
8.392
58.852
7.779
42.983
148.928
72.460
65.722
94.552
15.963
529.298
(37.2%); Outlet: 147.86 t
* Values are in metric tonnes, total phosphorus per year. Input data in Column 1, total loading in the
Districts is from Table 22.
-------
TABLE 26. SUMMARY OF SPECIFIC CRITICAL LOADINGS* OF TOTAL PHOSPHORUS (L )
FOR REGIONS OF LAKE CHAMPLAIN FOR SELECTED GIVEN VALUES OF THE CRITICAL CON-
CENTRATION OF TOTAL PHOSPHORUS [P]!p AT TIMES OF SPRING CIRCULATION (ug/1).
Region
A
B
C
D
E
F
H
J
K
L
M
S
EL
FM
Lake
Actual Area!
loading
g/m2/yr
1.140
0.518
0.777
1.462
0.414
3.424
0.477
1.688
2.509
0.716
1.180
1.328
0.615
2.302
0.661
Actual [P]
ug/l
47.5
30.0
23.2
28.5
7.4
47.7
15.8
16.7
21.7
11.2
33.8
44.2
31.5
Area! loading in g/m2/yr needed to
achieve indicated tP]CHvalues
P10 P20 P30 P40
0.240
0.172
0.335
0.508
0.914
0.530
0.300
1.009
1.153
0.640
0.282
0.301
0.601
0.541
0.209
0.360
0.258
0.502
0.763
1.371
0.795
0.451
1.513
1.729
0.960
0.423
0.451
0.901
0.811
0.314
0.480
0.345
0.670
1.017
1.828
1.060
0.601
2.018
2.305
1.280
0.564
0.602
1.202
1.081
0.418
0.719
0.518
1.005
1.526
2.742
1.590
0.901
3.026
3.458
1.920
0.846
0.902
1.803
1.622
0.628
* After equation 11 of Vollenweider (1976).
71
-------
extremely high levels of loading, and this applies to the lake as a whole.
Only Regions H, J, and L would be considered to be in the roesotrophic zone.
In Table 27 are outlined the necessary reductions of phosphorus from each
Region in order to obtain a selected degree of trophic state. For example,
Region A has a loading in excess of P = 30. The loading of 88.31 tonnes of
phosphorus would have to be reduced 36.9%, or by 32.6 tonnes before the
Missisquoi Bay would be just at the CP)30 level.
72
-------
TABLE 27. NECESSARY REDUCTIONS OF PHOSPHORUS LOADING TO LAKE CHAMPLAIN AND
ITS REGIONS WITH GOALS OF OBTAINING OLIGOTROPHY (P) 10, BELOW EUTROPHY (P)
20, OR BELOW DANGEROUS EUTROPHY CP) 30.
Region
A
B
C
D
E
F
H
J
K
L
M
S
EL
FM
LAKE
Present
loading
Tonnes/year
88.32
69.57
42.11
171.40
26.43
166.72
129.80
194.00
196.69
45.71
57.45
75.57
72.14
224.17
747.55
[P]!P = 10
Percent
78.9
66.8
56.9
65.3
-
84.5
37.2
40.2
54.0
10.7
76.1
77.3
**
76.5
68.4
15
Reduction
68.4
50.2
35.4
47.8
-
76.8
5.5
10.4
31.1
-
64.1
66.0
-
64.8
52.5
20
of Present
57.9
33.4
13.8
30.4
-
69.0
-
-
8.1
-
52.2
54.7
-
53.1
36.8
30
Loading
36.9
0.1
*
-
-
53.7
-
-
-
-
28.3
32.1
-
29.5
5.0
* Dashes indicate present loading is below the standard.
** On borderline and within rounding error.
73
-------
SECTION 7
SOURCES OF PHOSPHORUS IN THE DISTRICTS
GENERAL COWENTS
District Individuality
There Is much diversity in the source and means of introduction of phos-
phorus into the waterways that lead to the lake. There are differences in
the sources of phosphorus loading from one subwatershed to another within a
District, and there are also major differences in the manner that loading
occurs between the Districts.
The following comparison of the Missisquoi District (A) with District D
(Burlington-Winooski) is given as an example: District A is international and
predominantly rural and agricultural. The phosphorus loading is scattered
over a large area containing only two communities with populations of more
than 2,000. There are more than 30 communities with populations of less than
1,000, and the total input from these sources amounts to about 18% of the
total phosphorus entering the lake from District A.
District D is predominantly urban and suburban, and the prime agricult-
ural land is sandwiched between the expanding urbanization of the lake-shore
and the recreationally utilized high elevation terrain. As a result, about
80% of the loading is generated from point sources.
The same contrasts are to be found on the New York side of the lake where
the phosphorus contributions from point sources are much higher from the
urbanized District K (Plattsburg) than from the agricultural District J
(Chazy).
It must be recognized that the problems of phosphorus loadings are not
the same for all parts of the Champlain drainage basin, and that the ratio of
point source to non-point source loading varies considerably. Any nutrient
control policy should be addressed to generalized phosphorus reduction: as
in the elimination of phosphorus in detergents, as well as nutrient elimina-
tion in selected waste treatment plants.
Loading Categories
In the following discussion a very brief description of the District is
first presented followed by an iteroization of the assessment of the loadings
of total phosphate-phosphorus into the Region of the lake from all sources,
Including that entering the Region via mass transport from adjacent Regions.
74
-------
This is the best evaluation of what is entering the lake that is available.
Following, there is a discussion of the inventory of point-source loading
in the District as presented in full in Appendix E. Not all of the phos-
phorus that is introduced to the waterways in a District are actually trans-
ported into the lake. The relative amount of this transport loss is not
known at the present time.
The analyses of the point source loading, presented in Appendix E and
summarized in Table 28 are based on the following community categories: (a)
communities with individualized means of waste disposal (e^g_. septic tanks,
leach fields etc.), (b) communities that are on a sewerage system, but with-
out any treatment, (c) the communities that are served by primary treatment,
and (d) that population served by secondary treatment. As outlined in the
introduction to Appendix E, the base loading used is 1.6 kg of phosphate
phosphorus per capita per year, and this base value is reduced by a certain
amount according to treatment type and river distance from the lake.
DISTRICT EVALUATIONS
District A (Missisquoi)
The Missisquoi District (Fig. 7) has an area of 2,963 km2 and has a popu-
lation of 56,678. It is drained by the Missisquoi, Pike, and Rock Rivers in
addition to a number of smaller streams. About two-thirds of the population
are rural, or live in communities of less than 300 population. There are six
urban areas with a population of more than 1,000. Swanton, Vermont, and Bed-
ford, Quebec are the largest population centers, each with a population of
slightly more than 2,600.
The distribution of phosphorus to the lake from the Missisquoi District
is:
Missisquoi River 64,710 kg 73.3%
Pike River 14,280 16.2%
Rock River 6,390 7.2%
Charcoal Creek 310 0.3%
Diffuse (unmeasured) 1,230 1.4%
Precipitation 1»39Q 1.6%
Totals 88,310 100.0%
The total loading of phosphorus into the Missisquoi Bay is at the (P)47.5
level much above acceptable levels (Table 26). The present loading would
have to be reduced by 36.9%, or by 32.6 metric tonnes to bring the loading
down to the (P)30 level, and by 68% to reduce the loading to the (P)15 level
(Table 27).
An inventory of the point source loadings to the waterways in District A
is presented in Table 1 of Appendix E, and summarized in Table 28. The total
point source loading amounts to 15,880 kg/yr; 39% of this total is derived
from five secondary treatment facilities, and 34% from communities without
75
-------
I Nofre-Dame- de
Stanbridge
Newporf Center
5 MILES .
• -.
Figure 7. Drainage map of District A (Missisquot) locating major streams and villages
-------
TABLE 28. SUMMARY OF THE POINT SOURCE LOADING OF TOTAL PHOSPHORUS AS PRESENTED IN THE TABLES OF
APPENDIX E.
District
A
B
C
D
F
H
J
K
L
M
S
Total s :
%
No. of
points
38
1
24
32
30
1
12
35
9
5
33
221
Annual loading, tn Kg., by
class of disposal.
abed
2,230
-
1,360
490
880
-
640
360
360
-
3,430
9,750
3.1
5,350
-
6,610
1,560
1,730
-
2,900
12,640
970
1,340
14,260
47,360
15.
2,071
-
270
29,090
24,140
1,720
-
20,740
-
7,150
5,320
90,500
2 29.
6,230
11,520
3,280
81,110
4,520
-
5,040
41,230
-
860
11,020
164,810
0 52.7
% of total load from the
Totals district*
15,880
11,520
11,520
112,250
31,270
1,720
8,580
74,970
1,330
9,350
34,030
312,420
100
18.3
51.1
28.0
81.6
23.4
35.7
16.3
58.6
6.6
38.2
45.6
* Column 1 plus column 3 of Table 24.
-------
any waste treatment. The total point source loading is about 18% of the
total loading into the lake, and this is consistent with the rural nature of
the drainage basin.
District A is non-point source controlled since only 18% of the loading
is derived from point sources. Point source control would, however, be
effective in easing the extremely high loading presently being experienced.
A detergent phosphate ban in the State of Vermont would eliminate approxi-
mately 5,500 kg/P/yr, and reduce the area! loading from the present 1.140
g/m2 to 1.069 g/m2 (Tables 26,29). Subsequent tertiary treatment from the
two secondary plants on the Vermont side of the border would remove 90%, or
4,500 kg/yr. With the dual nutrient control measure, the total phosphorus
reduction would amount to 10,000 kg, or 11.5% of the land drainage input.
This would reduce the areal loading to 1.009 g/m2 (Table 26) and reduce the
trophic standard from (P)47.5 to (P)42.0. Additional reductions would have
to be obtained from non-point source control.
District B (St. Albans-Northeast Region)
This small District is a special case because most of the loading enters
the small and protected St. Albans Bay (Fig. 8). The morphometric values
given in Table 1 relate to the entire area between Malletts Bay and the
Missisquoi delta, and halfway between the islands and the main Vermont shore-
line. The eutrophic conditions are much more severe in St. Albans Bay than
indicated in the following discussion. Any alleviation of phosphorus loading
would have its initial influence on the bay, and later in the open waters
east of the islands, with the reservation that the phosphorus accumulation in
the bottom sediments in the bay (Corliss and Hunt, 1973) would delay recov-
ery.
The loadings into the Region are as follows:
*Stevens Brook 16,760 kg 24.1%
*Mill River 970 1.4%
Stone Bridge Brk. 1,120 1.6%
Trout Brook 350 0.5%
Diffuse 3,360 4.8%
Precipitation 2,420 3.5%
Transport from A 41,640 59.8%
Transport from C 2,960 4.3%
Totals 69,580 kg 100.0%
The asterisk indicates the loading directly into St. Albans Bay. Because
of the morphometry, we can divide the Region into (1) St. Albans Bay receiv-
ing 17,740 kg/yr (25.8%) and the outer region extending from Sand Bar to
Maquam Bay, with a much greater volume of water, receiving 75% of the load;
mainly by mass transport from adjacent regions.
Recommended phosphorus reductions to the [P]20 level amount to 33.4%, or
23,240 kg. For the north end of the outer region in the vicinity of Maquam
Bay, a reduction of about 12% of the load would proportionaly reduce the load
78
-------
^;v;/;;:-::^ " •
Ftgure 8. Drainage map of District B (St. Albans).
-------
coming in from Region A, a reduction of approximately 5,000 kg. Control in
the Missisquoi District would alleviate some of the problems in the northern
regions of the islands and Maquam Bay. In the same manner some nutrient
reduction in Malletts Bay would alleviate problems in the southern sector of
Region B around Sand Bar.
The total population in District B is 13,280, and the largest point
source is the St. Albans treatment plant contributing about 64,150 kg/yr, or
92% of the total. Much of this is lost in the wetland between the plant and
the sampling station on Stevens Brook, where the input has been calculated to
be 16,760 kg, or about a fourth of what is released from the treatment plant.
Because of the unusual situation existing in the Stevens Brook area, calcula-
tions of possible phosphorus reductions are based on the output from Stevens
Brook at the sampling station. A detergent phosphate ban would reduce this
loading by 6,700 kg or 9.6% of the total loading to the lake, and in effect
reduce the areal loading to 0.484 g/m2 (Tables 26, 29). A 90% reduction of
the remaining 10,060 kg by tertiary treatment would be 9,050 kg. Thus, by
the dual control measures, 15,760 kg of phosphorus would be removed annually,
or 22.6%, reducing the areal loading to 0.401 g/m2, bringing the critical
loading level below the [P]30 level (Table 26).
District C (Lamoilie-Mallets Bay)
The Lamoille River drains 95% of District C (Figure 9). This river origi-
nates east of the Green Mountains and flows 84.9 miles to Malletts Bay. At
Malletts Bay the channel divides into two arms, leaving a wetland island in
the middle. The Lamoilie delta houses a Federal and State wildlife refuge.
The total population in the District is estimated to be 32,853 (Table 4),
with approximately 22,923 living in the Lamoille drainage. The remaining
9,930 persons live in the small region of Colchester and Milton along the
lake north of Milton.
The total phosphorus loading into Region C is distributed as follows:
Lamoille River 37,810 kg 89.8%
Malletts Creek 1,540 3.6
Indian Brook 570 1.4
Allen Brook 510 1.2
Pond Brook 300 0.7
Diffuse 390 0.9
Precipitation 990 2.4
Totals: 42,110 100.0%
This amount of loading into Malletts Bay is presently below the [P]30
level (Table 26) but to reduce the loading to attain the l"P]20 standard
would require the reduction of 13.8%, or 5,810 kg. A total of 23,960 kg
would have to be removed to attain the oligotrophic standard of IP]10.
