EPA 660/ 3-73-021
DECEMBER 1973
Ecological Research Series
1
FIRST ANNUAL REPORTS
Of THE EPA
IFYGL PROJECTS
No.3
tfatipai fnvftORffieflfaf Research Centei
Bffice af Research MJmlopesl
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EPA~6$3-73-021
December 1973
FIRST ANNUAL REPORTS OF THE EPA
IFYGL PROJECTS
Program Element 1B1026
U.S. Environmental Protection Agency
Grosse lie Laboratory
Office of Research and Development
9311 Groh Road
Grosse He, Michigan 48138
NATIONAL ENVIRONMENTAL RESEARCH CENTER
OFFICE OF RESiEARCH 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
five series. These five broad categories were established to
facilitate further development and application of environmental
technology. Elimination of traditional grouping was consciously
planned to foster technology transfer and a maximum interface
in related fields. The five series are:
1. Environmental Health Effects Research
2. Environmental Protection Technology
3. Ecological Research
4. Environmental Monitoring
5. Socioeconomic Environmental Studies
This report has been assigned to the ECOLOGICAL RESEARCH STUDIES
series. This series describes research on the effects of pollution
on humans, plant and animal species, and materials. Problems
are assessed for their long- and short-term influences. Investigations
include formation, transport, and pathway studies to determine
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.
EPA REVIEW NOTICE
This report has been reviewed by the Office of Research and
Development, 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.
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PREFACE
The U.S. Chemistry-Biology Program in IFYGL
The field data collection phase of an intensive multidisciplinary
study of Lake Ontario was conducted in 1972-73 by agencies of the United
States and Canada. The scientific program was designed to further the
basic scientific knowledge of the Great Lakes, to provide the basis for
improved water quality and quantity management, and to comprehend the broad
impact of the lake on the environment of the Great Lakes Basin.
The Chemistry-Biology Program had three major objectives—material
balance studies, evaluation of the current ecologic status of the lake,
and the development of predictive mathematical models. The chemistry
program was conducted at the Rochester Field Office of Region II. The
biologically related studies were mainly performed through ten grants
administered by the Grosse lie Laboratory. This document is a first
attempt to bring together the annual.reports prepared by the Grantees.
It is hoped that distribution of these annual reports will provide for
a more complete analysis of the data collected during IFYGL.
Nelson A. Thomas
U.S. Co-Chairman
Biology-Chemistry Panel
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CONTENTS
Preface
Sections
iii
I Grant 800496
II Grant 800536
III Grant 800537
IV Grant 800605
V Grant 800608
VI Grant 800609
VII Grant 800610
VIII Grant 800646
New York State Department of Conservation
Hetling, Leo
"Occurrence and Transport of Nutrients and
Hazardous Polluting Solutions in Genesee
River Basin"
State University of New York at Albany
McNaught, Donald C.
"Zooplankton Production in Lake Ontario as
Influenced by Environmental Perturbations"
University of Wisconsin
Lee, G. Fred
"Algal Nutrients Availability and Limitation
in Lake Ontario During IFYGL"
University of Michigan
Stoermer, Eugene F.
"Analysis of Phytoplankton Composition and
Abundance During IFYGL"
University of Wisconsin
Lee, G. Fred
"Exploration of Halogenated and Related
Hazardous Chemicals in Lake Ontario"
University of Wisconsin
Armstrong, D. E.
"Phosphorus Release and Uptake by Lake
Ontario Sediments (IFYGL)"
Manhattan College
Thomann, Robert A.
"Mathematical Modeling of Eutrophication of
Large Lakes"
State University of New York at Oswego
Moore, Richard B.
"A Near-Shore Survey of Eastern Lake Ontario"
Sub Contract to Grant 800646
State University of New York at Albany
McNaught, Donald C.
"Planktonic Rotifera and Crustacea of the
Lake Ontario Inshore Region"
29
71
90
110
123
141
172
191
iv
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CONTENTS, Cent.
Sections Page
IX Grant 800701 State University College at Buffalo 218
Sweeney, Robert A.
"Analysis and Model of the Impact of Discharges
from the Niagara and Genesee Rivers of the
Near-Shore of Lake Ontario"
X Grant 800778 Enviromental Research Institute of Michigan 330
Polcyn, F. C.
"A Remote Sensing Program for the Determination
of Cladophora Distribution in Lake Ontario
(IFYGL)"
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OCCURRENCE AND TRANSPORT OF NUTRIENTS
AND HAZARDOUS POLLUTING SUBSTANCES
GRANT NUMBER: 800496
Progress Report
April 1972 - August 1973
Environmental Quality Research Unit
New York State Department of Environmental Conservation
Albany, Nfew York
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TABLE OF CONTENTS
;I INTRODUCTION 4
II PROJECT OBJECTIVES 5
III OVERALL PROJECT PLAN 5
IV SITE SELECTION 7
A. Genesee River Basin 7
B. Specific Site Selection 9
1. Water Quality Network 9
2. Point Source Network 12
V FIELD & LABORATORY METHODS 15
A. General 15
B. Sample Collection and Storage 15,
1. Water Samples 15
2. Sediment Samples 17
C. Analytical Methods 17
1. Water Samples 17
2. Sediment Samples 17
VI TIME AND COST ANALYSIS 19
VII PROGRESS TO DATE 19
A. Historical Review 19
B. Partial Sampling Results 19
C. Problems 19
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VIII FUTURE PLANS 21
A. Field Work 21
B. Data Analysis 21
1. Literature Data 21
2. Water Quality Nework Data 21
3. Point Source Stream Data 22
IX TABLES 23
X FIGURES 25
XI BIBLIOGRAPHY 28
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INTRODUCTION
The central objective of the International Field Year for
the Great Lakes (IFYGL) is the development of a sound scientific basis
for water resource management on the Great Lakes as an aid in solving
problems of water quality and quantity . In order to understand the mass
and energy transport into, within and out of Lake Ontario, a major portion
of the stuu-/ must be the determination and quantification of the significant
input sources, such as air and water-borne material.
Since the bulk of niass inputs -.0 Lake Ontario is likely to be
water-borne, a watershed study which includes rates of contaminant discharge
originating within an area and the transport, decay and storage of the
contaminant through the watercourse appears to be in order.
The transport and decay of the traditional polluting substances
(BOD, MPN, etc.) within streams is fairly well understood so that such
materials dc not need extensive study. However, modern society also
disposes of nutrient material and a great variety of synthetic, hazardous
materials whose fate in nature is poorly known. Many industrial inorganic
chemicals such as sulfides, cyanides, fluorides, heavy and 'noble metal, and
organic chemicals such as solvents, dyes and peroxides present public health,
ecological and economic problems after discharge. Within the agricultural
sector, many chemicals are broadcast over wide areas and enter watercourses
via runoff, percolation, rainfall and dustfall. Both inorganic and organic
biocides are presently in use and include such substances as lead arsenate,
parathion, chlorinated hydrocarbons and insect hormones.
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PROJECT OBJECTIVES
The goals of this project are the determination of the rates
of discharge of selected hazardous polluting substances and-nutrients in
selected drainage basins and the determination of the rates of transport,
storage and decay of the substances within the streams in the study area.
If successful, this study could provide a tool for predicting changes in
lake inputs with changing land use patterns.
OVERALL PROJECT PLAN
"Hie first part of this study was the determination of the general
background conditions in the study area. These conditions are' being measured
by a water quality network of 10 samplinc sites located in unpolluted reaches
of streams which have different predominant land uses. Both water
and sediment samples are being taken. The sampling program consists of
15 water analyses per station every two weeks for 18 months and 5 sediment
analyses per station once every 4 months for 16 months. In addition to
phosphorus and nitrogen, attention is being given to toxic metals, pesticides
and other exotic pollutants.
To supplement the water quality data, flow, land use and clima-
tological information is being collected. By combining the concentration
and flow data, fluxes for the various materials can be estimated. In this
way, the relative magnitudes of the yields will be estimated and a detailed
mapping of the seasonal variations by sub-areas made.
An attempt will be made to correlate the estimated rates of
discharge of hazardous agricultural chemicals and nutrients from given land
uses to rainfall, runoff, soil type and known application rates.
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Supplementing analyses being made as part of this project, an
aliquot of the samples collected as part of the water quality network is
being shipped to the University of Wisconsin for use in the IFYGL project.
entitled, "Algal Nutrient Availability and Limitations in Lake Ontario".
In addition to the operation of a general water quality network
a point source sampling network has been established to facilitate the
development of transport data for hazardous substances and nutrients.
Three streams are being intensively studied immediately upstream, downstream
every half mile for several miles, and at the outfall of treatment plants
to determine rates of mass transport, storage and decay in the system.
Each point is being sampled bi-weekly for 5 months. There will also be
an intensive sampling period of 5 continuous days on each stream. Addi- .
tional stations will be sampled during this period so that certain inputs
to the streams (particularly field drains and tributaries that are not
monitored on the normal bi-weekly trips) may be adequately checked. The
sampling program consists of 13 water analyses per station and 4 sediment
analyses per station during each sampling period. Plankton and macrophyte
samples are also being taken at selected stations along each stream.
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SITE SELECTION
Genesee River Basin
After consideration of watersheds available, it was determined that the
Genesee River Basin had the most desirable characteristics for meeting the project
objectives.
The Genesee River drains some 2,384 sq. miles in Central New York and
another 96 sq. miles in North-Central Pennsylvania (Figure l). The watershed is
roughly rectangular in shape, running north-south, and is about 100 miles long and
40 miles wide. The river flows north from Pennsylvania through New York to Lake
Ontario. In its course, it intersects the Barge Canal just south of Rochester and
continues on through the city. The Genesee River discharge .averages about 2,726 cfs
near Rochester, and the river flow is carefully regulated by a series of dams in and
near the city. Three substantial tributaries enter the Genesee River just upstream
of Rochester: Black Creek (mean discharge 101 cfs}, Oatka Creek (mean discharge
195 cfs), and Honeoye Creek (165 cfs).
The basin has a humid climate with cold winters and mild summers. The
average yearly temperature in the lower basin is 50°F. In the higher elevations the
average is 44°F. Average annual precipitation is 34 inches, decreasing from a high
of 42 in. in the upper basin to 28 in. in the lower basin. The entire watershed is
subject to local cloudburst-type storms*- '.
A summertime deficiency of rainfall often occurs in the Genesee Basin. The
deficiency extends through the upper four inches of soil as a regular occurrence
(2)
during part of the summer .
A wide variety of soil types and geochemical areas exist as one moves from
the mouth of the basin at Lake Ontario up to the upland areas in Pennsylvania.
Topographically, the Genesee River Basin consists of three terraces sepa-
rated by northward-facing escarpments^ ' (Figure II). The southernmost terrace is
the Allegheny Plateau whose northernmost edge is the Portage Escarpment which cuts
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across the basin north of Mt. Morris -on an east-west line. The soils in this area
are siltstone, shale and sandstone mixed on glacial till with moderate-to-somewhat-
f3\
poor drainage qualitiesv '.
Between the Portage Escarpment on the south and the Niagara Escarpment in
Rochester on the north, lies the Erie and Huron Plains area. This area has a rolling
surface with long, gradual slopes except along the tributary streams which lie in
deep ravines. Here the soils are predominately limestone with shale and sandstone,
on glacial till with good to moderately good drainage. There is clay concentrated
in the subsoil.
The harrow lake plain within the City of Rochester, north of the Niagara
Escarpment, consists of lacustrine silt and clay deposits. These soils are imper-
fectly to poorly drained.
A wide array of land use activities are represented in the basin as shown
in Table I.
The largest concentration of urban and residential area is in the Rochester
Metropolitan area where the population grew from 615,044 in 1950 to 882,667 in 1970.
All of this growth has occurred in the suburban areas since the central city popula-
tion in 1950 was 332,488 and fell to 296,233 in 1970. This population is concentrated
along the main stem of the Genesee River and near Lake:0ntario. Rochester itself is
heavily industrialized. The area is served by the Barge Canal, 5 railroads, 5 major
highways (including the New York State Thruway) and 3 airlines. The Barge Canal, in
particular, is still used to move bulky goods like oil, petroleum products, fertilizer
and scrap.
The Basin north of suburban Rochester is for the most part sparsely populated
and consists of primarily agricultural lands with some forested areas. Although the
agriculture is predominantly dairy, there are extensive truck and row crop areas
with a prevalence of vegetable crops and fruit orchards. Corn is the major crop.
Oats, wheat and barley combined occupy about the same acreage as corn.
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New York State has maintained 8 water sampling stations in the
Genesee River Basin and has collected historical water quality data, and
the U. S. Geological Survey has maintained stream gages on the river since
1935 and on its tributaries since 1945.
The State District Health and Environmental Conservation offices
are located in the Genesee Basin and have personnel familiar with the area.
An Environmental Protection Agency sampling station for the materials
balance aspect of IFYGL is also located at the mouth of this watershed and
will provide a connecting line between the two studies.
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Specific Site Slection
Water Quality Network
Sub-watershed areas with various single major land use in
the Genesee Basin were chosen by using the LUNR area data land use maps.
(3)
The New York State LUNR program is a detailed inventory of land
use and natural resources of New York State. A field survey was then
made to check any changes in land use that may have occurred since the
land use photos were taken in 1968. The streams in each of the sub-
watersheds were visited. Each stream had to be large enough to have some
flow during periods of dry weather and had to be accessible all year
round. The final areas chosen were: (Fig. 1 through 7)
Cropland - Spring Creek (North of Byron)
Pasture - Jaycox Creek (North of Geneseo)
Brushland - East Valley Creek (North of Andover)
Forest - Briggs Gully (East of Honeoye Lake)
High Density Residential - Dansville
Urban - Aliens Creek (East of Rochester)
Table II summarizes the flows, areas, and percent of various
land uses in each subwatershed.
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Station 501 (Cropland) is located on Spring Creek (Fig. 2),
north of Byron at the bridge on Route 237. There are 21 dairy farms
with a total of 1280 cows and 630 heifers in this area and 2 pig farms.
Approximately 54% of the cropland is in corn, oats, wheat and barley.
In the Urban area (Station 502) (Fig. 3), there are 26 active
farms, including one dairy farm and 4 horse farms, a total of 29 parks,
golf courses and recreational facilities, 21 schools, 13 churches, 1
prison, 1 sewage treatment plant and 30 apartment buildings. Storm and
sanitary sewers are separate with the storm sewers all draining into
Ellens Creek or its tributaries. From May through October, steel
siphons (2-10" and 1-8") drain water from the Barge Canal into Aliens
Creek. The sampling point is located at the U. S. Geological Survey
gaging station at the Aliens Creek Sewage Treatment Plant, upstream of
the-plant outfall.
The pasture area (Station 504)(Fig. 4) at Jaycox Creek is a
summer pasture for horses and cows. Samples are taken at 2 branches of
the Creek (Stations 503 and 505), upstream of the pasture area to monitor
the parameter levels of the inflow to the pasture area. Station 504 is
located at the bridge on Nations Road. Station 503 is located north of
Geneseo, where the northern branch of Jaycox Creek crosses Route 39.
Station 505 is located on the Lima Road, where the southern branch of
Jaycox Creek crosses the road.
May 1, 1973, we began sampling a small area (Station 512) further
downstream from the regular pasture area. This subdrainage basin begins
at Station 504 and covers a small cow pasture area. Since Station 512 is
inaccessible during bad weather, samples will be taken here from May 1, 1973
through November 15. There are no laboratory results available at this
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time for this Station.
The area draining the forest watershed (Fig. 5) is sampled at
Briggs Gully by the bridge on East Lake Road. Gaging of this stream is
extremely difficult due to the large amount of gravel washed down the
gully above the sampling point during the flood of June 1973. Most of the
flow was underneath the gravel until the stream bed was dozed out Sep-
tember 21, 1972.
At Dansville (Fig. 6), a sample is taken upstream of the high den-
sity residential area (Station 508), and a second sample at the down-
stream end of town (Station 507). The stream flows through residential
yards in the center of town and is routed under the streets. The banks are
perpendicular and lined with concrete in some sections and steel in other
places. In the park (an area 1 block square) where Station 507 is located,
the banks are mud and grass. The banks are about 5 feet high all through
the town.
The brushland area (Station 509) is drained by East Valley Creek
north of Andover (Fig. 7). The sampling site is by the bridge at the
first stream crossing on East Valley Road, north of Andover. This area was
predominantly agricultural, but the farms are gradually being abandoned.
There are a few cattle in some areas along the creek. The main crop is hay,
with a minimal amount of oats and corn still being grown in the area.
Normally, no fertilizers are used on these farms.
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Point Source Network
Three drainage basins have been selected for studying the
effect of point source discharges on a stream system. Each- of these
basins is characterized by primarily agricultural land use and one or
two small population centers. Each basin has within it a wastewater
treatment facility whose effluent discharge represents a significant
(greater than 10 percent) portion of the stream flow draining the basin.
On each system samples are taken of the wastewater discharge and one
stream sample upstream of the wastewater discharge and several downstream
samples at approximate one-half mile intervals. Sediment samples are
also taken at each stream sample station.
Fish Creek, in the Towns of East Bloomfield and Victor,
New York (Figure 8) drains an area of approximately 14 square miles along
a stream reach of about 8.5 miles.. The land use within the basin is
essentially all agricultural with a few cattle and horse farms. Three
tributaries along the reach of the stream contribute about one-half the
total stream flow. There are no marshes or swamps along the creek and
very few wooded areas. Most of the land in the basin has been cleared
and is either in active use or lying fallow.
The creek receives the treated wastewater from the combined
Holcomb-East Bloomfield Sewer District. The treatment facility includes
primary sedimentation, high rate trickling filtration, rapid sand fil-
tration and chlorination. The average flow is approximately 100,000
gallons per day, 10 percent of which is a pretreated (with C^} cyanide
waste from a metal products manufacturing firm-
Along the reach of the stream there are 11 regularly sampled
stations plus the wastewater discharge. There are an additional 11
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stations that represent tributaries and areas of difficult access
that are sampled on an irregular basis.
Spring Brook, in the Town of Lima, New York (Fig. 9) drains an
area of approximately 33 square miles while the reach of the stream being
sampled is about 4.5 miles. The land use of the area of the basin to
the south of the Town of Lima is essentially all related to agricultural
use, though there are some large swamp and marsh areas. North of the
Town of Lima the land use continues to have a predominant agricultural
character. There are two small tributaries within the reach of the
stream that is sampled. These tributaries represent about 15 percent of
the total stream flow.
The brook receives treated wastewater from the Town of Lima
wastewater treatment facilities. The treatment process includes primary
sedimentation, high rate trickling filtration and stabilization in an
oxidation pond. The average flow of the treatment plant is about 100,000
gallons per day.
There are a total of seven regularly sampled stream stations
plus the wastewater discharge. There are an additional four occasionally
sampled stations that are related to the tributaries.
Avon Creek, in the Town of Avon, New York (Fig. 10), drains a
basin of 3.5 square miles along a reach of 3.3 miles. The land use within
the basin is all of an agricultural nature with the major portion of the
land area devoted to crop production and some land used for grazing dairy
cattle. Along its reach the creek flows through two small 1 owl arid marshes
for about one-quarter mile each, about one-half mile of woc-.;:.i area and one
small impoundment about 100 yards long. The remainder of t'r,- land is open
and under active agricultural use. There are two significant tributaries
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that contribute about 40 percent of the stream flow.
The creek receives the treated wastewater from a 350 unit
trailer park. The sewage is treated via a contact stabilization system
with the effluent applied to slow sand filters the underdrains from
which discharge directly to Avon Creek. The average flow is about 45,000
gallons per day.
There are a total of nine regularly sampled stations along the
reach of the steam plus the wastewater discharge. There are an additional
four occasionally sampled stations related to tributary flow.
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FIELD AND LABORATORY METHODS
General
All stream samples collected are being analyzed for pH, total
organic carbon, ammonia nitrogen, organic nitrogen, nitrate, nitrite,
particulate phosphorus, soluble phosphorus, orthophosphate, chloride,
magnesium, calcium, and iron. In addition, the samples from the land use
stations are analyzed for sodium, potassium, reactive silica and sulfates.
The point source stream samples are also analyzed for aluminum. Additional
water samples are being collected 6 times during the study period for
pesticide screening and for the analysis of mercury, cadmium, zinc, lead,
copper, nickel, manganese, chromium and fluorides.
Sediments from Stations 501 thru 513 are being collected six times
and sediments from the remaining stations are collected during each sam-
pling trip. The sediments are analyzed for phosphorus, iron, magnesium,
aluminum and calcium.
Cloud cover, air temperature and stream temperature are noted and
recorded at each station at the time of sample collection.
The Division of Laboratories and Research, New York State Depart-
ment of Health, is providing the necessary laboratory services for the
water sample analyses. The State Geological Survey, State Science Service
of the State Education Department is doing the sediment analyses and pro-
viding technical advice on geochemistry.
The U. S. Geological Survey gages the streams at Stations 501,
502, 504, 506, 507, and 509 at the time of sample collection.
Sample Collection and Storage
Water Samples
A two gallon sample of water is collected from 1 to 2 inchest below
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the stream surface near the center of the stream in a container well
rinsed with the stream water at the site. At Stations 501, 502, 504, 506,
507, and 509, one gallon of well mixed sample is poured into quart Qabitainers ,
chilled, and sent to the University of Wisconsin in insulated containers.
Two 120 ml polyethylene bottles are filled with well mixed unfiltered
samples, for silica and sulfate analyses;
A 47 mm diameter, .45 yu membrane filter in a filtering apparatus
is covered with Celite by filtering 4 ml of a Celite suspension (10 g/1
distilled water) and discarding the filtrate. Then 300 ml of well mixed
sample is filtered and the filtrate distributed into a 120 ml polyethylene
bottle for orthophosphate and soluble phosphorus, into a screw-cap tube
for soluble carbon analysis, and the rest into a 500 ml bottle. Ten ml of
distilled water from a syringe equipped with a narrow gage needle is used
to flush the residue from the filter into a screw-cap tube for determina-
tion of particulate phosphorus.
A second 300 ml of sample is filtered the same as above. The
filtrate is flushed into a screw-cap tube for particulate carbon analysis.
The filtrate is poured into the partially filled 500 ml bottle for ammonia,
nitrate, nitrite, organic nitrogen, and chloride analyses.
All the above samples are immediately placed in insulated carriers and
packed with dry ice for transport to the Division of Laboratories and
Research, New York State Department of Health in Albany, where they are
stored until analyzed.
Samples for calcium, magnesium, iron, sodium and potassium are
prepared by adding 1 ml of concentrated HNOg to 100 ml of raw sample.
pH is determined using a Sargent-Welch Model PEL portable pH meter.
Then 100 ml of well-mixed sample is titrated for total alkalinity with
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mineral acid to pH 4.5. Time is allowed for any suspended calcium car-
bonate to dissolve and for a stable endpoint to be reached.
Sediment Samples
Two methods have been used for collecting sediment samples. The
first involves the use of a stainless steel scoop that has a flat bottom,
slanted sides and back, and a partial cover. The scoop was designed to
have a volume of one quart.
The sediment samples are collected with the scoop and placed
in one quart wide mouth containers. The samples are then iced and excess
water is decanted after twelve hours.
The second sediment sampling technique involves wet sieving the
sediment samples in the field. The method was adopted because the scoop
method was not providing a large enough sample of fine (less than 2.00 mm)
grained material. The technique involves sieving the samples for two
size fractions; less than 2.00 mm but greater than 250 microns and less
than 250 microns. The fraction less than 250 microns is retained on a
percale cloth with more than 186 threads per inch. The excess water is
then drained from each fraction and the fraction is stored on ice in a
small plastic bag.
Analytical Methods
Water Samples
Aside from the field measurements described here, all analytical
methods are carried out by the Enviror.rn-~r.tal Health Center, Division of
Laboratories and Research, New York Statv . -irtnent of Health. A detailed
description of methods utilized is giver; in Appendix A.
Sediment Sarnies
The sediment samples after collection are subjected to one of
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two analysis flow schemes shown in Figure 11. Several samples are sent
to the New York State Geological Survey for analysis of metals and miner-
ology. These samples are frozen immediately after collection and split
in the frozen state to provide equivalent samples for metal and minerology
analysis and nutrient analysis. Those samples riot split for metal and
minerology are subjected to nutrient analysis only.
The samples for chemical analysis are dried at 60°C for 24 hours
and then analyzed for total and organic phosphorus with approximately
25 percent of the samples further analyzed for iron, manganese, calcium
and aluminum bound phosphorus.
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TIME AND COST ANALYSES
The original cost estimate and time schedule is represented by
the solid lines in Figure 12. The dotted lines represent the deviation
from the estimate. The total Federal costs will be $108,105 as outlined
in the grant for 1973-74. The final report date will be June, 1974. The
State costs for the first year of this project were $24,955. For the
1973-74 fiscal year, the projected State costs will be $58,145.
PROGRESS TO DATE
Historical Review
A literature search has been conducted for available technical
information relating to the study. Industrial and municipal discharge
data have been accumulated from the records of the Department of Environ-
mental Conservation. Computer printouts of water quality data amassed by
the Department of Environmental Conservation have been collected for all
stations in the Genesee River Drainage Basin. Climatological data, soils
information, land uses, and other pertinent data have been collected.
Partial Sampling Results
Appendix B contains a computer printout of all the raw data
analyzed to this date. No detailed analysis of the data has been made.
Problems
The flood of June 1972 changed the sampling schedule considerably.
Gravel and sediments filled in several of the stream beds in the sampling
areas. During the summer and fall of 1972, these stream beds were cleaned
out and restored as closely as possible to their former state by dozing.
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Considerable problems with the analytical methods for phosphorus
were encountered. The Intel-laboratory comparisons were responsible for
changing the methods of analyzing phosphorus.
"Due to the results of the interlaboratory comparison, our method
of analyzing phosphorus was changed as of January 1, 1973. Our sampling
will continue until December 31, 1973, so there will be one complete year
of data using the same analytical technique. The State of New York will
provide any additional funding required for this sampling.
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FUTURE PLANS
Field Work
The stream quality network sampling will continue on a bi-weekly
basis through December 31, 1973.
The point source stations will be sampled bi-weekly through
October 31, 1973.
Data Analysis
Literature Data
A review of literature data will be made and reported concen-
trations and flux rates will be converted to common units and tabulated
along with information on the land use, geology and soil type of the
drainage area from which they were collected. Conclusions regarding the
universality of concentrations and flux rates will be made.
Water Quality Network Data
Each parameter collected at each water quality network station
will first be treated as a unique record and processed according to the
following scheme.*
Quick look (Visual
Display) of
Time History
Test for
Stationarity
-Non-Stationary-
Stationary
Test for
Randomness and
Normality
•Residuals
Separate Trends
and Cycles
Determine Means
and Variances
*This is a modification of a procedure suggested in Bendat, J. and Piersal, A.,
"Measurement and Analyses of Random Data", John Wiley & Son, New York 1966
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Conclusions regarding the adequacy of the sample size and
sampling period will be drawn from the above analyses. A comparative
analysis of the mean concentration with reported literature values will
be made.
If the. above indicates that an adequate sample is available,
the entire set of parameters will be analyzed as follows.
Correlate Flow
on Concentration
Data
Develop Hydrograph
for each Stream
Determine Seasonal
and Annual Flux
Rates
Conclusions regarding the nature of the chemical-physical system
will be inferred from the flow-concentration relationship. Finally,
attempts to correlate land type and use parameter and stream sediment type
with observed mean concentrations and loadings will be made. The effect of
land use on the sample variance will be determined. The results of all of
the above will be compared with reported literature values.
Point Source Stream Data
An attempt will be made to model the transport of nutrients below
the point sources using the following procedure.
1. Develop a conceptional time series model. Quantize the model
as much as possible utilizing reported literature values for
rate coefficients and the information from the water quality
network station for background.
2. Force fit the model to the data collected during the intensive
sampling period.
3. Check to see if the model verifies using the biweekly sam-
pling data.
-23-
-------
TABLE I
GENESEE BASIN LAND USE
Land Use*4) Square Miles^ %
Urban, Commercial, Industrial 99.7 4
Residential 52.5 2
Commercial and Industrial 15.3 1
Transportation 8.9 1
Extractive 23.0 1
Agriculture 1017.8 43
Row & close grown crops 46.8 2
Pasture & Meadows 969.3 41
Orchards & vineyards 1.7 1
Forested Land 1125.5 47
Recreation Land 33.5 1
No Major Use 88.7 4
Water 25.0 1
Wetlands 63.1 3
Barren Lands .6 1
Miscellaneous 18.8 1
Public Land 14.0 1
Urban Inactive 8. Construction 4.8 1_
2384 100
-24-
-------
LAND USE AND SUBDRAINAGE BASIN AREAS
Station No. 501
502 503 & 505
504
506
507
508
509
Major Land Use
Area (Acres)
Land Use (%)
Cropland
*High Intensity Agri.
**Brushland
Forage Crop
Pasture
Bogs & Wooded Wetlands
Forest
Misc.
Urban (residential, public
outdoor recreation,
commercial)
***High Density Residential
Industrial
Average cfs for 1st 9 months
of study 26.5 36.4
Cropland
13,824
57
16
8
6
6
6
1
.ic
Beginning
Urban Pasture Pasture
17,920 7,710 1,314
23
19
70
20 95
10
5
4
52
2
Beginning
High of High
Density Density
Forest Residential Residential
4,243 142 780
1 49
22
6
71 45
6
6
94
Brushland
4,666
30
53
16
1
8.7
11.2
2.15
8.79
* intense production of vegetables, berries, potatoes and other truck crops.
*•* brush cover up to fully stocked poles less than 30'
*** 50' frontage or less per residential lot.
TABLE II
-------
GENESEE RIVER BASIN
IFYGL SAMPLING STATIONS
Fiaure 1
-26-
-------
CO
•2
X
LJ
0
z
UJ
D.
X
UJ
Q
UJ
40
w
I
1-0
14.0 -
13.0 -
12.0
II.0
10.0-
8.0
•6.0
4.0
2.0
0
OCCURRENCE AND
HAZARDOUS
TRANSPORT
POLLUTING
OF NUTRIENTS AND
SUBSTANCES
TASK TWO
FIELD WORK PLANNING
TASK THREE - FIELD STUDIES
TASKFOUR
EVALUATION OF FIELD STUDY DATA
TASK FIVE
FINAL REPORT
PREPERATION
F EBTMAR.'APR.'MAY'JUN.'JUL.' AUG.'SER'OCT.'NOV.'DEC.] JAN.'FEB.'MAR! APR.'MAY'JUN.'JOL." AUO.'SER'OCT.'NOV.'DEC.JJAN."