The point source loading into District C (Table 2 of Appendix E, and Table
28) amounts to 11,520 kg/yr, or 28% of the total loading entering Malletts
80
-------
00
fcvr-N. Hyde Park -g
Q£y-«Johnson
X>^v
f'A)?> UnderhlllFlats
ensopfpae
. Hardwick'.''.
ireensborp Bend
•Q
* •
Figure 9. Drainage map of District C (Lamoille) locating major streams and villages.
-------
Bay. More than half of this loading is derived from communities in category
b, on a system without treatment. There must be a reduction of 13.8%
(5,810 kg) to attain the [P]20 trophic condition, or a 68% reduction to reach
the mesotrophic [P]15 level.
The elimination of phosphates in the detergents would remove 40% of the
phosphorus loading from the point sources in categories b, c, and d, or
4,100 kg. This by itself is a reduction of 9.7% of the total loading to
Malletts Bay, and would improve the trophic status of Malletts Bay from
[P]23.2 (Table 26) to [P]21.1. Tertiary reduction of the remaining loading
from the present primary and secondary facilities would remove an additional
1,900 kg. With this dual control, which would remove 6,000 kg/yr, the
loading to the bay would be reduced by 14%, bringing the areal loading of
0.777 g/m2 (Table 26) to 0.666, and bringing the loading below the critical
[P]20 level. Construction of additional waste control facilities for those
communities in category b should bring Malletts Bay to the moder-
ately mesotrophic standard.
District D (Burlington-Winooski)
This District of 1,162 Sq. miles is drained predominantly by the Winooski
River, but also by Potash Brook, Munroe Brook, and the LaPlatte River (Fig.
10). It includes the cities of Burlington, South Burlington, Winooski, Essex
Junction, Montpelier, and Barre. It has more point sources of phosphorus
loading per square mile than any other District. The population within the
District is estimated to be 131,674, or 30% of the entire population in the
Champlain basin. The population density is 113/sq. mi., ranking second in
density to St. Albans (B).
The complete inventory of phosphorus to the Region is as follows:
Winooski River 99,730 kg/yr
LaPlatte River 8,700
Munroe Brook 630
Potash Brook 740
Diffuse 660
Precipitation 2,110
Treatment plants 27,020
Mass transport 31,804
Totals: 171,390 100.0%
Because of the very large volume of water in Region D, and the fairly
long retention time of 1.02 years (Table 3), this loading falls short of the
critical [P]30 loading, but yet only 4.4% below this "dangerous" level. In
other words, the loading is only 7,500 kg/yr short of reaching the critical
level. With the projected population growth in the Burlington area (Fischer,
1976), this critical input may already have been matched.
To attain the [P]20. standard would require that the phosphorus loading be
reduced 30.4%, or by 52,110 kg/yr.; and to reach the [P]10 standard of oligo-
trophy would require a reduction of 65.3%, or 111,930 kg/yr. With all of the
82
-------
Figure 10. Drainage map of District D (Winooskt) locating major streams and villages.
-------
point sources in the District, this could be accomplished, since two-thirds
of the input is derived from surface drainage, 16% from sewage treatment
plants discharging directly into the lake, and 19% transported in from the
more southern part of the lake.
The point source loadings within this District are given in Table 3 of
Appendix E, and summarized in Table 28. The total introduction of effective
phosphorus amounts to 112,240 kg, or 65% of the total input for Region D
(80% of the tributary loading).
It should not be difficult to reduce the loading by a minimum of 50% to
achieve a [P]15 standard. A detergent phosphate ban, reducing the major
point source loadings by at least 40% would remove 44,700 kg, or 26.1% of the
total loading. This by itself would improve the trophic loading status of
the Burlington area of the lake from a [P]28.5 to [P]20.9. When the Vermont
schedule for many of the existing waste treatment plants in District D to
provide phosphorus elimination becomes effective in the early 1980's, there
will be anticipated an observed improvement in the conditions of the lake,
by the removal of an additional 59,500 kg.
District E (Charlotte)
This is a small segment of land between the two larger Districts of Ver-
mont and is inhabited by less than 800 people. The land consists mainly of
woodlands, orchards, and estates. Holmes Brook is the only real channel
draining the District, and it was dry during most of the collecting time so
that inadequate data are available to assess loadings. This District is con-
sidered completely as non-point source of phosphorus.
District F (Otter Creek)
Otter Creek, flowing for more than 100 miles and the largest river of the
basin is the dominant drainage in this District (Fig. 11). Lewis and Little
Otter Creeks also share in the drainage. This District contributes about 20%
of the entire basin loading of phosphorus, and the distribution of loading is
as follows:
Otter Creek 113,730 kg 68.2%
Little Otter Creek 10,810 6.5
Lewis Creek 5,780 3.5
Thorpe Brook 740 0.4
Hospital Clerk 510 0.3
Diffuse 2,170 1.3
Precipitation 880 0.5
Mass Transport 32.102 19.3
Totals 166,720 100.0%
Most of the input is derived from Otter Creek, and transported in from
the South end lake. The total loading of phosphorus into this District very
much exceeds the Vollenweider £P330 standard, and it would require a reduc-
tion of 53.7% (87.5 tonnes) of phosphorus to approach that standard. It would
84
-------
Figure 11. Drainage map of District F (Otter Creek) locating major streams
and villages.
85
-------
require a reduction of 76.8% to obtain the [P]15 level (Table 27).
Any reduction in phosphorus input in Region F will relieve some of the
pressure in the Burlington area that receives 18% of its loading from mass
transport from the Otter Creek Region.
The inventory of point source loading from the lower 85 miles of Otter
Creek is given in Table 4 of Appendix E, and summarized in Table 28. The
total point sources amount to 31,270 kg/yr, 23% of the watershed loading
into the lake from this District. Primary treatment plants contribute 77%
of this loading and 14% from secondary facilities.
A detergent phosphate ban would reduce this loading by 12,200 kg/yr, pro-
viding a 7.3% reduction in total loading into this Region of the lake, and a
9% reduction of the loading from District F watershed input. The detergent
phosphate ban would reduce the trophic status of Region F waters from a value
of [P]47.7 to [P]44.2.
Superimposing tertiary treatment for the present primary and secondary
facilities would remove an additional 15,500 kg, and the combined effect
would be a removal of 27,700 kg, or 16.7% of the total loading. This would
reduce the critical loading level to approximately [P]39.8, a major improve-
ment, though much above the eutrophic level of [P]20.
District S (South End Lake)
The morphometric structure of District S, a very large and complicated
drainage basin accomodating a long, narrow, and shallow basin, has been con-
sidered as another tributary to the lake (Henson and Potash, 1976). The
total District phosphorus input has been calculated to be 75,570 kg/yr
(Table 25).
This District can be divided into three sub-basins: (1) The Poultney
River drainage (Fig. 12) which forms part of the border between New York and
Vermont, (2) the Metawee River Drainage (Tig- 13) that is included in both
States, and also includes part of the Hudson-Champlain Canal, and (3), the
Lake George and western shore of the South End Lake (Fig. 14). Lake George
constitutes a sink for phosphorus entering from the Lake George Basin, and
that loading will not be included in this discussion; and towns along the
northern part of the lake are excluded.
The South End Lake is in a eutrophic status, and the phosphorus loading
to this basin exceeds the [P]30 level (Table 26). Phosphorus loadings must
be reduced by 32.1% (24,260 kg) to attain the [P]30 level, 54.7% to reach
the [P]20 level (41,340 kg) and 77.3% (58,420 kg) to reduce the loading to
the oligotrophic standard.
Table 5 of Appendix E lists point sources for an estimated 34,030 kg of
annual load from the three sub-basins, or about 45% of the total loading.
About 13,270 kg (39%) of this is derived from Vermont sources. A detergent
phosphate ban would reduce this by 5,300 kg/yr, or 7.0% of the total loading,
reducing the critical loading value from the present 1.328 g/m2 to a value of
86
-------
ubbardton;'
Bomoseen
Figure 12. Drainage map of the Poultney River sub-drainage basin of
District S.
37
-------
Gronville V- , '
•'. Queerisb'ury
District 13. Drainage map of Metawee River sub-drainage basin of District S.
-------
Lake George
BaltonJ-dg
Balton
Crosbyddle .
Jiconderoga Creek
iderdga
Figure 14. Drainage map of the Lake George sub-drainage basin of District S,
89
-------
1.234, but still above the [PJ30 value. After a detergent ban, the remaining
11,930 kg from category (c) and (d) point sources in New York and Vermont
could be reduced by 10,700 kg through tertiary treatment. The combined
reduction would amount to 16,000 kg or 21.2% of the total load, reducing the
critical loading values from the present 1.328 g/m2 to 1.047 still above the
[P]30 level, but improved.
The above analysis does not consider the potential reduction of the
10,927 kg/yr loading from an industrial plant discharging directly into the
South End Lake (EPA, 1974).
District M (Port Henry)
This small District (Figure 15) in the southwest corner of the basin, with
a population of 6,645, contributes about 3% of the total phosphorus to the lake,
The loading to the Region is distributed as follows:
Hammond Brook 1,210 kg 2.1%
Stacy Brook 730 1.3
Beaver Brook 930 1.6
Mullen Brook 120 0.2
Mill Brook 6,360 11.1
Diffuse 6,280 10.9
WT Plants 8,840 15.4
Precipitation 880 1.5
Mass transport 32,100 55.9
Totals: 57,450 kg 100.0%
According to Table 27, this loading must be reduced by 76% for oligo-
trophy, and 28.3% (16,260 kg) for the [P]30 level.
The two Moriah Sanitary District primary treatment plants generate about
2,850 kg/yr, so the total point source loading amounts to 9,350 kg. A 90%
(tertiary) reduction (7,200 kg) would represent about 12.5% of the loading.
Since two-thirds of the loading in Region M is derived from the South End
Lake, reduction there would ease the situation near Fort Henry.
District L (Bouquet)
The Bouquet District is drained by the Bouquet River (Figure 16). The dis-
tribution of the phosphorus loading into the Region is:
Bouquet River 19,430 kg
Diffuse 660
Precipitation 1,150
Mass Transport 24.470
Totals: 45,710 kg 100.0%
The population of slightly in excess of 4,000 is scattered in about a
dozen small communities. Elizabethtown, with a population of 607, is one of
90
-------
. '-y Beo. , Br
Figure 15. Drainage map of District M (Port Henry).
91
-------
5 MILES
Figure 16. Drainage map of District L (Bouquet)
-------
the larger villages. If the other eight communities along the Bouquet River
had populations of 300, the total contribution of phosphorus, at 1.5 kg/C/
yr, would be about 4,500 kg/yr. The potential point source loading is rela-
tively small.
Because of the large volume of water of Region L and the fairly high
retention time, the loading into this part of the lake falls below the [P]30
standard, and is about 11% above the L~P]10 level. A reduction of 4,890 kg/
yr would reduce the loading to the oligotrophic status. Phosphorus control
among the nine communities could account for about 4,400 kg, and reduction
in District M and S would contribute to a reduction through mass transport
input.
District K (Saranac-Ausable)
This is the largest District with an area of 3,548 km2, comprises 18% of
the Champlain drainage (Figure 17). It includes a total population of 77,094,
also representing 18% of the basin's total population. The total phosphorus
input to this Region is as follows:
Saranac River 68,920 kg 35.0%
Ausable River 33,810 17.2
Little Ausable R. 13,780 7.0
Scomotion Creek 4,200 2.1
Salmon River 3,840 2,0
Silver Stream 630 0.3
Diffuse 2,740 1.4
Precipitation 1,410 0.7
Mass Transport: D 35,550 18.1
Mass Transport: EL 31,810 16.2
Totals: 196,690 100.0%
This loading of nearly 200 tonnes of phosphorus is more than a quarter
C26%) of the total loading into the lake. Region K has a very large volume
of water; therefore the impact of phosphorus input is not severe except in
local and shoreward areas. Because of this morphometric situation the criti-
cal loading is below the [P]30 level. There must be a 54% reduction in the
phosphorus loading to approach the oligotrophic standard, and the loading
would have to be reduced 8.U to attain the mesotrophic standards, 'his
necessitates a reduction of 15,930 to 106,210 kg/yr to maintain good quality
standards in this part of the lake.
About a third of the phosphorus entering Region K is derived from the
mass transport from Regions D and EL. Even though phosphorus reduction ^
measures taken in Districts upstream would alleviate some of the tension
in Region K, much more than half of the phosphorus is derived from its own
drainage basin. The phosphorus entering the Region through mass transport
has less impact because it is more dilute than the amount discharging into
the lake, where sedimentation and biological uptake is more likely to take
place.
93
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"
am Lota
Ku*iaqua
Onchloto
Rainbow Lxika
Figure 17. Drainage map of District K (Ausable-Saranac).
-------
Table 7 in Appendix E, and Table 28 summarize the known major point
sources of phosphorus in the District, excluding those that are discharging
directly into the lake. The total yield amounts to 75.0 tonnes per year or
38.1% of the total input. A tertiary program for the communities providing
90% removal would account for a reduction of 55,800 kg (28.4%), a significant
reduction. Nutrient control in upstream Districts would allow reduction from
mass transport input.
District H (Islands)
The main point source in this District is the Town of A!burg (population
1,279), presently on a primary system, with scheduled tertiary in the plan-
ning stage. Total load is estimated to be 1,716 kg. Local control of mari-
nas and small communities along the waterfront should help to alleviate prob-
lems in the coves and bays. Nutrient reduction elsewhere, e_.£. Missisquoi
Bay, will reduce the amount of phosphorus entering by mass transport, and
will help alleviate present and potential problems. A detergent phosphate
ban would remove 686 kg of phosphorus, with scheduled tertiary capable and
removing an additional 927 kg leaves this source as very minor.
District J (Chazy-Rouses Point)
District J is the northwestern corner of the basin (1,030 km2) just
above the outlet at Rouses Point. It is drained by the Great Chazy and
Little Chazy Rivers, and the small Riley Brook (Figure 18). The total popula-
tion in the District is 19,861, 4% of the Champlain basin. The total loading
from the District, as listed below, amounts to 52.7 tonnes, 7% of the Cham-
plain loading. This is equivalent to 2.65 kg per capita, the highest per
capita loading from any District in the basin.
The loading is as follows:
Great Chazy River 35,990 18.5%
Little Chazy River 6,320 3.3
Diffuse 7,930 4.1
Precipitation 2,070 1.1
Rouses Pt. WTP 2,450 1.3
Mass transport, H 82,730 42.6
Mass transport, K 56,470 29.1
Totals 193,960 100.0%
Because of the shallow depth and low retention time of Region J, the
present loading is below the £P]20 level (Table 26). To attain the [P]10
level would require a reduction of 40.2%, or 77.970 kg.
Table 28 summarizes the inventory of point source loadings given in Table
6 of Appendix E. Secondary plants generate 5,040 kg of the total of 8,590^.
Tertiary treatment from these secondary plants would remove 4,500 kg., 8.6%
of the load draining from the District.
Because Region J serves to transport waters received from all other parts
95
-------
•-.
Perry
jses Pt.
Coopers vide.
Figure 18. Drainage map of District J (Chazy).
-------
of the lake to the outlet at Rouses Point, and there Is a rapid flow-through
time, the Impact of the heavy loading is minimized. Nearly three-fourths of
the loading to the Region ts from mass transport. Phosphorus leaving the
lake here through the outlet becomes the loading to the Richeleau River, and
this, in turn, eventually, contributes to the loading of the Atlantic ocean.
SUMMARY
In this section an assessment has been made of the total amount of phos-
phorus entering each region of the lake from the adjacent District, and by
mass transport from adjacent Regions. An inventory of point source loadings
within each District (Appendix E) has been applied to estimate effects of the
proposed detergent phosphate ban in Vermont, and to assess the amounts of phos-
phorus reduction that would take place if present primary and secondary waste
treatment plants were to add nutrient removal controls.
These matters are summarized in Table 29. It should be noted that the
data given in this table are conservative figures since (1) the reduction
through banning detergent phosphates was based on a 40% removal rather than
the commonly used value of 50%, and (2) the stated reductions of loading into
the lake do not consider the secondary effect of the reduced amounts of phos-
phorus being transported from Region to Region.
For the whole of Lake Champlain, about 42% of the total loading of 747.6
tonnes is derived from point sources, but this ratio ranges from 6% to 81%.
The dual nutrient control program would remove 249 tonnes of phosphorus, or
33% of the total loading. The revised regional loadings given in column 8 of
Table 29 should be compared with the information given in Table 26. The
revised trophic [P] standard for the whole of Lake Champlain would be reduced
from the present [P]31.5 to [P]21.0. Those four Districts (A, F, M, and S)
with still excessively high loading values should be given special attention
in order to reduce the significant influence of non-point sources.
97
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TABLE 2.9. SUMMARY OF THE POTENTIAL EFFECT OF NUTRIENT CONTROL POLICIES ON
THE REDUCTION OF PHOSPHORUS ON THE REGIONS OF LAKE CHAMPLAIN.
Load3
Tonnes
District yr
A
B
C
D
F
H
J
K
L
M
S
Lake
86.92
22.56
41.13
137.48
133,74
4.82
59.69
127.93
20.09
24.47
74.55
747.55
Point5 loss byc
Sources P-ban
tonnes/yr % tonnes/yr
15.88
11.52
11.52
112.25
31.27
1.72
8.58
74.97
1.33
9.35
34.03
312.42
18.3 5.5
51.1 6.7
28.0 4.1
81.6 44.7
23.4 12.2
35.7 0.7
16.3
58.6
6.6
38.2
45.6 5.3
41.8 79.2
loss by
tertiary
tonnes/yr
4.5
9.1
1.9
59.5
15.5
0.9
4.5
55.8
0
7.2
10.7
169.6
Total P
removed
tonnes/yr
10.0
15.8
6.0
104.2
27.7
1.6
4.5
55.8
0
7.2
16.0
248.8
Revised
load
g/m2
1.009
0.401
0.666
0.573
2.855
0.471
1.649
1.797
0.716
1.032
1.047
0.440
Revised
[P]
42.0
23.2
19.9
11.2
39.8
15.6
16.3
15.6
11.2
29.6
34.8
21.0
a: Annual load derived from District drainage in metric tonnes.
b: Loading from point sources in the District, from Table 28.
c: Assumes 40% phosphorus reduction from sewered populations by the proposed
Vermont detergent phosphate ban.
d: Assumes tertiary treatment provided only by those plants which now have
primary or secondary treatment.
98
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SECTION 8
SUMMARY OF LAKE-DRAINAGE BASIN INTERACTIONS
MISSISQUOI BAY
The in-lake concentration and theoretical total phosphorus value (0.50
and 0.40 mg/1 respectively) for Missisquoi Bay are some of the highest
values recorded for Lake Champlain and are within the eutrophic range. How-
ever, because of the shallow depth of the bay and the well mixed water col-
umn, many eutrophic characteristics do not occur. The impact of the high
phosphorus loading is apparently not manifested in significant increases in
productivity since only a small amount of the phosphorus that enters the
region is retained (5-6%) while the majority of it (94-95%) is flushed out
very rapidly. The total water volume of the bay is renewed approximately
six times per year with the bulk of the flushing occurring during the spring
runoff.
At the present time, more data are needed to determine the fate and
impact upon the Missisquoi Bay region of the 5-6% of the incoming phosphorus
that is retained within the basin. Part of this loading is indoubtedly
going into some production, which may be reflected in the important yellow
perch (Perca flavescens) fishery in the bay. Creel census information, for
example, indicate that over one million perch are caught each winter by ice
fisherman in the area (Countemesh, per. comn.). The Vermont Water Resources
Department has determined that the silt load entering from the Missisquoi
and Pike Rivers has a significant influence upon the bay. A total input of
10.7 x 103 tons/year results in an average accumulation rate of sediment of
1.0 mm/year. It is not known, however, what percentage of the loading is
from natural or man-made sources.
It has not been established whether the total phosphorus loading entering
via the Missisquoi River and Pike River actually reaches the surface waters
of the bay. Both tributaries pass through an extensive wetland area (Missis-
quoi National Wildlife Refuge) and some of the phosphorus may be lost to the
wetland vegetation and/or sediment. Also, there are no input data available
from Venice en Quebec, Quebec. It is suspected that phosphorus loading may
be quite high in this region due to the numerous shoreline cottages and high
summer population.
The discharge of significant amounts of phosphorus-rich Missisquoi Bay
water would have a significant effect on other areas of Lake Champlain. The
data on current patterns in the region suggest that the Missisquoi discharge
splits at the northern tip of North Hero Island, with part of the load enter-
ing the Maquam Bay and North Hero Island region and part moving south through
the Alburg Passage into the main lake east of Isle La Motte. Thus, it is
99
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anticipated that eutrophicatlon problems may occur in these areas. In
recent years, for example, the Vermont Water Resources Department has
received an increasing number of complaints about algal blooms in the
extreme northern portion of the northeast arm near Maquam Bay.
Recommendations for Missisquoi Bay
Although the input of phosphorus should be reduced, nutrient loading
apparently has minimal influence upon the observable trophic characteristics
in Missisquoi Bay; however, if the phosphorus loading into the bay were
reduced, it is believed that the potential eutrophication problems in other
areas of the lake (Maquam Bay, North Hero Island area, and Isle La Motte
region) would also be reduced. In order to lower the phosphorus levels in
Missisquoi Bay (Region A) to the levels of the immediate adjacent area
(Region B), there would have to be a 74% reduction in the total phosphorus
loading. The present loading level of 1.139 gms/nf would have to be reduced
to 0.30 gms/m2 in order for this to be accomplished. In order to reach P,Q,
PZO» or PSO levels within Missisquoi Bay, the phosphorus loading into the
bay would have to be reduced by 78.9%, 57.9% and 36.9%, respectively.
It is important to have a better understanding of the point and non-
point phosphorus sources from the Pike River, Rock River, and the community
of Venice en Quebec. This lack of data from these areas is a result, in
part, of jurisdictional problems related to the international boundary with
Quebec, Canada. For example, the State of Vermont only examines that por-
tion of the Pike River that flows through Vermont and ignores the Canadian
sections of the river in their management plans. It is essential that the
total drainage basin of Missisquoi Bay, a large portion of which is located
in Canada, be included in the United States Environmental Protection
Agency's management plans for Lake Champlain. The Vermont Water Resources
Department indicates that there has been cooperation between the two nations
on water resources issues, however, it appears that a better data exchange
is necessary.
In order to more fully quantify the total phosphorus loading impact on
Missisquoi Bay, it may be necessary to investigate the amount of phosphorus
that may be lost to the wetland from the Missisquoi and Pike Rivers and the
fate of phosphorus retained with the basin.
NORTHEAST ARM
The theoretical value (.040 mg/1) and the mean in-lake concentration
(.020 rng/1) of total phosphorus in the entire northeast area are quite low
because of the large volume of the region and the major loading entering the
region occurs in St. Albans Bay, which tends to retain it. A total of 25.0
metric tons/year of phosphorus is entering the northeast arm from drainage
basin (B) and 44.6 metric tons/year from regions (A) and (C). Of this
total, approximately 24% (16.8 metric tons/year) is entering St. Albans Bay
via Stevens Brook. In relation to its volume, the rest of the northeast arm
receives relatively little phosphorus input from other drainage basin
sources.
100
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The deeper open waters are considered mesotrophic, while the majority of
the embayment areas are typical shallow, mildly eutrophic situations. The
Vermont Water Resources Department carefully controls development and sewage
disposal in the shoreline areas, thus the only threats to these regions are
the loadings from Missisquoi Bay and St. Albans Bay. St. A!bans Bay pres-
ently has extensive eutrophic characteristics which include abundant sub-
mergent aquatic weed growth and some bluegreen algal blooms.
Recommendations for the Northeast Arm
The principle recommendation for this region is to reduce the phosphorus
loading into St. Albans Bay entering via Stevens Brook. The major point
source along Stevens Brook is the City of St. Albans Sewage Treatment Facil-
ity, although there may be some non-point loading from farmlands in low lay-
ing areas near the brook. Since algal productivity in St. Albans Bay and
other regions of the northeast arm is known to be phosphorus limited, a
reduction in the phosphorus input is essential to relieve the present and
future eutrophication problems. The phosphorus concentration for the entire
northeast arm is presently very close to the P3Q level. In order to reach
PIQ or POQ levels, the loading into the entire region would have to be
reduced by 59.9% and 13.8%, respectively. However, because of the specific
hydrologic situation of St. Albans Bay, and extremely poor estimates of
retention time of the water in the Bay, we can offer no quantitative values
for suggested phosphorus reduction other than striving for a 100% reduction
in culturally derived input.
The sediments within St. Albans Bay contain extremely high concentrations
of phosphorus (mean = 983 p.p.m.). It is important that the transport
exchange between the sediments and the water column under different phos-
phorus concentrations by understood. The probability is small that there
will be a significant increase in phosphorus flux from the sediments to the
water column upon reduction of the phosphorus loading. Oxygen depletion
near the bottom has not been recorded, thus conditions for the release of
soluble phosphorus are poor. If there were a prolonged period of calm
weather in the summer, the bay may stratify for short periods, and a signifi-
cant oxygen depletion would be expected. Under such circumstances, a short-
term phosphorus release from the sediments may be realized.
Approximately 51% of the phosphorus input into the northeast arm is
retained with the basin. A major portion of this phosphorus load is appar-
ently retained in St. Albans Bay, by being incorporated into the submergent
aquatic vegetation and the sediments. However, it is important that the
fate of this input within the northeast arm be determined to completely
understand the impact of the total region.
Reduction in the phosphorus loading from Missisquoi Bay would aid in
reducing the potential eutrophication problems of the northeast arm, espe-
cially in the northern portions of the area.
MALLETTS BAY
Malletts Bay presents an interesting conflict among the low in-lake phos-
101
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phorus concentration (mean = .012 mg/1), the relatively high calculated the-
oretical phosphorus level (.060 tng/1), and the high retention of phosphorus
1n the region. Approximately 42 metric tons/year of phosphorus enters Mal-
letts Bay, with approximately 92% of this loading (37.8 metric tons/year)
entering through the La Moille River. However, even though the calculated
retention of phosphorus is very high (about 72%), it is not reflected in the
surface water concentrations, which are the lowest found in Lake Champlain.
As a result, most of the surface water characteristics for Mallets Bay are
oligo-mesotrophic.
At present, there is little understanding of the fate of phosphorus once
it enters the bay. Since the La Moille River flows through an extensive
marsh area (Sandbar Wildlife Management Area), some of the phosphorus may be
lost to the aquatic vegetation and/or the sediments of the wetland. Or per-
haps the phosphorus is being lost to the sediments of the deeper portions of
the basin and not recycled to the water column. This pathway for phosphorus
is somewhat difficult to accept since the hypolimnial waters in Malletts Bay
suffer from almost complete oxygen depletion during the stratified period.
As a result, conditions in the lower waters and at the sediment/water inter-
face are conducive to formation of soluble phosphorus as indicated by rapid
increases in soluble reactive phosphorus concentrations in the lower waters
during stratification.
Recommendations for Halletts Bay
There is a need to understand the fate of the phosphorus entering via
the La Moille River in order to assess the future potential impact of load-
ing upon the bay region. According to the present figures, the phosphorus
loading is below the P3Q level. In order to accomplish PJQ or P?o levels,
the loading into the bay would have to be reduced by 56.956 and 13.8%, respec-
tively.
It is important to understand the mechanisms responsible for the severe
hypolimnial oxygen deficit in the summer. This should include a determina-
tion of the total BOD loading from the La Moille River and its transport
and fate within the bay. It may also be necessary to investigate the total
contribution of BOD to the hypolimnion of the aquatic weed beds in the
shallow areas of the bay.