1972 Figurel2 1973 1974
-------
SEDIMENT SAMPLE ANALYSIS FLOW SCHEME
Field Collection
and Refrigeration
of Sample
Frozen
New York State
Geological Survey
New York State
Division of
Laboratories
and Research
Grain
Analysis
Clay
Analysis
Total P
Organic P
Fe, Mn, Ca,
Bound P
Al
Figure 3
-28-
-------
Zooplankton Production in Lake Ontario as
Influenced by Environmental Perturbations
Donald G. McNaught
Marlene Buzzard
Department of Biological Sciences
State University of New York at Albany
Albany, New York 12222
Yearly report (year I, April 1972-March 1973) based upon research
supported by Environmental Protection Agency (Grant 800536 to
D. McNaught, S.U.N.Y. Res. Found. 20-5003-A).
-------
Table of Contents
Page
Review of Subj ect 30
Status of Program 31
Planned versus Actual Operation 32
Areas of Program behind Schedule 32
Summary of Results 33
Development of Sonar 33
Calibration of Sonar 34
Biological Comparisons 40
Impace of Large Cities on Community Structure
of Zooplankton in Lake Ontario 46
Historical (1939-72) Appendix
-29-
-------
Review of Subject
Long-term changes in water quality in the Great Lakes have resulted, in
part, from accumulated inputs of materials either stimulatory or inhibitory
to the primary producers. Changes first observed in primary production have
later "been observed in zooplankton and fish production. Most important,
when aquatic sysifems have been perturbed for long periods dramatic changes
in community structure may make attempts at reversing cultural eutrophication
difficult, if not impossible. Thus an initial purpose of the efforts
described here was (l) the interpretation of ecological changes in zooplankton
populations using indices based upon the concepts of diversity and niche
structure. Likewise, we wanted to (2) measure the production of zooplankton
communities in Lake Ontario, using both traditional and acoustical collection
techniques. Within the team approach designed within IFYGL, we proposed (3)
to understand the functioning of natural and disturbed zooplankton communities.
Finally we agreed to (U) participate in a broadscale approach to modeling the
Lake Ontario ecosystem, under the primary direction of the modeling group from
Hydroscience.
The first object, the interpretation of long term changes in zooplankton
populations in Lake Ontario, has been in part accomplished with the submission
of our report "Changes in zooplankton populations in Lake Ontario (1939-1972),"
for publication (appendix).
The second objective, to measure the production of zooplankton communities
in Lake Ontario, is partially completed. Acoustical techniques have been
developed for measuring the biomass of zooplankton in specific size-classes,
the hardware constructed, measurements made on the IFYGL Biological-Chemical
cruises, the system calibrated, and a system for reduction of data developed
(Sectionpg5). The acoustical data will be processed within the next few months,
while the biological data will require many months more work.
-30-
-------
Improved understanding of perturbed zooplankton communities vill come
when the biotic components of the Lake Ontario ecosystem are described and
their standing crops and/or productivities estimated. This phase must await
the completion of related projects, and considerable interaction among
principle investigators.
Status of Program
Field work was completed on 15 June 1973. On ten chemical-biological
cruises we collected 2k$k biological samples and 1195 acoustical profiles
(Table l). Since each acoustical profile contains 100 separate estimates
with depth, we have approximately 119,500 acoustical estimates of biomass.
To date many of the biological samples for the May, June, July and
August 1972 cruises have been processed. A method for reducing acoustical
data has been developed and is described herein.
Table 1. Resume of data collected on zooplankton in IFYGL Biological Program.
Cruise
Zooplankton Samples
Acoustical Profiles
No.
1
2
3
k
5
6
7
8
9
10
Inclusive 'Dates
15-19 May 1972
12-16 June 1972
10-1 U July 1972
21-25 August 1972
30 Oct. -3 Nov. 1972
27 Nov.-l Dec. 1972
5-9 February 1973
2U-28 April 1973
15-19 May 1973
11-15 June 1973
(at 'No. stations)
22i» (33)
399 (60)
380 (60)
36k (60)
355 (60)
2hh (60)
125 (38)
132 (U6)
116 (33)
155 (k9)
2k9h
(at No. frequencies)
100 (2)
50 (3)
200 (3)
2hQ (U)
2hO (h)
no sonar
11*7 (U)
no sonar
10k (k)
15U (5)
1195
-31-
-------
Planned versus Actual Operation
Generally the project has followed the plans presented in the original
and renewal proposals. Some deviations are noteworthy. Equipment funds
($U825) originally proposed for sonar development were used to purchase a
Wang 600 calculator to reduce data stored on paper-tape describing
acoustical returns from zooplankton layers.
Considerably more in-house programming has been handled in Albany than
anticipated. Since the onset of the program a part-time programmer has been
working to develop data reduction routines, programs for productivity
estimates, niche analysis, etc.
Areas of Program behind Schedule
Only one aspect of the program causes concern, that being the time involved
in processing biological samples. To expedite processing, I now plan to hire
an additional full-time technician on 1 September, 1973. Thus we should
complete counting by the termination date of the contract.
-32-
-------
SUMMARY OF RESULTS
Development of Sonar
With the demands of large scale data collection and analysis to understand
lakewide zooplankton distributions, Mr. Robert Zeh of SUWY at Albany designed a
high frequency sonar capable of handling information from weak targets, as
characterized by the zooplankton.
Basically his approach was to transmit an exact waveshape and detect the
return in a fashion providing a maximum amount of information on the target.
The sonar is similar to many others, in that it transmits a periodic tone
burst and then listens for the reflected returning waves and measures the
elapsed time and amplitude of the returns. However, it has certain basic
differences in circuitry because of target characteristics.
The circuitry starts with the oscillator (Fig. l), which serves a dual
function. It provides the reference signal for both the phase-sensitive
synchronous demodulator and the transmitted tone burst. The tone burst is
precisely clocked, the duration controlled by the pulse generator. It is
then amplified and fed to the transducer. The return signal is received by
a separate hydrophone. Any series of returning signals which were originated
by the same tone burst may be stored and examined. Single series of returning
signals can be recorded in 1000 channels of memory on a transient recorder.
This type of analysis should lead eventually to an ability to fingerprint
return signals, i.e. to identify the components of the scattering layer.
The returning signal is also simultaneously fed into an (inphase and
quadrature phase) synchronous demodulator. This provides a DC signal
proportional to the amplitude of the returning tone burst and is independeht
of the phase of the incoming signal. The output of the demodulator is fed
to a storage oscilloscope, providing a picture (depth vs time) similar to the
typical sonar chart familiar to most investigators. Then the signal from the
-33-
-------
demodulator is stored in a. signal averager, the heart of the system, for we
are interested in the average return from typically "clumped" distributions
of zooplankton. The average returns, in one percent increments of depth,
are printed on a teletype and displayed on an X-Y plotter (Pig. l). Data
on paper-tape from the teletype can then be later processed using a Wang 600
programmable calculator.
Advantages of this acoustical recording system include (a) ease in taking
large amounts of data, (b) real-time display of distributions of particles on
X-Y plotter, and (c) the ease in processing large amounts of data from paper-
tape. Obviously the system is not sensitive to differences in individual species
at^ this time.
Calibration of Sonar
Three basic corrections have been applied to the raw data (as displayed on
the X-Y plotter) to convert return signals to relative biomass. These include
a correction for the different characteristics of the transducers (normalization),
for the relative attenuation of sound (attenuation) and for the beam angle
(Table 2). When these have been applied to the raw data we have a plot of
biomass within size category for small targets (Fig. 2). Each higher frequency
is sensitive to smaller particles; for example, 80kHz is capable of detecting
particles larger than k mm, whereas the 200kHz transducer adds another size-
class down to 2 mm and 500kHz still smaller particles to O.U mm.
On June 11, 1973 we visited station 95 in HE Lake Ontario. Complete
reduction of data collected at three frequencies (80, 120 and 200kHz) has
provided the profile of zooplankton biomass shown in Fig. 2. At a given depth
of 2m, many large particles are evident (80kHz), but an approximately equal
number of "crustacean" particles down to less than 2 mm are also evident
-34-
-------
Fig. 1. Description of acoustical data acquisition system.
-35-
-------
Table 2. Correction factors for acoustical returns necessary to equate
returns to biomass of zooplankton.
formula; Intensity x normalization x attenuation
beam correction
Sample Calculation;
example: 120 KHz at k m depth
Intensity x 2.3* x 1.55
1.51
(Step 1)
frequency Hormalization
Zero Correction Bottom Cctrr
Corrections factor (-) factor (x)
(Step 2)
Attenuation factor (x)
Equiv.
Channel Depth (M)
(Step 3)
Beam Correction
factor (5° angleKj)
80 KHz
120 KHz
200 KHz
.0593
.0853
.0987
I*
5
2.321 6
7
8
2.203 9
10
11
12
1.1*
1.7
2.0
2.U
2.7
3.1
3.J*
3.7
U.1
1.08
1.12
1.17
1.2U
1.29
1.37
1.U2
1.U8
1.55
1 m
2 m
3 m
1* m
5 m
6 m
7m
8 m
9 m
10 m
1,00
1.36
1.33
L.51
£.71
1.92
2.13
2.37
2.61
2.86
-36-
-------
X-Y Recorder
-------
Fig. 2. . Distribution of biomass within size categories (80kHz = >k mm,
120kHz = >3 1/2 mm, 200kHz = >2 mm), for station 95 on 11 June
1973. Note abundance of larger organisms near surface.
-38-
-------
OJ
vO
I
200kHz
20kHz
80kHz
4567
Depth in meters
8
9
10
-------
(200kHz). These data were processed manually using the forementioned
corrections for beam angle and attenuation. Presently we have approximately
1195 acoustical profiles for Lake Ontario to process automatically using the
Wang 600 calculator and teletype interface.
Biological Comparisons
For the use of other investigators we have made two tabulations of
biological data and a statistical comparison, including the following:
a) a comparison of densities of zooplankton at 0-5m depth at inshore
(<50m) versus offshore stations (>50m depth) for the cruises of
May, June and July 1972 (Table 3).
b) a comparison of densities of zooplankton for k depth intervals for
May 1972 (Table 1»).
c) a statistical comparison of the inshore-offshore densities (Table 5).
During May, June and July of 1972 the limnetic zooplankton of Lake Ontario
were dominated by the copepedites of cyclopoid copepods, Cyclops bicuspidatus,
and Bosmina longirostris (Table 3). The same is true on a yearly basis (see
McNaught and Buzzard, Appendix). Bosmina is likely a filter feeder preferring
small nannoplankton" and bacteria. Cyclops is likely omnivorous, feeding mainly
on copepedites, nauplii and immatures of other organisms, as well as its own.
Many of these limnetic zooplankters are most abundant near the surface
(0-5m) in offshore (>50m) waters (Table k). This is true of Cyclops^ bicuspidatus
and Diaptomus minutus. However, Bosmina longirostris is apparently more abundant
inshore, and it is in these waters that its grazing pressure is exerted.
Such comparisons between inshore and offshore populations must have
statistical validity, due to the commonly recognized problems of patchiness.
It can be demonstrated that Cyclops is more abundant offshore, while Bosmina
exhibits preference for inshore waters, with comparisons made at the 95$ level
(Table 5).
-40-
-------
Table 3. Mean Density of Organisms at 0-5 m. Inshore Stations vs. Offshore
Stations for Cruise 1 '(May 15-19, 1972), Cruise 2 (June 12-16, 1972)
and Cruise 3 (July 10-l^, 1972).
Species/Location May #/m3 June #/m3 July #/a>3
Leptodora
kinditti
Bosmina
coregoni
Bosmina
longirostris
Daphnia
retrocurva
Ceriodaphnia
laoustris
Chydorus
sphaericus
Cyclopoid
copepedites
Cyclops
bicuspidatus
Cyclops
vernalis
Tropocyclops
pra sinus
In
Off
In
Off
In
Off
In
Off
In
Off
In
Off
In
Off
In
Off
In
Off
in
Off
0
0
12
10
119
10
12
3
0
0
1
0
183
322
1+8U
920
1
1
1
0
1
3
38
k
61*3
133
9
7
2
1
6
2
505
359
571*
1558
22
5
6
1
2
1
61
67
13190
9355
116
ll*9
32
15
39
h
1020
1598
13138
7788
73
115
1*3
10
-41-
-------
Species/Location May #/nr June #/m3 July #/
Mesocyclops
edax
In 0 1 0
Off 0 1 26
Calanoid
copepeditas
In 22 6l 111*
Off 53 5^ 113
Diaptomus
admit us in 85 1*5 35
Off 1^5 205 75
Diaptomus
oregonensis
In 10 6 30
Off 21 1*2 18
Diaptomus
sicilis
In 11 15 k2
Off 1*6 U6 U6
Limnocalanus
macrurus
In 162 21*0 66
Off 216 182 69
Eurytemora
affinis
In 0 16 2l*
Off 0 21
-42-
-------
Tabled . Comparison of species abundance (#/m3) with depth (meters) for
whole lake (WL), inshore (in) and offshore (Off) stations for
cruise of May 1972.
Species/Location
Leptodora
kinditti
Bosmina
coregoni
Bosmina
longirostris
Daphnia
retrocurva
Ceriodaphnia
lacustris
Chydorus
sphaericus
Cyclopoid
copepedites
Cyclops
bicuspidatus
Cyclops
vernalis
Tropocyclops
pr a sinus
WL
In
Off
WL
In
Off
WL
In
Off
WL
In
Off
WL
In
Off
WL
In
Off
WL
In
Off
WL
In
Off
WL
In
Off
WL
In
Off
0-5 M
#/m3
0
0
0
8
12
10
66
119
10
6
12
3
0
0
0
1
10
0
251*
183
322
696
U8U
980
1
1
1
1
1
0
0-10 M
#/m3
1
1
0
Ik
27
1
70
138
1
6
12
1
1
1
0
1
2
0
222
310
133
520
493
547
1
6
0
i
0
1
0-25 M
#/m3
—
0
0
6
Ik
I
27
53
3
2
5
1
0
0
0
1
2
0
161
266
95
1*82
422
518
2
4
0
0
0
0
0-50 M
#/m3
—
_
0
1
-
1
4
_
4
1
-
i
0
-
0
1
-
1
141
-
141
608
-
608
i
-
i
0
-
0
-43-
-------
Species/Location
Mesocyclops
edax
Calanoid
copepedltes
Diaptcmus
mlnutus
Diaptcmus
oregonensis
Diaptcmus
sicllis
Limnocalanus
macrurus
Eurytemora
af finis
WL
In
Off
WL
In
Off
WL
In
Off
WL
In
Off
WL
In
Off
WL
In
Off
WL
in
Off
0-5 M
#7*3
0
0
0
37
22
53
Ilk
85
Iks
15
10
21
28
11
U6
216
188
162
0
0
0
0-10 M
#/m3
0
0
0
26
25
28
80
72
89
16
15
16
Ik
k
25
138
105
172
0
0
0
0-25 M
#/m3
1
U
0
25
2k
26
73
59
82
15
15
Ik
Ik
10
17
188.4
239
157
0
0
0
0-50 M
#/m3
0
-
0
30
_
30
87
-
87
11
-
11
15
-
15
206
-
206
0
-
0
-44-
-------
Table 5. Significant differences (* = p<.05, NS = not significant) between
inshore and offshore populations for cruises of May, June and
July 1972.
Species
Cyclops copepedites
Cyclops bicuspidatus
Cyclops vernalis
Tropocyclops prasinus
Bosmina coregoni
Bosmina longirostris
Ceriodaphnia lacustris
Chydorus sphaericus
Mesocyclops edax
Daphnia retrocurva
Calanoid copepedites
Diaptomus minutus
Diaptomus oregonensis
Diaptomus sicilis
Limnocalanus macrurus
May (31df)
1.38 NS
1.82 NS
.50 NS
1.2l* NS
1.2? NS
2.75 *
1.11 NS
1.22 NS
0 NS
2.99 *
2.87 *
1.67 NS
1.18 NS
2.83 *
.81 NS
June (57df)
.75 NS
2.15 *
2.26 *
1.75 NS
1.78 NS
1.1*6 NS
1.75 NS
1.57 NS
.73 NS
.36 NS
.1*5 NS
3.61 *
1.1*9 NS
1.1*2 NS
.38 NS
July (58df)
1.32 NS
1.52 NS
.98 NS
1.22 NS
.17 NS
.86 NS
1.53 NS
1.77 NS
1.87 NS
.63 NS
.01* NS
1.61 NS
1.00 NS
.18 NS
.15 NS
-45-
-------
Impact of Large Cities on Community Structure of Zooplankton in Lake Ontario
Water quality and the abiotic factors which influence the biota of
Lake Ontario are of prime interest in the IFYGL program. Initially we
proposed to subject our processed data to an analysis, using niche theory to
derive indices which would detect changes in community structure. The data
on zooplankton (species and abundance) for June and July 1972 have now been
subjected to community analysis. A program in Fortran IV was written for
the Univac 1108 computer to calculate diversity and various niche parameters.
Niche parameters employed in this comparison include the community
competition coefficient (a), the theoretical community carrying capacity (K),
*
the ratio of observed to theoretical carrying capacity (N/K), and diversity
(H). Each of these parameters is discussed in the attached manuscript on
long-term changes in Lake Ontario (Appendix).
The mean number of zooplankton Crustacea (N), the theoretical carrying-
capacity (K) and the N/K ratio do not differ when populations off Toronto,
Rochester, Hamilton and Oswego are compared to populations at greater
depths around the remainder of the lake (Table 6).
The diversity of planktonic communities off the forementioned large cities
is less than one-half that for communities, at the same time and similar depths,
but distant from large cities (Table 6). This is rather startling information,
since longshore currents in Lake Ontario transport zooplankton past urban areas
rather rapidly (0.9 km/hr). In fact, in June 1972 the diversity off large
cities was 1.21 as opposed to 3.^ for similar inshore communities away from
urban influences. In July a similar comparison showed a diversity of 1.^5 off
urban areas, as opposed to 3.^*7 off less inhabited shorelines. These differ-
ences in diversity are significant at the 95% level (Table 7).
Such reductions in diversity near cities are due both to a reduction in
-46-
-------
Table 6.
Impact of "Big Cities" (Toronto, Rochester, Hamilton, Oswego) on
Community Structure of Zooplankton in Lake Ontario.
Total N
Alpha
(variance)
Total K
N/K
Diversity
(H)
June 1972
"Big
Cities"
2073
.517 (.12) 28885
.07
1.21
June 1972
Rest of
Lake
2893 .235 (.09) 28887
.10
July 1972
"Big
Cities"
.396 (.12) 185978 .12
1.U5
July 1972
Rest of
Lake
28962 .21*1 (.09) 292^35
.10
3.1*7
-47-
-------
Table 7.
A statistical comparison of Alpha and other factors between tvo Cruises
in June and July on the Big Cities vs Rest of Lake.
Alpha
N/K
Diversity
Total N
Total K
Cities
Lake
Cities
Lake
Cities
Lake
Cities
Lake
Cities
Lake
June 1972
.517
.235
.07
.10
1.21
2073
2893
28885
28887
July 1972 t05 df p < .05
.396
3.U 1 NS
.21*0
.12
0.2 1 NS
.10
1.1*5 xx
20.2 1 signif.
3.^7 (p < .05)
1.3 1 NS
28962
185,978
1.0 1 NS
292,^35
-48-
-------
the number of species present (richness) and a redistribution of relative
numerical dominance (evenness). In June 1972, when the diversity near the
cities was 1.21 compared to 3.UH for the rest of the lake, there were 5 less
species (lU as opposed to 19) in water-masses adjacent to our four large
cities (Table 8). In July there were 7 less species (12 as opposed to 19)
in these inshore areas influenced by urban living patterns.
This reduction in richness was attributable to the loss of similar.
species from "Big City" watermasses in both June and July 1972. In June
Daphnia galeata, Ceriodaphnia lacustris, Chydorus sphaericus and Holopedium
gibberum were missing from urban watermasses. In July these same cladocerans
plus Diaptomus oregonensis were missing. Replacing them and causing a shift
in evenness (Table 8) was Cyclops bicuspidatus. We know that Cyclops (Table 3)
is dominant in deep open waters (>50m), but when the cladocerans are lost, it
moves inshore near cities. The loss of these k cladocerans surprised us.
Normally the Diaptomids are thought to be most sensitive to environmental
perturbation.
It is important to make similar comparisons of nutrients, phytoplankton
and fishes at precisely these same "urban" stations. But we feel that we
have at present evidence for significant environment perturbation offshore
from urban areas adjacent to Lake Ontario.
-49-
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Table 8. Richness and evenness components of diversity, showing reduced
richness in areas of Lake Ontario adjacent to "Big Cities".
Date and Locality
Number
Diversity Number/m3 of
(H) Richness Evenness (N) Species (S)
June 1972 Big Cities 1.21
Rest Lake 3.M»
July 1972 Big Cities 1.U5
Rest Lake 3.^7
3.92
5.20
2.52
U.OV
1.05
2.69
1.3U
2.71
2073
2893
22l»lU
28962
Ifc
19
12
19
-50-
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Appendix: Changes in Zooplankton Populations in Lake Ontario (1939-1972).
-51-
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CHANGES Ity 'ZOOPLAKKTOH POPULATIONS IN LAKE ONTARIO (1939-1972):
D. C. MclTaught and M. Buzzard
Department of Biological Sciences
State University of Nev York at Albany
Albany, Hew York 12222
U.S.A.
Revised 20 July 1973
1 Contribution — of the IFi'GL Biology-Chemistry Program. Supported
by Grant 800536 from the U.S. Environmental Protection Agency.
-52-
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Abstract
Since 1968 the crustacean limnoplankton of Lake Ontario has been
dominated in July by Cyclops bi scuspidatus and Bosmina longirostris.
Apparently in 1939 Daphn ia spp. and Diaptoreus spp. were relatively more
abundant at the sajae tirae. Generally summer standing crops of zooplankton
in tee inshore waters (<50m) do not shov significant increase from 1939 to
1972. At the same tine the composition of these communities has shifted
from dominance by the cyclopoids and calanoids (8l/0 to the cladocerans
(U8-8U/5). Concomitantly numerous nev species have been recorded, the most
recent being Diaptonius ashlandi in 1972. Two additional trends are evident
since 1968. The species diversity has increased in the inshore waters from
1.77 to 2.98, due to increases in the evenness component. At the same time
their theoretical carrying-capacity for zooplankton has also increased.
-53-
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Introduction.
Aquatic ecosystens have characteristically been perturbed through
either the addition of nutrients stimulatory to phytoplankton production,
by substances toxic to such production, or by the addition of new exotic
fishes. The crustacean zooplaakters in such systems respond, as evidenced
by changes in community structure, to changes in food resources and to
selective predation. Thus whether aquatic ecosystems are perturbed from
the top downward or stimulated from the first trophic level upward, the
crustaceans are sensitive integrators of such changes.
It is the purpose of this review to examine suitable available data
on zooplankton populations of Lake Ontario to determine whether significant
changes in community structure have occurred since 1939- Our first approach
will be to examine comparable collections for significant changes in zoo-
plankton density (N) and relative composition at the ordinal (Copepoda and
Cladocera? and generic levels. Secondly, for the years 1969-1972, when
extensive collections were made, we will utilize niche theory to predict
the theoretical carrying capacity (K) of the Lake Ontario ecosystem, the
extent to vhich this capacity is filled (N/K), changes in the diversity of
the system (H) and whether these changes involve the influx of new species
(richness) or changes in relative abundance (evenness). In making these
later comparisons, we will present new species records and information on
community structure which we collected during the IFYGL program.
Seven investigations since 1912 provide an insigh't into changes in
zooplankton community structure (Table l). The collections by Patalas (1969)
made in 19&7 constitute the first intensive lakewide study, followed by that
of Nauwerck et al. (1972) in 1970 and our current IFYGL study which commenced
in May 1972. In addition, Whipple (1913) nade a single useful collection at
-54-
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the mouth of the Genesee River in 1912 and Tressler ejb ol_. (19^0) made a
limited collection in the sane ax-ea in 1939. Anderson and Clayton (1958)
did not make extensive collections, but discovered a nev genust Suryteaora,
previously not observed in the Great Lakes. hicUaught and Fenlon (1972)
took limited inshore samples in 19o9 and 1970 in the Oswego area.
Differences in collecting gear make comparisons of.zooplankton abundance
difficult. Patalas (1969) used a net with a mesh aperture of 77 y and
Nauwerck et_ aJL. a similar net of 6k u, whereas McNaught and Fenlon (1972)
and our current IFYGL study have employed nets of 15^ 1J -aperture. Tressler
and Austin (19^0) likely used a net with an aperture of 6*4 p attached to
their Juday trap, whereas Whipple (1913) did not describe his net.
Thus all investigators failed to sample copepod nauplii and copepodites
were sampled with differing efficiency. Most conservative comparisons will
thus be between numbers of adult forms. However, all nets were capable of
sampling Bosmina, a point critical to our conclusions, as evidence by our
large catches of this animal in 19&9 with a coarse net (McNaught and Fenlon
(1972)).
Additional problems arise when we consider the numbers of samples
collected. Whipple (1913) took a single sample in August 1913, and Tressler
and Austin (19^0) a vertical series of eight samples in 1939. With the advent
of intensive studies in recent years more information is available. Nauwerck
et_ aJL. (1972) collected approximately 30 samples on each of 12 cruises in
1970. Currently we are examining 60 stations in the IFYGL program, taking
1-5 vertical hauls at .each station.
Theory Used in Comparisons of Commun: .y Structure
Two basic assumptions underlie th£ use of niche theory (Levins, 1968) to
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predict the maximum theoretical carrying-capacity of an aquatic environment.
First we have assumed that crustacean populations exhibit sigtnoid growth in
nature, and that the concept of an environmental carrying capacity is real
for them. Secondly, we have assumed that with connunity development, a
likely evolutionary strategy includes the reduction of interspecific
competition, i.e. a reduction of the mean community competition coefficient
(a).
Assuming that crustacean populations continually push against an ever
changing carrying-capacity, we mist first estimate the competition co-
efficient (Levins, 1968):
n
(1) a^
- h=l
Plh P2h
' rlh
h=l
where h is an environment and P^ and P^ are tne proportion of species 1 and
species 2. This alpha assumes that competition for resources is proportional
to the probability of occurrence in an environment h (Lane and McNaught,
1970). Then, from the logistic:
(2)
dt
where r^ is the instantaneous growth rate of species 1, we can calculate the
maximum theoretical carrying capacity (K) for specie's 1, where:
n
(3) K! = N! + Z a2>1 N2
This maximum carrying-capacity is the r.axir.un density which a species would
-56-
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obtain if no competitors were present, where the calculation is made vith
on assumption of steady-state vith equation (3) and derived from (2) at
Finally, Shannon-V.'eaver speciss diversity values vere determined for
inshore and offshore waters for the years 1969-1972, where-
H = -
where p^ = proportion of individuals belonging to the ith -species.
Changes in Population Density and Composition
Standing-crop data for crustacean zooplankton are available for the
inshore waters of Lake Ontario for the month of July in the years 1912,
1939, 1969, 1970 and 1972 (Table 2). For 1912 and 1939 the' means are
based on one (l) and eight (8) samples respectively, making significant
comparison with the 1969-72 densities difficult. Even with these restrictions
certain general trends are evident.
The cyclopoid copepod Cyclops bicusr>idat"us thomasi Forbes and the
cladoceran Bosmina longirostris (Deevey) were dominant in July (1969-72)
just as- they are seasonally (Patalas, 1969; llauwerck _et_ al_. , 1972).
Tropocyclops prasinus mejticanus (Kiefer)j Mesocyclo-ns edax (Forbes), and
Cyclops^ vernalis (Fischer) were the cyclopoids of secondary importance.
The calanoids, which are represented by only 0.6-3.0$ of the 'population,
are composed of three species of Diaptomus , as well as EuryteTaora affinis
(Poppe) and Lin-no calanus_ macrurus (Sars). Among the cladocerans we have
presented limited evidence for a shift from dominance by Daphnia spp. in
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1939 (Tressler and Austin, IQ^O) to Bos:aina spp. some tins between 1939 and
1969. CeriOQap'nnia lacustris (Birge) and Chydorus sphaericus (Muller) have
been of secondary importance. We should also note an apparent decline of
Leptodora kiridtii (Focke) in 1970 and 1972, possibly due to size-selective
predation by fishes.
A basic trend at the ordinal level is evident (Table 2). Copepods
dominated these vaters in 1939 but had given way by 1969 to the cladocerans
(Fig. 1). Let's examine this trend, vhich cannot be supported by statistics
due to the fev samples collected in early years. This tr.end is not likely
to be confounded by sanrpling-gea r problems, as Tressler and Nauwerck used
comparable fine-mesh nets,, vhereas McNaught and Fenlon (197.2) found even
more Bosaina in 1970 with their coarser net. Thus, for the inshore vaters
of Lake Ontario ve have provided evidence that increases in standing crop,
for the few years sampled between 1939 and 1972, are associated with
increases in the relative proportion of cladoceraj with 19&9 aj-1 exceptionally
high year. The cladocerans constituted only 19$ of the July population in
1939, as contrasted to h8-8W from 1969 through 1972 (Table l).
A second trend suggesting & general increase in standing crop between
1939 and 1972 cannot be supported (Table 2). Obviously differences in mesh-
size of the nets used cause problems vith an equivalent sampling of
copepodites (Table 2). Thus ve have elected in addition to compare the
total numbers of Daphnia. spp. for June of 1939 and 1970, as uesh size was
the same. The comparison was further restricted to a comparison of the
seven samples collected by Tress3.er off Rochester to three collected by
llauwerck et_ al_. in the same area. The (3) July 1970 samples did not contain
Daphnia spp., the pulse of which was apparently delayed, until August 1970.
However, as shown below, the density-of Daj^hnia spp. in July 1939 was not
-58-
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significantly (p > 0.3) different than that in either J\>0y or August 1970.