Once the fate of the phosphorus and BOD loading in Malletts Bay is
determined, then a management strategy involving these two parameters can be
Initiated.
SOUTH LAKE
The total phosphorus input into the south lake is approximately 75.6
metric tons/year while about 64.2 metric tons/year leave the area. The major
point source is the International Paper Company at Ticonderoga, New York,
which contributes approximately 10.9 metric tons/year* (about 14.4% of the
* May be a low estimate (U.S.E.P.A., 1974).
102
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total phosphorus loading). Even though there are high inputs into the
region and the in-lake and calculated theoretical phosphorus values are
extremely high (.050 and .486 mg/1, respectively), the development of severe
eutrophication problems in the south lake are not expected. This is mainly
due to the high natural turbidity of the waters which limits the development
of extensive algal blooms and submergent aquatic weed beds. The only excep-
tion may be the potential for the floating aquatic weeds, Trapa natans and
Nymphoides peltatum to expand significantly in the nutrient rich waters. In
addition to turbidity, the lack of thermal stratification and the rapid flow
through of water in the south lake also limit the development of some eutro-
phic characteristics.
Since the south lake has such a rapid flushing rate (approximately 8.25
times/year) and the phosphorus retention coefficient is low (about 15%),
there could be a significant loading influence upon the southern basin of
the main lake north of Crown Point, New York. The extent of any influence
is not well understood however. There is the possibility that when the flow
rates through the south lake slow down in the broad main lake, absorptive
phospnorus is carried to the sediments with the settling clay particles. It
appears that this process may be occurring in regions (F & M), as indicated
by the low in-lake phosphorus value (mean = .018 mg/1) and the very high
retention coefficient (78%) between Crown Point, New York and Split Rock
Point.
The BOD loading from pulp and paper manufacturing is apparently
becoming an increasingly significant problem in the south lake. The impact
is mainly upon benthic invertebrate populations, which in turn, will even-
tually affect fish populations. The present major contributor of high BOD
loading in the region is the International Paper Company plant in Ticon-
deroga, New York.
Recommendations for South Lake
At the present time, it appears that any reduction in the phosphorus
loading would have little effect upon reducing eutrophication in the south
lake However, it should be confirmed whether the high phosphorus loading
from the south lake has a significant impact upon portions of the main lake.
It is logical to assume that the 64 metric tons/year of phosphorus entering
the south basin of the main lake will eventually have some impact. This is
expecially true since it is known that the majority of the phosphorus is
retained within the region. Therefore all efforts should be made to keep
phosphorus lading levils from the south lake as low as possible. "order
to reduce phosphorus loading in the south lake to P]0, P20> or P30 levels, it
must be reduced by 77.3%, 54.7%, and 32.1%, respectively.
The long term effects of the present BOD loading from point sources
should be investigated. Some evidence indicates that the problem is expand-
ing This should be continuously monitered in order to possibly readjust
current loading levels.
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MAIN LAKE (SOUTHERN, MAIN, AND NORTHERN BASINS)
The southern basin of the main lake (Districts p & M) receives 160 met-
ric tons/year phosphorus loading from the drainage basin (the largest con-
tribution being from Otter Creek) and 64 metric tons/year via mass transport
from the south lake. Approximately 78% of the input (175 metric tons/year)
is retained within the southern basin, resulting tn the highest retention
coefficient for the lake. The theoretical total phosphorus concentration
(.094 mg/1) is quite high when compared to the in-lake value (mean = .018
mg/l)i suggesting a significant loss of phosphorus from the water column. As
mentioned in the previous section, it is proposed that much of the phosphorus
is moving to the sediment in this region.
The peripheral regions of the main basin are receiving most of the
impact from phosphorus loading in the main lake. Deep open water areas and
some embayments have oligo-mesotrophic conditions, while those bay and shore-
line areas near population centers are showing signs of increased eutrophica-
tion. •
The volume of the main basin appears to be large enough to accommodate
the present loading, although 60-70% of the incoming phosphorus is being*
retained. A potential eutrophication problem still exists however, and it
must be established how much of the entering phosphorus is being biologically
assimilated by the system and how much is being lost to the sediments. There
is some evidence that productivity, even in the deep open areas of the main
basin, is accelerating.
Major inputs of phosphorus from sewage treatment facilities and local
tributaries into Shelburne Bay, Burlington Bay, and Cumberland Bay are having
significant local impact. Cumberland Bay, although it receives high phos-
phorus loading from two sewage facilities, is probably not affected as
greatly, because mass water movement to the open lake prevents retention of
phosphorus in the region. Burlington Bay is more confined than Cumberland
Bay, but has significant northerly and southerly mass water flow which
reduces somewhat the retention of phosphorus. However, phosphorus impact has
been evident along the east shore of the lake, especially along the south
shore of Colchester Point, Vermont, where there have been reports of high
Cladophora sp. and aquatic weed growth. Shelburne Bay is the most confined
of these bay areas and is showing signs of rapidly accelerating eutrophica-
tion. The extreme inner bay is especially affected by phosphorus loading,
exhibiting dense weed beds, bluegreen algal blooms, and growth of Cladophora
sp. on the shoreline.
The northern basin of the main lake receives water from all other areas
of the lake. The phosphorus retention in the region is quite low (approxi-
mately 24%) and it is probably a result of the shallow nature of the area
and the strong currents flowing toward the outlet. There are extensive weed
beds throughout the area especially at major input sites such as the mouth of
the Great Chazy River in Kings Bay, east of Isle La Motte, and from Point Au
Per north to Rouses Point, New York. At present, there is no quantitative
evidence as to an expansion of these weed bed areas.
104
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Recommendations for the Main Lake
Reduction of phosphorus loading from sewage treatment facilities and
local tributaries into Cumberland Bay, Burlington Bay, and Shelourne Bay will
help alleviate growing eutrophication problems in these regions. Also, since
the entire main lake, including the embayment areas, is phosphorus limited,
reduced loading would help alleviate increasing productivity in the deeper
portions of the lake. It is recommended that phosphorus loading be reduced
by the following percentages in the various drainage areas, in order to
accomplish P-JQ, P2Q, or P3Q levels:
Drainage Area P-|Q P2Q P3Q
D 65.3 30.4 below
E below below below
F 84.5 69.0 53.7
H 37.2 below below
j 40.2 below below
K 54.0 8.1 below
L 10.7 below below
M 76.1 52.2 28.3
It is necessary to understand the fate of phosphorus in the main basin
of the lake in order to determine the significance of the high retention of
phosphorus in the region.
It is necessary to understand the fate of phosphorus entering the
southern basin of the main lake from the south lake, so that the impact of
south lake water on this region can be determined. There is also a need for
an assessment of the amount of phosphorus being retained by the wetlands in
the Otter Creek area.
Throughout the main and northern basins of the lake, there are a large
number of private and some municipal water intake sites. Since it is import-
ant to retain high water quality in these areas, a careful monitoring of
water conditions should be maintained in the region.
105
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SECTION 9
CURRENT RESEARCH AND MANAGEMENT PROGRAMS RELATED TO EUTROPHICATION
OF LAKE CHAMPLAIN
VERMONT ENVIRONMENTAL CONSERVATION AGENCY, MONTPELIER, VERMONT*
1. Vermont is presently completing an 18 month study on St. Albans Bay
and Shelburne Bay (including the LaPlatte River system). Basic objectives
were to determine point and non-point loading sources into the bays and to
characterize the limnological conditions of the receiving waters. Completion
date is December, 1976.
2. A National Water Quality Surveillence System station on Missisquoi Bay
is monitored once monthly and is maintained and operated by the Vermont
Department Water Resources (Carl Pagel).
3. Water quality monitoring stations are maintained on six major Vermont
tributaries to Lake Champlain; Poultney R., Otter Creek, Lamoille R.,
LaPlatte R., Winooski R., and Missisquoi R. Each station is sampled six
times/year (Carl Pagel).
4. The following monographic studies on the benthic invertebrates of
Lake Champlain are in various stages of completion:
Profundal benthos of Lake Champlain (C. Pagel)
Sphaeriidae (Mollusca) of Lake Champlain (C. Pagel & J. Pagel)
_. Chironomiidae of Lake Champlain (C. Pagel)
d) Oligochaetes of Lake Champlain (C. Wade)
5. A number of water quality surveillence stations are maintained in the
south lake region. Four stations are sampled four times/year for chemical
and biological characteristics (Doug Burnham).
6. Cold Water Fisheries Program - Ecological studies on the forage fish
populations are being conducted. Stocking and monitoring of Atlantic Salmon,
Steel head Trout, and Lake Trout populations are also being conducted (Jon
Anderson & Jim Stuart).
* Additional studies are listed under the International Joint Commission.
106
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UNIVERSITY OF VERMONT, BURLINGTON, VERMONT*
1. Limnological studies on Missisquoi Bay (1965-1974) have been com-
pleted and the data are in manuscript form (E. B. Henson and Milton Potash,
Department of Zoology).
2. Studies on the distribution of zooplankton populations in various
basins of Lake Champlain are in progress (Jeffrey Kantor, Department of
Zoology).
3. Studies on the distribution and biology of the deep water crustacean
Myjsjs relicta are near completion (Thomas Gutowski, Department of Zoology).
4. Studies on the feasibility of commercial fishing on Lake Champlain
are in progress (George W. LaBar, Department of Natural Resources).
5. Rates of protease activity in waters of different trophic conditions
(J. Little).
6. LANDSAT studies of agricultural systems in New England (crop speci-
fic) (A. 0. Lind).
NEW YORK STATE DEPARTMENT OF ENVIRONMENTAL CONSERVATION, ALBANY, NEW YORK*
1. New York is presently maintaining two water quality surveillence sta-
tions at Rouses Point and Crown Point, New York (Ronald Maylath).
2. Monitoring stations are maintained on the following New York tribu-
taries: Saranac (at Treadwell Mills), Ausable (at Keeseville), Bouquet (at
Willsboro), and Ticonderoga Ck. (at Ticonderoga) Twenth-fiye water quality
parameters are measured monthly for nine months of the year (Ronald Maylath).
3. The effluent from the International Paper Company Plant in Ticonder-
oga, New York is monitored on a continuous basis.
4. Cold Water Fisheries Program - Ecological studies on the forage fish
& sUnTtffiffi T^^cL«t sssaoS-^i
Sicted ToSuglas Sheppard, Daniel Plosila, and Walter Kretser).
5. New York Wetlands Mapping Program - c°v?rntyP^PPJn?°tthF"iS°
New York State wetlands on Lake Champlain is being completed (Eric Fried).
STATE UNIVERSITY OF NEW YORK, PLATTSBURGH, NEW YORK*
l Studies on the vertical and horizontal water movements (currents
of Earth Sciences and Physics).
*-TOrbional studies are listed under the International Joint Commission.
107
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2. Studies on the seasonal and spatial dynamics of phytoplankton popula-
tions throughout the lake are in manuscript form (Gerhard K. Gruendling,
Department of Biological Sciences).
INTERNATIONAL JOINT COMMISSION
The following studies are being supervised, in part, by the I.J.C. in
relation to the environmental impact of water level regulation of Lake Cham-
plain. Most of these studies will be completed in July, 1977.
1. Fisheries Studies (New York Department of Environmental Conservation
and Vermont Conservation Agency).
2. Wildlife and Waterfowl Studies (New York Department of Environmental
Conservation and Vermont Conservation Agency).
3. Wetlands Mapping and Ecology of Wetland Plant Associations (Donald J.
Bogucki and Gerhard K. Gruendling, State University of New York, Plattsburgh,
N. Y.).
4. Contour Mapping of Shoreline and Wetland Areas (Chicago Aerial Sur-
veys Inc., Chicago, Illinois).
5. Studies on nutrients in Malletts Creek wetland (E. B. Henson, Depart-
ment of Zoology, University of Vermont, Burlington, Vermont, and John Turk,
U. S. Geological Survey, Albany, N. Y.).
6. Assessment of Impact on Aquatic Plants (William Countryman, Aquatec,
South Burlington, Vermont).
NEW ENGLAND RIVER BASINS COMMISSION, BOSTON, MASSACHUSETTS
1. Presently phasing into a "Level B Study" which would develop strate-
gies for addressing some of the issues of water quality of Lake Champlain.
Study would plan for future development in the area as well as identify
alternative projects and uses of water and related land uses.
2. "Lake Champlain Planning Guide for Water and Related Land Resources"
which was published in June, 1976, provides additional information about
management programs and research plans of various local, state, and federal
agencies for Lake Champlain.
108
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SECTION 10
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changes associated with autumnal overturn. Int. Assoc, Grt. Lakes Res.,
Proc. llth Conf.:565-570.
62. Potash, M., S. E. Sundberg, and E. B. Henson. 1969. Characteristics of
water masses of Lake Champlain. Verh. Internat. Verein Limnol. 17:140-
147.
63. Sage, L. E. 1969. A comparative study of the vertical migration of
crustacean zooplankton under three thermal water column conditions.
M. S. Thesis, University of Vermont, Department of Zoology. Ill pp.
113
-------
64. Sanderson, W. W. 1953. Studies on the character and treatment of wastes
from duck farms. Proc. 8th Industr. Waste Conf., Purdue Univ. Exten.
Serv. 83:170-176.
65. Sherman, J. W. 1972. Diatom Assemblages in Lake Champlain. M. S.
Thesis, Department of Geology, University of Vermont. 81 p.
66. Stewart, K. M. and S. J. Markello. 1974. Seasonal Variations in Con-
centrations of Nitrate and Total Phosphorus, and Calculated Nutrient
Loading for Six Lakes in Western New York. Department of Biology, State
University of New York, Buffalo, NY, vol. 44, 1, pp. 61-89.
67. Sundberg, S. E. 1972. Thermal properties of Mallets Bay, Lake Cham-
plain. Ph.D. Thesis, University of Vermont, Department of Zoology.
148 pp.
68. Taylor, A. W. and H. M. Kunishi. 1971. Phosphate equilibria on stream
sediment and soil in a watershed draining on agricultural regions.
J. Agr. Food Chem. 19:827-831.
69. Tremblay, R. H. 1967. Projections of dairy farm numbers in Vermont,
1967-1980. Preliminary Research Report, Dept. Agr. Economics, Univ.
Vermont, Ag. Econ 68-2., 19 pp.
70. Vermont Dept. Fish & Game. 1962. Vermont Stream Survey. Vt. Dept Fish
& Game, Final Report on Project F-2-R, Statewide Stream Survey by Water-
sheds.
71. Vermont Department of Water Resources. 1974. Missisquoi River Basin
Water Quality Management Plan. Montpelier, Vt. 22 pp. & 13 appendices.
72. Vermont Department of Water Resources. 1975. Otter Creek Basin Water
Quality Management Plan. Montpelier, Vt. 27 pp. & 10 appendices.
73. Vermont Department of Water Resources. 1975. Poultney-Mettawee Water
Quality Management Plan. Montpelier, Vt. 50 pp. & appendices.
74. Vermont Department of Water Resources. 1976. Unpublished water quality
data 1974-76 for Missisquoi Bay, St. Albans Bay, Burlington Harbor,
Shelburne Bay, and Southern Lake Champlain. Agency of Environmental
Conservation, Montpelier, Vt.
75. Vollenwelder, R. A. 1968. Scientific fundamentals of the eutrophica-
tion of lakes and flowing waters with particular reference to nitrogen
and phosphorus as factors in eutrophication. Paris, Rep. Org. for
Economic Cooperation and Development, DAS/CSI 68.27, 192 pp.
76. Vollenweider, R. 1976. Advances in defining critical loading levels
for phosphorus in lake eutrophication. Memorie dell'lstituto Italiano
di Idrobiologia. Dott. Marco De Marchi 77, Pallanza.
114
-------
77. Wade, C. 1976a. A study of Oligochaeta of several areas of Lake Cham-
plain. Unpublished report, Dept. of Zoology, University of Vermont.
62 P.
78. Wade, C. 1976b. Depth distribution of the aquatic gastropods in Outer
Mallets Bay, Lake Champlain. Unpublished report, Department of Zoology,
University of Vermont. 22 p.
79. Wetzel, R. G. 1976. Limnology. W. B. Saunders Co. 741 pp.
80. Wood, L. W. 1972. Biological indicators of water quality in the Ticon-
deroga section of Lake Champlain in October, 1972. New York Department
of Health. 65 p.
115
-------
SECTION 11
APPENDIX
LIST OF APPENDICES
Page
Appendix A. Conversion factors used in this document. 117
Appendix B. Method for estimating the Champlain basin 118
population, 1810-1970.
Appendix C. Inventory of tributary streams of Lake Champlain.
Table 1. Inventory of the tributaries draining 121
into Lake Champlain.
Table 2. Listing of the 34 tributaries with 128
drainage basins with drainage areas of 10 square
miles or larger.
Appendix D. Primary data on the median concentrations of 129
total phosphate-phosphorus of the major tribu-
taries in each District, and the loadings of
total phosphorus for each tributary, and for
the Districts.
Appendix E. Inventory of the point-source loadings in the 132
Districts of the Champlain basin.
116
-------
APPENDIX A
CONVERSION FACTORS USED IN THIS MANUSCRIPT
A. Time: 1 year
B. Length: 1 mile
1 meter
1 Km
C. Area: 1 Acre
1 Sq. mile
1 sq. Km
D. Volume: 1 cu. ft.
1 m3
1 gal.
E. Weight 1 pound
1 kg
1 mg
1 pg
F. Miscl: P04-P
1 cfs
= 31.5569 X 106 seconds
= 365.25 days
= 1.60935 Km
= 1,609.35 m
= 0.62137 mile
= 4,046.873 m2
= 2.589998 Km2
= 2.589998 X 106 m2
= 0.3861 sq. mi.
= 1 X 106 m2
= 0.02831701 m3
= 1000 1
= 35.31445 cu. ft.
= 0.0037854 m3
= 0.4535924 kg
= 453.5924 g
= 2.2046 pounds
= 1000 grams
= 0.001 g
= 1000 ug
= 1 X 10-6 kg
= 0.001 mg
= 0.32614 P04
= 0.028317 mVsec
1 cfs/sq. mi.
1 gal/day
1 ug/1
= 31.5569 X 10s c.f. yr.
= 0,0109332 m3/km2
= 1.3826 m3/yr
= 1 mg/m3
117
-------
APPENDIX B
METHOD FOR ESTIMATING THE CHAMPLAIN BASIN POPULATION, 1810-1970
In the introductory section of the text, Figure 2 graphically presents
the estimated loading of phosphorus into Lake Champlain from 1810 to 1970, a
160 year history. Me are interested in presenting some historical perspec-
tive to the phosphorus loadings, and this has not been done before. We must
speculate on the best information at hand. To construct this graph, we have
attempted to evaluate the population in the Champlain Valley during the past
160 years, and plot the probable phosphate loading.
The Census
The first problem is the evaluation of the present population in the
basin. The method for estimating the contemporary basin population was as
follows: With the 1970 Census report, the population of all of the towns
completely within the drainage basin were totaled. This left these towns
along the outer boundaries to be appraised. The Vermont Water Resources
Department, as background information for their "Water Quality and Pollution
Control" series, examined topographic maps, counted houses, etc., and esti-
mated the number of persons of each town in or out of a drainage basin.
These percentages were used to asses the 1970 population in the basin.
On the New York side, where such information was not available, we examined
the maps, and determined which village was or was not in the drainage. The
population outside the drainage was then subtracted from the town census.
Canada presented a problem in that the census reports consulted were incom-
plete, but a best estimate was made.
The final population estimate for the basin was 438,255. This figure
evolved about a week or so before Fischer (1976) came out with the "Lake
Champlain Basin Planning Guide", and we were pleased to note that the two
independent population evaluations were within 2%.
For the 1970 census, therefore, the estimated total population in the
entire Champlain basin is 438,255, or 98.63% of the total State of Vermont
population of 444,330 (U.S. Census).
To evaluate the population in the Champlain basin for the past years it
was deemed impossible to apply the same technique for the 160 years, so
short-cut estimates were needed. Knowing that in 1970, the population in the
Champlain basin was 98.63% of the Vermont State population, this ratio was
applied to the previous years, resulting in estimated population data that
were obviously incorrect. In other words, population growth in the Champlain
basin did not parallel growth in the State of Vermont.
118
-------
As a second approach, we had available in the files some data from Soper
(1905) (who presented census data from 1810-1900) for 11 of the 16 towns of
New York bordering the lake, and 6 of the 22 Towns and Cities bordering the
lake in Vermont. With this sampling of 45% of the bordering towns on the
lake, we have in Appendix B, Table 1 estimated the population in the basin
for the last 160 years. To make this estimate, we first noted that the popu-
lation of the sampled towns bordering Lake Champlain was 27.67% of the
Champlain basin population, which was 98.63% of the Vermont State population.
Instead of tying the basin population to the Vermont State population, it was
tied to the bordering town population, on the assumption that the town popu-
lations would more effectively reflect the populations in the entire basin.
We therefore estimated the basin population by multiplying the border town
population by I/.27665 = 0.361468.
To estimate phosphorus loadings from these populations, we have used a
conservative estimate of 1.6 kg/C/yr. For advanced societies, the value of
1.7 kg/C/yr has been suggested. We have no real evaluation for early soci-
ety. Our estimates are calculated on the basis of 1.6 kg/C/yr., a figure
that is conservative in modern times, but liberal for the early years.
119
-------
APPENDIX B (Cont.)
Table 1. Estimations of the population 1n the Lake Champlain basin, and estimates of the total phos-
phorus loadings into the lake for the years 1810 - 1970.
Year Population in selected lakeside towns Total Vt. % Vt. Pop. Estimated basin Phosphorus load
M V a V* b Tntal« Pnn laUocf^a nnnnlaHnn Im/x/r
ro
o
N. Y.
Vt.1
Totals
Pop.
1810
1820
1830
1840
1850
1860
1870
1880
1890
1900
1910
1920
1930
1940
1950
1960
1970
17,523
25,176
32,408
38,574
37,089
39,786
44,555
44,095
43,002
-
-
-
51,411
53,431
67,677
67,344
8,472
10,735
11,671
14,406
15,813
26,120
23,287
26,691
30,696
32,190
35,651
37,956
40,868
47,058
50,156
53,901
24,002
25,995
35,911
44,079
52,980
52,902
65,906
67,842
70,786
73,698
(81,194)
(85,182)
(88,141)
92,279
100,489
117,833
121,245
217,895
235,981
280,652
291,948
314,120
315,098
330,551
332,286
332,422
343,641
355,956
352,428
359,611
359,231
377,747
389,881
444,330
lakeside
11.02
11.02
12.80
15.10
16.87
16.79
19.94
20.42
21.29
21.45
22.51
(23.57)
(24.63)
25.69
26.60
30.22
27.29
population
86,762
93,964
129,807
159,331
191,506
191,223
238,229
245,227
255,869
266,395
293,490
307,906
318,602
333,559
363,236
425,929
438,262
kg/yr.
138,816
150,342
207,691
254,930
306,409
305,958
381,167
392,363
409,390
426,231
469,585
492,649
509,762
533,694
581,177
681,486
701,219
a. Total census figures for the towns: Champlain, Chazy, Plattsburgh Concluding the City), Chester-
field, Willsboro, Essex, Westport, Moriah, Crown Point, Ticonderoga, and Whitehall.
b. Total census figures for the towns: St. Albans (including city), Burlington, Orwell, Benson, West-
haven, and Vergennes.
-------
APPENDIX C
INVENTORY OF TRIBUTARIES ENTERING LAKE CHAMPLAIN
Table 1. Inventory of the tributaries entering Lake Champlain.
No.
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
Region
H
H
H
H
H
H
H
H
H
H
H
H
H
H
H
H
H
H
H
H
H
H
H
H
A
A
A
A
Code Name
4-0010
4-0030
4-0031
4-0033
4-0050 Sucker Brook
4-0070
4-0073
4-0077
4-0090
4-0093
4-0097
4-0099
4-0101
4-0103
4-0105
4-0107
4-0110
4-0113
4-0130
4-0133
4-0135
4-0137
4-0150
4-0170 Mud Creek
4-0190
4-0195
4-0210 Bloods Creek
4-0230
Area
mi2
3.29
0.94
0.41
0.37
1.78
0.91
0.30
0.49
0.48
1.29
0.26
0.35
1.62
0.58
1.46
0.32
1.94
1.44
1.30
0.63
0.87
1.21
0.13
11.55
0.93
2.63
1.91
5.26
Lake
Code
055
055
055
055
053
050
Pt.
050
043
043
071
081
081
082
082
082
081
081
081
086
086
095
094
094
094
093
093
092
090
Location
Windmill Pt. , east
Mud Point, north
Mud Point, north
Mud Point, north
LaMotte Passage
S. Hero Is., Nichols
S. Hero Is., Wilcox
Bay
S. Hero Is., Sawyer
Bay
S. Hero Is., Barnes
Bay
S. Hero, Outer Mal-
letts Bay
S.W. Savage Sea
Paradise Bay
Keeler Bay
Keeler Bay
Keeler Bay
Cooper Bay
Pearl Bay, south
Pearl Bay
The Gut
Hi board Bay, The Gut
N. Hero, Macomb Bay
N. Hero, S. of Stony
Pt.
Dillenbeck Bay
Ransoms Bay
Chapman Bay
Chapman Bay
Campbell Point
Peel Head Bay
121
-------
CHAMPLAIN TRIBUTARIES, p. 2
29
30
31
32
33
34
35
36
37
38
39
40
41
42
43
44
45
46
47
48
49
50
51
52
53
54
55
56
57
58
59
60
61
62
63
64
65
66
67
A
A
A
A
A
A
A
B
B
B
B
B
B
B
B
B
B
B
B
B
B
B
B
C
C
C
C
C
C
C
C
C
C
C
C
C
C
C
C
4-0250
4-0270
4-0330
4-0350
4-0370
4-0390
4-0410
4-0430
4-0450
4-0470
4-0490
4-0510
4-0530
4-0550
4-0570
4-0590
4-0595
4-0610
4-0630
4-0650
4-0670
4-0690
4-0710
4-0730
4-0750
4-0770
4-0790
4-0810
4-0830
4-0850
4-0870
4-0890
4-0895
4-0910
4-0930
4-0935
4-0950
4-0970
4-0990
4-1010.