July '39 July '70 Aug. '70
Mean Density 5900 0 5>i22
Students t 1.1|5 (HS) 0.123 (HS)
We must conclude that the extreme variation between the July 1939 samples
makes comparison impossible.
New Records for Species in Limnoplankton of Lake Ontario
In 1958 Anderson (1959) discovered the presence of Eu_ryteiao_ra affinis
(Poppe), a calanoid cppepod usually found in brackish waters, in Lake
Ontario. Since that time it has been discovered in Lake Erie in 1961 and
in Lake Huron in 1965 (Faber and Jermolajev, 1966). Nauwerck et_ al_, (1970)'
added Along, intermedia (Sars) and Macrocyclops albidus (Jurine) to the
Ontario fauna, two rare benthic foms constituting less than 0.02/5 of the
mean annual standing crop.
We have discovered three additional species, one of which is commonly
planktonic. Piaptomus ashlandi (Marsh) was collected in the shallow HE
sector at IFYGL stations 95 and 98 and at station 83 (0-lOm) in May 1972.
Macrothrix 1aticornis (Jurine) was- found in a 30m haul at station 96 and in
a 5m haul at station 8 off Toronto in August 1972. Ilyocryptus spinifer
Herrick vas found at station 31 offshore from 30 Male point in May 1972.
Both of these latter forms are conmonly substrate feeders, and may have
been taken when our net hit bottom.
Recent Changes in Community Structure
For comparative purposes Lake Ontario has been divided into inshore
-59-
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(9-50m depth) and offshore (> 50n depth) zones. Within these zones we have
compared total populations of zooplankton studied from 196? (Patalas, 19&9)
through 1972 (current report).
Total crustacean density (N), the community competition coefficient (a),
the theoretical community carrying-capacity (K), and the ratio of the
observed to theoretical carrying-capacity (N/K) are employed in these
comparisons. Each of these theoretical parameters (other than N) was
calculated from original values for each station, and not from lumped means
by cruise, using a program in Fortran IV written for the Univac 1108
computer.
Inshore: Two trends, including an increase in diversity (H) from 1969 to
1972 and the seasonal pattern of fluctuations in observed: theoretical
carrying-capacity, are noteworthy. Changes in yearly abundance (N) are
associated with gear selectivity, while the mean yearly community competition
coeffici/ent has not changed significantly (Table 2-3).
The diversity of the inshore populations increased from 1.77 bits in
1969 to 2.98 bits in 1972 (Table 3). The 1969 figure is for the Nine Mile
Point Area (Mcllaught and Fenlon, 1972), while the 1970 and 1972 estimates
are whole-lake averages. Use of the non-parametric Wilcoxon two-sample
statistic indicated a significant difference at the 80$ level (p <0.2)
between the 1969 and 1970' means, when July data were considered (Table 5).
This obvious increase in diversity was not due to the, addition of new species
(richness) in 1970, but to a change in their relative--abundance (evenness),
as clearly illustrated'in Table 5. The genera Eosmir.a and Cyclops were
relatively more abundant in 1970. An additional increase in diversity
occurred in these 2 months in 1972, but it was due tf the observation of
additional species (richness). This trend nust be explored in the future,
-60-
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for if it persists it indicates a change toward increased stability in inshore
areas. Usually shallow areas are more productive and less diverse with regard
to fauna and flora.
Additionally the theoretical carrying-capacity increased for comparable
months (June-July) from 1969 to 1970 (Wilcoxon non-parametric, p <0.2).
This change, however, must be treated with caution, since finer mesh nets
were employed in 1970, and numerically (U) 19^9 was not significantly
different than 1970.
The ratio of observed (N) to theoretical maximum (K) carrying-capacity
constitutes a new measure of the ability of r-selection animals to push
against environmental resistance (Lane and McNaught, 1973). R-selection
animals, by definition, have high population growth rates (r). An
interesting seasonal pattern has been observed for 1970. The K/K values
are highest in the spring (February-April). It is logical to hypothesize
that an increase in some available food resources nay permit zooplankton
populations to operate closer to theoretical carrying capacity in the spring.
Traditionally r-selection organisms have been described as filling only a
small fraction of their potential carrying-capacity, and this range for 1969
to 1972 is a consistent 6-2k% (yearly mean 9-12%} (Table 3).
Offshore: A similar pattern in the N/K ratio for the Crustacea vas noted
for the offshore waters in 1970 (Table M, with values greater 0.1^4 from
February through mid-July. In these offshore waters the mixing of nutrients
from deep waters may prolong the period of apparent stimulation of zooplankton
growth, as logically intermediated by increased autotrophic production.
As expected, diversity values are generally higher and more constant
for these offshore populations. This would imply a more stable environment
than in the inshore areas.
-61-
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Inshore-Offshore comparisons: Standing crops of crustacean zooplankton were
approximately three times as great in inshore vaters -per- unit volume in 1970
than in offshore areas (Tables 3~'»). Linited data for 1972 show less
difference. Along with differences in diversity, with the inshore vaters
slightly less diverse in terms of their crustacean populations (2.23 bits
vs. 2.56 bits), we have for 1970 the inage of a more productive but less
stable inshore zooplankton community. We will be able to deny or confirm
this observation when the 1972-73 IFYGL data have been processed. These
initial trends, preliminary in mature, should suffice to .draw our attention
to the limited perturbation of these communities today.
Significance
Crustacean abundance has been directly related to the degree of trophy,
especially phosphorus loading rat&s, in the Great Lakes (Patalas, 1972).
Lake Ontario is currently considered a morphometrically oligotrophic lake.
Its zooplankton populations, dominated to an increasing degree by the
Cladocera and Cyclopoida (Table 2), suggest that it is generally more
eutrophic than the upper Great LaJ--.es. This is especially true in the case
of Lake Superior, which is dominated by Calanoida (D i apt onus s i c i 1 i s ).
Relative to our stated purposes, ve have illustrated a shift at the
ordinal (Calanoida to Cyclopoida and Cladocera) and generic (Dajphnia and
Diaptoraus to Cyclops' and Bosruna) levels for the peri'od 1939-1972. At the
same time no significant change was discovered in total density of zoo-
plankton. For the recent period 1959-1972, significant increases in diversity
have occurred, due to increases in the evenness conponent. Conconitant changes
in carrying-capacity are questionable due to ssnip]ing techniques.
Standing crops of zooplankicn, even when they arc- as different as they
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References
Anderson, DrV., and D. Clayton. 1959. Plankton in Lake Ontario. Ontario
Dept. Lands and Forests, Phys. Kes. Note No. 1:7.
Faber, D.J. , and E.G. Jencol'ajev. 19^6. A new copepoci genus in the plankton
of the Great Lakes. Lionel. Oceanogr. 11:301-303.
Lane, P.A. , and D.C. McNaught. 1970. A mathematical analysis of the niches
of Lake Michigan zooplankton. Proc. 13th Conf. Great Lakes Res. 1970:
^7-57.
. 1973. A niche anslysis of the Gull Lake (Michigan, U.S.A.)
zooplankton community. Verh. Internat. Verein. Limiol. 18: (in press).
Levins, R. 1968. Evolution in changing environments. Princeton: Princeton
Univ. Press. 120 pp.
McNaught, B.C., and M. Fenlcn. 1972. The effects of thermal effluents upon
secondary production. Verh. Internat. Verein. Limnol. 18:204-212.
Nauverck, A., G. Carpenter, and L. Devey. 1972. The crustacean zooplankton
of Lake Ontario:1970. Tech. Rept., J. Fish. Res. Bd. Can. (in prep.).
Patalas, K. 19^9. Coraposition and horizontal distribution of crustacean
plankton in Lake Ontario. J. Fish. Res. Bd. Can. 26(8) :2135-2l6!4.
. 1972. Crustacean plankton and eutrophication of St. Lawrence
Great Lakes. J. Fish. Res. Bd. Can. 29(10) :ll*51-lli62.
Tressler, W.L., and T.S. Austin. 19^0. A linnological study of some bays
and lakes of the.Lake Ontario watershed. In 29th Ann. Rept. !?ev York
State Conserv. Dept., pp. 188-210. Albany, 1F.Y.
I
Whipple, G.C. 1913. Effect of the sewage of Rochester, H.Y., on the Genesee
River and Lake Ontario under present conditions. In Report on the sevege
disposal system of Rochester, H.Y., ed. E.A. Fisher, pp. 177-239.
Hew York: Wiley.
-63-
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Fig. 1. Changes, in ir.can yearly density (r.uir.ber/n3) and relative abundance
of- crustaceans of inshore vaters of Lake Ontario (1912-1972).
-64-
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90,000 r
90
c
ro
cr
UJ
h-
LJ
:> 60,000
cr
LJL)
CL
CT
L'J
CO
.>
5
z:
< 30,000
Lil
O
H
CD
Z)
cr
o
60
30
o
o:
LU
O
O
o
-------
Table I. Comparison of data sets used to compare zooplankton communities.
Author and
Year Published
Whipple (1913)
Trcssler and Austin
(19^0)
Pat alas (1969)
& Me Naught .and Fenlcn
' (1972)
Nruivsrck et al.
(1972)
McNaught and Buzzard
(this publ , )
Inclusive
Dates
Collection
15 August 1912
20- July 1939
June-Oct. 1967
Aug. -Oct. 1969
July-Aus- 1972
Jon. -Dec. 1970
15 Nay-lU July
1972
Gear and
Diameter
Cone net
Juday trap
Wisconsin net,
25 cm
Clarke-Bumpus
Cone net ,
Uo cm
Cone net,
30 cm
Mesh
Aperture
(y)
unknown
likely
6h y
77 y
13U y
6U M
151* u
Time
day/night
daytime
daytime
day/ night
daytime
day /night
day/night
Number
Samples
1
8
190
110
360
152
Depths
0-6m
0, 5, 10,
15, 20, 30,
ho and ^5m
0-5 Om
0, 5, 10,
15, 20, 30,
0-50 m or
0-bottom
0-5m
Area
1.6 km off
Rochester
U.8 km off
Rochester
vhole lake
1-8 km off
Osvego
vhole lake
whole lake
-------
TABLF 2. Xooplankton standing crops for July in inshore waters of Lake Ontario, with the exception of August 1972, in.number per meter^.
oo
o
Source
Year of Whipple
Order and species collection 1912
Cyclopoida
Copcpoditcs
Cvt'/ !>/>.•? liiriis/titlahif:
Trt>/»ir\'cl»]>s pyasi nits
Mi'siicyclojis cilax
Cycli>f>.-t n' malts
Total cyclopoida
Calanoida
Copopodiles
l)iti/>lttinii!i in inn t us
/)/«/>/< u»i«s or ego n CHS is
Diii/tlointts sicillis
I'uryli •iiiniti ntfiiiis
l.iiinii'Cftltiiinn inacfimis
Total cnlanoida
Total ropcpoda
Cladocora
lias in ina lniiffirost.ris
n-.ifil'.iiin >v/roc»/»"»Yi
1 )/i />/; n in 1 itiifi'ire niia
Ci'i'i'iilrtfilniia lactmlris
C 'liyi/onis it /iliac ricus
Li'(>lt>ilara kiiiellii
Total cladocora
Total cnistacca 30,000
Relative numbers
'.','. Cyclopoida —
fd Calanoida —
''.'• Cl:uloccx*a —
Tressler McNaught
and Austin and Fenlon
1939 • 1969
1,061
+ 15
0
0.
17
1,093
+ 215
0 "~
38
253
25,300 1,346
4,423^
302
5,900
218
95
0
30
5,900 6,958
31,200 8,304
81 1~ 13-2
' 3.0
18.9 83.8
McNaught
and Fcnlon
1970
29,207
0
0
0
0
29,267
510
0
15
531
29,7!)8
58,315 "I
1,187
74
148
220
38
59,982
89,780
32.6
O.G
CG.8
Nauwerck
' et al.
1970
+
1,191
32
0
80
20,000
346
28
20
4
429
20,429
31,731
24
219
MM!
G2
32,099
52,528
38.1
0.8
60.9
McNaught
and Buzzard
1972
1,020
13,138
43
26
73
14,300
114
35
30
42
17
GG
274
14,574
13,190
61 —
n
108
32
39
3
13,433
28,007
51.1
1.0
47.9
o
2.
O
a
g
0.
W
G,
!S3
D
-------
Table 3. Iv.shore populations, community structure during 1969, 1970 and 1972, including density, conpetition
coefficient, diversity, theoretical maximum carrying capacity and ratio of densitytcarrying capacity.
(N = Nauwerek; M = McNaught and Buzzard; P = Patalas.)
Year Day Month
1969 10 July
3.6 July
<* August
2'i August
27 August
31 October
MEAN 1969
1970 3-8 February
3-8 March .
31 March-!* April
28 Apr i 1-1 May
25-20 May
22-27 June
16-20 July
23 July
30 July
7 August
16-20 August
l't-19 September
13-3.7 October
16-20 November
7-11 December
KEAN 1970
1972 15-1? May
12-16 June
10-lU July
Data
Source
K
M
M
M
M
M
N
Jf
K
N
N
N
N
M
M
M
K
N
N
N
N
M
M
M
Total
Density
Crustacean
Eoonlankton
"(N)
number /m3
5,197
9,350
12,623
7,821
l*,5l*2
8,917
8,075
31*1
1,1*70
1,201*
1,89U
5,118
1»,253
1*0,1*8?
102,1(26
69,750
58,870
3l* ,085
28,165
1*2,761
7,^38
2,573
26,722
1,272
2,236
25,665
Community
Competition
Coefficient
(a)
with
variance ()
.50 (.13)
.56 (.10)
.1*8 (.lU)
.33 (.12)
.36 (.10)
.32 (.18)
.1*3
.1*9 (.08)
.56 (.10)
.1*1* (.11)
.35 (.09)
.38 (.22)
.28 (.1).)
.28 (.12)
.3U (.11)
.33 (.07)
.36 (.08)
.1*8 (.1C)
.39 (.10)
.52 (.11)
.U. (.08)
.55 (.1U)
.1*1
.1*3 (.15)
.30 (.09)
.27 (.06)
Theoretical
Carrying
Capacity
(K)
number/m^
1*6,857
9!*,l61*
8l,l7l»-
71,1*86
33,796
51,626
63,181.
2,137
11,072
5,103
10,753
71,922
31,705
377,91*3
967,581
573,701)
1*33,160
277,51*9
196,155
393,1*26
66,260
25,877
229,623
9,866
36,1*13
303,770
Ratio
Observed to
Theoretical
Carrying-
Capacity
(N/K)
.11
.-10
.12
.11
.13
.17
.12
.16
.13
.2U
.18
.07
.13
.11
.12
.12
.11*
.12
.11*
.11
.11
.10
.13
.13
.06
.08
Diversity
(H)
1.90
1.57
1.56
1.8U
2.01*
0.57
1.77
2.29
1.149
2.50
2.36
0.99
2.27
2.07
2.1)1
2.11*
2.30
2.57
2.6l
2.1*0
2.63
2.55
2.23
3.00
2.86
3-07
MV.AN 1972
9,72).
.33
15,'
.09
2.98
-------
Table 4. Offshore populations, community structure during 1968, 1970 and 1972, including density, competition
coefficient, diversity, theoretical maximum carrying capacity and ratio of density:carrying-capacity.
(N = Nauverck; M = McNaught and Buzzard; P = Patalas.)
Yea
1968
1970
,
&
VO
1
1972
r Day Month
12-13 September
3-8 February
3-8 March
31 Mareh-1* April
28 /Voril-1 May
25-29 May
22-27 June
16-20 July
16-20 August
il|-19 September
13-17 October
16-20 November
16-20 December
MEAN 1970
15-19 May
12-16 June
10-1 '4 July
Data
Source
P
N
N
N
N
N
N
N
N
N
N
N
N
M
M
M
Total
Density
Crustacean
Zooplankton
(N)
number/m3
28.7
793
987
661
1,581
8U6
2,168
9,787
32,269
19,139
19,3l»8
U,637
l,ll*6
7,780
952
3,1*10
31,963
Community
Competition
Coefficient
U)
with
variance ( )
.52 (.11*)
.1*6 (.09)
.51* (.10)
M (.HO
.^3 (.09)
.61 (.13)
.39 (.13)
.32 (.09)
.U8 (.20)
.1*9 (.07)
-55 (.11)
,>*5 (.13)
.57 (.05)
.1*8
.51 (.11)
.28 (.08)
.27 (.09)
Theoretical
Carrying
Capacity
"(K)
number/m3
509
1*,097
5,502
2,527
6556U
6,121
11,078
71,067
283,256
153,952
185,019
1*2,18)4
7,51*2
6U,909
7,6l8
27,1*53
358,969
Ratio
Observed to
Theoretical
Carrying-
Car)acity
(N/K)
.06
.19
.18
.26
.21*
.11*
.20
.11*
.11
.12
.11
.11
.15
.16
.13
.12
.09
Diversity
(K)
2.93
2.59
2.56
2.28
2.70
2/UH
2.37
2ji8
2..55
2.69
2.82
2J'8
2. '7 3
2/56
3.07
2.81*
2.77
MEAN 1972
12,108
.35
131,3^7
,11
2.89
-------
Table 5. Richness and evenness components of diversity for inshore waters
of Lake Ontario during June-July (1969-1972).
Date
10 July 1969
16 July 1969
20 July 1970
23 July 1970
30 July 1970
12-16 June 1972
10-14 July 1972'
Diversity (bits)
1.90
1.57
2.07
2.141
2. Ill
2.814
2.77
Richness
3.92
3.8?
2.60
1.80
2.70
5.37
H.5H
Evenness
1.71
1.1.1
2.07
2.^1
1.98
2.22
2.10
-70-
-------
ANNUAL PROGRESS REPORT
ALGAL NUTRIENT AVAILABILITY AND LIMITATION IN
LAKE ONTARIO DURING IFYGL
Grant Number 800537
July 1, 1972 - June 30, 1973
G. Fred Lee
William Cowen
Nagalaxmi Sridharan
Environmental Chemistry
Department of Civil Engineering
Texas A&M University
College Station, Texas 77843
-------
OBJECTIVES OJr' THE PROJECT
The objectives of this project were to 1) determine the
limiting nutrient or nutrients in tributary and open waters
of Lake Ontario with the standard Algal Assay Procedure
(AAP) test; 2) estimate the extent of nutrient regeneration
from Cladophora after death of the organism-; and 3) determine
the availability to algae of particulate-phosphorus forms
in tributary waters, urban stormwater drainage, and
precipitation, and the extent of mineralization of particu-
late nitrogen in tributary waters.
The original operational plan also included a study of the
nitrogen and phosphorus nutritional status of Cladophora
growing along the New York State shore.. This project and
much of the Cladophora nutrient regeneration study had to
be curtailed because of the difficulty of receiving fresh
algal samples. The funds to be used for these projects were
instead used to sample the New York tributaries during the
high flow period of 1973.
STATUS OF THE PROGRAM
Very limited Cladophora nutrient regeneration studies were
performed during the fall and summer of 1972, along with
some work on nitrogen and phosphorus availability in
tributary and runoff waters. The major part of the sampling
"This project is also conducted at the University of
Wisconsin, Madison, Wisconsin.
-71-
-------
for the bioassay program was accomplished during field
trips on 6-7 April, 30 April-1 May, 27-28 May, and lb-17
June, 1973. Figure 1 shows-the sampling sites for
tributaries and open lake stations. Samples have also been
received from the New York State Department of Environmental
Conservation since July of 1972, and from Dr. Moore in
Oswego since February of 1973. New York rain gage water_
samples were not received until July of 1973, so that this
phase of the program is considerably behind schedule.
Laboratory work on all samples except the last set of open
lake water and the rain gage water has been essentially
completed. As specified in our contract, we will try to
bioassay additional rain gage samples as they are received.
With this exception, the laboratory research should be
completed by mid-August, 1973.
SUMMARY OF RESULTS TO DATE
Cladophora Nutrient Regeneration
Tables I-III summarize the limited data available from
fresh Cladophora samples collected in Lake Ontario and
(for comparison) Lake Mendota, Wisconsin. The' cellular
nitrogen (N) and phosphorus (P) data were obtained from
Kjeldahl-digested and wet-ashed subsamples of algae, on
an oven-dry basis. The subsamples were spun-dry to oven-dry
weight, so-that the cellular N and P levels of the spun-
dry algae used in the regeneration tests could be calculated.
The samples were stored under aerobic conditions i?n darkness
at 22-27°C., with and without chloroform for phosphate
regeneration and without chloroform for nitrate regeneration.
Tables I and II show that the percent of cellular phosphate
converted to dissolved reactive phosphorus (DRP) reactive
to a molybdenum-blue color reagent (Standard Methods, 13th
ed., 1971) was extremely variable, ranging from 21 to 100
percent. Generally, the maximum extent of regeneration
was completed by 5-7 days with chloroform and by 50 days
without chloroform.
The conversion of cellular nitrogen to nitrate (Table III)
was somewhat less variable, with a range of 12-40 percent.
The nitrogen mineralization was relatively show, with
increases in NOl still occurring between 50 and 100 days.
-72-
-------
Figure 1
Lake Ontario and Tributary Water Sampling Sites
geconnaifjonte No.
Beaver Is. D&te
Park Time
Bu"*'° KILOMETERS
Black
River
-------
Table I
Release of Dissolved Reactive Phosphorus
from Chloroformed Cladophora
SampJLe
Mendota - 1
Mendota - 2
Oswego
Rochester
Date
Collected
15 Jun 72
23 Jun 72
8 Jul 72
21 Jul 72
P Content
ug P/mg Algae
0.9
1.1
0.7
1.1
Incubation,
Days
5
5
5
5
P Release in 5 days,
ug P/mg Algae (Range)*
0.59-0.94
0.86-1.3
0.24-0.46
0.70-0.90
% P Released
(Range)*
66-104
75-118
34-65
64-82
* Three portions of algae from each sample.
Table II
Release of Dissolved Reactive Phosphorus
from Cladophora Incubated in Darkness
Sample
Mendota - 1
Oswego
Rochester
Toronto
Date
Collected
15 Jun 72
8 Jul 72
21 Jul 72
16 Aug 72
P Content
ug P/mg Algae
0.9
0.7
1.1
1.6
Incubation,
Days
50
50
51
50
Max P Release
in 50 Days
ug P/mg Algae (Range)*
0.50-0.58
0.64-0.86
0.87-0.98
0.34-0.38
% P Released
(Range)*
57-64
90-121
79-89
21-24
* Three portions of algae from each sample,
-------
Table III
Formation of Nitrate
from Cladophora Incubated in Darkness
Sample
Mendota-1
Oswego
Rochester
Toronto
Date
Collected
15 Jun 72
8 Jul 72
21 Jun 12
16 Aug 72
N Content
ug N/mg Algae
20
57
22
27
Incubation,
Days
102
100
100
100
N03-N Released
in 100 Days
ug N/mg Algae (Range)*
4.4-4.9
6.8-10
8.4-8.7
6.2-9.0
% N Released
(Range)*
22-24
12-18
38-40
23-33
*Three portions of algae from each sample
-------
AAP Study on Nutrient Limitation in New York Tributary Waters
and Lake Ontario Water
All samples assayed were autoclaved at 15 psi for 15 minutes,
then cooled and filtered through 0.45 micron pore-size
millipore filters before inoculation with nutrient spikes
and Selenastrum capricornutum. Growth stimulation was
followed By absorbance measurements (7bO nm) at 48-hour
intervals until a plateau was reached.
Figure 2 is a representative summary of an AAP test nutrient
spike study, performeo on the Genesee River sample #34,
collected 7 April 1973. Only the averages of three replicate
flasks of each treatment are shown, for clarity. Neither
N spikes nor N+ micronutrient spikes significantly enhanced
the growth of Selenastrum in the sample over the unspiked
control. In contrast, the phosphorus spike alone caused a.
significant growth response, indicating phosphorus limitation.
No conclusions about limitation in the rivers can be made,
however, until all the data have been compiled from the
spring sampling trips.
Carbon-14 assimilation rate measurements made on Lake Ontario
water (open-lake and near shore) collected before February
1973, generally showed stimulation of the natural phyto-
plankton only when spiked with P+N, or P+N+micronutrients.
The data from water collected on spring sampling trips by
the Canadian Centre for Inland Waters is still being
processed.
Nitrogen Mineralization in New York Rivers
Table IV shows the results obtained thus far from river samples
collected in the spring of 1973. The results are expressed
as the maximum percent of the total N which appeared as
nitrate in the incubations. In some cases the experiments
have not been completed, so the most recently reported valme
is given.
The overall range of nitrogen availability was found to be
60-91 percent of the initial total nitrogen (total Kjeldahl-N
plus nitrate) of the samples. In all cases, the final
ammonia levels were not significant compared to the nitrate
levels, so tnat "readily available" nitrogen was considered
to be represented by nitrate alone. Experimental results
from later samples collected in May and June have not yet
been evaluated.
-76-
-------
0.8
0.7
0.6
0.5
0.4
0.3
0.2
0.1 -
O O O Sample #34
O n D Sample #34 H- P
A A A Sample #34 + N
O O O Sample #34 + P + N
A A A Sample #34 + N + Micro
• • • Sample #34 + P + N
+ Micro
12 16
Time, Days
20
24
-77-
-------
Phosphorus Availability in Tributary Waters to Lake Ontario
The samples used for particulate-phosphorus availability
studies included those from the New York rivers and from the
Genesee River Basin study. Table V shows the sampling
stations and the major land use classifications of the
Genesee Basin study. Only selected samples were studied for
particulate-phosphorus (PP) availability because of the
very low concentrations of PP in many of the samples.
Tables VI and VII summarize the phosphorus chemistry of the
samples extracted with dilute HC1-H2S04, O.lW NaOH, Dowex-1
anion exchange resin, or with Selenastrum in growth assays.
Only two samples showed a PP availability of greater than
50 percent; these were found with acid extractions. Ex-
tractions with base and resin showed less available P than
did acid extractions in most cases, and 18-day algal assays
showed the lowest levels of available P. Autoclaved particles
showed availability percentages similar to basic extracts.
In all tests, the particles were isolated on 0.45 micron
pore size tilters. Total P, total soluble P and PP data are
based on a persultate digestion method (Standard Methods,
13th ed., 1971).
The same types of tests were conducted on Genesee River
particulate matter, as shown in Table VIII. The results of
acid extracts were extremely variable, while the results
o± the base, resin and algal extractions were similar to
those from the Genesee Basin study (Table VII).
Bioassays of river particulate matter generally showed
that less than 6 percent was available to Selenastrum over
18 days (Tables VIII and IX). In contrast, autoclaved
particles released 26-57 percent of their phosphorus for
algal growth.
In an effort to directly estimate the availability of total
phosphorus (TP) in the river samples, chloroform was added
and the resultant increase in DRP was monitored with time,
as proposed by Berman (197-0). Figure 3 illustrates a
typical 7-day release pattern for an Oswego River sample,
with and without a condensed phosphate (sodium tripoly-
phosphate--TPP) spike added to demonstrate the presence of
active phosphatases in the chloroformed sample. The final
DRP level exceeded the initial total soluble P (TSP) value,
demonstrating that some of the released DRP must have come
from an insoluble source, i.e., particulate-phosphorus.
Table X summarizes the data from such tests run on other
river samples. The Genesee results were extremely variable,
while the results from other rivers seemed to be less
variable, with averages of 33-64 percent of the TP available
in the test.
-78-
-------
Table IV
Mineralization of Kjeldahl Nitrogen
in Samples Incubated in Darkness
NO~-N, mg N/l
Sample
Oswego
Oswego
Oswego
Oswego
Genesee
Genesee
Niagara
Black R
Black R
No.
R - #28
R - #31
R - #35
R - #43
R - #34
R - //42
R - /Ml
- #36
- #44
Date
Collected
2
28
7
1
7
1
30
7
1
Mar
Mar
Apr
May
Apr
May
Apr
Apr
May
73
73
73
73
73
73
73
73
73
Day
Maximum Maximum
Initial Observed Observed
0.61
0.68
0.56
0.46
0.98
0.56
0.14
0.47
0.24
1.
1.
1.
0.
1.
1.
0.
0.
0.
06
01
05
92
32
05
32
56
37
82
64**
64**
28
64**
28
28
64**
28
Initial
Total N,*
mg N/l
1.
1.
1.
1.
2.
1.
0.
0.
0.
34
27
16
42
21
52
45
89
59
Max % Total N
Avail as NO^-N
mg N/l
79
80
91
65
60
69
71
63
63
* Kjeldahl N + NOg-N before incubation
** Experiment still in progress
-79-
-------
Table V
Station
No.
U.S.G.S.
Map Name
LOCATION OF SAMPLING STATIONS
GENES'EE RIVER BASIN
Land Use
1
2
3
4
5
6
7
8
9
Byron-
Rocheste* East
Geneseo
Geneseo
Geneseo
Springwater
Dansville
Dansville
Andover
Cropland Spring Creek
Urban Allen Creek
(Beginning of pasture)
Pasture Jaycox Creek
(Beginning of Pasture)
Forest Bri'ggs Gully
High density residential
Beginning of H.D.R.
Brushland Eas't Valley Creek
-80-
-------
Table VI
Phosphorus Forms
in Genesee River Basin Samples
Sample
Number
402-6
402-8
404-8
407-8
409-8
402-9
409-9
502-1
502-7
507-7
502-8
504-8
507-8
507-9
502-10
502-11
507-11
501-12
502-12
507-12
501-13
507-13
501-14
502-14
507-14
Date
Collected
6 Oct 72
3 Nov 72
2 Nov 72
2 Nov 72
2 Nov 72
15 Nov 72
14 Nov 72
15 Dec 72
22 Mar 73
20 Mar 73
4 Apr 73
4 Apr 73
3 Apr 73
17 Apr 73
1 May 73
6 May 73
15 May 73
30 May 73
30 May 73
30 May 73
12-13 Jun 73
12-13 Jun 73
26 Jun 73
26 Jun 73
25 Jun 73
DRP
72
70
182
27
<1
55
14
27
24
19
54
6
2
15
37
2
3
43
2
1
5
6
59
9
Phosphorus,
TSP
77
78
193
29
8
66
26
35
26
4
27
60
4
2
22
46
5
12
55
4
4
9
7
66
10
ug P/l
TP
118
188
350
361
131
112
2140
60
69
39
59
452
29
27
79
81
22
60
165
32
31
239
38
129
284
PP
41
110
157
332
123
46
2110
25
43
35
32
392
25
25
57
35
17
48
110
28
27
230
31
63
274
-81-
-------
Table VII
Chemical and Biological Extraction
of Particulate-Phosphorus in Genesee River Basin Samples
Average Per Cent of Particulate-P Extracted
by
Station No.
1 (Byron)
2 (Rochester East)
4 (Geneseo)
7 (Dansville)
9 (And over)
Sample
Number
501-12
501-13
501-14
Averages
402-6
402-8
402-9
502-1
502-7
502-8
502-10
502-11
502-12
502-14
Averages
404-8
504-8
Averages
407-8
507-7
507-8
507-9
507-11
507-12
507-13
507-14
Averages
409-8
409-9
Averages
Acid
25
18
22
22
42
40
60
—
—
—
—
46
49
52
48
29
29
29
35
34
—
29
28
30
28
30
30
23
35
29
Base
11
18
10
13
27
29
37
—
37
25
—
29
27
27
30
18
19
18
18
26
32
10
16
24
15
10
19
16
21
18
Resin
1
7
10
6
27
24
22
—
28
18
—
28
27
25
25
17
18
18
10
6
8
12
16
14
14
5
11
7
11
9
Algae
< 4
—
<10
< 7
•__
—
—
<12
22
21
24
< 1
< 5
< 2
<12
_r*nr
7
7
«.—
< 3
< 5
< 2
< 3
< 1
—
2
< 3
m.^
—
—
Algae
(Particles
Autoclaved)
__
16
20
18
__
—
—
—
—
—
—
—
—
34
34
_w
—
—
__
—
—
—
—
— .
8
10
9
-82-
-------
Table VIII
Chemical and Biological Extractions
of Genesee River Particulate-Phosphorus
Average Per Cent of Particulate-P Available to
Algae
PP Algae (Particles
Sample No. ug P/l Acid Base Resin (Selenastrum) Autoclaved)
Genesee R - #34 360 79 11 9 2
Genesee R - #42 105 58 18 24 <6
Genesee R - #51 62 44 27 31 <2 41
Genesee R - #58 146 21 12 5 <1 36
-83-
-------
Table IX
Biological Extractions of New York
River Particulate-Phosphorus
Average Per Cent of
PP Particulate-P Available to Algae (Selenastrum)
Sample No. ug P/l Particles Not Autoclaved Particles Autoclaved
Niagara R - #50 19 <5 57
Niagara R - #56 26 — 33
Oswego R - #43 50 <1
Oswego R - #47 48 <2
Oswego R - #52 47 <2 44
Oswego R - #59 86 — 32
Black R - #44 20 5
Black R - #53 25 <3 45
Black R - #60 75 — 26
-84-
-------
180 -
O—OO Sample (55 +CHC13
Sample i?55 +CHC13
+ 100 ug P/l TPP
100 ug P/l TPP
CHCl3.in H20
20 _
Days Incubation
-85-
-------
Table X
Increase of Dissolved Reactive Phosphorus
During Incubation of New York River Water with Chloroform
DRP. ug P/l
% TP available
Sample No.
Fort Niagara
Niagara R - #27
Niagara R - #33
Niagara R - #50
Niagara R - //56
Beaver Island Park
Niagara R - #49
Niagara R - #57
Genesee
Genesee R - #34
Genesee R - #51
Genesee R - #58
Oswego
Oswego R - #22
Oswego R - #23
Oswego R - #24
Oswego R - #26
Oswego R - #29
Oswego R - #31
Oswego R - #35
Oswego R - #52
Oswego R - #54
Oswego R - #55
Oswego R - #59
Black
Black R - #25
Black R - #36
Black R - #53
Black R - #60
* 8 days
** 9 days
Date
Collected
26 Feb 73
28 Mar 73
27 May 73
15 Jun 73
27 May 73
15 Jun 73
29 Mar 73
28 May 73
16 Jun 73
7 Aug 72
7 Aug 72
1 Sep 72
1 Sep 72
12 Mar 73
28 Mar 73
29 Mar 73
28 May 73
31 May 73
4 Jun 73
17 Jun 73
28 Aug 72
29 Mar 73
28 May 73
17 Jun, 73
Initial
4
5
1
26
2
3
26
104
49
58
49
4
79
78
43
47
50
40
35
46
14
7
5
13
+CHC13
(1 day)
9
11
12
27
14
17
32
111
63
64
66
59
96
80
46
62
61
49
51
77
19
11
15
28
+CHC13
(7 days)
10
14**
16
30*
22
20*
36**
122
76*
71
63
46
75
82
49
67**
70
57
59
88*
16
15**
17
37
TP
ug P/l
18
34
26
59
Average
51
86
Average
386
173
204
93
96
88
154
131
95
105
104
87
96
147
Average
53
34
41
99
Average
+CHC13
(7 days)
56
41
62
51
53
43
23
33
9
70
37
76
69
67
62
62
52
64
67
66
61
60
64
30
44
41
37
38
-86-
-------
Dark, long-term incubations of river water with and without
Dowex-i anion exchange resin have also been conducted on
these samples; however, the data have not been completely
evaluated at this time. In addition, AAP-type growth assays
have recently been run on autoclaved, filtered samples to
quantitate the level of available P resulting from such
treatment.
REFERENCES
Herman, T. Alkaline Phosphatases and Phosphorus Availability
in Lake Kinneret, Limnol. Oceanogr., 15, 663-674 (1970).
APHA, AWWA WPCF. Standard Methods for the Examination of
Water and Wastewater, 13th Ed. APHA NY (1971).
-87-
-------
ANNUAL REPORT
Grant Number R-800605
ANALYSIS OF PHYTOPLANKTON COMPOSITION AND ABUNDANCE DURING IFYGL
E. F. Stoermer
Great Lakes Research Division
University of Michigan
-------
This project was initiated as part of an integrated series of investigations
of Lake Ontario under the general aegis of the International Field Year Great
Lakes. In its original conception this project was planned primarily as an
attempt to construct a precise model of the hydrological characteristics of Lake
Ontario. Since it was recognizedjfhat the unique bank of physical data generated
by this project would have great utility in constructing a more general process
model of the Lake Ontario 'ecosystem, an attempt has been made to also gather a
similar bank of coherent biological and chemical data to facilitate the con-
struction of the more general model. This effort was carried out largely within
the constraints imposed by the demands of original project concept.
The specific objectives of the particular project discussed here are to
provide an assessment of the phytoplankton populations present in the lake and
their seasonal cycles of distribution and abundance. Operationally, the problem
was approached through a sampling design of 60 stations (shown on Figure 1)
sampled at monthly intervals during prime growth periods and bimonthly otherwise.
Samples are taken from standard depths at all stations. At deepest stations, a
total of 12 samples are taken and sampling sequence is truncated in shallower
depths.
The major effort in the project is devoted to development of population
abundance estimates for the species of phytoplankton occurring in Lake Ontario.
Method used is direct microscopic identification and enumeration from material
prepared as semipermanent slides in the field. Rapid gross estimates of total
particle abundance are also made on all samples, using an automatic optical
occlusion particle counter-slzer operating in the range of 5-150um.
Splits from the same samples used in preparation of slides analyzed in the
project are also filtered, preserved, and set aside as permanent archival ref-
erences. It was felt that this project furnished a unique opportunity to
-90-
-------
develop a coherent set of base line information of the type sadly lacking in the
Laurentian Great Lakes. At the end of the project, this material will be deposited
with the Smithsonian Institution.
Partially as an independent cross calibration, and partially as a comparison
with the methods used by other projects, a limited number of extracted chlorophyll
determinations were made by the fluorometric method generally utilized in our
laboratory. These measurements were made on samples taken from 5 "master"
stations. Primary responsibility for development of standing crop estimates
through chlorophyll measure is part of another project.
There has been considerable deviation from the original concept and plan
in the actual sampling operation serving this project. The original plan called
for sampling beginning in April and proceeding throughout the year with the same
basic array of stations being sampled on every cruise. Due to the unavailability
of a sampling platform, it was necessary to "scratch" the planned cruise in
April of 1972. Due to adverse weather conditions and the constraints on platform
availability, sampling on the May cruise was only about 50% effective. Due to
these problems, plus the fact that highly unusual weather conditions introduced
the possibility that biological responses in the spring of 1972, during the grand
period of phytoplankton growth might be atypical, led to the consideration of
extension of the originally planned sampling exercise. After consultation with
representatives of other projects involved in biological and chemical measurements,
it was decided to extend the sampling operation through June of 1973. Due again
to the constraints on availability of sampling platforms, it was necessary to
somewhat restrict the number to stations sampled during each cruise. The total
effect on this particular project has been to considerably increase the amount
of time devoted to field sampling operations and to somewhat increase the total
number of samples that it is necessary to analyze beyond the number originally
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planned. Requests for time extension and funding increase consistant with the
increased work load have been submitted with this year's renewal request.
Current Status of Project
Archival Samples
All archival samples have undergone final processing and labels have been
printed. Material is presently being labeled and packed for shipment to final
repository. A total of 3677 samples are available. Summary listing of the
samples available is shown in Appendix A. Printouts of sample labels can be
furnished on request. This phase of the project is essentially on schedule.
Particle Count Analyses
Initial analysis has been completed on all samples and raw data from these
runs is given in Appendix B. Work is presently underway to calibrate these
values against other estimates of phytoplankton standing crop. Card form raw
data summaries can be furnished on request, but potential users should be advised
that raw data reflects total particulates. This phase of the project is essentially
on schedule. Further progress will depend on availability of chlorophyll and
cell count data.
Microscopic Cell Counts
Analysis has been completed for all surface stations. Summary representations
of total cell numbers are included in Tables 1-10 following. Numerical data
for particular stations or distributions of particular species can be furnished
if urgently needed but we ask that such requests be kept to a minimum due to
expense involved in dumping interum summaries. Current emphasis in this phase
of project is in completing analyses of depth series data from master stations.
This phase of project has suffered most from extension of -sampling program due to
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the necessity of diverting personel from lab to field operations. At present
we estimate that this phase of the investigations is approximately 2 months
behind originally projected schedule.
Summary of Results to Date
Perhaps the most striking feature of the phytoplankton data we have developed
so far is the extreme variability of the phytoplankton assemblage both in respect
to total abundance and in respect to the distribution of particular entities.
The dominant seasonal pattern, as would be expected, appears to be the
development of a spring bloom beginning-at isolated localities nearshore during
March and developing in all nearshore waters by April. In 1973, high concen-
trations of phytoplankton were first noted at isolated stations on both the north
and south Chores in March (Fig. 8). By April of the same year cell counts over
2000 cells/ml were noted at most stations on the north shore east of 79° (Fig.
9). Total abundance figures were less for stations on the south shore, running
between 1000 and 2000 cells/ml, except at stations near Rochester and near
Thirty Mile Point, where they exceeded 2000 cells/ml. During this sampling period
counts appeared to be lower in the extreme western end of the lake and higher
in the northeastern island area. There, however, did not appear to be any
consistant east-west trend in phytoplankton abundance in the offshore open water
region of the lake. During the May 1972 sampling period (Fig. 1) total cell
counts over 2000 cells/ml were noted at shoreward stations east of 78° 30' with
highs of over 5000 cells/ml at stations in Mexico Bay and in the North Channel-
Prince Edward Bay region. At this time ce]JL counts in the mid-lake region were
on the order of 1000 cells/ml. During this sampling period there appeared to be
a trend toward lower values in the western end of the lake, both in the waters
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nearshore and in the open lake but a large portion of the eastern region was
not sampled. During the June 1972 sampling period (Fig. 2) total cell counts
over 2000 cells/ml were noted at most stations sampled. Much lower abundances
were noted at a rather narrow band of stations offshore (near 43° 30" N) and
near Niagara. Much higher counts were found over a wide area near Toronto and
at two isolated stations in the eastern end of the lake. During the June 1973
sampling period, however, distribution was much less consistent (Fig. 10). Total
cell counts greater than 5000 cells/ml were noted at isolated stations offshore
and there did not appear to be any consistent trend, either east-west or with
respect to distance from shore. In July 1972, total phytoplankton abundance
declined rather drastically from levels reached in June of the same year (Fig. 3).
At this time, highest cell counts were found at stations just east of Niagara.
Somewhat lower peaks, somewhat more than 2000 cells/ml, were noted at isolated
stations near Toronto and offshore in the eastern end of the lake. In August
of 1972 fotal phytoplankton abundance declined at all stations in the western
sector of the lake, with somewhat higher abundances being maintained in the
vicinity of Toronto and Niagara (Fig. 4). Total cell counts in the eastern
sector, however, increased with total cell counts in excess of 2000 cells/ml
being found at stations near Rochester and at all stations sampled in the eastern
islands region. During the October 1972 sampling period phytoplankton abundance
was moderately high at all stations sampled, with no particularly striking areal
pattern being evident (Fig. 5). Highest abundances were noted at stations between
Hamilton and Niagara at stations nearshore. Total phytoplankton abundance
continued to decline and during the November 1972 sampling period (Fig. 6). No
particularly striking trends were evident, but there appeared to be a tendency
toward higher abundance in the sectors of the lake near Toronto and Rochester.
Lowest overall abundances noted during the study to date were found in February
1973 sampling (Fig. 7). Total cell counts were less than 200 cells/ml at most
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stations in the southern and western portions of the lake, with somewhat higher
levels being found in the vicinity of Toronto, Niagara, Rochester and Oswego.
Higher values were found at stations near the northern and northeastern shore,
with highest values, on the order of over 1500 cells/ml, found at stations
south and east of Prince Edward Point. It appears that during this sampling
period phytoplankton abundance was significantly higher at all stations in the
northeastern sector of the lake, although the reduced sampling density makes the
overall distribution pattern somewhat difficult to interpret.
In inspecting the summaries presented in the figures, it should be kept in
mind that the numbers refer only to cell counts and are not correct for cell
volume. In some cases further refinement of the data may tend to smooth some
of the apparent inconsistencies that are present, but it is doubtful that any
major change in interpretation will result.
In some respects it is surprising that the phytoplankton density data do
not more clearly reflect the presence of major pollution sources. In certain
cases, such as June 1972 and February 1973, such trends are apparent but in many
instances particularly high phytoplankton abundances are not obviously related
to major pollution sources. Perhaps the most surprising result in this context
is the apparent initiation of the spring bloom and consistently high values
found in the northeastern sector of the lake.
It is apparent from inspection of the phytoplankton preparations that grazing
may play a significant part in modifying apparent trends in phytoplankton
abundance. Prepared slides from many localities have unusually high levels of
protozoans and rotifers in addition to the phytoplankton. Although we have not
made quantitative estimates of the abundance of these entities, it appears that
their abundance is quite closely related to localities having apparent nutrient
sources. Further analysis of this situation awaits input from the ztfoplankton
projects.
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Although we have not yet attempted to plot the distribution of particular
species in detail, it is obvious from inspection of the raw data that there is
an extermely high degree of variability in population dominance at different
stations.
During the initial sampling period in May 1972 the predominant taxa were
the smaller species of Stephanodiscus, including jS. minutus, jS, tenuis, J3.
subtilis, and at certain stations _§_. binderanus. Often large but highly
variable populations of microflagellates were noted at most stations. The
most abundant species were Cryptomonas erosa and Rhodomonas minutus, although
several other species were occasionally present in high numbers. Scenedesmus
bicellularis was particularly abundant at stations where high total counts
were found. Most abundant taxa at offshore stations were Melosira islandica,
Asterionella formosa and occasionally Fragilaria crotonensis. Occasional high
populations of Per id inium spp., Ankistrodesmus falcatus et var., and Anacystis
incerta were also noted. Although not numerically dominant at any station,
Surirella angustata was common in most collections as was Diatoma tenue var.
elongatum.
Essentially the same dominant assemblage was present in the June 1972
collections with Stephanodiscus binderanus, several species of microflagellates
and Scenedesmus bicallularis being the overall predominant forms, particularly
at stations having high standing crop levels. Melosira islandica, Fragilaria
crotonensis and Asterionella formosa remained relatively abundant at some sta-
tions, particularly offshore. Isolated abundant occurrences of Gloeocystis
planctonica and Coccomyxa coccoides were also noted.
During July the former of these two species continued to increase, while
most of the dominant species in the early spring flora were on the wane.
Microflagellates continued to be abundant but dominant forms at most stations
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were Chrysochromulina parva and Dinobryon spp. although Cryptomonas erosa
continued to be abundant. Stephanodiscus subti-lis and Diatoma tenue var. elongatum
were the most abundant diatoms.
In August the dominant species at most stations were Pragilaria crotonensis,
Gloeocystis planetonica, and several members of the genera Anabaena, Oocystis,
and Pediastrum. At some stations the green flagellates Eudorina and Phacotus
were quite abundant along with species of Botryococcus, Ulothrix, Gomphosphaeria
and the only diatom which occurred in abundance at this time, Stephanodiscus
subtilis. Although still present in most samples, the abundance of microflagellates
was strongly reduced during this sampling period.
In October the abundance of microflagellates again increased with Chrysochro-
mulina parva, Rhodomonas minuta and Chlamydomonas spp. being the primary taxa
present. During this sampling period there was also a considerable relative
increase in populations of the blue-green algae Gomphosphaeria wichurae,
Anacystis incerta, and A. cyanea. The diatoms Fragilaria crotonensis,
S t epha nod is cu s subtilis and J3. tenuis were also conspicuous dominants at several
stations.
In November the species of Gomphosphaeria and Anacystis and the microflag-
ellate taxa which had become established the previous month remained abundant,
but the diatom component of the flora was dominated by Asterionella formosa.
Somewhat surprisingly, the two blue-green taxa which were abundant in
November remained conspicuous in the February collections. Otherwise the rather
depauperate assemblages collected during this sampling period were dominated
by S t ephanod iscu s alpinus, S_. hantzschil, Asterionella formosa and Scanedesmus
bicellularis.
During March the diversity of the phytoplankton assemblage appeared to
increase substantially with the spring dominants noted the previous year being
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the most abundant taxa. This pattern of dominance remained about the same
throughout the rest of the sampling period, with one notable exception.
Stephanodiscus binderanus which had been the overall dominant, especially in
June of the previous year, was strikingly reduced in abundance at all stations.
Although it was still present ±n most collections, it tended to be replaced in
dominance by the smaller species of Stephanodiscus referred to earlier and,
particularly at some stations in June, by JS. subsalsus which had been quite rare
in collections taken the previous year.
The overall impression gained from our preliminary observations on Lake
Ontario is that of a highly disturbed system in which the biological operators
and seasonal trends differ considerably from those found in the upper Great Lakes.
The striking nature of this difference led one of the people working on the
project to make the succinct observation that Lake Ontario more resembles a
series of eutrophic ponds flying in formation than it does a great lake so far
as the phytoplankton flora is concerned.
So far as the species composition of the flora is concerned, the oligo-
trophic diatom and chrysophycean flagellate taxa which dominate the offshore waters
of the upper lakes are conspicuous by their absence in Lake Ontario. Virtually
all of the abundant taxa in the Lake Ontario flora either require, or are at
least tolerant of, eutrophic conditions. Taken as a whole, the phytoplankton
assemblage of the lake is quite unique. A number of the elements reported from
other large, disturbed, lakes are present in Lake Ontario but their relative
abundance and seasonal succession appears to be substantially different from
most cases reported in the literature. The effect that this highly unusual
primary producer community has on higher trophic levels can only be speculated
upon at this time, but our observations would tend to indicate that, compared
to the upper Lakes, protozoans and rotifers are extremely abundant.
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Although the limited overlap in sampling does not furnish sufficient
basis for complete comparison, it is apparent that there were substantial
differences between June of 1972 and June of 1973 in terms of both the compos-
ition of the phytoplankton flora and the abundance of phytoplankton at compar-
able stations. At this juncture, it appears that the relative instability of
the phytoplankton flora in Lake Ontario may present serious problems in data
interpretation and modeling activities.
It perhaps should be stressed that the phytoplankton count data presented
here pertains only to near surface samples. Although the depth transect
microscopic count data is not yet sufficiently developed to allow any general-
ization, inspection of the particle count data (Appendix A) indicates that there
are large vertical differences within the mixed water column. The data do,
however, suggest the accumulation of particles within the epilimnion, and part-
icularly at the level of the thermocline, during sampling periods when thermal
stratification was present.
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Figure 1. Distribution of total phytoplankton abundance in near surface waters of Lake Ontario during May 1972
cruise. Area not sampled is indicated.
80
LAKE ONTARIO
-------
Figure 2. Distribution of total phytoplankton abundance in near surface waters of Lake Ontario during June 1972
cruise.
June
LAKE ONTARIO
move (w 5(356
cells/ml
ce'
C* Us/ml
1000-
500-
cells/r*vf
-Man 2.00
-------
Figure
3. Distribution of total phytoplankton abundance in near surface waters of Lake Ontario during July 1972
cruise.
80
Ju y
LAKE ONTARIO
-------
Figure 4. Distribution of total phytoplankton abundance in near surface waters of Lake Ontario during August 1972
cruise.
J
1 1
m
80*
LAKE ONTARIO
o
LO
I
j -. A-,..'"-
.'; >'' '•- '
Toronto
-5(300
cells/ml
2000-5300
1000
cell:
500-
200-
ce Us/ml
|€55
2.00
-------
Figure 5. Distribution of total phytoplankton abundance in near surface waters of Lake Ontario during October 1972
cruise.
80'
0 ct
LAKE ONTARIO
ni _ «j«v_am »a^-i5m"~~
200-
cells/rwl
-------
Figure 6. Distribution of total phytoplankton abundance in near surface waters of Lake Ontario during November 1972
cruise. Area not sampled is indicated.
LAKE ONTARIO
-------
Figure 7. Distribution of total phytoplankton abundance in near surface waters of Lake Ontario during February 1973
cruise. Stations nor sampled are circled.
UNSAftPLSTD STATIONS
CIRCLE />
celts
m
IOOO-
200 -
jes-5
-------
Figure 8. Distribution of total phytoplankton abundance in near surface waters of Lake Ontario during March 1973
cruise. Stations not sampled are circled.
LAKE ONTARIO
--u.gn... (\&\ OrnV t 4? 15m
t e1 rwm ->^ J"_^rt^jm^*^tf ^^rrr
2-°°
-------
Figure 9. Distribution of total phytoplankton abundance in near surface waters of Lake Ontario during April 1973
cruise. Stations not sampled are circled.
so'
fl TO
LAKE ONTARIO
43'
UNSAttPLCD STATIONS
ARF CIRCLED
may*. -fi<\ri -5060
cells/ml
5-00-
200-^
-Hian 2.00
-------
Figure 10. Distribution of total phytoplankton abundance in near surface waters of Lake Ontario during June 1973
cruise. Stations not sampled are circled.
80"
une
(973
LAKE ONTARIO
A
D STATIONS
ARE CIRCLE D
move. n 5300
cells/ml
2000-5QOO
C£ I Is/ml
1000-
cells/mi
200 -
|e55
2.00
-------
ANNUAL REPORT
EXPLORATION OF HALOGENATED AND RELATED HAZARDOUS
CHEMICALS IN LAKE ONTARIO
Grant Number 800608
April 1, 1972 to March 31, 1973
G. Fred L'ee and Clarence L. Haile
Environmental Chemistry
Department of Civil Engineering
Texas A&M University
College Station, Texas 77843
-------
1. Project Objectives
The early explorations of pesticides in the Great Lakes
with gas chromatographic techniques revealed that chlorinated
pesticides such as DDE are present in the fish from several
lakes at concentrations greater than those which, are
thought to be safe for higher organisms and man. The use
of more sophisticated analytical instrumentation such as
mass spectrometry has led to the identification .of trace
amounts of many other potentially toxic organic chemicals,
ana the likelihood that the food resources of the Great
Lakes are being jeopardized by current industrial, municipal,
and agricultural practices is suggested. Veith (1970)
confirmed the presence of chlorobiphenyls (PCBs) in Lake
Michigan fish at levels exceeding the action limit established
by the Food and Drug Administration. Zabek (1970) found
pentachloronaphthalenes eluting simultaneously with DDE
from the gas chromatograph in the analysis of Great Lakes
*This project is also conducted at the University of
Wisconsin, Madison, Wisconsin.
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fish. Stalling (1971) has reported the presence of phthalate
esters (industrial plasticizers) in several aquatic environ-
ments .
In addition to these groups of chemicals, which are
commonly detected with routine analytical techniques, the
presence of still other toxic chemicals at levels below
normal detection limits have been confirmed with the gas
chromatograph/mass spectrometer after careful pre-column
concentration steps. The chemicals generating the major
concern are the chlorodibenzo-p-dioxins which may be trace
contaminants in chlorophenol formulations (U.S. Senate,
1970) and the chlorodibenzofurans which may be trace con-
taminants or derived from PCB formulations (Vos and Koeman,
1970; Vos, Koeman ejt al. , 1970). Both of these classes of
chemicals produce teratogenic effects at levels below orfe
microgram/gram. Furthermore, these chemicals may be
responsible for many of the effects commonly attributed to
pesticides which mask the presence of the dioxins or furans
because of their greater relative concentrations.
The objectives of this study are to:
1. collect fish, water, sediment, benthos, plankton,
and Cladophora from four regions of Lake Ontario
and to
2. isolate and identify the major and minor trace
halogenated and related potential hazardous chemicals
in the Lake Ontario ecosystem through the use of
gas chromatography and gas chromatography/mass
spectrometry.
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This study will provide complete chemical characteri-
zation of trace contaminants in the Lake Ontario ecosystem
with special emphasis on the possible presence of hazardous
chemicals such as the chlorinateddibenzo-p-dioxins and
chlorinated dibenzofurans which have been detected in
industrial chemicals. The results of this study will provide
baseline information concerning the major contaminants and
may serve as an early warning of hazardous chemicals
heretofore undetected by routine monitoring programs.
2. Planned Operation Versus Actual Operation
There has been no deviation from the original objectives
with the exception of a slightly expanded sampling program
in order to obtain more complete data from the lake system
and to gain information concerning halogenated organic inputs
for the lake. Thus fish, water, sediment, and plankton
samples have been collected from more than four lake regions.
Also, fish and water sampling is planned for the major rivers
feeding Lake Ontario,
3. Cost to Program Because of Study Deviations
The expansion of our sampling program has not increased
the project costs since these samples were collected in
conjunction with the initially planned sampling. The extrac-
tion, extract clean up, and analysis of these extra samples
has thus far not contributed appreciable cost nor consumed
significantly more than that for the originally projected
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sample load. It is felt that this increased sampling program
will contribute much toward achieving the overall objectives
of the study without making excessive demands on manpower
or resources.
4. Status of Program
Sampling
The major effort for this year's work was devoted to
sample collection, extraction, and extract clean up in
preparation for the gas chromatographic analysis to follow.
Fish, water, benthos, sediment, net plankton, and Cladophora
samples were collected from various areas of the lake but
the most extensive sampling was conducted in the near shore
waters off Rochester, Oswego, and Hamilton with lesser
sampling off Olcott, Cobourg, and at the extreme eastern
end of the lake. Figure 1 shows the regions from which
these lake system samples were taken.
Water samples were usually taken at I/2am and 10 m
depths in addition to 10 m above the sediment at each
station, Cladophora was gathered at 1-2 m depths, plankton
netted at depths ot 5 - 10 m, and fish were trawl netted
at 10 - 40 fathoms. Sediment was sampled by dredging and
benthos was collected by an epibenthic sled. All samples
were transported frozen or very cold to minimize decompo-
sition.
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FIGURE I
LAKE ONTARIO SAMPLING
I
1-1
.t-
I
Reeonnoi»»once No.
Date
Ti me
KILOMETERS
water
O fish
sediment
D benthos
• plankton
A Cladophora
-------
Sample Processing
Water
Each water sample was extracted at the collection site
by passage through a column of six polyurethane foam plugs
at a flow rate of 250 ml/man. The plugs had been previously
exhaustively extracted with hexane-ethyl ether azeotrope to
remove contaminants before coating with a 1% solution of
silicone oil (DC-200) in hexane and then air dried.
Following the water extraction, the plugs were removed from
the column, the column rinsed -with acetone, and the plugs
again exhaustively extracted with hexane-ether (column
washings were added to the extract). The extracts were
reduced to about 5 ml before placing on an 8 g column of
a florisil (Fisher F-100, 60 - 100 mesh, washed with hexane
and activated by heating to 650°C for 2 hr). The samples
were eluded with 25 ml of 6% ether in hexane before changing
receivers and eluding with 50 ml 12% ether in hexane. The
receiving flasks were changed again and. the columns stripped
with 50 ml ether. All three fractions were reduced to 10 ml
and then diluted to 25 ml for storage (freezing) awaiting
later GC analysis. In the first fraction are PCBs and many
chlorinated hydrocarbon pesticides, the second fraction
contains the phthalate esters, and the final fraction contains
those compounds more polar than the phthalate esters.
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Fish
The whole fish samples were extracted and the extracts
cleaned up by liquid chromatography after Veith (1970).
After grinding the frozen fish twice to homogenize the flesh,
six 10 g sub-samples of flesh were weighed out for each
specie collected from each sampling site. Generally only
three species were taken at each site: alewife, smelt,
and sculpin. Each 10 g sample was thoroughly mixed with
70 g anhydrous sodium sulfate and placed in an all glass
thimble for extraction. The sample was extracted (Soxhlet)
for at least 3 hours with 170 ml of a 1:1 ethyl ether-hexane
mixture (v/v). The resulting extract was concentrated by
evaporation to about 10 ml before diluting to 20 ml with
hexane and removing a 2 ml aliquot for fat analysis (weight
of residue after evaporation at 150°C for 20 min). The
remaining extract was placed on a 20 g column of florisil
topped with a little anhydrous sodium sulfate. The sample
was eluded with 20 ml of 6% ether in hexane, the receiver
was changed before further elution was 200 ml of 12% ether
in hexane, and the receiving flask changed again before
final elution with 300 ml of 50% ether in hexane. The first
fraction contains the PCBs and many chlorinated hydrocarbon
pesticides, the second holds the phthalate esters, and the
final fraction contains those compounds more polar than the
phthalate esters.