4-1030
4-1050
Pike River
Rock River
Carman Brook
Dead Creek
Missisquoi R.,
Missisquoi R.,
Missisquoi R.,
Charcoal Creek
Maquam Creek
Stevens Brook
Mine Brook
Mill River
Stone Bridge Br
Trout Brook
Lamoille River,
CN)
Lamoille River,
(S)
Allen Brook
Malletts Creek
Pond Brook
Indian Brook
Peel Head Bay
Missisquoi Bay
Missisquoi Bay
Missisquoi Bay
Goose Bay
Missisquoi Bay
Donaldson Bay
Maquam Bay
Maquam Bay
Cheney Point, north
St. Albans Bay
St. Albans Bay
St. Albans Bay
N.E. Savage Sea
Beans Point, north
E. Savage Sea
S.E. Savage Sea
S.E. Savage Sea
S.E. Savage Sea
S.E. Savage Sea
Sandbar Wildlife
Refuge
Sandbar Wildlife
Refuge
Sandbar Wildlife
Refuge
737.20 071 Outer Malletts Bay
2.37
199.80
57.68
2.34
5.90
(E)862.25
CN)
(w)
3.07
2.60
0.59
1.62
22.68
2.45
24.78
1.28
0.18
. 10.77
0.40
4.50
0.06
0.21
0.23
0.26
1.20
092
092
091
091
091
092
092
093
093
088
088
088
083
083
083
080
080
080
080
080
080
080
080
080
080
0.27
0.22
1.38
0.37
0.70
4.71
0.04
18.90
4.37
12.14
1.96
0.15
0.27
1.45
0.54
072
072
072
072
072
072
072
072
072
072
072
072
072
072
072
Malletts Bay
Malletts Bay
Malletts Bay
Malletts Bay
Malletts Bay
Malletts Bay
Malletts Bay
Malletts Bay
Malletts Bay
Malletts Bay
Malletts Bay
Malletts Bay
Malletts Bay
MalleUs Bay
Malletts Bay
122
-------
CHAMPLAIN TRIBUTARIES, p. 3
68
69
70
71
72
73
74
75
76
77
78
79
80
81
82
D
D
D
D
D
D
D
D
D
D
D
D
D
D
4-1070
4-1090
4-1095
4-1110
4-1130
4-1150
4-1170
4-1190
4-1195
4-1210
4-1230
4-1250
4-1270
4-1290
4-1310
83
84
85
86
87
88
89
90
91
92
93
94
95
96
97
98
99
100
101
102
103
104
105
106
107
108
109
110
111
112
113
E
E
E
E
E
F
F
F
F
F
F
F
F
F
F
F
F
F
F
F
F
F
F
F
F
F
F
F
F
F
F
4-1313
4-1315
4-1317
4-1330
4-1335
4-1350
4-1370
4-1390
4-1410
4-1430
4-1435
4-1450
4-1451
4-1452
4-1453
4-1454
4-1455
4-1456
4-1457
4-1458
4-1459
4-1470
4-1471
4-1472
4-1473
4-1474
4-1475
4-1476
4-1477
4-1478
4-1479
Winooski River 1
Burlington sewer
Potash Brook
Munroe Brook
LaPlatte River
Holmes Creek
Thorpe Brook
Kimball Brook
Lewis Creek
Little Otter Cr.
Otter Creek
Hospital Creek
,092.00
0.14
-
0.79
0.36
7.49
0.40
0.96
0.38
0.12
0.17
5.32
53.48
0.20
0.52
1.43
0.21
0.22
6.00
0.50
5.23
2.80
85.80
70.50
950.50
0.24
0.59
0.70
0.64
0.52
0.21
0.43
0.15
0.16
0.21
0.12
0.16
0.12
0.03
0.07
0.03
0.15
0.90
0.68
0.08
3.26
037
033
033
033
033
030
030
030
030
030
030
030
030
030
021
021
021
021
021
020
016
016
016
016
017
015
014
014
012
012
012
012
012
012
012
on
on
on
on
on
on
on
on
on
on
on
Colchester Pt. , south
Burlington Bay
Burlington Bay
Burlington Bay
Burlington Bay
Shelburne Bay
Shelburne Bay
Bartletts Bay
Bartletts Bay
Bartletts Bay
Shelburne Bay
Shelburne Bay
Shelburne Bay
Shelburne Bay
Quaker Smith Pt.,
south
Meach Cove
Meach Cove
Hill Point, north
Hill Point, south
Converse Bay
Town Farm Bay
Town Farm Bay
Hawkins Bay
Hawkins Bay
Fort Cassin Pt.
Basin Harbor
Button Bay
Button Bay
Arnold Bay
White Bay
Spaulding Bay
Potash Point, north
Potash Point, north
Potash Point
Potash Point
Potash Bay
Potash Bay
Potash Bay
Potash Bay
Potash Bay
Potash Bay
Potash Bay
Potash Bay
Owls Head Bay
Crane Point, north
Chimney Point, north
123
-------
CHAMPLAIN TRIBUTARIES, p. 4
114
115
116
117
118
119
120
121
122
123
124
125
126
127
128
129
130
131
132
133
134
135
136
137
138
139
140
141
142
143
144
145
146
147
148
149
150
151
152
153
154
155
156
157
158
159
160
161
162
G
G
G
G
G
G
G
G
G
G
G
G
G
G
G
G
G
G
G
G
G
G
G
G
G
G
G
G
G
G
G
G
G
G
G
G
G
G
G
G
G
G
G
J
J
J
J
J
J
4-1490
4-1491
4-1493
4-1495
4-1497
4-1499
4-1510
4-1515
4-1530
4-1550
4-1570
4-1590
4-1610
4-1630
4-1650
4-1670
4-1690
4-1710
4-1730
4-1735
4-1750
4-1770
4-1790
4-1810
4-1830
4-1850
4-1870
4-1890
4-1910
4-1930
4-1950
4-1970
4-1990
4-2010
4-2030
4-2050
4-2070
4-2090
4-2110
4-2130
4-2150
4-2170
4-2190
4-0020
4-0040
4-ooea
4-0062
4-0064
4-0066
Whitney Creek 3.18
0.55
0.12
0.41
0.71
0.25
0.21
0.23
0.22
Braisted Brook 2.32
0.48
0.49
0.73
1.14
3.00
1.33
0.31
0.57
0.13
0.28
2.87
4.12
East Creek 34.75
0.72
Big Brook 1.30
0.49
0.85
0.67
2.04
1.82
0.87
1.67
0.18
Norton Brook 2.50
0.38
0.22
1.06
0.88
0.10
0.23
1.11
0.25
Poultney River 267.20
0.98
Great Chazy River 309.80
Little Chazy River 67.60
0.54
0.19
0.72
009
009
009
009
009
009
009
009
009
009
009
009
008
008
008
008
008
008
008
008
008
007
007
006
006
006
006
006
006
005
005
005
005
003
003
003
003
003
003
003
003
003
003
056
056
054
054
054
054
Willow Point, north
Willow Point, north
Willow Point
Plumies Point, north
Plumies Point, north
Pluroies Point, north
Plunjies Point
Pluraies Point, south
Giards Bay
Giards Bay
Leonard Bay
Leonard Bay
Lapharo Bay
Five Mile Point
Stony Cove
Stony Cove
Stony Cove
Watch Point, south
Watch Point, south
Watch Point, south
Hands Cove
Beadles Cove
Larrabees Point, south
Allen Bay, north
Stevens Bay
Benson Bay
Stony Point, north
Stony Point
Benson Landing
Red Rock Bay
Narrows of Dresden
Maple Bend
East Bay
Kings Bay
Kings Bay-
Long Point, south
Long Point, south
Trombley Bay
Trombley Bay
124
-------
CHAMPLAIN TRIBUTARIES, p. 5
163
164
165
166
167
168
169
170
171
172
173
174
175
176
177
178
179
180
181
182
183
184
185
186
187
188
189
190
191
192
193
194
195
196
197
198
199
200
201
202
203
204
205
206
207
208
J
J
J
J
J
J
J
K
K
K
K
K
K
K
K
K
K
K
K
K
K
K
K
K
K
K
K
K
K
K
K
K
K
K
K
K
K
K
K
K
L
L
L
L
L
L
4-0080
4-0100
4-0120
4-0140
4-0160
4-0162
4-0164
4-0130
4-0200
4-0202
4-0204
4-0206
4-0208
4-0210
4-0220
4-0240
4-0260
4-0262
4-0280
4-0300
4-0320
4-0340
4-0341
4-0342
4-0343
4-0344
4-0345
4-0346
4-0347
4-0348
4-0360
4-0362
4-0364
4-0380
4-0382
4-0384
4-0400
4-0402
4-0404
4-0420
4-0424
4-0440
4-0442
4-0460
4-0462
4-0464
4-0480
Guay Crpsk
Rile1, Broofc
Woocruff Pond
Scomotion -?-s
Saranac River
Salmon River
Silver Stream
Little Ausable R,
Dead Creek
Ausable R., (N]
Ausable R., (Sj
Marsh Brook
Watson Brook
Little Trout Br.
Warm Pond Creek
Big Brook
Bouquet River
0.21
3.50
1.12
10.71
1.58
0.42
C-12
10.34
":I9.20
C.25
0.43
0.61
0.81
0.63
64.10
6.83
60.70
1.29
513.45
3.62
1,40
0.09
0.08
0.25
0.31
0.29
0.24
0.07
0.40
4.99
0.34
0.65
1.02
0.26
0.37
12.73
0.52
0.87
2.56
0.35
278.05
0.68
2.45
0.23
1.98
3.26
054
054
054
C54
051
051
051
046
046
044
044
044
044
044
044
044
042
042
042
039
039
039
039
039
039
039
036
036
036
036
036
036
031
031
031
031
031
031
031
035
022
022
022
022
020
020
Trombley Bay
Monty Bay
Monty Bay
Monty Bay
Treadwell Bay
Martin Bay
Martin Point
Cumberland Bay
Cumberland Bay
Bluff Point, north
Bluff Point, south
Day Point
Ausable Point, north
Ausable Point
Ausable Point
Wickham Marsh
Port Kent
Trembleau Point
Trembleau Point
Trembleau Point
Cor1 ear Bay
Corlear Bay
Corlear Bay
Corlear Bay
Corlear Bay
Corlear Bay
Corlear Bay
Brown Point
Wfllsboro Bay
Willsboro Bay
Willsboro Bay
Willsboro Bay
Wfllsboro Bay
Willsboro Bay
Willsboro Bay
Willsboro Point
Bouquet River Pt.
Bouquet R. Pt., south
Essex
Whallon Bay
125
-------
CHAMPLAIN TRIBUTARIES, p. 6
209
210
211
212
213
214
215
216
217
218
219
220
221
222
223
224
225
226
227
228
229
230
231
232
233
234
235
236
237
238
239
240
241
242
243
244
245
246
247
248
249
250
251
252
253
254
255
256
L
L
L
M
M
M
M
M
M
M
M
M
M
M
M
M
M
M
M
M
M
M
M
M
M
N
M
M
M
N
M
M
N
N
M
N
M
M
N
N
N
M
N
N
N
N
N
N
4-0481
4-0482
4-0483
4-0484
4-0485
4-0486
4-0487
4-0488
4-0500
4-0520
4-0522
4-0540
4-0542
4-0544
4-0560
4-0562
4-0564
4-0565
4-0566
4-0580
4-0582
4-0600
4-0602
4-0604
4-0620
4-0622
4-0640
4-0660
4-0680
4-0682
4-0700
4-0702
4-0720
4-0721
4-0722
4-0740
4-0760
4-0762
4-0764
4-0780
4-0782
4-0800
4-0802
4-0804
4-0806
4-0820
4-0840
4-0860
Hoisington Brook
Stacy Brook
Beaver Brook
Mullen Brook
Kenney Brook
Mill Brook
Stony Brook
McKenzie Brook
Grove Brook
Putnam Creek
0.32
0.31
0.20
0.19
0.10
0.12
0.11
0.14
0.51
0.43
0.39
0.43
0.21
0.17
0.62
0.37
0.19
0.13
1.01
12.12
0.94
0.52
0.26
0.27
5.61
0.12
4.60
5.64
1.46
0.09
0.85
0.92
27.99
0.21
0.19
1.79
9.92
0.76
0.20
7.57
1.03
2.36
2.93
0.13
0.10
0.13
0.47
61.33
020
020
020
017
017
017
017
017
017
015
015
015
015
015
015
013
013
013
013
013
013
012
012
012
012
012
012
on
on
on
on
on
on
on
on
on
010
010
010
010
010
010
010
009
009
009
009
009
Whallon Bay
Whall on Bay
Wtiallon Bay
Ore Bed Point
Louis Clearing Bay
Louis Clearing Bay
Louis Clearing Bay
Snake Den Harbor
Barn Rock Harbor
Rock Harbor
Rock Harbor
Hunter Bay
Hunter Bay
Northwest Bay
Northwest Bay
Northwest Bay
Northwest Bay
Northwest Bay
Northwest Bay
Northwest Bay
Northwest Bay
Moore Point
Coll Bay
Coll Bay
Coll Bay
Coll Bay
Stevenson Bay
Mullen Bay
Mullen Bay
Craig Harbor
Port Henry
Port Henry
Port Henry
Port Henry
Port Henry
Bulwagga Bay
Bulwagga Bay
Bulwagga Bay
Bulwagga Bay
Bulwagga Bay
Bulwagga Bay
Murdocks Point, south
Murdocks Point, south
School house Bay
Porters Marsh
Gilligans Bay
126
-------
CHAMPLAIN TRIBUTARIES, p. 7
257
258
259
260
261
262
263
264
265
266
267
268
269
270
271
272
273
274
275
276
277
278
279
280
281
282
283
284
285
286
287
288
289
290
291
292
293
294
295
296
N
N
N
N
N
N
N
N
N
N
N
N
N
N
N
N
N
N
N
N
N
N
N
N
>N
N
N
N
N
N
N
N
N
N
N
N
N
N
N
N
4-0862
4-0864
4-0880
4-0900
4-0920
4-0940
4-0960
4-0980
4-1000
4-1020
4-1040
4-1042
4-1060
4-1064
4-1080
4-1100
4-1120
4-1140
4-1160
4-1162
4-1180
4-1182
4-1200
4-1220
4-1240
4-1260
4-1280
4-1282
4-1284
4-1285
4-1286
4-1 300
4-1320
4-1340
4-1360
4-1380
4-1400
4-1420
4-1440
4-1460
Grant Brook
Fivemile Creek
Ticonderoga Creek
Charter Brook
Nigger Marsh
Mill Creek
Chubbs Brook
Pease Brook
Pine Lake Brook
297
4-1480
South Bay portal
Mettawee River
and Canal
0.44
0.32
4.31
0.09
9.20
0.64
1.00
1.04
256.30
6.81
0.36
0.10
5.35
1.10
11.26
0.22
0.10
0.12
0.39
0.19
0.13
0.16
0.56
1.83
2.16
0.27
0.51
0.78
0.85
0.58
2.49
2.00
3.58
0.38
0.48
0.55
0.44
0.63
0.25
39.90
099
008
008
008
008
008
008
008
007
007
006
006
006
006
006
006
005
005
005
005
005
005
005
005
005
003
003
003
003
003
003
003
003
003
003
003
003
003
003
003
Spar Mill Bay
Miller Marsh
Stony Point
Kerby Point, north
Kerby Point, north
Ticonderoga Bay
Charter Marsh
Gourlie Point, north
Gourlie Point, south
Sixmile Point
Mill Bay
Mill Bay
Pulpit Point
Chi 1 son Bend
Chi 1 son Bend
Narrows of Dresden
Barrel Bay
Maple Bend
Maple Bend
Maple Bend
Maple Bend
Maple Bend
Cat Den Bay
Duso Marsh
423.62 003
127
-------
APPENDIX C
Lake Champlain tributaries draining basins of ten square miles
Name
Winooski River
Otter Creek
Nissisquoi River
Lamoille River
Saranac River
Ausable River
Metawee River and
Canal
Great Chazy River
Bouquet River
Poultney River
Ticonderoga Creek
Pike River
Lewis Creek
Little Otter Creek
Little Chazy River
Saloon River
Putnam Creek
Little Ausable
River
Rock River
Laplatte River
Scoirotion Creek
South Bay Portal
East Creek
Mill Brook
Mill River
Stevens Brook
Malletts Creek
Warm Pond Creek
Mill Creek
Hoisington Brook
Indian Brook
Mud Creek
Stone Bridge Brook
Riley Brook
Table 2.
or more.
District
D
F
A
C
K
K
P
J
L
G
N
G
F
F
J
K
N
K
A
D
K
N
G
M
B
B
C
K
N
M
C
H
B
J
Lake
No.
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.
Champ
Code
1070
1430
0410
0790
0200
0280
1480
0040
0440
2190
1000
0270
1390
1410
0060
0220
0860
0260
0330
1270
0180
1460
1790
0720
0570
0530
0930
0400
1080
0580
0950
0170
0610
0144
Region
Vt. 1
Vt.
Vt./Que.
Vt.
NY
NY
NY./Vt.
NY./Vt.
NY
Vt.
NY
Que.
Vt.
Vt.
NY
NY
NY
NY
Que./Vt.
Vt.
NY
NY
Vt.
NY
Yt.
Vt.
Vt.
NY
NY
NY
Vt.
Vt.
Vt.
NY
Area
Mi2
,092.0
950.5
862.3
737.2
649.2
513.5
423.6
309.8
278.1
267.2
256.3
199.8
85.8
70.5
67.6
64.1
61.3
60.7
57.7
53.5
40.3
39.9
34.8
28.0
24.8
22.7
18.9
12.7
12.4
12.1
12.1
11.6
10.8
10.7
Accum.
Area
1,092.0
2,042.5
2,904.8
3,642.0
4,291.2
4,804.7
5,228.3
5,538.1
5,816.2
6,083.4
6,339.7
6,539.5
6,625.3
6,695.8
6,763.4
6,827.5
6,888.8
6,949.5
7,007.2
7,060.7
7,101.0
7,140.9
7,175.7
7,203.7
7,228.5
7,521.2
7,270.1
7,282.8
7,295.2
7,307.3
7,319.4
7,331.0
7,341.8
7,352.5
Accum. %
Total Area
14.4
26.9
38.3
48.0
56.6
63.4
69.0
73.0
76.7
80.2
83.6
86.3
87.4
88.3
89.2
90.1
90.9
91.7
92.4
93.1
93.7
94.2
94.6
95.0
95.3
95.6
95.9
96.1
96.2
96.4
96.5
96.7
96.8
97.0
128
-------
APPENDIX D
PRIMARY DATA ON MEDIAN CONCENTRATIONS OF TOTAL PHOSPHATE-PHOSPHORUS OF THE
MAJOR TRIBUTARIES IN EACH DISTRICT, AND THE CALCULATIONS FOR LOADING OF
TOTAL PHOSPHORUS FOR THE STREAMS IN THE DISTRICTS.
In the following sequence of tables is presented, for each District, the
name of the tributary with its drainage area, the median concentration of
total P04-P values measured between 1970 and 1974, the number of measurements
made, and the calculated load of PO"*-P in Kg/Yr (Refer to page ). Below
each table are the calculations that provide estimates of direct loading
from the District, and the estimated loading from the unmonitored tributar-
ies. Table headings are given only for the first table.
Table D-l. District A, Missisquoi. Discharge Coef., 1.3
Tributary Area mg/1 No. Kg/PO*-P/Yr Kg/P/Sq. Mi.
Pike River
Rock River
Missisquoi River
Charcoal Brook
199.80
57.68
862.25
3.07
0.080
0.124
0.084
0.086
11
12
7
5
14,283.04
6,391.20
64,712.47
306.70
71.5
110.8
75.1
99.9
Weighted District concentration:
Total tributary loading
Diffuse loading
Total District loading
0.085 mg/1
85,693.41
1,228.33
86,921.74
Table D-2. District B; Northeast and St. Albans. Disch. Coef. 1.1
Stevens Brook 22.68 0.752 9 16,764.44
Mill River 24.78 0.040 10 974.29
Stone Bridge Brk. 10.77 0.106 12 1,122.15
Trout Brook 4.50 0.078 12 345.01
739.2
39.3
104.2
76.7
Weighted District concentration:
Total tributary loading
Diffuse loading
Total District Loading
0.311 mg/1
19,205.89
3,357.47
22,563.36
129
-------
Table D-3. District C; Larooille-Malletts Bay. Disch. Coef . : 1.4
Lamoille River
Allen Brook
Mai letts Creek
Pond Brook
Indian Brook
er 737.20 0.041
4.71 0.087
tek 18.90 0.065
4.37 0.053
: 12.14 0.037
11
17
16
13
16
Weighted mean concentration:
Total tributary loading
Diffuse loading
Total District loading
37,812.26
512.63
1,536.88
302.78
573.97
0.042
40,738.52
392.03
41,130.55
51.3
108.8
81.3
69.3
47.3
Table D-4. District D: Burl ing ton- Winooski. Disch. Coef. : 1.4
Minooski River 1,092.00 0.073 11 99,726.13 91.3
Potash Brook 7.49 0.111 19 742.92 99.2
Nunroe Brook 5.32 0.095 18 632.26 118.8
LaPlatte River 53.48 0.130 20 8,697.58 162.6
Weighted mean concentration: 0.076
Total tributary loading 109,798.89
Diffuse loading 662.91
Total District loading 110,461.80
Table D-5. District F: Otter Creek- Vergennes. Disch. Coef. : 1.3
Otter Creek 950.50 0.103 11 113,728.19 119.7
Lewis Creek 85.80 0.058 17 5,780.88 67.4
Little Otter Creek 70.50 0.132 17 10,810.40 153.3
Thorpe Brook 5.23 0.122 17 741.21 141.7
Hospital Creek 3.26 0.134 7 507.46 155.7
Weighted mean concentration: 0.102
Total tributary loading: 131,568.14
Diffuse loading 2,172.59
Total District loading: 133,740.73
Table D-6. District H: The Islands. Disch. Coef. : 1.1.
Mud Creek 11.6 0.194 5 2,212.01 190.7
Weighted mean concentration: 0.194
Total tributary loading: 2,212.01
Diffuse loading 2,069.00
Total District Loading 4,281.01
130
-------
Table D-7. District J: Chazy. Disch. Coef. 1.15.
Great Chazy River 309.80 0.130 7
Little Chazy River 67.90 0.091 7
Weighted mean concentration:
Total tributary loading:
Diffuse loading
Total District loading:
35,988.20
6,321.52
0.123
42,309.72
7,933.27
50,242.99
116.2
93.5
Table D-8. District K: Saranac-Plattsburgh. Disch. Coef. 1.1
Scomotion Creek 40.34 0.106 5 4,203.10 104.2
Salmon River 64.10 0.061 6 3,843.40 60.0
Saranac River 649.20 0.108 8 68,917.63 106.2
Silver Stream 6.83 0.094 7 631.07 92.4
Little Ausable R. 60.70 0.231 5 13,782.52 227.1
Ausable River 513.45 0.067 7 33,814.35 65.9
Weighted mean concentration: 0.095
Total tributary loading: 125,192.07
Diffuse loading: 2,737.88
Total District loading: 127,929.95
Table D-9. District L: Bouquet. Disch. Coef. 1.15
Bouquet River 278.05 0.068 7 19,429.65 69.9
Weighted mean concentration: 0.068
Total tributary loading: 19,429.65
Diffuse loading: 660.14
Total District loading 20,089.79
Table D-10. District M: Port Henry. Disch. Coef. 1.2
Hammond Brook
Stacy Brook
Beaver Brook
Mullen Brook
Mill Brook
k 12.12 0.093
5.61 0.122
4.60 0.188
5.64 0.020
27.99 0.212
6
5
4
6
6
Weighted mean concentration:
Total tributary loading:
Diffuse loading:
Total District loading
1,208.65
733.90
927.33
120.96
6,362.90
0.156
9,353.74
6,281 .82
1mm f**\T* T~ C
5,635.56
99.7
130.8
201.6
21.4
227.3
131
-------
APPENDIX E
INVENTORY OF POINT SOURCE LOADINGS IN THE CHAMPLAIN DISTRICTS
Definitions
Point sources are defined as those discharges into a receiving water from
a single pipe or conveyor. Non Point sources are those discharges spread
over a large area, such as runoff from the land through channeled or unchan-
neled pathways, sheet runoff, drainage from highways, and ground water seep-
age. It also includes input from precipitation (Loehr, 1974). In addition
to these standard terms, the term semi point source refers to those situa-
tions where distinct non-point sources are concentrated in a short stretch of
a stream. Specifically it distinguishes those small communities with septic
tanks, leach fields, and other individualized means of waste disposal clus-
tered in a small area.
Calculation of loading
The amount of loading is a function of disposal type, and distance from
the lake. In calculating loading, a base value of 1.6 kg/P/capita/yr was
used, reduced according to the following formula:
kg/C/yr
a. Semi point source communities with individual means of disposal: 0.75
b. Communities on a sewer system without any treatment: 1.60
c. Communities with primary treatment facilities, less 10%: 1.44
d. Communities with secondary treatment facilities, less 20%: 1.28
These values are further scaled down according to distance from the lake
as follows:
0-25 river miles 100% of value
25-50 river miles 75% of value
50 and more miles 50% of value
132
-------
The following table summarizes the constants used in calculating load-
ings; these constants, when multiplied by the population, yield the estimated
phosphorus loading in kg/yr:
Disposal River miles from Lake Champlain
class 0-25 25 - 50 50 plus
a 0.75 0.5625 0.375
b 1.60 1.20 0.750
c 1.44 1.08 0.720
d 1.28 0.96 0.64
133
-------
APPENDIX E
POINT SOURCE INVENTORY
Table 1. Inventory of contributions of phosphorus from District A (Missis-
quoi). Loading values in kg/yr of total PO.-P.
Kg/yr Phosphorus loading
Disposal Type from
Community Miles Popul. abed
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.
Swan ton 7.5
Pike River c 8.0
Venise en Quebec 1.0 e
Phillipsburg 1.0
Highgate Cntr.
E. Highgate 18.6
Sheldon 25.2
Sheldon Sprgs. 26.0
Fairfield Sta. 31.6 e
Fairfield 31.9
E. Fairfield 31.9
Enosburg Falls 33.5
E. Berkshire 40.4 e
E. Fletcher 41.6 e
Montgomery 45.7
Richford 45.9
Montgomery Ctr. 47.8
Bakers field c.50.0
E. Richford 52.3
Glen Sutton 52.4 e
Dun kin
Highwater e
N. Troy 67.9
Troy 77.3
Westfield 81.1
Lowell 87.8
Newport Center 75.8
Mansonville, 50 +
Que.
S. Bolton
Bolton Centre e
Eastman 52.7
Abercorne, Que.
Sutton, Que.
Notre Dame Standbg
2,630
250
100
391
350
200
250
568
50
180
182
1,266
50
50
200
1,527
275
200
70
100*
486
100
774
253
120
160
700
725 +
436
100
681 +
368
1,684
100
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
_
75
293
_
150
188
28
101
_
-
28
28
113
-
155
113
26
38
182
38
-
-
25
60
-
272
164
38
-
-
-
-
3,366
200
_
_
560
_
_
682
_
_
218
1,519
_
-
-
1,466
-
-
_
_
_
-
619
202
-
-
560
-
-
-
511
236
1,078
80
Canada
Canada
Canada
Canada
Canada
Canada
Canada
Canada
Canada
Canada
134
-------
APPENDIX E
Table 1 Ccont'd).
Load
Community
35.
36.
37.
38.
Freilighsburg
Bedford, Que.
Standbridge
St. Armond
Table 2. Inventory
Miles
Popul .
345
2,876
200
100
a
X
X
of contributions of
Bay-Lamoille). Loading
1.
2.
3.
4.
5.
6.
7.
8.
9.
10.
11.
12.
13.
14.
15.
16.
17.
18.
19.
20.
21.
22.
23.
24.
Milton
Fairfax
Cambridge
Jeffersonville
Westford
Jericho VI g.
Watervi 1 1 e
Belvidere Cr.
7.
16.
23.
31.
20.
30.
35.
40.
Johnson College 41.
E. Johnson
Belvidere Ctr.
Johnson
Hyde Park
N. Hyde Park
Morris ville
Underhill Ctr.
Wolcott
Eden
Eden Mills
N. Wolcott
Hardwick
E. Hardwick
Greensboro Bnd
Craftsbury
42.
42.
41.
47.
48.
50.
35.
59.
53.
54.
61.
66.
values in
6
5
5
0
2
3
6
0
0
5
8
0
0
8
3
9
0
4
8
0
5
71.0
. 74.
94.