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The pesticide fraction was concentrated and then diluted
to 50 ml before removing a 5 ml aliquot for preliminary GC
analysis of DDE (DDE is generally the most prominant peak
on the chromatogram). The remainder of the pesticide
fraction was concentrated to less than 10 ml before placing
it on a 20 g column of silicic acid, partially deactivated
with 2.1% water. Elution with 250 ml hexane and eludent
concentration to 25 ml produced the PCB fraction for GC
analysis. Further elution with 200 ml of 3:1 dichloromethane-
hexane (v/v) and concentration to 25 ml produced the pesti-
cide fraction for GC analysis.
Sediment
Kept frozen or cold until processed, portions of the
samples were allowed to air dry at room temperature before
weighing out six 25 g sub-samples for analysis.. The 25 g
samples were thoroughly ground (mortar and pestle), mixed
with anhydrous sodium sulfate, and extracted in a large
Soxhlet extractor (glass thimble) with 170 ml 1:1 hexane-
ether for four hours. The extracts were concentrated to about
10 ml before cleaning up by liquid chromatography o± florisil
and silicic acid utilizing the same procedures as for the
fish samples described above.
Benthos
Benthic fauna samples were also kept frozen or very
cold until processed. After drying at room temperature,
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at least three 10 g sub-samples were weighed out for each
sample. There was no attempt to segregate species. These
sub-samples were then extracted and cleaned up according to
the procedures outlined above for sediment samples.
Plankton
The frozen plankton samples were allowed to air dry at
room temperature before transferring to tared centrifuge
tubes. The samples were centrifuged at 2000 rpm for 25
minutes. After rapidly decanting the supernatant into a
separatory funnel, 2 ml acetone was added to the tubes and
the samples allowed to air dry. The tubes were weighed to
determine sample weight. The water decanted from each tube
was extracted twice with 25 ml portions of hexane to
recover organics released from the cells. About 35 ml of
tnese hexane extracts were added to the corresponding sample
tubes and the tubes shaken periodically over a 36 hour
period. The extracts were then decanted and the extraction
process repeated with 35 ml portions of fresh hexane. The
extracts were concentrated to about 5 ml before placing on
8 g florisil columns and cleaning up utilizing procedures
outlined above for water samples.
Cladophora
Cladophora samples from the south shore of Lake Ontario
were extracted and cleaned up as with the net plankton
samples with the exception that sample size was sufficient
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so that the samples could be subdivided. The number of sub-
samples varied from three to six.
Sample Analysis
Areas of sample analysis completed thus far are fats
analysis and p,p'-DDE analysis on the lake fish samples.
The fat data was obtained from the residue weight after
drying an aliquot of crude whole fish extract at 150°C for
20 minutes. Since p,p'-DDE is generally the largest peak
in the gas chromatogram, the fish samples were subjected
to initial screening for p,p'-DDE by GC. A five foot coiled
glass column of 3% DC-200 coated on 80/100 Chromasorb W
was used in conjunction with the tritium foil electron
capture detector on a Varian Aerograph 1700 GC. The column,
detector, and injector temperatures were 200°C, '210°C, and
225 C, respectively. The carrier gas was purified nitrogen
at 41 pounds/square inch. This preliminary screening not
only gives initial data input, but also provides a good
overview of sample composition in order to facilitate the
more complete analysis to follow.
Progress has. been made in determining optimum gas
chromatographic columns and column conditions for the bulk
of the GC analyses to follow. Several columns utilizing
liquid phases such as OV-1, DC-200, OV-17, and mixed liquid
phases such as OV-17/QF-1, DC-200/QF-1, and OV-l/QF-1
coated on 80/100 mesh Gas-Chrom Q, 100/120 mesh Gas-Chrom Q,
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or 10O/120 mesh Chromasorb G packed in 2 mm ID coiled glass
columns 5-7 feet in length were prepared and evaluated
using standard pesticide solutions, pesticide cocktail
solutions, and some Lake Ontario fish extracts. Columns
showing high potential for separation with reasonable
retention times include those prepared with DC-200, OV-17,
OV-17/QF-1, and OV-l/QF-1. Column temperatures of 160-'200°C
were utilized with carrier gas flows of 7 - 35 ml/min.
5. Areas of Program Which Are Behind Schedule
Although progress has been fairly smooth, it is felt
that our sample analysis should be at a 'Slightly more advanced
stage. The primary reason for delay has been the absence
of Clarence L. Haile, graduate student working with the
project. Mr. Haile was engaged in the service of the U.S.
Army for a 90 day period, necessitating his absence from
January 10 to April 16, 1973. It is foreseen, however, that
this will cause no delay in the final project completion,
nor will it disallow the ±ull achievement of the project
objectives.
6. Summary of Results to Date
Since the major portion of this year's work has been
directed toward preparing for the bulk of the analyses, only
a small amount of data has been obtained. Fats analysis
and preliminary p,p'-DDE data have been determined. Table I
shows the resultant percentage of fats from the Lake Ontario
fish sampled. These values are quite within the expected
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range. Table II shows preliminary p,p'-DDE data for the
lake fish. These values are also not unusual. It should
be emphasized that these are preliminary DDE values and
were evolved in conjunction with extract screening to obtain
a broad overview of extract content.
TABLE I
FISH FAT CONTENT
(in %)
Location
Hamilton
Olcott*
Rochester
Mexico Bay
Galloo-Stony
Prince Edward
Point
*Three Spine _
Location
Hamilton
Olcott *
Rochester
Mexico Bay
Galloo-Stony
Prince Edward
Point
Smelt
4.85
2.99
4.12
5.95
6.71
Stikleback has 1.61%
TABLE II
p,p'-DDE IN
(ug/g)
Smelt
1.33
0.83
1.30
0.91
0.82
Species
Alewife
3.59
5.17
3.38
3.14
2.38
1.18
fats .
FISH
Species
Alewife
0.44
0.74
0.67
0.76
0.92
0.81
Sculpin
9.78
5.10
4.30
5.68
8.61
7.57
Sculpin
0.94
0.98
1.06
1.2QX_
0.57"
0.80
*Three Spine Stikleback had 0.71 ug/g DDE.
-121-
-------
LITERATURE CITED
Stalling, D.L. Analysis of Organochlorine Residues in
Fish, Presented at 2nd International Congress of
Pesticide Chemistry, February 22-26, Tel Aviv, Isreal,
(1971).
U.S. Senate. Effects of 2,4,5-T on Man and the Environment,
Hearing held on April 7 and 15, (1970).
Veith, G.D. Environmental Chemistry of PCBs in the
Milwaukee River, Ph.D. thesis (Water Chemistry)
University of Wisconsin, Madison, 180 p., (1970).
Vos, J.G. and Koeman, J.H. Comparative Toxicologic Study
with Polychlorinated Biphenyls in Chickens with
Special Reference to Porphyia, Edema Formation, Liver
Necrosis, and Tissue Residues, Toxicol. and Applied
Pharmacology 17_, 656-668, (1970).
Vos, J.G., Koeman, J.H., von der Mass, M.C., ten Noever de
Brauw and de Vos, R.H. Identification and Toxicological
Evaluation of Chlorinated Dibenzofuran and Chlorinated
Naphthalene in two Commercial PCBs, Food and Cosmetics,
Toxicol. £, 6^5-633, (1970).
Zabek, M. Contribution at PCB Workshop, National Water
Quality Laboratory, Duluth, Minnesota, March, (1970).
-122-
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Progress Report
PHOSPHORUS UPTAKE AND RELEASE
BY LAKE ONTARIO SEDIMENTS (IFYGL)
Grant Number 800609
D. E. Armstrong and R. F. Harris
R. Bannerman
S. Halaka
University of Wisconsin, Madison, Wisconsin
-------
Project Objectives;
1) To determine the forms, amounts and mobility of phosphorus
in sediment cores from Lake Ontario.
2) To determine the rate and extent of phosphorus movement in
sediment cores as a function of sediment properties and environmental
conditions.
3) To predict the release and uptake of phosphorus by Lake Ontario
sediments as a function of sediment properties and conditions in
the overlying water.
Research Approach;
Sediment cores were obtained and sectioned to allow evaluation of
the characteristics of the surface sediments. Measurements were made
of the forms and mobility of sediment phosphorus. Intact cores were
transported to the laboratory for measurement of P release under controlled
conditions. Subsequent sampling will emphasize separating interstitial
water in situ for subsequent phosphorus and iron determinations.
-123-
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Sampling:
Sediment cores (7 cm diameter) were obtained with a Benthos
gravity corer. Cores were sectioned at 5 cm intervals and transported
to the lab for analysis. Major emphasis was on the surface 5 cm layer,
but some measurements were made on subsurface layers.
For the initial sampling trip (June 21, 1972), 10 sampling stations
were selected to allow comparison of the three major lake basins and the
postglacial mud and the glacio-lacustrine clays (Fig. 1). Four cores were
c
taken at each station to allow comparisons of station and interstation
variability. General characteristics of these sediments were described
in Thomas et al. (1972). Based on this classification, stations 83,
75, 92, 45, 32 and 10 were postglacial muds, stations 34 and 52 were
near-shore glacio-lacustrine clays, and station 62 was near a between-basin
sill of glacio-lacustrine clay.
For the second sampling trip (November 6, 1972), station 30 (located
in near-shore silts according to the classification of Thomas et al., 1972)
and 60 of the inshore zone were selected in addition to those sampled in
June except station 32 and 96 (Fig. 1). Cores were obtained at some
stations to provide intact cores for transport to the laboratory and
comparison of station and inter-station variability. The surface 5 cm
layer of several cores was squeezed in situ to obtain interstitial water
for dissolved inorganic phosphorus determination.
The third sampling trip (September to October, 1973) will emphasize
squeezing different core sections in situ and analyzing the interstitial
water for phosphorus and iron in the laboratory.
-124-
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Measurements^
Measurements of the forms and mobility of sediment P were made by
procedures described elsewhere (Sommers e£ al., 1970; Shukla et al.,
1971; Williams et al., 1971 a, 1971 b; Li jet al., 1972). These measurements
included total P, total inorganic P, total organic P, sediment exchange-
able inorganic P, interstitial inorganic P, NH.C1-P, NaOH-P, CDB-P and
HC1-P and the P sorption and desorption characteristics of the sediments.
Inorganic P fractionation provides evidence on the chemical mobility of
sediment inorganic P (Syers
-------
pressure-membrane apparatus will be used to obtain interstitial water on
board ship.
Results and Discussion;
A brief discussion of results obtained from the first and second
sampling trips is presented. Because data acquisition is incomplete,
only tentative interpretation will be made at this time.
Amounts of total P, total inorganic P and total organic P varied
between stations for both trips (Tables 1 and 2). Phosphorus values were
similar for the same station sampled on both trips. The surface 5 cm
layer usually exhibited higher phosphorus values than subsurface layers
(Table 2). Amounts of organic P were low especially in the inshore zone
stations. The organic P increased in the 15 to 20 cm core section
(Table 2).
Differences among stations were more apparent in the forms of
inorganic P present than in the amounts of total P or total inorganic or
organic P» The inshore zone stations tended to contain small amounts
of NaOH-P and CDB-P but a high proportion of HC1-P (Tables 3 and 4). The
basin stations contained similar proportions of NaOH-P and HC1-P and
small amounts of CDB-P. Apparently, the proportion of immobile" P
(apatite, extracted by HC1) is high in the inshore zone, while the
basin muds contain a high proportion of potentially mobile Fe and Al-bound
P (NaOH-P). The proportion of NaOH-P decreased with increasing depth
below the sediment surface for station 30. This, along with the drop in
sediment water content below 5 cm at station 30 (Table 5), indicates
that the surface 5 cm layer was composed of sediments of substantially
-126-
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different composition from the subsurface layers.
Values of sediment exchangeable P were in agreement with the differences
in chemical mobility of inorganic P observed between stations based
on measurements of inorganic P forms. The inshore stations contained
small amounts of exchangeable P relative to the basin stations (Table 6).
The basin sediments apparently contain a higher proportion of inorganic
P in a form available for interaction with the associated interstitial
water. Station 62 exhibited- an exchangeable inorganic P level similar to
the inshore zone stations rather than 'the basin stations.
Several factors suggest a possible difference in phosphorus forms
for station 62 from those in basin stations. According to a map
presented by Thomas £t alL. (1972), station 62 lies close to the Scotch
Bonnet sill which is composed of glacio-lacustrine clay, while the major
basins are predominately postglacial muds (Thomas et_ al., 1972). The sediment
water content at station 62 was lower than observed in most cases for
the basin stations (Table 5). Furthermore, the proportion of NaOH-P
was lower at station 62 than for basin stations (Table 4). The above
evidence suggests that station 62 sediment is different in composition
from the basin stations and is more closely related to the inshore zone
stations.
Interstitial inorganic P values are currently under investigation
and a complete set of data cannot be presented. However, initial data
indicate the interstitial inorganic P values to be higher than the dissolved
inorganic P values in the overlying water column. This suggests a
potential exists, due to the concentration gradient, for release of
dissolved inorganic P to the overlying water. Relatedly, a net transport
-127-
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of P from the water to the sediment likely occurs through deposition of
particulate P.
The amount of dissolved inorganic P observed after equilibration of
suspensions of Lake Ontario sediments varied from station to station
and usually decreased with depth below the sediment surface (Table 7).
Further investigation of inorganic P desorption is planned. The
data obtained suggest that Ontario sediments contain sufficient loosely
bound inorganic P to maintain a dissolved inorganic P value higher than
that of the lake water.
Sorption of added inorganic P was investigated to determine the
ability of sediments to remove inorganic P from water at concentrations
in the range of those expected for lake or interstitial waters. In
most cases, the inshore zone sediments sorbed less added inorganic P
than the major basin sediments (Tables 8 and 9). Station 30 was the
exception for the inshore zone and station 62 was the exception for the
major basins. These stations have been discussed previously as possibly
differing in composition from their respective areas of the lake. Little
change in sorption ability with depth below the sediment surface was
observed (Table 8). At levels of inorganic P expected in the interstitial
water and bottom lake water, the major basin sediments sorbed most of
the added inorganic P. However, the amounts remaining in solution were
in the range of soluble phosphate concentrations in the water column of
Lake Ontario (Shiomi and Chawla, 1970).
Dissolved inorganic P released from intact cores incubated at 8° C
in an air or nitrogen system ranged up to 35 ug/1 after a 70-day period.
At present, insufficient information is available to estimate rates of
-128-
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release.
The preliminary results obtained indicate that Lake Ontario sediments
contain varying amounts of"mobile and potentially mobile inorganic P,
and that a tendency exists for the release of dissolved inorganic P
from the sediment. Major differences exist between the inshore zone
sediments and major basin sediments. Subsequent research during the
remainder of 1973-74 will emphasize the investigation of the amounts of
mobile phosphorus in the sediment and the ability of the sediment to
maintain the existing levels of mobile phosphorus. This data combined
with previous data will be used to estimate the potential impact of
Lake Ontario sediments on the phosphorus status of the lake water.'
Literature Cited:
1. Reeburgh, W. S. 1967. An Improved Interstitial Water Sampler.
Limn. Oceanogr. 12; 163-165.
2. Shiomi, M. T. and V. K. Chawla. 1970. Nutrients in Lake Ontario.
Proc. 13th Conf. Great Lakes Res., 715-732.
3. Li, W. C., D. E. Armstrong, J. D. H. Williams, R. F. Harris, and
J. K. Syers. 1972. Rate and Extent of Inorganic Phosphate
Exchange in Lake Sediments. Soil Sci. Soc. Amer. Proc. 36:
279-285.
4. Shukla, S. S., J. K. Syers, J. D. H. Williams, D. E. Armstrong,
and R. F. Harris. 1971. Sorption of Inorganic Phosphorus
by Lake Sediments. Soil Sci. Soc. Amer. Proc. 35: 244-249.
5. Sommers, L. E., R. F. Harris, J. D. H. Williams, D. E. Armstrong,
and J. K. Syers. 1970. Determination of Total Organic
Phosphorus in Lake Sediments. Limnol. Oceanogr. 15; 301-304.
6. Syers, J. K., R. F. Harris, and D. E. Armstrong. 1972.
Phosphate Chemistry in Lake Sediments. J_. Environ. Qual. _2
(in press).
-129-
-------
9.
Thomas, R. L., A. L. W. Kemp, and C. F. M. Lewis. 1972.
Distribution, Composition and Characteristics of the Surficial
Sediments of Lake Ontario. J_. Sed. Petrology 42; 66-84.
Williams, J. D. H., J. K. Syers, R. F. Harris, and D. E. Armstrong.
1971 a. Fractionation of Inorganic Phosphate in Calcareous
Lake Sediments. Soil Sci. Soc. Amer. Proc. 35; 250-255.
Williams, J. D. H., J. K. Syers, D. E. Armstrong and R. F. Harris.
1971 b. Characterization of Inorganic Phosphate in Noncalcareous
Lake Sediments. Soil Sci. Soc. Amer. Proc. 35: 556-561.
-130-
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I
LO
M
R.
Figure 1 (Thomas ejb _al. , 1972)
-------
Table 1 Total P, Total Inorganic P, Total Organic P in Lake
Ontario Core Samples from June 21, 1972 Sampling Trip
Sampling
Station
52
92
83
75
32
45
10
96
Sediment Phosphorus for 0 to 5 cm core Section
Total P Total Inorganic P Total Organic P
ug/g
945
1146
1058
1013
1233
1442
1431
982
Inshore Zone
891
Rochester Basin
1000
(867
872
Mississauga Basin
995
1176
Niagara Basin
1229
Kingston Basin
810
54
146
191
141
239
266
201
172
-132-
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U)
I
Table 2 Total P, Total Inorganic P and Total Organic P at Various Sediment Depths in
Lake Ontario Cores from the November 6, 1972 Sampling Trip
Sampling
Station
0-51
34 955
30 888
60 548
92 1270
62 950
75 1163
45 1310
10 1448
Total P
5-10 10-15 15-20
890 900 1010
685 610 612
500 500 567
966
980
1103
1028
1108 1335 1182
0-5
940
790
548
1140
810
1050
1065
1218
Total Inorganic P
5-10 10-15 15-20
UCT AT
"3' J
Inshore Zone
890 900 885
675 600 550
500 500 522
Rochester Basin
860
945
1020
Mississauga Basin
833
Niagara Basin
935 1132 895
Total Organic
0-5
15
98
22
130
140
113
245
230
5-10 10-15
0 0
10 10
0 0
100
35
83
195
173 202
P
15-20
125
62
45
287
Sediment depth in centimeters.
-------
Table 3 Ratio of P in NaOH, CDB and HCl Fraction to Total
Inorganic P in Lake Ontario core Sample from June 21,
1972 Sampling Trip
Sampling
Station
34
52
83
92
75
45
32
NaOH/
2
4
30
33
46
60
53
Ratio of P Values for the
0 to 5 cm Sediment Layer
p.l CD%.
*1 *!
o/
Inshore Zone
6
5
Rochester Basin
17
14
6
Mississauqa Basin
15
14
Niagara Basin
HCl/
/Pi
91
90
48
41
42
31
42
10 48 10 32
Kingston Basin
96 18 10 72
PJ = Total inorganic phosphorus.
-134-
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Table 4 Ratio of P in NaOH, CDB and HCl Fraction to Total Inorganic P in Lake
Ontario Core Samples from the November 6, 1972 Sampling Trip
Sampling
Station
30
60
34
62
92
75
45
10
Ratio
0-
NaOH
i
28
8
3
22
37
40
46
50
of
5 cm
CDB
Pi
16
6
6
18
15
17
19
19
P Values
at
Following Depths Below the Sediment
5-10 cm 10-15 cm 15-20
HCl NaOH
Pi P
53
81
85
57
36
29
20
22
i
10
4
2
15
30
50
45
51
CDB HCl NaOH CDB HCl NaOH CDB
Pi Pi Pi ?i Pi Pi Pi
/o
Inshore Zone
5 72 .8 6 82 67
2 95 2 4 91 24
6 86 2 5-97 2 8
Rochester Basin
18 65
15 50
11 32
Mississauga Basin
8 35
Niagara Basin
7 35 50 6 32 58 8
Surface
cm
HCl
Pi
88
95
88
39
V
P- — T^f-rsl T«O -rrt^n i f7 T3 Vi r-» c? l*i"h r\ v- n a
-------
Table 5 Sediment Water Content of Lake Ontario Cores from the
November 6, 1972 Sampling Trip1
Sampling
Station
34
30
60
92
62
75
Water Content at Following
Depths Below the Sediment Surface
0-5 cm
52
50
25
56
58
76
5-10 cm
n/
/o
Inshore
50
30
24
Rochester
54
42
68
Mississauga
10-15 cm 15-20 cm
Zone
48 46
28 26
19 20
Basin
Basin
45 77 71
Niagara Basin
10 74 71 65 68
% water = weight of water divided by weight of water +
sediment.
-136-
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Table 6 Sediment Exchangeable Inorganic P in the 0 to 5 cm
Sediment Layer of Lake Ontario Cores from the November
6, 1972 Sampling Trip
S ampl ing
Station
34
30
60
31p
soln
2.4
0.45
1.05
Sed Exch 31
1 1 n / rr .
Inshore
13.3
9.0
20.3
P^
°/
Zone
1
1
4
Total Exch
n rr /n
uy/ y j
15.7
9.45
21.3
PI
2
1
4
Rochester Basin
62 4.1 29.0 4 33.1 4
92 1.5 167.2 15 168.7 15
75 1.2 193.3 18 194.5 18
Mississauga Basin
45" 0.88 139.6 13 140.4 13
Niagara Basin
10 1.2 193.9 16 195.1 16
1 Sed Exch P^ is expressed as percent of inorganic P in sediment
phase; Total Exch P. is expressed as a percent of inorganic
P in the sediment ana water phases.
-137-
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Table 7 Dissolved Inorganic P in a 4% Sediment Suspension of
Lake Ontario Sediment After a 40 hour Equilibration in
Distilled H2O
Sampling
Station
34
30
60
52
92
62
75
Dissolved Inorganic P Values for
4% Sediment Suspension of Following Core Sections
0-5 cm
101
243
55
107
135
172
393
5-10 cm 10-15 cm
LLT/1
Inshore Zone
78 42
41
33
73
Rochester Basin
59
179
255 201
Mississauga Basin
45 920 78
Niagara Basin
10 304 72
-138-
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Table 8 Sorption of Added Inorganic P by Lake Ontario Sediments
From First Sampling
Sampling
Station
34
52
92
32
Core
Section
0-5 cm
5-10 cm
0-5 cm
5-10 cm
10-15 cm
0-5 cm
0-5 cm
5-10 cm
10-15 cm
Added
P S orbed (%) for Added P
Level (ug of P per g)
2.5
80
83
73
93
95
100
100
100
100
25 250
Inshore Zone
80 48
7Z 41
60 24
78 50
85 57
Rochester Basin
98 82
Mississauga Basin
100 87
100 48
95 89
of
2500
20
25
17
37
31
52
57
46
52
Sediment in 4% sediment suspensions where ug/liter = ug/g x 40
-139-
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Table 9 Sorption of Added Inorganic P by Lake Ontario Sediments
from the 0 to 5 cm Core Sections of the November 6,
1972 Sampling Trip1
Sampling
Station Added P
6.25
34 71
30 100
60 91
92 100
62 66
75 93
45 98
Sorbed (%) for Added P Level (ug/g) of
12.5 25
Inshore Zone
70 65
98
89
Rochester Basin
98
66
98 98
Niagara Basin
99
50
59
99
75
98
53
98
99
100
99
62
98
46
99
Equilibrations performed with 4% sediment suspension where
ug/1 = 40 x ug/g.
-140-
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MATHEMATICAL MODELING
OF
EUTROPKICATION
OF
LARGE LAKES
(EPA Project No. R 800610)
Annual Report - Year #1
April 1, 1972 - March 31, 1973
Robert V. Thomann
Dominic M. DiToro
Donald J. O'Connor
Richard p. Winfield
July 1973
Environmental Engineering and Science Program
Manhattan College, Bronx N.Y. 10471
-------
SUMMARY
The major thrusts of the research effort during the
first year were to compile data prior to IFYGL and to develop
preliminary models of eutrophication of Lake Ontario. Data
were obtained from a variety of sources including STORET/ and
CCIW, prepared for computer storage and have been displayed in a
variety of summaries to aid in the model building process.
The preliminary models constructed during the first year
were three in number: (1) a spatially dependent model for a
conservative tracer (2) a kinetic interactive model (Lake 1) of
three mixed layers representing the epilimnion, hypolimnion and
benthos, and (3) a kinetic interactive model of seven vertical
layers, Lake 2. Primary effort was devoted to analyses of
eutrophication phenomena using the Lake 1 model. This model
contains ten interactive systems including phytoplankton and
four higher trophic levels and some major aspects of the nitrogen
and phosphorous cycles.
The results to date indicate the importance of higher
order predation on phytoplankton populations at average
grazing rates of 1.2 literu/mg carbon-day at 20 C. Phytoplankton
settling velocity and the importance of vertical mixing has been
also investigated in detail. Using two zooplankton levels and
average sinking rates of 0.05 meters/day, a bimodal distribution
of phytoplankton during a year is obtained. The results agree
reasonably well with observed chlorophyll a levels averaged
over the entire lake. Phosphorous values are also in good
-141-
-------
agreement whereas nitrogen forms are only approximately in
agreement with observed data.
Plans for the second year include expansion of the model
to include some horizontal spatial detail and additional
interactive variables. A total of 1400 compartments is
envisioned for the expanded model.
-142-
-------
Table of Contents
SUMMARY
I. Subject Review 144
II. Planned Operation Versus Actual Operation 146
III. Project Status 149
IV. Summary of Results 149
1. Data Compilation 149
2. Preliminary Kinetic Model - Lake 1 153
a. Variable Vertical Mixing 157
b. Variable phytoplankton settling velocity 159
c. Comparison of Lake 1 model with observed data 165
-143-
-------
Mathematical Modeling of Eutropication
of Large Lakes
Annual Report
April 1, 1972 - March 31, 1973
I. Subject Review
The purpose of this research is to structure a mathematical
mpdeling framework of the major features of eutrophication in
large lakes. Lake Ontario/ the subject of intensive field
work as part of the International Field Year for the Great Lakes
(IFYGL) is used as the problem setting. The overall objectives of
the research include 5
a) determination of. important interactions in
lake eutrophication
b) analysis of lake water quality and biological
responses to natural and man-made inputs
c) formation of a basis for estimating the direction
of change to be expected under remedial
environmental control actions
-144-
-------
The problems of impairment of the quality of lake systems
are magnified for "large lakes", such as the Great Lakes. The
size of these lakes is such as to preclude any immediate improve-
ment in quality after control actions are taken. Further, it is
much more difficult to obtain reliable data on water quality,
biological structure and hydrodynamic circulation, again because
of the difficulty of sampling large lake systems. Deep water
circulation may be known only in its broad outlines; indeed the
general circulation itself may not be adequately known in relation
to climatological and hydrological factors. In the biological
area, measures of phytoplankton populations such as species com-
position are usually temporally and spatially dependent and may
change rapidly. The degree of such spatial dependence especially
in the near-shore boundary layer is especially important since
water use interferences (municipal water supply, bathing, etc.)
as a result of excessive phytoplankton growth are often related to
near-shore uses. Finally, in the physical, chemical and biochemical
area, complex forms of nutrients can exist again both temporally
and spatially. Sediment chemistry, interaction with upper layers
and ''thermal bar" effects all play a role in describing the
ecosystem of large lakes.
-145-
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The basic modeling structure consists of sets of
deterministic differential equations regresenting the biological
subsystem and chemical-biochemical subsystems. The lake
hydrodynamics are externally supplied by other investigators
and previous work. The interactions between the biological
and chemical subsystems are both linear and non-linear and
attempt to reflect the major effects of man made and natural
nutrient inputs.
II. Overall Project Plan
The research is planned to be carried out according to the
following tasks:
a) Data compilation and preliminary analysis for
mathematic modeling purposes
b) Formulation of major sub-model structures such as
i biological sub-model
ii chemical-biochemical sub-model
c) Formulation of interactive models using components
of (b) above,
d) Sensitivity analysis of model interactions and
components,
e) Verification analysis of sub-models and model
structure
f) Simulation analysis of selected future environmental
controls.
-146-
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These steps are not necessarily to be carried out
sequentially since/ for example, verification analyses, formulation
and sensitivity analyses are really part of an iterative loop
in the construction of a mathematical model.
The project during the first year has generally followed this
plan of operation. As the first year 6f the project progressed,
a more detailed modeling strategy was developed and is
summarized in Figure 1.
As shown, two parallel paths are being followed. The first
part involves examination of the transport and dispersion structure
of Lake Ontario and the gathering of data on the lake georaorphology,
A conservative tracer model is used for this purpose with some
spatial detail provided by a forty segment model. The second
modeling path simplifies the spatial dimensions to a horizontally
completely mixed lake with vertical layers. The emphasis in
the latter models is on the development of preliminary
interaction kinetics between various components of each
of the sub-models. These models therefore relate directly
to tasks b) and c) of the research plan outlined above.
As indicated above, the project has essentially followed
the original research plan. Therefore, there has not been any
significant deviation in the type of tasks originally laid out
although there has been an increased need for additional com-
putational effort in the second year of the study. During the
period covered by this annual report however, there was no
additional cost to the program above that originally budgeted.
-147-
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SPATIAL DEFINITION
SYSTEM
GEOMETRY
PREPARATION
Flow Tronsporl
Depths,Surfocs Areo,Volume ._
Dispersion ^
Inputs ^
CHLORIDE MODEL
40 SEGMENTS
00
I
TEMPORAL 8 KINETIC DEFINITION
Solar Rodlotion^
Temperature
Flow
Nutrients
LAKE I MODEL
3 VERTICAL LAYERS
Ph'ytoplanMon 8 Zooplankton
Dynamics
LAKE 2 MODEL
7 VERTICAL LAYERS
SYNTHESIS OF KINETIC Q SPATIAL MODELS
Temperature Verification Phytoplonkton,
Chemistry & Sediment Interaction*
SYNTHESIZED
SPATIAL-KINETIC
MODEL
70 SEGMENTS
NON LINEAR
COARSE GRID MODEL
!400 COMPARTMENTS
I
5000 j
COMPARTMENT »-
MODEL
I
(FINE GRID MODEL)
FIGURE I
EUTROPHICATION MODELING STRATEGY
-------
III. Project Status The three years planned for this project
are scheduled as follows:
Year #1:. During the first year, attention is to be
directed toward data compilation and first preliminary
analyses to provide the necessary information for the overall
modeling structure.
Year # 2; The second year will begin incorporation of major
sub-systems into the modeling framework. Verification and
sensitivity analyses using previous data and IPYGL data will
be completed on preliminary models and will be applied using the
more detailed spatial models (See Fig. 1).
Year #3; Final verification analyses of the larger
detailed spatial model will be completed during this year.
Simulations will be prepared of selected future environmental
controls.
The project is essentially on target and the goals of Year
#1 have been completed as discussed more fully below in Sect. IV,
Summary of Results. No areas of the project are behind
schedule at the present time.
IV. Summary of Results
1. Data Compilation
A major effort during the first year was devoted
to the gathering and analyses of data collected on Lake
Ontario prior to IFYGL.
-149-
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IV. Project Status The three years planned for this project
are scheduled as follows:
Year II; During the first year, attention is to be
directed toward data compilation and first preliminary.
analyses to provide the necessary information for the overall
modeling structure.
Year f2; The second year will begin incorporation of major
sub-systems into the modeling framework. Verification and
sensitivity analyses using previous data and IFYGL data will
be completed on preliminary models and will be applied using the
more detailed spatial models (See Fig. 1}.
Year 13: Final verification analyses of the larger
detailed spatial model will be completed during this year.
Simulations will be prepared of selected future environmental
controls.
The project is essentially on target and the goals of Year
#1 have been completed as discussed more fully below in Sect. IV,
Summary of Results. No areas of the project are behind
schedule at the present time.
TV. Summary of Results
1. Data Compilation
A major effort during the first year was devoted
to the gathering and analyses of data collected on Lake
Ontario prior to IFYGL.
-150-
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The bulk of data used in the first year effort was
obtained primarily from three sources.
1. Limnological Data Reports, Lake Ontario, 1966-
1969, Canada Centre for Inland Waters (CCIW).
2. STORET, Environmental Protection Agency.
3. Report to the International Joint Commission
on the Pollution of Lake Ontario and the
International Section of the St. Lawrence River;
International Lake Erie Water Pollution Board
and the International Lake Ontario - St. Lawrence
River Water Pollution Board, 1969.
These sources were supplemented with other data available in
the literature.
This data base after being surveyed to determine
completeness was used for model inputs and as data for
verification analyses.
The Limnological Data Reports (LDR) of CCIW comprise
the largest single source of Lake Ontario survey data
available. CCIW's cruises not only had adequately dense
spatial grids but also comprised good temporal coverage for
the years surveyed. It was therefore decided to use the data
contained in the LDR as a verification data base. The CCIW
data were also manipulated to aid in the formulation of a
modeling framework.
A display procedure showing the spatial variations
in Lake Ontario, using contours, for a given cruise and sampling
depth was tested. A preliminary set of contours for a given
year and certain variables was generated for use in the first
year development of the model. Contours will be used not
-151-
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only to give insight into where model grid detail will be
important but also as a means to facilitate data comprehension.
Due to the magitude of data in the LDR, a reduction
mechanism had to be found which would make the data easily
compatible with model output to facilitate comparison. Since a
segmentation scheme was used which represented the lake as 3
or 7 vertically layered completely mixed volemes, temporal
plots of variabj.es were made.
The program which generated the plots has the option
to retrieve selected stations of the cruises by testing the
depth of the station and thereby limiting a retreival to
near shore or main lake stations. A further option which
can be selected is that only samples collected between a
specified depth interval will be retreivedi, Latitude - long-
itude constraints are also possible.
After reviewing the years surveyed for completeness
of variables measured and time coverage of cruises, 1967,
1969 and some data for 1970 were chosen as the years for model
comparison. Plots were generated for key variables using depth
intervals corresponding to the vertical segmentation of the
model. Since the model LAKE 1 considers the lake as 3
vertical layers, the main lake option was selected. The
program plots all points against time and calculates the mean
and standard deviation for each time (i.e. cruise).
The base data are then compared with model generated
data. This comparison is facilitated by plotting model output
and overplotting the mean and mean plus standard deviation
for the base year, for the key variables versus time.
-152-
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Storet, the Environmental Protection Agency's water
quality storage and retreival system is the prime residence of
all U.S. collected water quality data. A water quality
inventory using a polygon retreival, was run for Lake Ontario.
This gave a summary of all historical data collected on Lake
Ontario. A retreival was also run which listed all the data
and punch card output was also generated. Storet's main
utility will be for IFYGL data and will also be used as a data
base for tributary nutrient concentration data and flow records,
and also as supplement to the LDR of CCIW.
The report to the International Joint Commission
(IJC) on Lake Ontario is a comprehensive pollution study, giving
an excellent overview of the Lake. The values reported were
used in the forty segment chloride model for chloride discharge
loading and in the development of a transport structure. The
transport was structured by translating the velocity vectors
given for mean circulation patterns into intersegment flows.
The vertically layered phytoplankton model used the
IJC's discharge loadings as nutrient forcing functions. This
loading information, which is divided by source of discharge
is categorized under three headings; municipal, industrial and
tributory. These loadings are used as boundary conditions and
forcing functions for the nutrient systems in the spatially
defined phytoplankton models.
2. Preliminary Kinetic Model - Lake 1
As outlined in Fig. 1, the modeling strategy developed
for structuring the overall framework calls for preparation
of a preliminary model with emphasis on the interactive kinetics
-153-
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of major components of the eutrophication phenomena. The
development of such a model was dictated by the recognized need
to maSe a number of computer runs to elucidate system sensitivity
and to compare model output to observed data. The kinetic model
of necessity will have a finite life as new systems are added
to the modeling structure and new insights are gained.
The model has been designated as the Lake 1 model. The
basic physical features included in the model are shown in
Fig. 2. As shown, the model is well-mixed horizontally and
vertically is divided into the epilimnion, hypolimnion and
o
benthos. Mixing in the vertical direction is allowed during
isothermal conditions and is restricted during the summer to
simulate vertical stratification.
The sub-systems included in Lake 1 have evolved over
the past year from a basic seven system (variable) model to a
present configuration of ten systems shown in Fig. 3. The Lake
1 model is divided into two broad areas, a biological sub-model
and a chemical-biochemical sub-model. The interactions shown in
Fig. 3 are both linear and non-linear. Detailed mathematical
expressions are written for each system and interaction. The
ten systems and the three spatial segments shown in Fig 2
result in a total of 30 simultaneous non-linear differential
equations to be solved.
If one defines a compartment as one dependent variable
at a particular spatial location, LAKE 1^ is considered as a
thirty compartment model. A finite difference scheme is used
-154-
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NUTRIENT INPUTS
NIAGARA RIVER")
TRIBUTARIES I :
MUNICIPAL [
INDUSTRIAL WASTESJ
ENVIRONMENTAL INPUTS
fSOLAR RADIATION
-IWATER TEMPERATURE
| LIGHT EXTINCTION
^SYSTEM PARAMETERS
VERTICAL
EXCHANGE
EPILIMNION
-*• TRANSPORT
J 1
f ^SETTLING
HYPOLIMNiON
BENTHOS
ilirniiHIlin1
FIGURE 2
MAJOR PHYSICAL FEATURES INCLUDED IN LAKE I MODEL
-155-
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I
t-1
Ul
I
UPPER TROPHIC
LEVEL *2
CARBON
J
UPPER TROPHIC
LEVEL #1
CARBON
1
;
>
CARNIVOROUS
ZOOPLANKTON
CARBON
j
HERBIVOROUS
ZOOPLANKTON
CARBON
i
i
1
I
PHYTOPLANKTON
CHLOROPHYLL
j NITROC
1
1
1
L ORGANIC . AMI
J NITROGEN " HfTl
1
1
!
L_
JEN CYCLE
rfONIA ^ NITRATE
SOGEN NITROGEN
j I
PHOSPHOROUS CYCLE "j
f '"' •'•' ' r -i ' '
^ ORGANIC
PHOSPHOROUS
t
1
. AVAILABLE
PHOSPHOROUS |
1
J
BIOLOGICAL
SUB-MODEL
CHEMICAL- BIOCHEMICAL
SUB -MODEL
FIGURE 3
SYSTEMS DIAGRAM-LAKE I MODEL
-------
to solve the equations using explicit time-space differencing.
For the LAKE 1 model, a time step of 0.5 days was used. For
a one year simulation, the .central processing unit (CPU) time
required for execution is about 7 seconds. Total CPU time
required however is 30 seconds with additional overhead converted
to equivalent CPU time being 115 seconds. The CPU time excluding
overhead is equal to about 1.4 milliseconds per compartment
step. A number of runs have been made using the Lake 1 model
structure. The purposes of these runs are to 1) test program
elements 2) study the behavior of the system and its sensitivity
to various system parameters and inputs and 3) prepare a
preliminary verification of the Lake 1 model using data collected
prior to IFYGL. These early runs therefore represent a type
of "tuning" of the model using pastdata preparatory to a more
independent verification of the IFYGL data. The Lake 1 model
has been used to examine several areas including:
1) Variable levels of spring and fall vertical mixing
2) Settling velocities for phytoplankton.
3) Zooplankton grazing rate
4) Zooplankton and higher-order predation using up to
four trophic levels
Some of the output from these areas is discussed below:
(a) Variable Vertical Mixing
Vertical mixing and dispersion are important
phenomena in the dynamics of phytoplankton population in lakes.
Fig. 4 shows the effect of vertical dispersion on chlorophyll a.
The runs include a sinking velocity of 0.05m/day. A bimodal
-157-
-------
a.
o
a:
2
a
25
20
15-
i*
la "A
a. -
a.
No Mixing
Mixing Regime (2)
Mixing Regime(1)
M
r^ r i i \ t
MJ J ASON
X
•a
IN
£
'o
•^
Z
O
DISPERSI
wi
^
O
i
LU
3.5-
30-
v« V
2.5-
2.0-
1.5-
0.5-
Cb)
\?)
• »
*.
* A
* •
• *
* «
* »
\ /
• •
* •
* *
* n
ft «
* *
* »
* •
• •
» k
• ,
P) \ /
* \ • /
• I */
\\ 1
\\ jf
' 1 ^
i i i j i j r i J _ i « _
•102
•^
o
i
CM
E
o
M
M
N
FIGURE 4 EFFECT OF VERTICAL DISPERSION
(a) PHYTOPLANKTON AS CHLOROPHYLL a
(b) VERTICAL DISPERSION REGIMES
-158-
-------
distribution of phytoplankton occurs in all cases due to the
interaction of the two higher zooplankton levels used in these
runs. As populations build up in the spring, the herbivorous
zooplankton increase. This together with nutrient depletion
decreases the phytoplankton population and at about the same
tinue, the carnivorous zooplankton prey on the next lowest
trophic level. The phytoplankton can then increase again in
the late summer.
As shown in Fig 4, the main effect of vertical mixing
is in the spring where populations increase more rapidly when no
mixing is allowed and reach a peak earlier. With mixing, the
first peak is delayed and reduced in magnitude. The results
in the summer and early fall are generally comparable under the
different dispersion regimes although the timing of maximum and
minimum is changed.
(b) Variable Phytoplankton Settling Velocity
A number of analyses using the Lake 1 model have been made
to examine the behavior of the phytoplankton population under
different settling velocities. The literature has been reviewed
for typical ranges of phytoplankton settling velocity and it
subsequently became clear that many of the published values for
phytoplankton sinking in quiescent water are much too high
to support growth. This is due to the importance of other
factors such as vertical dispersion and the interaction
between the sinking of phytoplankton and their physiological
state. Phenomema such as the generation of gelatinous sheaths
-159-
-------
by phytoplankton have been shown to be of importance in settling.
Published values of the sinking velocity of phytoplankton range
from 0.07 - 18 meters/day. In some instances, of course the
settling velocity is zero or negative as in the case of blue
green algae. Some net deposition of phytoplankton must occur
in lakes, like Lake Ontario on the basis of examinations of
the sediments. Accordingly, the model should include this
phenomenom and during this stage of the work, the settling
velocity has been treated as a parameter at two levels - 0.5,
0.05 meters/day in addition to the zero settling velocity case.
Fig. 5 summarizes the results from several analyses
using differing sinking velocities. For these runs, zooplankton
grazing was set at 0.06 1/mgcarbon-day-°C and no vertical mixing
was used. At a velocity of O.5m/day phytoplankton populations
never exceed about 3yg chlor/1 and total zooplankton carbon
Fig. 5b) never exceeds about 0.08 mg Carbon/1. Both values are
considerably less than observed as shown later. The reason for
the low levels is that under a settling velocity of 0.5m/day
(which for the 17 meter depth of the epilimnion represents a
"decay" coefficient of .03/day), the phytoplankton are not
retained in the upper layer long enough to undergo net growth.
As a consequence, zooplankton levels are also low and the nutrient
concentrations remain high and are not reflective of observed
nutrient depletion. On the basis of runs like those shown in
Fig, 5, it was concluded that if a reasonable grazing coefficient
is used, net settling velocities for that model must be
substantially less than 0.5m/day. Using a velocity of 0.05m/day,
-160-
-------
30-
o.
g
3
O
<
0.
1
20-
15-
5-
0
PHYTOPLANKTON
SETTLING VELOCITY
M ft
M
J ' J ' A
0-5 m/day
0.05 m/day
S ' O ' N D
(b)
o
m
_
a.
O
O
.15-
.10-
.05-
0-
.15-
.05-
•HERBIVOROUS
2OOPLANKTON
CARNIVOROUS
ZOOPLANKTON
FOR
>—CD
ABOVE
HERBIVOROUS
ZOOPLANKTON
CARNIVOROUS
ZOOPLANKTON
FOR
(2>
ABOVE
J ' F MANl'j J ASO
N D
FIGURE 5 EFFFCT OF PHYTOPLANKTON SETTLING VELOCITY
a) PHYTOPLANKTON
b) ZOOPLANKTON
-161-
-------
the behavior of the phytoplankton biomass is quite different as
shown in Fig, 5 (a). Now, the lower trophic levels have a chance
to grow and a reasonable predator -prey relationship begins to
develop. Curve \_ of Fig. 5 (a) exhibits the two peaks in
chlorophyll discussed above. Zooplankton biomass carbon as
shown in Fig 5b for the lower settling velocity is greater than
0.1 rag carbon/1 and approaches 0.2 mg carbon/1. These values
are closer to observed zooplankton carbon levels. The sinking
velocity of phytoplankton also has an important effect on the
nutrient uptake as shown in Fig. 6 which is a plot of the
nitrate and orthophosphate concentrations calculated under
the two velocity conditions. In addition, Fig.6 shows the
nitrogen and phosphorous limitation terms, i.e. the ratio of
total inorganic nitrogen to total inorganic nitrogen plus the
Michaelis or half-saturation constant for nitrogen and similarly
for available phosphorous. The half-saturation constant for
nitrogen for these runs was set at K = 25yg/l and for
phosphorous at K^ = lOyg/1. It can be seen that nutrient
uptake and growth limitation is minimal for the case of sinking
velocity = 0.5m/day. This is a result of the minimal
phytoplankton growth as shown in Fig, 5. At the lower sinking
rate, however, nitrate uptake is increased and the computed
values approach but do not reach those that are observed. As
indicated in the upper curves of Fig. 6, nitrogen does not
significantly limit growth.
The lower curves representing the phosphorous dynamics
however do exhibit a limiting effect. If attention is directed
-162-
-------
en
H
Z
i i
NITROGEN LIMITATION - N/KmnfN
1
.5-1
(1) (2)
J ' F ' M ' Ar M ' J ""j * A n S ' O ' N ' D
curve 1 - 0.05 m/day settling velocity
curve 2 - 0.50 m/day > >
1.0-
.5-
PHOSPHORUS LIMITATION-
M ' A
M'J 'J'A 'S'O'N'D
EFFECT OF PHYTOPLANKTON SETTLING VELOCITY ON NUTRIENTS
AND NUTRIENT LIMITATION
FIGURE 6
-163-
-------
to the phosphorous limitation term, it is seen that for both
settling velocity cases/ levels of phosphorous are such that
a limitation of .50 - 0.60 prevails during the early and later
parts of the year. However, substantial differences occur in the
spring and late summer. At day 135, a minimum value of 0.2^
is calculated indicating that phosphorous is acting as a
significant limiting factor in the phytoplankton growth. This
helps explain the decrease in phytoplankton biomass beginning
at day 120, (see Fig 5). Two effects are occuring: a)herbivorous
zooplankton are growing rapidly and b) phosphorous levels are
being depleted to below the half-saturation constant thereby
acting to reduce the growth rate. It is interesting to note then
that a biomodal distribution in phytoplankton can be obtained
without a species differentiation. The latter is often offered
as the explanation for the observed two peaks in the phytoplankton.
In order to accomplish this however, at least two trophic levels
must be included above the phytoplankton. This permits a
higher order predation, e.g. carnivorous zooplankton which
reduces the lower zooplankton level. The reduction (as shown at
day 210 of Fig 5b, for the lower settling velocity) permits
phytoplankton to grow again in late summer.
The sequence of events just described, and the
display of the calculations in Figs 4 - 6 is not put forth as
any definitive explanation of the "true" course of events. Much
work remains to be done on the model; the results are simply
©
presented to show the behavior of the system and to offer
possible effects that may be important. The veracity of even
-164-
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tiie preliminary model depends to some degree on the comparison
of model output with observed data.
(c) Comparison of Lake 1 model with Observed Data
Figs 7 and 8 show observed data for the main lake stations
for phytoplankton chlorophyll a and zooplankton carbon. As seen,
chlorophyll a levels are generally less than Spg/l during the
winter and early spring and the increase to 5 - 10yg/l during the
late spring. There is some indication of a summer minimum
especially in 1967 and 1969. During the late summer and early
fall, chlorophyll levels again increase to slightly greater than
5ug/l.
The 1967 data are an exception to the general level of
chlorophyll a of 5ug/l. As shown in Fig. 7, a spring average
concentration of about 20yg/l is reported for the main lake
stations. This order of concentration for the entire lake has
not since been reported and is considered, for purposes of
preliminary model verification, to be an anomalous situation.
The zooplankton carbon ranges shown in Fig. 7-were obtained
from published sources and represent only approximately the lake
wide situation. The important point from a modeling point of
view is that zooplankton carbon of greater than O.lmg/1 should be
calculated by the preliminary model. (See for example, Fig. 5b).
Figs 9 and 10 show comparison of model output with observed
chlorophyll a range, total Kjeldahl nitrogen, nitrate nitrogen
and reactive phosphate.
The model structure used in the output shown in Figs 9 and
10 includes the following:
-165-
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J8 30-
1 25-
^^ fit w
|
< en
O
H
z 10-
<
^ J
a.
o 5_
0.
w
o
Mi
-
n
—
o- Nicholson Data ISO/
IJC Report
X-FWPCA 1965
"^T" • Monthly Averages and
Ranges - UC Report
JQ^CCIW- Means ± Standard
o ' Deviation
JL*
: "T
: :
m 2 • ^^^
* 4flT* 1
^ •l«M ^SJ_ AA.
y# ^^^ •^•"^H'^" MfM ®F
wS fr 1 J^j II J^^^
Z|!-^3Ci .i. o -j*
o*-
M
A ' M ' J ' J ' A ' S • O ' N ' D
.6-
.5-
2
O
K:_
cu o>
O E
O
M
o
-3
.2-
.1-
APPROXIMATE RANGE AND LAKE WIDE
AVERAGE OF ZOOPLANKTON CARBON
1967 _
J£cladocerans { copepods
M'A'M'J'T'A'S'O'N^D*
FIGURE 7 PHYTCPLANKTuN CHJLOROPHYLLa , 1965,1987 & ZOOPLANKTON
CARBON - LAKE WIDE AVERAGES
-166-
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35-
o.
O
t£.
2
2
a.
30-
25-
20-
15-
10-
5-
i r i
J F M A
M
N O
a.
O
ce:
s
I
o
30-
25-
20-
(b)
_
a.
O
>-
X
D.
15-
10-
5-
M
i i
M J J
N
FIGURE 8 PHYTOPLANKTON CHLOROPHYLLa FOR SOME MAIN LAKE STATIONS
a) I969
b) I970
-167-
-------
a.
o
O ^
t- O)
* a.
Q.
O
0.
1967 Spring Peak
1967,69,70
Approximate
Data Range
N
FIGURE 9 COMPARISON OF MODEL OUTPUT WITH RANGE OF
OBSERVED CHLOROPHYLLa DATA
-168-
-------
01
O
o
a:
x
LU
2
tu
O
O
a
3X> 60
90 120 150 180 210 240 270 300 330 360
UJ
a. a>
LU
a
.025"
.020-
.015-
.010
.0.05-1
JFMAMJJASOND
COMPARISON OF MODEL OUTPUT WITH OBSERVED NUTRIENT DATA
FOR 1967- MAIN LAKE
FIGURE 10
-169-
-------
1) Mixing regime (2) of Fig 4(b)
2) Two zooplankton levels - grazing coeffecient of
each = .06 1/mgCarb - day - °C
3) Settling velocity for phytoplankton = 0.05m/day
4} Half-saturation constant for total inorganic
nitrogen = 25ng Nit./I
5} Half-saturation constant for phosphorous = lOug p/1
In general, the preliminary verification is quite good and
reproduces some of the major features of phytoplankton dynamics
and nutrient uptake. In all cases, the order of magnitude is
reproduced and the dynamics are approximately correct although
there are several areas that warrant more detailed work. For
example, the nitrate nitrogen is not depleted in the model as
much as is observed. This is attributed to the coarseness of
the preliminary model with its single volume representation of the
epilimnion. The observed nitrate data shown in Fig. 10 are
for the surface of the lake while the model output represents an
average over the top 17 meters.
-The 1967 high values of chlorophyll are not duplicated by
the model. Indeed, the model indicates that a very substantial
nutrient input would be required to grow up to 20yg/l
chlorophyll over the entire lake.
Overall, the results are encouraging although it should be
recalled that the model does not yet exhibit any horizontal
detail. Further, it should be stressed again, that the model as
presently constituted is not considered to be a definitive
-170-
-------
explanation of the observed data. The model does indicate
however, that some major features of phytoplankton and nutrient
behavior can be reproduced and the model therefore . provides a
basis for extension to the more detailed spatial computation.
-171-
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GRANT NUMBER 800646
A NEAR SHORE SURVEY OF
EASTERN LAKE ONTARIO
PART I
Under Grant Agreement R-800646
from
United States Environmental Protection Agency
by
Richard B. Moore
Lake Ontario Environmental Laboratory
State University of New York
College of Arts and Science
at Oswego
November 1973
-------
Near Shore Study of Eastern Lake Ontario (IFYGL)
INTRODUCTION
The Great Lakes System is truly one of nature's wonders
which contain an estimated 20 percent of the world's fresh
water sjupply. Thirty-five million people live within the drain-
age basin of the Great Lakes--St. Lawrence River System with
this number rising to forty-four million by 1980. Intensive
use for multiple purposes of this water system has resulted in
controversy and increasingly difficult management problems.
Information is needed to serve as the basis of rational
management decisions to solve the problems of eutrophication,
multiple use and crossing of international boundaries. An effort
to gather this information resulted from the International Year
for the Great Lakes (IFYGL), a joint study of Lake Ontario by the
United States and Dominion of Canada.
The primary objective of the IFYGL was to investigate a
number of problems associated with hydrology, meteorology, physical
limnology, biology, chemistry and geology of Lake Ontario and its
drainage basin.
The following is an initial report summarizing chemical and
biological studies of Eastern Lake Ontario.
REASONS FOR PROJECT
Most substances enter Lake Ontario from rivers and surface
runoff. The major effects of these substances is first seen in
the near shore waters. Such physical parameters as currents and
the thermal bar tend to trap and retain these materials within
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these near shore areas. Effectively, then, the near shore
region remains separate from the rest of the lake .and has
chemical and biological parameters which are distinctly differ-
ent from the remainder of the lake.
The southern shore of Lake Ontario includes the outflows
from two large polluted rivers and from a number of smaller
streams. There are several estuaries, some of which are highly
eutrophic. Two conventional and two thermonuclear power plants
release heated effluents into the study area Many more are
planned. All of these inputs influence the biology and chemis-
try of the lake and, in turn, the uses of the lake.
Many cities and towns along the southern shore obtain their
water from the lake. Even inland cities, such as Syracuse, New
York, use the lake as a source of water. This study has provided
data for use in evaluating the areas from which present supplies
are obtained and for use in locating possible sites for future
supplies.
Most of the recreational activities on the lake occur in the
near shore region. Here the results of increased nutrient input
and pollution in general are most easily seen. Beaches become
clogged with Cladophora. Large mats of this alga tend to float
throughout the near shore waters usually at a time when this
region is most intensely used for recreation. Most sports also
place within the near shore zone. Biological, chemical and physi-
cal parameters within this area directly affect fishing patterns
and the amount and species of fish present.
-173-
-------
A hydrographic survey of the type reported here provides
baseline data from which future changes in the lake can be measured,
The survey also •"Dints up areas which require more detailed study.
N«w areas of enrichment, whether chemical or thermal change, can
be evaluated in terms of the reference conditions found.
The results of this study also provides input for the formu-
lation of lake models. Since most of the physical, chemical and
biological activity occurs first in the near shore waters, the
information provided by this study is essential to any proposed
modeling of lake processes.
PROGRAM OBJECTIVES
1. To obtain information on present status of Lake Ontario
throughout the near shore region. TMs can be used as a
baseline for future informational requirements and to
provide input for the information of predictive models of
lake processes.
2. To determine the flow of nutrients into, within and out of
the near shore including movements within the biological
system.
3. To ascertain the space-time distribution and identification
of zooplankton, phytoplankton and benthos populations within
the eastern near shore area.
4. To examine the extent of Cladophora growth throughout the
eastern near shore region and to determine its growth patterns
and to attempt to find means by which this problem alga can be
controlled.
-17A-
-------
5. To determine the distribution.of polychlorinated biophenyls
(PCB's) and chlorinated pesticides in water, s.ediment and
organisms.
AREA OF STUDY
The region of study was the southeastern portion of the
near shore zone of Lake Ontario comprised of 140 km of shorline
extending from Rochester, New York, to Stony Point on the east
(Figure 1). A total of fifteen sampling transects consisting of
three stations each were established at ten meter intervals
along the coast (Figure 2). The stations along each transect
were normal to the coast line and located at 0.5, 4.0 and 8.0
Km from shore. These stations were located during each cruise
with the aid of a Decca Navigational System. Decca coordinates
were determined from Decca charts specially prepared for IFYGL.
Latitude and longitude i-rere also determined for each station
from these charts. Table 14 Appendix 1, lists station number,
latitude and longitude, Decca coordinates and depth of water in
meters.
Intensive sampling of the Oswego River and Black River mouths
was accomplished to determine the chemical and biological impact
of these rivers on contigrous parts of the lake. There were
twenty sampling stations on the Oswego River (Figure 4) and
fifteen stations on the Black River.
A total of ten cruises were completed in the period of April
through December, 1972. The first cruise was not implemented until
June 1972 because of late funding and subsequent delays in delivery
of equipment. Each cruise consisted of 45 stations on the eastern
end of Lake Ontario as prescribed in the operation plan.
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Samples collected on each cruise consisted of water,
chlorophyll, zooplankton, and phytoplankton. Specific samples
collected seasonally were benthos, pesticides, Cladophora, and
sediments for various chemical analyses. In all, over 6,000
samples of all types were collected and preserved for analysis.
Listed below is a breakdown of sample numbers by type.
Samples Collected on Eastern Near Shore Program
Water Samples
Heavy Metals Analysis 666
Dissolved Nutrients 720
Total Nutrients 912
Chloronhyll Analyses 711
Phytoplankton Quantitation 551
(Lugols Treated)
Zooplankton Quantitation 1094
Benthos, 272
Sediment" Chemistry
Pesticides
Heavy Metals 59
Nutrients 402
Phytoplankton Biomass
Pesticide Chemistry and
Pr.B Quantitation 500
(water, sediment, plankton,
fish)
Cladophora Biomass 120
TOTAL 6007
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METHODS AND MATERIALS
Methods of Sample Collection and Analyses
for the Eastern Near Shore Survey of Lake Ontario (IFYGL)
The eastern near shore survey of Lake Ontario consisted
of fifteen transects with three stations per transect for a
total of forty-five stations, Each station required the collec-
tion, initial analysis and preservation of water samples, and
the collection and preservation of ohytoplankton and zooplankton.
Light and temperature readings were also required at each station.
Periodically throughout the field year, benthic and sediment
samples for nutrient analysis were taken as well as water and
s§d.iment samples for pesticide studies.
WATER SAMPLES
The water samples were collected at every station from three
depths; surface, mid-depth, and bottom. The samples were collec-
ted using 8.1 liter Van Dorn water samplers suspended simultaneously
at the prescribed depths on a vinyl coated cable. Since the water
was analyzed for heavy metals, PVC sample bottles were used. When
the water samples were brought aboard, dissolved oxygen content
was immediately determined. The Winkler Method was used as per
Standard Methods for Water and Wastewater Treatment (13th Edition).
The results were reported in milligrams per liter.
Total alkalinity was also determined shipboard. One thousand
mis of sample water was titrated with .020 N ^304 using 5 drops of
methyl orange as an indicator. The samples were titrated to a color
of salmon pink against a standard made up of 100 mis of deionized
waiter and 5 drops of methyl orange. The burett reading was multi-
plied by 10 to give the total alkalinity reported as milligrams per
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liter as calcium carbonate.
The pH of the sample water was determined using a Photo*
volt model 126A pH meter.
The light transmission of the waters at each station was
recorded using a tsuruml Seike Submarine photometer. The instru-
ment is equipped with both deck and submarine photocells so a
deck illumination reading and submarine illumination readings were
taken. Submarine readings were taken at 0.2 meters, 1 meter and
at one meter intervals to the depth where there was zero light
penetration. Light intensity in lux was determined from standard
curves.
The temperature of the water was taken at the surface and at
one meter intervals down to the bottom. A Whitney model TC-5C
thermister was used. The temperatures were reported in degrees
centigrade.
Besides the preliminary analysis of the water, samples were
also sent to EPA Rochester Field Station for further analyses.