5
0
1,164
500
235
383
90
275
397
e 100
250
e 100
179
1,296
418
100
2,116
1,198
676
513
e 100
e 100
1,500
195
e 100
175
kg/yr
X
X
X
X
X
X
X
X
X
X
bed semi -point point
X
X
phosphorus from
of total P04-P.
X
X
X
X
X
X
X
X
X
X
X
X
X
X
_
276
2,071
75
38
District
-
-
176
-
68
155
-
56
-
56
-
-
^ ^
56
—
674
—
on
38
o o
38
—
oo
38
"
-
-
Canada
Canada
Canada
C (Malletts
1,862
800
-
460
-
-
476
-
270
—
215
1,244
502
™
2,031
C" rt*7
507
*\C\ C
385
~
IT 1C
,125
1 A C
146
1 01
131
135
-------
APPENDIX E
Table 3. Inventory of the contributions of total phosphate-phosphorus from
District D (Burlington-Winooski). Loading values in kg/P/yr.
Loadings
No.
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.
Community
WTP, S. Burl.,
Bartl .
WTP, Shelburne
WTP. Burlington,
main
WTP. Burlington,
N. End
Hinsburg
Shelburne FDI2
WTP, Burlington,
Rvrsde
WTP, Winooski
City
WTP, S. Burl.,
Airpt.
WTP, Colchester
FD#1
Essex Town
Essex Jet., VI g.
Essex Jet. , IBM,
Dom.
Williston
Richmond VI g.
Waterbury VI g.
Vt. St. Hospital
Stowe Village
Jonesville
Montpel ier
Williams town
Berlin
Barre City
Northfield VI g.
Webs tervi lie
E. Barre
Plainfield Vlg.
Marshfield
Miles
0
0
0
2.1
10.0
4.0
9.6
9.7
11.3
12.4
14.1
17.8
18.9
20.7
29.7
43.2
44.1
53.7
54.7
58.5
59.1
61.5
63.8
66.2
67.0
71.1
80.4
Popul .
1,000
1,328
21,500
7,000
350
800
9,000
7,400
5,600
2,200
1,000
6,350
875
300
926
2,800
860
1,760
e 50
8,860
510
1,500
10,575
3,300
e 50
4,430
e 100
322
abed
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
136
Semi-Pt. Pt. sources
1,280
1,700
27,520
8,960
448
1,152
11,520
9,472
7,168
3,520
1,444
9,144
1,120
225
889
2,688
929
1,320
19
6,379
326
950
7,514
2,112
488
3,190
282
241
-------
Appendix E
Table 3 (cont'd).
Loadings
No. Conmunlty Miles Popul. abed Semi-Pt. Pt. sources
29.
30.
31.
32.
Cabot
Moretown
Waitsfleld
Duxbury
85.4
50 +
50 +
50 + e
244
150
175
50
X
X
X
X
102
56
66
19
_
-
-
-
Totals: 487 111,756=
112,243 kg
Table 4. Inventory of the contributions of total phosphate-phosphorus from
District F (Otter Creek-Vergennes). Loading values in kg/P/yr.
1. Vergennes City 7.3 2,242 X - 3,228
2. Vergennes City 7.3 - X - o°4
3. Wey bridge e 50 X 38 -
4. Middlebury 25.7 3,688 X - 3,983
5. Leicester Jet. 100 X 56 -
6. Brandon 49.6 1,720 X - 1,858
7. Otter Valy Un. 51.7 e 600 X 225
8. Ferrisburg 170 X 64 -
9. Pittsford 62.6 682 X - 436
10. Proctor 63.4 1,978 X - 1.424
11. Rutland Twn, 70.6 2,248 X - 1,619
12. Rutland City 71.8 19,293 X - 13,891
13. W. Rutland 72.6 2,250 X - 1,140
14. Walingford 84.4 1,676 X - 1.085
15. Panton 50 + 35 X 13
16. Bridgeport 50 + e 100 X 38
17. Shoreham 50+ 130 X 49
18. Shoreham Ctr. 50 + e 50 X 19
19. Whiting 50 + 70 X 26 -
20. Sudbury 50 + 50 X *
21. Cornwall 50 + 40 X *
22. W. Cornwall 50 + e 40 X j£
23. New Haven Mills 50+ 150 X **> -
24. Bristol 50+ 1,421 X - 1.066
25. W. Lincoln 50 + 70 X IQ ~
26. Lincoln 50 + e 50 X 9
27. S. Lincoln 50 + 30 X '"
28. E. Middlebury 50 + 320 X 120
29. Ripton 50+ 70 X 26
30. Salisbury 50 + 130 X **
Totals: 39,453 884 30,394
137
-------
Appendix E
Table 5. Inventory of the contributions of total phosphate phosphorus from
District S (South end). Loading values in kg/P/yr.
No. Comnunity
Miles Popul. abed
Loading (*)
Semi-Pt. Point
Poultney River:
1.
2.
3.
4.
5.
6.
7.
8.
9.
Benson
Fair Haven
Hortonville
Hydesville
Castelton
Poul tney
E. Poultney
E. Hubbardton
W. Rutland
15.0
16.5
20.0 e
20.4
24.0
26.1
28.0
31.6 e
34.0
583
2,777
100
300
2,837
3,217
300
100
2,302
X
X
X
X
X
X
X
X
X
_
-
75
225
-
-
-
56
1,295
746
3,555
—
-
3,631
3,088
360
-
-
*
*
*
*
*
*
*
*
*
Subtotal:
Metawee River:
12,516
Subtotals:
10,054
1,651 11,380
1.
2.
3.
4.
5.
6.
7.
8.
9.
10.
11.
12.
13.
14.
Pawlet
Wells
Dorset
Rupert
Granville
N. Rupert
Whitehall
Middle Granville
N. Granville
Corns toe k
Fort Anne
Smith's Basin
Kings bury
Queensbury
e
e
e
e
e
e
1,184
200
300
150
2,784
50
3,764
869
50
100
453
50
50
50
X
X
X
X
X
X
X
X
X
X
X
X
X
X
-
150
225
113
-
38
-
652
38
75
-
38
38
38
1,894
-
-
-
4,454
-
6,022
-
-
-
725
-
-
-
*
*
*
*
*
1,405 13,095
138
-------
Appendix E
Table 5 (cont'd).
Loading
No. Community Miles Popul. abed Semi-Pt. Point
Lake George South Shore
1.
2.
3.
4.
5.
6.
7.
8.
9.
10.
Ticonderoga
Chilson
demons
Dresden Station
Putnam
Putnam Station
Wright
District:
Chipman's Point
Ironville
Crown Point Center
Subtotals:
Grand totals:
Table 6. Inventory
3,568
e 50
500
e 50
e 100
e 50
e 50
100
e 50
50
4,568
27,138
X
X
?
X
X
X
X
X
X
X
38
_
38
75
38
38
75
38
38
378
3,434
5,318
800
_
^
..
_
-
_
-
6,118
30,593
of contributions of phosphorus from District J (Chazy-
Rouses Point). Values i
No.
1.
2.
3.
4.
5.
6.
7.
8.
9.
10.
11.
12.
Community
Rouses Point,
WTP
Coopersville
Chazy
Champlain
West Chazy
Ingraham
Moers
Altona
Alder Bend
Crazy Lake
Ellenburg Depot
Ellenburg
Total s :
n
Miles
0
1
5
6
12
-
18
24
_
37
37
39
.2
kg/yr of
Popul .
2,320
200
.0 600
.5
.0
.9
.9
.2
.7
.7
1,620
566
e 50
536
400
e 50
e 100
e 100
e 150
6,682
total P04-P.
Disposal Type
abed
X
X
X
X
X
X
X
X
X
X
X
X
Annual
Serai-point
^
150
-
_
-
38
-
300
38
56
56
™
638
Load
Point
2,970
-
960
2,074
906
-
858
-
-
-
—
180
7,948
139
-------
Appendix E
Table 7. Inventory of point source contributions of phosphorus from Dis-
trict K (Saranac-Ausable-Plattsburg). Values in kg/yr of total PO.-P.
Disposal class Annual Load
No. Community Miles Popul. abed Semi-point Po i n t
Saranac River:
1.
2.
3.
4.
5.
6.
7.
8.
9.
10.
11.
12.
13.
14.
15.
Plattsburg Town
WTP
Plattsburgh
Morrisonville
Picketts Corner
Saranac
Moffitsville
Dannemora
Village
Dannemora Prison
Redford
Clay burg
Franklin Falls
Trudeau
River view
Bloomingdale
Saranac Lake
Subtotals:
0 1
0.1 30
6.6 5
10.9 e
16.7
18.8 e
20.0 1
20.0 3
23.3 e
25.3 e
e
e
29.3 e
45.0
55.0 6
,000
,000
,300
50
400
50
,800
,300
50
50
50
50
100
536
,915
X
X
X
X
X
X
X
X
X
X
X
X
X
X
X
—
-
-
38
-
38
-
-
38
28
28
28
56
-
-
1,440
38,400
8,480
-
640
—
2,592
4,752
-
-
-
-
-
643
4,979
Ausable River:
1.
2.
3.
4.
5.
6.
7.
8.
9.
10.
11.
12.
13.
14.
Ausable Chasm
Keeseville
Clintonville
Rogers
Ausable Forks
Hasel ton
Jay
Upper Jay
Wilmington
Keene
Keene Valley
Lake Placid
North Elba
St. Huberts
4.1 ee
5.2 2
11.7 e
13.2 e
17.3
e
22.3
25.5 e
26.4
31.5 e
36.5
42.5 2
e
38.5 e
100
,213
50
50
500
50
400
50
700
50
500
,731
50
50
X
X
X
X
X
X
X
X
X
X
X
X
X
X
75
-
38
38
-
38
-
28
-
28
-
-
28
28
^
2,833
—
-
800
-
640
-
840
-
600
2,949
-
-
Subtotals:
140
-------
Appendix E
Table 7 (cont'd).
Disposal class Annual Load
No. Community _ Miles Popul . abed Semi -point Point
1.
2.
3.
Lapham Mills
Peru
Harkness
e
e
100
2,800
50
X
X
X
75
-
38
«•
4,032
-
Subtotals:
Salmon River:
1.
2.
3,
S. Plattsburgh
Schuyler Falls
Peasleeville
2.
6.
11.
5
1
2
e
e
e
100
100
50
X
X
X
75
75
38
.
-
•"
Subtotals:
Totals: 60,345 856 74,620
Table 8. Inventory of point source contributions of phosphorus from District
L CBouquet). Values in kg/yr of total P04-P.
1. Essex 0 e 100 X 75
2. Bouquet 8.1 e 100 X 75
3. Whallensburg 11.9 e 50 X 38
4. Wadhams 15.0 e 50 X 38
5. Reber e 50 X 38
6. Lewis e 50 X 38 -
7. Elizabethtown 22.3 607 X - 971
8. New Russia 28.0 e 50 X oo "
9. Euba Mills e 50 X <&
Totals: 1,107 358 971
Table 9 Inventory of point source contributions of phosphorus from District
M (Westport-Port Henry). Values in kg/yr of total P04-P.
1. Westport 0 673 X - 861
2. Port Henry 0 1,800 X - Z,592
3. Willsboro 3.0 838 X - J.341
4. Moriah, SD#2 2.0 2,900 X - 4,175
5. Moriah, SD#1 4.0 270 X - *»
Totals:
6,481 9'358
141
-------
TECHNICAL REPORT DATA
(Please read Instructions on the reverse before completing)
1. REPORT NO.
EPA-600/3-77-106
3. RECIPIENT'S ACCESSION NO.
4. TITLE AND SUBTITLE
The Trophic Status and Phosphorus Loadings of Lake
Champlain
5. REPORT DATE
September 1977
6. PERFORMING ORGANIZATION CODE
7. AUTHOR(S)
E. B. Henson and Gerhard L. Gruendling
8. PERFORMING ORGANIZATION REPORT NO.
9. PERFORMING ORGANIZATION NAME AND ADDRESS
University of Vermont
Burlington, VT 05401
and
State University of New York
Pittsburgh, NY 12901
10. PROGRAM ELEMENT NO.
1BA208
11. CONTRACT/GRANT NO.
CC6991931-J
CC6991932-J
12. SPONSORING AGENCY NAME AND ADDRESS
Environmental Research Laboratory—Corvallis, OR
Office of Research and Development
U.S. Environmental Protection Agency
Corvallis, Oregon 97330
13. TYPE OF REPORT AND PERIOD COVERED
Final - 08/76 - 08/77
14. SPONSORING AGENCY CODE
EPA/600/02
15. SUPPLEMENTARY NOTES
This report is co-sponsored by Region 1, U.S. Environmental Protection Agency
J.F. Kennedy Federal Building, Boston, MA 02203
16. ABSTRACT
Information on the trophic status of the several basins of Lake Champlain is
summarized, the amounts and distribution of total phosphorus loading into the lake
are evaluated, and recommendations for further study are made. The general objective
is to provide basic background information to assist in the development of nutrient
control policies for proper lake management. There is a short discussion of the
role of phosphorus in the lake ecosystem, how recent thinking is leading to studies
of eutrophication models, and a presentation of estimated historical loadings.
Ongoing studies by various agencies and universities are listed and an extensive
bibliography is provided.
17.
KEY WORDS AND DOCUMENT ANALYSIS
DESCRIPTORS
b.IDENTIFIERS/OPEN ENDED TERMS C. COS AT I Field/Group
Lakes
Limnology
Phosphorus
Algae
Aquatic Biology
Eutrophication
Trophic Level
02H
04A
05C
07B
18. DISTRIBUTION STATEMENT
RELEASE UNLIMITED
19. SECURITY CLASS (This Report}
UNCLASSIFIED
21. NO. OF PAGES
153
20. SECURITY CLASS (Thispage)
UNCLASSIFIED
22. PRICE
EPA Form 2220-1 (Rev. 4-77)
142
•fi U. S. GOVtSNMcNT PRINTING OP^lCt- !977—7Q-}-~'T6 224 REGION 10
------- |