Liter plastic sample bottles were throughly washed then rinsed
twice with a solution of one part concentrated nitric acid and one
part water. The bottles were then rinsed twoce with deionized
water. The bottles were filled with sample unfiltered water and
treated with 2.5 ml concentrated nitric acid and 2.5 mis concen-
trated redistilled hydro chloric acid. Five hundred mis of the
sample water was placed untreated in a plastic bottle and frozen
immediately. Another five hundred ml sample was first filtered
through a millipore apparatus using a filter with a 45 micron pore
size. The water was then transferred to plastic sample bottles
and frozen at -20°C.
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Another 2 liters of the sample water was drawn and used for
chlorophyll analysis. The water was drawn through a 47 mm glass
fibre millipore filter and discarded. The filter was wrapped in
aluminum foil and frozen. Chlorophyll samples were collected at
the same depths before mentioned.
ZOOPLANKTON
As part of the procedure at-each station, zooplankton
samples were taken. The samples were secured using a 1.5 mesh.
Plankton tows were drawn from 5 meter intervals up to 30 meters
in depth, then every 10 meters down to SO meters and from the bottom.
If the bottom was over 100 meters in depth, then an additional
tow was made from 70 meters. The plankton in the net was washed
into the cup by spraying the net with lake water from a hose from
the outside of the net as to avoid contamination of the samples.
The samples wer^ then transferred to 250 ml plastic bottles. The
zooplankters were narcotized with carbonated water for ten minutes
and preserved with formalin buffered with sodium acetate to pH 8.
PHYTOPLANKTON
Quantitative samples of phytoplankton were taken at every
5 meters and bottom at near shore stations and every 15 meters and
bottom at mid and outer stations. 2 liters of the water was con-
centrated by pouring it through a NO. 25 mesh plankton cup. The
contents of the cup was then transferred to a 250 ml sample bottle.
The plankton cup was rinsed three times with deionized water and
the rinsing also poured into the sample bottle to assure the
quantitative transfer of the organisms. The samples were preserved
with a Lugols solution.
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PHYTOPLANKTON BIOMASS
Biomass samples were taken at each station. -These samples
consisted of two verticle tows, using a 1.5 meter No. 25 mesh
plankton net, from the bottom. The contents of each tow was
transferred to a separate sample bottle and frozen immediately.
BENTHIC AND SEDIMENT SAMPLES
Benthic and sediment samples were collected using a .05 sq
meter ponar dredge. Three replicate samples were taken at each
station, each sample being washed through a #20 mesh screen. The
samples were preserved separately with a 10% rormalin solution.
For the sediment samples, mud was packed in mason jars and cooled
to 5°C.
CLADOPHORA BIOMASS
Cladophora samples were taken at 3 times during the field
year. The samples were secured by divers using scuba. A Plexi-
glass box was placed and the substrate covering in area of 1000
square centimeters. All of the Cladophora in that area was re-
moved, packed in jar1: and chilled for transportation to the on
shore lab where they were frozen at -20°C until analysis.
Temperature measurements, transparency, pH, alkalintiy and
dissolved oxygen values were also taken at each Cladophora
station. The temperature was recorded for every meter in depth
using the Whitney Thermister. The transparency of the water was
arrived at by using a Sechi Disk. The pH, alkalinity and dissolved
oxygen were all taken the same way as previously described.
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LABORATORY METHODS
Chlorophyll Analysis
Frozen filters were trimmed and ground in a glass mortar
with a teflon pestle. The sample was extracted with 901 acetone in
water overnight. All extractions were performed in total darkness.
The extract was centrifuged at 3000 rpm for ten minutes.
The supernatant was decanted into spectrophotometer cells and
the absorbance determined at 750, 663, 645, and 630 mu.
Pheophytin A was determined after acidification of the sample
with 10% HCL.
Concentrations of chlorophylls and pheophytin were deter-
mined by the SCOR/UNESCO equations and method of Lorenzen,
respectively.
BENTHOS
Triplicate samples from each station were washed in the
laboratory to remove silt, and all organisms were sorted by hand.
Each organism was mounted on microscope slide and identified to
species whenever possible.
In addition to species identification and enumeration,
length of each organism was recorded to the nearest 0.5 mm.
Observations of sexual maturity and instar stages were also
recorded.
Type specimens of each new organism were preserved for
future reference, Type collections were augmented with photo-
micrographs. A particular effort was made to document photo-
graphically all species which were mounted on slides.
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PHYTOPLANKTON ENUMERATION
Samples preserved in Lugol's solution -were left undisturbed
for 24 hours. This allowed sufficient time for the phytoplankton
to settle to the bottom of the container. All preservative in
excess of 50 ml was removed with a pipette. The sample was
rinsed from the bottle into a 100 ml graduated cylinder. The
sample was allowed to settle overnight again and the volume re-
duced to 18 ml with a pipette. The sample was stored in a 20 ml
vial until counted.
After mixing the contents of the vial, a subsample was trans-
ferred to a Sedgeqick-Rafter counting chamber with a volume of
1 CC. Th° contents of the counting chamber were allowed to settle
for 15 minutes and counted. Thirty fields, 10 on each of three
counting chambers, were counted. A magnification of 100X was used
for- all work.
Identification was made to species whenever possible. Photo-
micrographs of all species were made for documentation purposes.
After counting all, samples were saved for future reference and
possible exchange of samples with other laboratories.
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ORGANIC NITROGEN - REVISED ORION PROCEDURE
General Procedure:
1. Sample - use 500 ml of unfiltered water or 1 g. of dried, ground
sediment dissolved in 500 ml double distilled water
(ammonia free). Place in 1 liter wide-mouth Erlenmeyer
flask.
2. Ammonia removal - add 15 ml of phosphate buffer, and boiling chips.
Boil at moderate temperature until slightly less
than 200 ml remains. Let cool. Add SO ml of
digestion reagent.
3. Digestion - boil sample as rapidly and as hotly as possibly; at
least 340°C. Yellow-white fumes of S03 should be
given off. Continue to boil until less than 200 ml
is left.
4. Preparation - transfer sample to graduated cylinder. Make volume
up to 200 ml with double distilled water. Take a
50 ml aliquot, add 40 ml double distilled water.
Add 10 ml alkaline reagent. Check pH with meter,
should be greater than 11.5. If sediment samples
are cloudly at this point, filter through glass
fiber filter in Millipore apparatus.
5. Determination - Place sample in 150 ml beaker and stir with magnetic
stirrer. Read ABS millivolts using ammonia specific
probe. Determine mg of ammonia from standard curve
prepared from known concentrations.
6. Notes - Let sample run until the millivolt reading has stabilized.
At low 'concentrations this could take S-10 minutes. Keep
the probe in a beaker of double distilled water between
readings and wash and dry membrane- carefully after each
reading. Store probe in 0.1M NH.C1 solution overnight or
for longer periods.
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Total Phosphorus (Stannous Chloride Method)
1. Apparatus: (to run 6 samples and a blank)
(a) Seven 250 ml beakers
(b) Seven 250 ml graduated separatory funnels
(c) Seven 50 ml volumetric flasks
(d) Pipets:
1. Seven 25 ml
2. Two 5 ml
3. One 1 ml
4. One 'hiedicine dropper" type
(c) Graduated cylinder, 50 ml
(f) Two 50 ml burets, buret clamp and stand
(g) Two hot plates (four beakers to each plate)
(h) Safety aspirator for pipeting
(i) Spectrophotometer, set at 625 nm, with either JL cm
cuvettes for 1.0 - 0.05 ppm or 5 cm for 0.1 - 0.002
ppm ranges.
2. Reagents:
(a) Cone. HC1 and cone. HN03
(b) 3.6N H2S04: carefully add 100 ml cone. H2S04 to 1 liter
of distilled water.
(c) Phenophthalein indicator solution
(d) 4.ON NaOH: dissolve 156 g. NaOH in 1 liter dis. water.
(e) 0.2N l^SO.: Add 5.55 ml cone, acid to 1 liter water.
(f) Benzene-isobutanol solvent: Mix equal volumes of benzene
and isobutyl alcohol.
(g) Ammonium molybdate reagent (I): Dissolve 25 gm. of
(NH4)6M07024'4H20 in 175 ml dist. water.
Cautiously add 280 ml cone. H2S04 to 400 ml
dist. water. Cool, add the molybdate sol'n,
dilute to 1 liter.
(h) Ammonium molybdate reagent (II): Dissolve 40.1 gm of
(NH4)5Mo7024'4H20 in about 500 ml dist. water.
& Slowly add 396 ml of reagent (I). Cool, dilute
to one liter.
(i) Alcoholic sulfuric acid solution: Cautiously add 20 ml
cone. H2S04 to 980 ml methyl alcohol, mixing
continuously.
(j) Stannous chloride reagent (I): Dissolve 2.5 g SnCl2'2H20
in 100 ml glycerol. Heat and stir to hasten
solution.
(k) Stannous chloride solution (II): Mix 8 ml SnCl2 solution
(I) with 50 ml glycerol.
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3. Procedure:
(a) Place 100 ml of sample into 250 ml beaker. Add 3 ml
cone. HC1 and 0.5 ml cone. HNC>3 to each sample. Run
a control sample with each batch using 100 ml of
distilled water.
(b) Place samples on hot plates and evaporate to about
30 ml. Do NOT let the beakers go dry! Add 4 ml of
3.6N sulfuric acid and evaporate to about 3-5 ml,
when the nitric acid begins to fume. Do not let the
samples go to dryness. Cool, dilute with about 20 ml
distilled water. Add a drop of phenophthalein and
titrate with 4N NaOH to a pale-pink color. Back-titrate
with o.2N H2S04 until the pink just disappears. Transfer
to a separatory funnel, washing with dist. water, and
dilute to 40-45 ml with more distilled water.
(c) Add 50 ml of benzene-isobutanol solvent and 15 ml of
molybdate (II) reagent to each sample. Close funnel
and shake for 1 minute. Pipet off 25 ml of the top
layer, and transfer to a 50 ml volumetric flask. Add
10-15 ml of alcoholic sulfuric acid solution to each.
(d) To each volumetric flask add 10 grops of stannous
chloride (II) solution and swirl vigorously. Dilute
to volume with alcoholic sulfuric acid solution and
mix thoroughly.
(e) After 10 minutes but before 30 minutes, read transmittance
against the blank at 625 nm.
Since the distilled water may contain a finite amount
of phosphates, use a blank consisting of 25 ml of
alcoholic sulfuric acid solution, 25 ml benzene-iso-
•butanol, and 10 dreps stannous chloride (II).
Find the ppm of P04-P using graph prepared from
standard solutions.
Notes: If the transmittance is less than 47%, immediately
dilute the colored sample with alcoholic sulfuric
acid until transmittance is between 47 and 97%.
Multiply result by amount of dilution.
The blank sample of distilled water is run to determine
the amount of contamination from the glassware. All
glassware should be rinsed with a 50/50 solution of
101 HC1 and 10% H2S04, followed by two rinses with
double distilled water, then acetone.
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DETERMINATION OF CHLORINATED PESTICIDES AND PCB'S
Extraction of Water (1)
The water was filtered before a 500 ral aliquot was trans-
ferred + 0 a 18, separator/ funnel. After dissolving 5g of sodium
chloride in the sample, it w«>s extracted with 100, 50, and 50 ml
of petroleum ether, shaking for 30 seconds each time. Each ex-
tract was dried by passing it through anhydrous sodium sulfate.
The combined extracts were evaporated almost to dryness and then
diluted to an approximate volume for analysis by gas chromatography.
Extraction of Sediment and Algae
A lOOg subsample was extracted for 3 minutes in a Waring
blender with 200 ml of a (1+1) mixture of hexane and 2-propanol.
The homogenate was filtered into a 16 separatory funnel. A 500 ml
portion of distilled water and 5g of sodium chloride were added to
the extract. The funn«l «as shaken gently for 30 seconds. After
the layers separated, the bottom aqueous layer was discarded. Thfi
hexane was then washed once more with distilled water. The volume
of hexane remaining after the second wash was measured and recorded.
The hexane was dried with anhydrous sodium sulfate and evaporated
almost to dryness. The residue was taken up in 10 ml of hexane and
processed through the Florisil column step.
Extraction of Fish (2)
A 50g subsample of ground fish was weighed into a blender bowl.
A lOOg portion of anhydrous sodium sulfate was added and the mix-
ture was blended for one minute. The sample was extracted for 2
minutes with 150 ml of oetroleum ether. The ether was decanted off
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through a piece of filter paper. The sample was then re-extracted
twice more with 100 ml of petroleum ether each time. The combined
extracts were evaporated just to dryness and the lipid content
was determined. The fat was then transferred to a T25 ml separator/
funnel with a total of IS ml of petroleum ether. The ether was
extracted with 4 x 30 ml of acetbnitrile (previously saturated with
petroleum ether), shaking 1 minute each time. The combined
acetonitrile extracts were evaporated just to dryness. A 20 ml por-
tion of hexane was added and the sample was again evaporated to
dryness. T^e residue was taken up in 10 ml of petroleum ether
and processed through the Florisil column steps.
Florisil Column (3)
A 22 mm i.d. chromatographic column was prepared by adding a
plug of glass wool, 20g of Florisil, and lOg of sodium sulfate.
The volumn was rinsed with 50 ml of hexane before the concentrated
sediment or fish extract was added. The column was eluted with
200 ml of a 201 dichloromethane in hexane solution. When the
solvent Beached the top of the column, the receiver was changed and
the column was eluted with 200 ml ^f a (50 + 0.35 + 49.65%) solution
of dichloromethane and acetonitrile and hexane. Both eluates were
evaporated just to dryness and taken up in an appropriate amount of
hexane for analysis.
Separation of PCB's from Chlorinated Pesticides (4)
A 22 mm i.i. chromatographic column was prepared by adding a plug
of glass wool and a (4 + 1) mixture o£ actibated siliric gel and
Celite. The concentrated extract was added and the column was eluted
•with 250 ml f petroleum ether. When 250 ml of chrate were collec-
ted (containing possible PCB and aldrin residues), the receiver was
changed and DDT and analogs were eluted with 200 ml of a (1 + 19 +
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80) mixture of acetonitrile and hexane and dichloromethane. The
eluates were evaporated just to dryness and taken up in an appro-
priate amount of hexane for analysis.
Gas Chromatographic Analysis
An aliquot of the final solution was injected into a gas
chromatograph equipped with an electron capture detector. Peak
areas of the sample were compared with those from standard injec-
tions to determine the -amount of residue present.
Note (1)
For fish samples it is expected that the first eluate from the
Florisil column will have to be put through the siluic and column
to separate the PCBs from chlorinated pesticides. This separation
will be used on the types of samples also if there is a hint that
PCBs are present.
C2)
Sample weight for alga will probably be lOg since it was
difficult to obtain a large sample.
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References
Similar to procedure given by
(1) Zweig, G. and Devine, J. M,, Residue Reviews 26, 17-36 (1969).
(2) Porter, M. L., Young, S. J. V., and Burke, J. A., J. Asso. Offic,
Anal. Chem. 53., 1300-1303 (1972).
(3) Mills, P. A., Bong, B. A., Kamps, L. R. , and Burke, J. A., J.
Asso. Offic. Anal. Chem. 55., 39-43 (1972).
(4) Armour, J. A., and Burke, J. A., J. Asso, Offic. Anal. Chem.
53, 761-768 (1970).
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All biological, physical and chemical data submitted by
Dr. Moore with his annual report will be in STORE! by
February 1, 1974 under agency code: 51IFYGL.
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PLANKTONIC ROTIFERA AND CRUSTACEA
OF TEE
LAKE ONTARIO INSHORE REGION
Donald C. McNaught
Samuel J. Markello
Daniel Giovannangelo
State University of Nev York
Department of Biological Sciences
Albany, New York 12222
Research Supported by Environmental Protection Agency
Year I (April 1972-March 1973) summary report from subcontractor
to SUC Oswego (SUNY Research Foundation grant 20-5001-A).
-------
CONTENTS
Page
Planktonic Rotifera 192
Introduction 192
Methods and Materials 193
Testing 193
Results and Discussion 194
Summary 197
References 199
Table I 201
Table II 203
Table III 204
Table IV 206
Planktonic Crustacea 207
Introduction 207
Community Theory 208
Methods 209
Results and Discussion 210
Summary 211
References 213
Table V -214
Table VI 216
Table VII 217
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Planktonic Rotifera of the Lake Ontario Inshore Region
by
Samuel J. Markello
Introduction
This study represents only one component of the Lake Ontario Inshore
Zooplankton Survey. Information on the planktonic rotifer community of Lake
Ontario was scarce prior to the recent lakewide study-'-by Nauwerck (1972).
Nauverck cited data on the seasonal variation- and relative abundance-of
various species averaged over three stations (Burlington Bay, central basin,
eastern region).
The objectives of this study included an analysis of the effect of
sampling locality (region along the shore and distance from shore) on
rotifer population dynamics. Subsequent to significant findings, an analysis
for underlying causes, both biotic and abiotic, will be conducted. In essence
the problem involved the effect of local perturbations on zooplankton production.
Various parameters of the rotifer community should be especially sensitive
to local influences. Diversity, production, and biomass of the rotifers are
known to respond positively to enhanced levels of food resource and temperature
in nature (Nelson and Edmondson, 1955; Hillbricht-Ilkowska and Weglenska, 1970;
Patalas, 1970; Nursall and Gallup, 1971). Community-alpha, a coefficient of
competition at the community level, is likewise expected to vary directly with
resource levels and should be especially evident among stations at various
distances from shore. In addition to the above there are species of rotifers
generally agreed upon as indicators of eutrophic conditions (Pejler, 1957).
This report contains a partial assessment of the samples analysed to date.
These include all surface samples (0-5M) from Cruise I (May 30-June 20), three
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transects (13, I1* and 15) from Cruise II, and five sampling dates for the
three stations of transect 9.
Methods and Materials
Samples were taken at each of three stations (O.h, k.O and 8.0 kilometers
from shore) on 15 transects located between the mouth of the Genesee River and
Stony Point. Zooplankton were collected with a conical net (aperture 6k p,
0.5 M diameter). Vertical hauls were taken at 5-meter intervals (0-5, 0-10,
0-15, etc.) down to 30 meters or bottom, 10 meter intervals between 30 and
50 meter depths, and 50 meter intervals thereafter.
All samples were initially treated with carbonated water (a relaxant for
the organisms) and preserved with sufficient formaldehyde to yield a k%
solution.
In the laboratory, subsamples were taken and dilutions made accordingly
to insure at least 50 individuals of the dominant species/count. A count of
all specimens in three subsamples was found to be adequate (tested by analysis
of variance) to detect differences in the major species between samples from
randomly selected stations. References consulted for keying included
Ahlstrom (19^0, 19^3), Voigt (1956), Nipkow (1957), Koch-Althaus (1963),
Sudzuki (196*0 and Pourriot (1965). Despite this there is uncertainty about
three species, Polyarthra dissimulans, Polyarthra longiremis and Synchaeta sp.
Testing
To determine the effects of distance from shore (DFS) and location along
shore (LAS) on density of each species, a non-parametric test was employed
(Friedman's method of randomized blocks). The possibility of interaction
between the fixed main effects (DPS and LAS) prohibited the use of a Model I,
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2-way factorial ANOVA without replication.
To test for density differences between two specific regions (the average
of transects 1, 2 and 3 versus transects 13, I1*, 15) a Model I, 2-way factorial
ANOVA (with transects as replicates) was utilized. The effects of time and
DPS on density at transect 9 were tested with a mixed-model, 2-way factorial
ANOVA.
Results and Discussion
l) General
Most species of rotifers, encountered in the inshore region of Lake
Ontario on Cruise I (Tables 1-H), were likewise observed by Nauwerck (1972)
in June 1970. In addition we found specimens'of Keratella crassa, Polyarthra
major and Trichocerca multicrinis occurring in June while Nauwerck observed
them later in the season. Species unique to the inshore study include
Brachionus quadridentatus (innermost station of transects 1 and h), Brachionus
urceolaris ("IN" of'transect 1, and "IN" plus "Mid" of transect II), Polyarthra
euryptera (transects 3, 8, 9) and 'Polyarthra dissimulans plus P_. longiremis
(occurring at all transects). The latter combined species of Polyarthra are
difficult to separate considering overlapping sizes, identical number of
ovarian nuclei and both possessing a pair of ventral appendages (Nipkow, 1957).
Because of their large size the combined species of Polyarthra are easily
distinguished from P_. dolichoptera.
For the purposes of this study, Keratella earlinae, 1C. irregularis and
1C. cochlearis, V_. robusta have been combined. Nauwerck (1972) combined'the
first two but kept the third separate. All three are morphologically alike
with considerable overlap in body and spine lengths They are easily
distinguished by the plague pattern on the empty lori'ca; however, most
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specimens taken are intact and time does not permit the close scrutiny needed
to separate them.
An additional point of taxonomic significance was the presence of ill-
species of rotifers during Cruise I (indicated in Table l) which are often
associated with eutrophic conditions.
Comparison of the composition of the rotifera over 12 transects (Fig. I)
indicated dominance by the Synchaetidae (Synchaeta and Polyarthra) over most
of sampling area. Keratella equalled the Synchaetidae at transect II
(directly off the Oswego River). Nauwerck's mean data for three sampling
areas in June 1970 indicated a smaller percentage of Synchaetidae (especially
Polyarthra), and a greater contribution by "others." The mean density of
total Rotifera (Fig. I) give one the impression of lower concentrations in
the Western region of our sampling area. However, transects 11-1^ were
sampled earlier in June and the density difference could simply reflect
overall lower production at that time.
2) Effect of location along shore (IAS) and distance from shore (DFS)
on species density.
To assess (LAS) effects it is necessary to minimize time effects. This
is especially important for the Cruise I data (collected between day 151 and
172 of 1972), this being the usual time of increased production. The data In
Table 1 represent.mean densities (for the 0-5 meter depth interval) averaged
over the three stations (IN, MID and OUT) at each transect. Dividing the
transects up into two groups (1-8 and 9-1*0 based on sampling times, and
testing the variation of each species over the transects within each group,
resulted in a significant LAS effect for only one species (Synchaeta
lakowltziana). This species is a cold water form, absent during the summer
and fall (July-November), The absence of significance for additional species
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is surprising, particularly when vieving the variability in densities among
transects (Table I).
One difficulty in testing for LAS effects is the lack of replication at
sampling stations. Thus, it was decided to combine transects and compare
regions using stations of equal distance from shore as subgroup replicates
within regions. The regions tested (Table 2) involved transects 1-3 (Genesee
River area) and transects 13-15 (Mexico Bay). Data for the latter area were
taken from Cruise II in an attempt to minimize the difference in sampling
time between regions (8 days). A significantly higher mean concentration of
Asplanchna priodonta, Kellicottia longispina, Keratella earlinae +_ irreg. +_
coch. robusta was found in the Mexico Bay region, while the reverse was true
of Keratella hiemalis and Synchaeta lakowitziana (both cold water species).
While not significant at the 5$ level, at least four othei species tested
had greater mean concentrations in the surface waters of Mexico Bay (Keratella
cochlearis^ cochlearis, K.. quadrata, Polyarthra dolichoptera and P_. vulgaris).
The two remaining, Brachionus angularis (a good indicator of eutrophy) and
Synchaeta stylata had higher levels around the Genesee River area. Ecological
interpretation of these differences must await analysis of the temperature and
food resource data.
To assess distance from shore (DFS) effects, densities at each of the
three locations (IN, MID and OUT) were averaged over 12 transects (transects
with missing stations were omitted). Of the 33 species tested^ only two
(Kellieottia longispina and Keratella cochlearis) displayed significantly
higher concentrations shoreward (Table 3). Many of the remaining species
displayed a similar gradient however at a lesser degree of consistency among
transects. Inconsistency suggests a possible interaction between LAS and DFS
effects on density. In the absence of replicates/station interaction cannot
-196-
-------
be tested.
3) Effect of time and DFS on density
One transect was selected from which all three stations had been sampled
on the same day {or within a 2k hour period) on each of five different dates.
Densities reported for each date (Table k) represent a mean over the three
stations. As is readily apparent and expected, most of the species displayed
significant seasonal variations over the sampling interval (June 9-September 25).
Of interest in the data is the absence of significant changes in Keratella
cochlearis, a eurythermal species. This species is often known to undergo a
marked decline in early to mid-summer and a resurgence in late summer. Five
sampling dates may simply have been insufficient to detect the characteristic
changes. Another possibility, which must be examined, is the presence of
factors unique to transect 9> which permit this species to maintain its
population. In the near future, data for the remaining transects will be
analyzed and compared with those in Table h.
The effect of DFS over time (for transect 9 only) was found to be non-
significant for all species. It is presumed that DFS effects are dependent
upon time of year.
Summary
Considering the surface samples of the southeast Lake Ontario inshore
region during June 1972, we observed some 35 species of planktonic rotifers,
representing 13 genera. Fourteen of the species are often found in association
with eutrophic conditions, Two genera (Synchaeta and Polyarthra) comprised the
built of the surface rotifer community.
Our data show a significant horizontal heterogeneity with respect to the
density distribution of select rotifers. In general, many rotifer species
-197-
-------
displayed a density gradient of increasing concentration shoreward, although
differences for only two species were statistically significant. A comparison
of standing crop for 11 species, between the Mexico Bay area and the region
near the Genesee River mouth, indicated seven species (three significant) with
greater abundance in Mexico Bay and four (two significant) more dense around
Rochester.
-198-
-------
References
1. Ahlstrom, E. H. 19^0. A revision o/T the rotatorian genera Brachionus
and Platyias with descriptions /of one new species and two new varieties.
Bull. Am. Mus. Nat. Hist., Ttfilk3-184.
2. 19^3. jk'revision of the rotatorian genus Keratella
with descriptions of /three new species and five new varieties. Bull.
Am. Mus. Nat. Hist.^ 80:Ull-U57.
3. Hillbricht-Ilkowskai, A. and T. Weglenska. 1970. Some relations between
production and zocbpiankton structure of two lakes of a varying trophy.
Pol Arch. Hydrotfiol., 17:223-2^0.
U. Koch-Althaus, /8. 1963. Systematische und okologische studien an
rotatorien d£s Stechlinsees. Limnologica, 1:375-^56".
5. Nafuwerck, #. 1972. Notes on the planktonic rotifers of Lake Ontario.
Unpublished.
6. Nelson, jfc. R. and W. T. Edmondson. 1955- Limnological effects of
fertilizing Bare Lake, Alaska. U.S. Fish and Wildlife Service Fishery
BulO/ No. 102 56:lH3-U36.
7. Nijfjkow, F. 1957. Die Tattung Polyarthra Ehrenberg im plankton des
Zy^richsees und einiger anderer Schweizer Seen. Schweiz. Z. Hydrol.,
1U:135-181.
8. Nursall, J. E. and D. N. Gallup. 1971. The responses of t.he biota of
Lake Wabamun, Alberta, to thermal effluent. Proc. Int. Symp. Ident. and
Mass. Env. Pollut., Ottawa, p. 295-30^.
9. Patalas, K. 1970. Primary and secondary production in a lake heated by
a thermal power plant. Proc. Inst. Env. Sci., l6th Ann. Tech. Meet.,
Boston, p. 267-271.
-199-
-------
10. Pejler, B. 1957. Taxonomica£ .and ecological studies on planktonic
rotatoria from Central Sweden. Kun&L. Svenska Vetenskapsakad.
Handligar., 6:1-52.
11. Pourriot, R. 1965. Notes taxinomiques siSr quelques Rotiferes
planctoniques. HydroMologia, 26:579-6oU.
12. Sudz.uki, M. "L9Sk. New systematical approach to the Japanese planktonic
rotatoria. Hydrotiologia, 23:l-12lt.
13. Voigt, M. 1957. Rotatoria: Die Radertiere Mitte&europas. Borntraeger.
Berlin.
-200-
-------
Table I. Cruise I, Mean Surface Density (Number/Liter) per Transect (June 1972).
Transects
Species
Asplanchna priodonta
^rachionus angularis
1B. calyciflorus
1B. quadridentatus
1B. urceolaris
Collotheca mutabilis
Conochilus unicornis
^uchlanis dilatata
^ 1Filinia longiseta
o
M
1 Kellicottia longispina
Keratella cochlearis
cochlearis
K. earl}- + irregj + coch.
robust a
1K. cochlearis fa. tecta
*K. crassa
K. hiemalis
^K. quadrata
K. quadrata v. canadensis
Notholca acuminata
1
2.1
1.5
0.1+
1.1*
0.1
0
1.1
0
0.1*
19.9
26.U
33.6
O.U
1.0
0.1*
22.7
3.0
0.1
2
0.6
0.3
0.1
0
0
0
0.1
0
0.1
7.1*
7.6
lit. 3
0.1
0.1
0.1*
5.6
0.8
0.1
3
1.7
1.8
0.2
0
0
0
1.1
0.2
0.3
23. k
30.6
3lt.O
0.1
0.9
1.1*
17.1*
2.1*
0.03
1*
1.2
0.2
0
0.2
0
0
0.7
0
0.2
11.1
ll*.6
18.5
0
o.i*
0.9
6.8
1.6
0
5
2.0
2.1*
0
0
0
0
1.8
0
0
32.0
28. U
31*. 9
0.1
1.0
0.9
10.8
2.5
0
6
2.6
1.9
0
0
0
0
1.5
0
0
53.1
21.5
77.0
0
0.8
0.2
10.1*
3.6
0
8
l.l
0.8
0
0
0
0
0.5
0
0
20. k
7.9
1*6.0
0
0.1
0.1
5.8
1.1
0
9
0
1.3
2.1
0
0
0
0.2
0.1
1.0
11.5
10.8
27.1
0.8
0.1
14.8
30.3
5.3
0.1*
11
1.9
2.8
3.6
0
0.7
0
2.6
0
0.5
1.7
51.9
26.2
0
1.2
2.3
314.1*
2.9
1.1*
12
1.2
0.9
1.9
0
0
0.1
0.8
0
0.3
2.7
11.2
It. 6
0.1
0
1.0
11.0
0
0.2
13
0.1
0.1*
0
0
0
0
0.5
0.1
0.1
3.6
6.3
8.5
0.1
0
0.6
11.6
3.1*
0.2
111
0.9
0.2
0.2
0
0
0
0.7
0
0.1
2.9
7.U
8.1
0
0.1
0.03
0.9
0.2
0
-------
Table X (continued) Transects . . _
Species 1 2 3 U 5 6 8 9 11 12 13 lU
N. squamula 0.2 0.3 0.8 0.5 0.!* 0.1 0 0.2 0.6 1.2 0.3 0.5
N. striata 0.1 0.1 0 0.1 0.03 0 0 0.1 0.1 0.2 0.3 0.1
Notholca foliacea 0.1 0 0 0.03 0.1 0.2 0 0.1 000 0
1Ploeosoma truncata 0 0 0 0 0 0.10.2000 0 0
^olyarthra euryptera 0 0 0.2 000 0.1 0.1 000 0
P. dissimulans + longiremis 6.0 O.U U.I 2.5 9.5 15.U 1.6 8.3 3.7 2.7 13.U 1.7
P. dolichoptera 96.1 U5.2 109.0 65.9 7U.2 12U.7 35.2 98.6 23.2 50.6 U9.3 20.3
P. major 11.0 2.9 11.7 2.8 5.9 6.5 0.2 2.0 0.1 3.0 U.U 0.1
P. remata 3.9 3.7 7-8 0.8 2.7 2.U 10.0 3.5 0.2 2.9 5.9 6.5
^ P. vulgaris 100.6 38.9 80.U 69.0 59.0 72.1 77.1 35.7 11.3 U.6 11.7 5.0
o
1 *Synchaeta lackowitziana 1.2 11.0 9.6 13.5 U.3 U.6 2.5 51.3 75.0 81.5 5U.9 Ul.6
S. pectinata O.U 0.1 1.0 0 0.1 0 0 1.1 U.8 U.8 1.2 0.8
S. stylato 119.6 138.0 106.0 69.2 25.3 56.7 129.6 U.5 2.0 l.U 5.0 U.U
^richocerca multicrinis 0 0 0.20 0.1 0 0 0 0 0 0 0
Sampling date 166 166 167 167,168 168,172 172 171 l6l 151 152 158,160 158
Species often associated with eutrophic conditions (Pejler, 1957; Nauwerck, 1972).
*0nly species to show significant difference in density among transects (1-8), P < .025
-------
Table II. A Comparison of Mean Surface Density (#/£) between Regions I
{Genesee River area) and II (Mexico Bay)2.
Regions-
Transects-
Sampling Dates-
Asplanchna priodonta
1Brachionus angularis
Kellicottia longispina
Keratella cochlearis
cochlearis
K. ^arl. + 1irreg. +
coch. robvista
K. hiemalis
*K. quadrat a
Polyarthra dolichoptera
P. vulgaris
Synchaeta lakovitziana
S. stylata
I
1, 2, 3
166-167
1.5
1.2
16.9
21.6
27. 3
0.7
15.3
83.5
73.3
6.5
121.2
II
13, lU, 15
17J*
6.2
0.7
55.8
UH.7
102.U
O.OU
2U.O
118.5
11*6.3
1.6
10*1.6
F-value
11.689**
1.037NS
9.^78**
2.875NS
18.762***
8.9^5*
2.017NS
1.270NS
2.1*29NS
5.857*
0.213NS
US - Not Significant
* - P < 0.05
** - P < 0.01
*** _ p < 0.001
Species associated with eutrophic conditions.
2Data for this region taken from. Cruise II.
-203-
-------
Table III. Mean Surface Density (#/£) over 12 Transects.
Cruise I
Species
Asplanchna priodonta
Brachionus angularis
Brachionus calyciflorus
Brachionus quadridentatus
Brachionus urceolaris
Collotheca mutabilis
Conochilus unicornis
Euchlanis dilatata
Filinia longiseta
Kellicottia longispina
Keratella cochlearis cochlearis
K. earlinae + irregularis +
cochlearis robusta
K. cochlearis fa. tecta
K. crassa
K. hiemalis
K. quadrata
K, quadrata canadensis
Notholca acuminata
N. squamula
N. striata
N. foliacea
Ploeosoma truncata
Polyarthra euryptera
IN
1.6
2.1
1.5
O.U
0.2
0.03
1.5
0.1
0.5
20. U
37.2
3U.6
O.U
0.7
0.5
21.6
3.U
0.5
0.3
0.06
O.OU
0
0.05
MID
1.8
1.2
0.5
0
0.03
0
1.2
0.02
0.2
20.5
13.2
33. U
0
0.6
1.7
12.9
2.5
0.1
0.5
0.2
0.06
0.02
O.OU
OUT
0.5
O.U
0.2
0
0
0
0.3
0
0.1
6.5
5.7
15.2
0.05
0.08
1.1
7.5
0.7
0.1
O.U
0.07
0.03
O.OU
0.01
Chi-Square
3.875NS
5.292NS
1.983NS
O.UU2NS
O.U8UNS
0.061s8
3.875NS
0.317NS
1.733NS
9.5**
9.5**
3.167NS
2.608NS
3.792NS
0.375NS
3.500NS
U.875NS
O.UU2NS
2.667NS
0.792NS
0.06TNS
O.U8UNS
0.109KS
-204-
-------
Table III (continued)
Species
IN
Cruise I
MID OUT
Chi-Square
P. dissimulans + longiremis
P. dolichoptera
P. major
P. remata
P. vulgaris
Synchaeta lackowitziana
S. sp. (?)
S. pectinata
S. stylata
Trichocerca multicrinis
6.3
61.2
U.I
5.0
61.5
26.7
7.0
1.9
50.0
0.2
7-1
91.7
6.1
5.0
1+9.1
30.3
0.3
1.1
78.2
0.1
lt.0
U'5.2
2.U
2.6
30.7
30.8
0.9
0.6
37.3
0
0.500NS
0.66'7NS
0.067NS
NS - Not Significant
** - P < .01
-205-
-------
Tatle IV. Mean Surface Density Averaged Over Three Stations for Transect 9
on Each of Five Sampling Dates.
Date
Species
Asplanchna priodonta
Conochilus unicomis
Kellicottia longispina
Keratella cochlearis
cochlearis
K. earl. + irreg. +
coch. robusta
K. crassa
K. hiemalis
K. quadrata
Ploeosoma truncata
Polyarthra dolichoptera
P. major
P. vulgar is
Synchaeta lakowitziana
S. stylata
Trichocerca multicrinis
6/9
0
0.2
n.5
10.8
27.1
0.1
1*.8
30.3
0
98.6
2.0
35.7
51.3
4.5
0
7/5
2U.1*
4.7
10.3
10.3
146.1*
0.7
0
1.5
o.i*
37.6
0.8
138.7
5.1
72.0
0
8/7
8.1*
336.1
8.1
11.8
56.5
3.2
0
14.3
3.1*
5.1
201.5
1*80.1*
0
4.7
0.1
8/31
5.8
78.1
0.2
6.3
54.9
21.8
0
0
86.7
3.5
51.8
101*3.1*
0
18.6
29. 4
9/25
4.2
0
0.5
15.9
53.2
64.3
0
0
20.6
1.6
36.2
189.7
0
21.7
2.7
F-value
6. in*
17.37**
7.60**
1.18NS
3.89*
48.53**
3.46NS
20.23**
28.49**
19.63**
2.39NS
32.36**
11.07**
9.08**
7.19**
NS - Not Significant
* - P < .05
** - P < .01
-206-
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Planktonic Crustacea of the Lake Ontario Inshore Region
*y
Donald C. McNaught and Daniel Giovannangelo
Introduction
In the inshore waters (<50 m) of Lake Ontario the cyclopoid copepod
Cyclops bicuspidatus thomasi (Forbes) and the cladoceran Bosmina longirostris
(Deevey) have been dominant since 19&9. Hovever, in 1939 Daphnia and
Diaptomus spp. were relatively more abundant (McNaught and Buzzard, 197*0.
These changes are likely due to the accelerated cultural eutrophication of
Lake Ontario.
The inshore waters are first to receive the nutrient load of tributary
streams. Here such nutrients are ultimately involved in stimulating algal
growth, as well as in determining the succession of dominant algal groups.
Both the net production of these algal communities, as well as their species
composition, influence the number and relative abundance of the species of
zooplankton. Thus the zooplankton reflect changes in lake ecosystems
usually considered only in terms of the algae.
Such changes in zooplankton composition have been recorded in the
literature for Lake Ontario. Seven investigations since 1912 have detailed
changes in tjtie crustacean zooplankton, but largely ignore the rotifers.
Recent basinwide studies by Patalas (1969, 1972) and Carpenter et al. (1972)
describe extensive collections made by investigators from CCIW in 1968 and
1970. Limited useful collections were made near Rochester by Whipple (1913)
in 1912 and Tressler et_ al. (19^0) in 1939. The discovery of a brackish-
water calanoid copepod was reported by Anderson and Clayton (1958). McNaught
and Fenlon (1972) took limited inshore samples in the Oswego area in 1969 and
-207-
-------
1970. Generally, then, the zooplankton of Lake Ontario are well-known
t economically, but little is known of their feeding habits, predators, a,*u.
especially the response of such populations to pollutants.
The purpose of this study is to identify inshore areas of Lake Ontario
which exhibit perturbation of the zooplankton community. We have employed
two distinct approaches in the analysis of our data. First, the densities
of organisms have been compared with respect to the distance from shore
(DFS) at which samples were collected. Secondly, after determining the
relative densities of all taxa, the sample means have been subjected to
community analysis.
Community Theory
Two basic assumptions underlie the use of niche theory (Levins, 196
to predict the maximum theoretical carrying-capacity of an aquatic environ-
ment. First we have assumed that crustaceans exhibit sigmoid growth in
nature, and that the concept of an environmental carrying capacity is real
for them. Secondly, we have assumed that with community development, a
likely evolutionary strategy includes the reduction of interspecific
competition, i.e. a reduction of the mean community competition coefficient
(a).
Assuming that crustacean populations continually push against an ever
changing carrying-capacity, we must first estimate the competition
coefficient (Levins, 1968):
(i)
n
h=l
n
h=l
p P
plh P2h
-208-
-------
where h is an environment and P^ and ?2 are the proportion of species 1 and
species 2. This alpha assumes that competition for resources is proportional
to the probability of occurrence in an environment h (Lane and McNaught,
1970, 1973). Then, from the logistic:
(2) dN, K, - H, - cu Np
dT'-i1" Kl >
where r, is the instantaneous growth rate of species 1, we can calculate the
maximum theoretical carrying capacity (K^) for species"1 1, where:
m
(3) % = H! + I 02.! N2
2=1
This maximum carrying-capacity is the maximum density which a species would
obtain if no competitors were present, where the calculation is made with
an assumption of steady-state ( - = 0)..
dt
Likewise it is possible to estimate tne -corax numoer 01 species -one
community will hold -from the covariance of alpha (Levins, 1968). In general,
when the variance of alpha (Tables 2-3) is small the community is predicted
to hold more species, as indicated by the ratio observed: theoretical number.
Finally, Shannon-Weaver species diversity values were determined for
inshore and offshore waters for the years 1969-1972, where:
H = -
where p^ = proportion of all species belonging to the ith species.
Methods
Samples were collected as in the concurrent study of the rotifers (Part l).
In the laboratory approximately 100 individuals of the dominant species were
-209-
-------
counted from each sample.
To determine significant differences in distribution with regard to
distance from shore, ve used an unpaired t-test.
Results and Discussion
(l) General trends
The inshore community vas dominated from May through July 1972 by
Cyclops bicuspidatus and, most likely, the copepodites of this cyclopoid
copepod, as veil as by Bosmina lorigirostris (Table V). Diaptomus (minutus
+ sicilis), Limnocalanus macrurus and calanoid copepodites were of
secondary importance. Chydorus sphaericus vas common inshore in May and
June of 1972. This chydorid is interesting because of its habit of hitch-
hiking on buoyant colonies of blue-green algae. Daphnia (galeata +
retrocurva), Tropocyclops prasinus and Eurytemora affinis were relatively
uncommon (less 60/m3).
(2) Effect of distance from shore (DPS) on species density
The effect of distance from shore (DFS) on species density for
crustacean zooplankton vas assessed for cruises I and II over the three
stations (IN, MID, OUT) using an unpaired t-test (Table VI). From Table V
it would appear that many species are more abundant near shore (in). However,
only Tropocyclops prasinus exhibited a significant difference (p < .05) vhen
IN densities vere compared to OUT for cruise I.
Generally we conclude that the planktonic crustaceans do not show
significantly higher concentrations shoreward within our narrow zone of study.
(3) Community analysis
The community competition coefficient (a), the theoretical carrying
-210-
-------
capacity (K) and the ratio of the observed density: theoretical carrying
capacity (N/K) provide insight into community interactions sensitive to
pollution.
Alpha is an index of potential interspecific competition (Table VII).
It is a valuable index in itself. In these preliminary data we see evidence
that interspecific competition is potentially greatest in MID shore areas.
But the chief reason for calculating alpha is to approximate the theoretical
carrying-capacity (K).
Theoretical community carrying-capacity (K) for planktonic crustaceans
should be responsive to available food resources. In the cases of cruises
I and_ II the theoretical carrying capacity is greatest in the IN shore
locations. These data signify that something is accounting for such high
densities (N) and carrying-capacities (K). We suggest initially that a
high K is indicative of community perturbation.
If the theoretical carrying-capacity is large, and it is actually
realized on a relative basis (N/K), this provides additional evidence of
perturbation. For example, in the case of cruise I, the OUT stations had
a predicted capacity of 7^,778 animals/m3 and 15$ of this capacity vas
realized (N/K), the maximum for the two cruises discussed. In the final
analysis of our data we will use a. combination of K and N/K "to indicate the
probable degree of perturbation of a given community. Presently we can
state that the N/K ratio for this Oswego sector (this study) ranges from
.08 to .15 and this range is similar to the lake-wide range of .07 to ,2k
(McNaught and Buzzard, 1971*).
Summary
The crustacean zooplankton of the inshore waters of Lake Ontario near
-211-
-------
Oswego are dominated in summertime by Cyclops bicuspidatus and Bosmina
longirostris. At present we find no evidence that these dominant forms
are at significantly higher concentrations as we proceed shoreward.
However, the theoretical carrying capacity of such populations is greatest
close to shore. The extent to which this carrying capacity is realized is
greatest farther off shore (OUT stations). In the future, should the•
theoretical carrying-capacity and the degree to which it is realized both
reach a maximum inshore or near sources of high nutrient input, we will
have evidence for community perturbation.
-212-
-------
References
Anderson, D.V., and D. Clayton. 1959. Plankton in Lake Ontario. Ontario
Dept. Lands and Forests, Phys. Res. Note No. 1:7.
Carpenter, G., L. Devey, J. Leslie and A. Nauverck. 1972. The crustacean
zooplankton of Lake Ontario:1970. (Manuscript).
Faber, D.'J., and E.G. Jermolajev. 1966. A nev copepod genus in the plankton
of the Great Lakes. LimnoU. Oceanogr. 11:301-303.
Lane, P.A., and B.C. McNaught. 1970. A mathematical analysis of the niches
of Lake Michigan zooplankton. Proc. 13th Conf. Great Lakes Res. 1970:
^7-57.
. 1973. A niche analysis of the Gull Lake (Mighican, U.S.A.)
zooplankton community. Verh. Internat. Verein. Limnol. 18: (in press).
Levins, R. 1968. Evolution in changing environments. Princeton: Princeton
Univ.. Press. 120 pp.
McNaught, B.C., and M. Fenlon. 1972. The effects of thermal effluents upon
secondary production. Verh. Internat. Verein. Limnol. 18:20^4-212.
, and M. Buzzard. 197^. Changes in zooplankton populations in
Lake Ontario (1939-72). Proc. l6th Conf. Great Lakes Res. (in press).
Patalas, K. 1969. Composition and horizontal distribution of crustacean
plankton in Lake Ontario. J. Fish. Res. Bd. Can. 26(8):2135-2l64.
. 1972. Crustacean plankton and eutrophication of St. Lawrence
Great Lakes. J. Fish. Res. Bd. Can, 29(10):lU51-lU62.
Tressler, W.L., and T.S. Austin. 19^0. A limnological study of some bays
and lakes of the Lake Ontario watershed. In 29th Ann. Rept. Nev York
State Conserv. Dept., pp. 188-210. Albany, N.Y.
Whipple, G.C, 1913. Effect of the sewage of Rochester, N.Y., on the Genesee
River and Lake Ontario under present conditions.- In Report on the sewage
disposal system of Rochester^jf.Y., ed. E.A. Fisher, pp. 177-239.
New York: Wiley. _2i3_
-------
Table V. Mean Density of Organisms with Respect to Distance from Shore (DPS)
for Cruise I (May 30, 1972-June 22, 1972) and Cruise II (June 22,
1972-July 6, 1972).
Species/location #/m3 (Cruise I) #/m3 (Cruise II)
Bosmina longirostris
IN
MID
OUT
Daphnia galeata
IN
MID
OUT
Daphnia retrocurva
IN
MID
OUT
Ceriodaphnia lacustris
IN
MID
OUT
Chydorus sphaericus
IN
MID
OUT .
Cyclopoid copepodite
IN
MID
OUT
Cyclops Mcuspidatus
IN
MID
OUT
Tropocyclops prasimus
IN
MID
OUT
Calanoid copepodite
IN
MID
OUT
Diaptomus minutus
IN
MID
OUT
Diaptomus sicilis
IN
MID
OUT
2,798
1,530
UU7
1*8
2
1
21
2
1
1
k
1
913
95
18
15,225
15,987
3,912
9,^62
925
1*61
1
37
35
126
ll»8
99
61
31
9
0
0
1
6,982
5,611
3,125
2U
33
1
13
3
6
151
72
10
lUU
9U
121
U,6i6
3,Uo6
5,675
3,162
880
2,01*9
57
86
92
ikB
108
133
82
50
53
22
6
U
-214-
-------
Table V (continued)
Species/location #/m3 (Cruise I) ff/m3 (Cruise II)
Limnocalanus macrurus
IN
MID
OUT
Eurytemora af finis
IN
MED
OUT
Nauplii
IN
MID
OUT
28
398
252
0
0
1
8,798
10,598
7,529
2
52
2U
9
0
0
3,070
2,1+66
6,137
-215-
-------
Table VI, A Comparison of Mean Density (#/m3) as an Effect of DSF for Locations IN, MID, and OUT,
1-0
M
cr>
Organism
Bosmina longirostris
Daphnia galeata
Daphnia retrocurva
Ceriodaphnia lacustris
Chydorus sphaericus
Cyclopoid copepodite
Cyclops Mcuspidatus
Tropo cyclops prasimus
Calanoid copepodite
Diaptomus minutus
Diaptomus sicilis
Limnocalanus macrurus
Eurytemor$ affinis
Nauplii
^05
Cruise I
IN vs MID.
.7582
1.0170
1.1182
.8005
1.0123
.0552
1.0211
2.1632
.1899
.8373
.9^97
.301*0
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
^05
Cruise I
MID vs OUT
2.0108
.733*+
.1+1*89
1.0062
1.5^3
1.1107
1.1593
.1123
1.3657
1.2657
.3355
1.0000
.6817
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
U05
Cruise I
IN vs OUT
1.3807
.9981
1.0151
.1|636
1.1156
1.238
1.W+
2.1*528
.5061*
1.5770
1.1209
1.0l»27
.2556
NS
NS
NS
NS
NS
NS
NS
*pc .05
NS
NS
NS
NS
NS
"05
Cruise II
IN vs MID
.38U9
.3**07
.7776
.5391
.9015
.7771*
l^SO
.6562
.8609
.651*1*
.7751
1.7658
.3131
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
"05
Cruise II
MID vs OUT
1.7^08
1.3798
.U293
1.0U77
.2221
1.0683
1.2378
.501*1*
,0.068
.0893
.3219
.9503
1.2965
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
^05
Cruise II
IN vs OUT
1.1+1*52
1.8586
.5011
1.0987
.31*20
.31*10
.1+851
1.0131+
.3356
.1*880
.821+3
1.9387
.9277
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
NS
-------
Table VII. Community Analysis for Crustacean Zooplankton.
Total Number (#/m3) Observed Species/ Theoretical (K)
of Zooplankton (N) Alpha (Variance) Theoretical Species Carrying Capacity '(ff/m3) N/K Diversity
Cruise I
IN 31+.606.05
MED 29, 107. 5!+
OUT 11,399.86
Cruise II
IN 20.U39.6
MID 12,991+
i OUT 20,31*1+
.318 (.161)
.31+5 (.130)
.265 (.076)
.333 (.076)
.1+16 (.118)
.360 (.11+7)
1U/5
lU/6
lU/7
1V7
13/6
lU/6
1+08,397
222,221
71+, 778
222,959.1
110,769
171,916
.085
.13
.15
.09
.12
.12
1.79
1.73
2.16
2.1+8
2.23
2.50
-------
ANNUAL REPORT
ANALYSIS AND MODEL OP
IMPACT OF DISCHARGES FROM
NIAGARA AND GENESEE RIVERS
OF THE NEAR-SHORE ZONE
Sponsored by
EPA GRANT #800701
to
Great Lakes Laboratory
State University College at Buffalo
1300 Elmwood Avenue
Buffalo, New York 1*4222
August, 1973
-------
TABLE OF CONTENTS
Page
I. Introduction 221
II. Biological Studies 229
A. Phytoplankton 229
1. Objectives 229
2. Plans vs. Accomplishments 230
3. Status 231
4. Summary of Results 232
B. Zooplankton 236
1. Objectives 236
2. Plans vs. Accomplishments 236
3. Status 237
4. Summary of Results 237
C. Benthos 239
1. Objectives 239
2. Plans vs. Accomplishments 239
3. Status 240
4. Summary of Results 240
D. Cladophora 241
1. Objectives 241
2. Plans vs. Accomplishments 241
3. Status 244
4. Summary of Results 244
-218=
-------
TABLE OF CONTENTS
Continued
Page
E. Chlorophyll-a 246
1. Objectives 246
2. Plans vs. Accomplishments 246
3. Status 246
4. Summary of Results 246
III. Chemical Studies 247
A. Sediments 247
1. Objectives 247
2. Plans vs. Accomplishments 249
3. Status 250
4. Summary of Results 250
B. Water 321
1. Objectives 321
2. Plans vs. Accomplishments 321
3. Status 322
4. Summary of Results 322
IV. Physical Studies 324
A. Ship-Board 324
1. Objectives 324
2. Plans vs. Accomplishments 324
3. Status 325
4. Summary of Results 325
-219-
-------
TABLE OF CONTENTS
Continued
Page
B. Other Physical Measurements in Study Area 328
1. Objectives 328
2. Plans vs. Accomplishments 328
3. Status 328
4. Summary of Results 328
V. Budget vs. Accomplishments 329
-220-
-------
INTRODUCTION
The objectives of the U.S. Environmental. Protection
Agency (EPA) sponsored multi-year project, which is part
of the International Field Year on the Great Lakes (IFYGL),
are as follows:
a. To formulate a model that could.be employed in the
prediction of ecological responses to inputs in the
near-shore region of large lakes.
b. To ascertain the nature, extent and interactions on
inputs, including pollutants, on the aquatic
biological and chemical processes in the near-shore
region of Lake Ontario.
c. To evaluate the rate of flow of nutrients into, out
of, and within the study area, including movements
between aquatic and benthic habitats.
d. To examine the role, if any, of a thermal bar on
nutrient transport and recycling, as well as a biological
barrier.
e. To develop an ecological baseline that could be of
.value in the evaluation of the impact of proposed
developments (i.e., sewage treatment plants, electric
power generating stations, etc.) along the Lake
Ontario shoreline and tributaries, as well as in the
determination of the present status and rate of
eutrophicatlon of Lake Ontario.
f. To measure the extent of Cladophora growth and factors
which influence the morphology of this area. Emphasis
will be directed toward the formulation of means
through which the problems caused by this plant can be
reduced.
This report details the plans and accomplishments by
the staff of the Great Lakes Laboratory (GLL) on the above
-221-
-------
project during the period from 1 April 1972 through
31 March 1973. The majority of the GLL's efforts in
1972-73 were concerned with the collection of biological and
chemical samples as well as making physical measurements
in the study zone. The latter consisted of an area eight (8)
kilometers wide (as measured from the shore into .the lake)
and extending in length from the Weiland Canal through
Rochester. Forty-five (^5) near-shore stations were
established. These were situated one-half (1/2), four (4)
and eight (8) kilometers from shore along lines ten (10)
kilometers apart. In addition twenty-four (24) and twelve (12)
stations were located in the mouths and plumes of the Niagara
and Genesee Rivers respectively. The number and location of
each of the stations is shown in Table I. Collection sites for
Cladophora were established at five (5) locations along lines
extending into the lake and perpendicular to the shore. The
location of the intersection of these lines and the shore
is given in Table II. Sampling of the attached alga was
conducted along the line in water depths of 1, 2, 3, 4, 5
and 6 meters.
-222-
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Near-Shore
Station #
201
202
203
204
205
206
207
208
209
210
211
212
213
214
215
216
217
218
219
TABLE I
Near-Shore and River Mouth
COLLECTION STATIONS
Zone
Longitude
79013148"
79°13'48"
79°13'1»8"
79°06f54"
79°07'36"
79°07tl8"
79°01'l8"
79°01'48"
79°02'30"
78°54'12"
78°55'00"
78°55'48"
78°47T 6"
78047'48"
78°48'36"
78°39'48"
78°40'36"
78°4l'30"
78°32'36"
Latitude
'43°19'i»8it
43°21'36"
-223-
-------
Table I, continued
Near-Shore Zone
Station #
220
221
222
223
224
225
226
22?
228
229
230
231
232
233
234
235
236
237
238
239
240
211
242
243
244
245
Longitude
78"33IOU"
78°33'30"
78°25'12"
78°25'24"
78°25'36"
78017'36"
78°17'36"
78°17'36"
78°10'l8"
78°10'30"
78°10'48"
78°02f 48"
78°02'36"
78°02'24"
77°55f30"
770511154''
77°54fl8"
77048'12"
77°il7'48"
77°47'12"
77°4l'l8"
77°39'54"
77°38'06"
77°35'30"
77033'54"
77°32tl8"
Latitude
I43"24'li!"
43°26t24"
43°22'48"
43°24'36"
43°26'48"
43°22'36"
43°24t30"
43°26'36"
43°22'36"
43°24'30"
43°26'3611
43°22'30"
43°24'24M
43026'30"
43°21'48"
43°23'36"
43°25f42"
43°20'48"
43°22'36"
43°24'48"
43°l8'30"
43°19'54"
43°r21'36"
43015'18"
43°l6'48"
43°l8'42"
-224-
-------
Table I, continued
Genesee River Mouth
Station # Longitude
351 43°15t58."
352 43°15'53"
353 43°l6'10"
354 43°16'01"
355 43°15'55"
356 43°16'33"
357 43°l6'30"
358 43°l6 '20"
359 43°16'08"
360 43°15'54"
361 43tf15f37"
362 43°l6l28"
Niagara River Mouth
Station # Longitude
363 79°05t24"
364 79°05to6"
365 79°05'08"
366 79°04t45"
367 79°04*50"
368 79°04'50"
369 79°04«26"
370 79°04'24"
Latitude
77°35'54"
77°35f48"
77°36'02"
77°35'42"
77°35'19"
77°36'29"
77°36'07"
77°35'4l"
77°35'21n
77°34'58»
77°34'36"
77° 35 T 30"
Latitude
43°l6fOO"
43°15'55"
43°l6f10"
43°15'50"
43°16'06"
43°16'20»
43°15'40"
43°l6'00"
-225-
-------
Table I, continued
Niagara River Mouth
Station #
371
372
373
371*
375
376
377
378
379
380
381
382
383
38U
385
386
Longitude
79°04'35"
79°04'10"
79°04'15"
79°04'10"
79°04'10"
79°04'08"
79°04'05"
79004'05"
79°03'56If
79°03f50"
79003,^5,,
79°03'40»
79003'25"
79°03!23"
79°03'10"
79°02'50"
Latitude
i»3°l6'35"
-226-
-------
TABLE II
CLADOPHORA COLLECTION STATIONS
Station #
20?
216
222
228
237
Longitude
79°01'18"
79°39'48"
79°25'12"
79010'18"
77°48'12"
Latitude
43°l6'l8"
43°20'48"
43°22'l8"
43°22'06"
43°20fl8"
Between 1 April 1972 and 31 March 1973 a total of
ten (10) near-shore, eight (8) Genesee river and six (6)
Niagara mouth and six (6) Cladophora sampling runs were
conducted. The dates of the above are shown in Table III.
TABLE III
COLLECTION DATES
Niagara River
Near-Shore^
Run # Julian Dates Gregorian Dates
1 109-124 18 Apr.-3 May
2 131-1^4 10 - 23 May
3 171-180 19 - 38 June
4 194-203 12 - 21 July
5 207-215 25 July - 2 Aug.
g 31+0-3117 5-12 December
-227-
-------
TABLE III, continued
Genesee River
Ru_n_ #
1
2
3
4
5
6
7
8
Julian Dates
151-153
156-157
157-158
158-159
164-165
235-237
241-242
332-333
Gregorian Dates
30 May - 1 June
4-5 June
5-6 June
6-7 June
12-13 June
22-24 August
28-29 August
27-28 November
Cladophora
Run #
1
2
3
4
5
Julian Dates
172-180
193-202
209-214
221-230
292-301
Gregorian Dates
20-28 June
11-20 July
27 July - 1 Aug
8-17 August
18-27 October
It should be noted that a total of eleven (11)
near-shore, twelve (12) river mouth and five (5) Cladophora
sampling runs had been planned. However, due to a combination
of problems including delayed funding of the project, inclement
-228-
-------
weather and minor mechanical difficulties with the major
research vessel, the sampling program had to be reduced.
All sampling runs undertaken were completed with the exception
of the 11-14 December collection that had to be curtailed
after twenty-two (22) stations due to severe icing and
wave conditions.
Since the overall project consisted of biological,
chemical and physical components, each of the latter will be
discussed separately.
II. BIOLOGICAL STUDIES
A. Phytoplankton
1. Objectives
This phase of the field survey was designed
to ascertain the nature and extent of primary
productivity in the near-shore zone as well as
impacts of temperature stratification, as a result
of the presence of thermoclines and thermal bars,
and tributaries, particularly the Niagara and
Genesee Rivers, on these processes. The relationship
between the quantity and quality of the algae and the
physical and chemical conditions in the collection
areas also was to be measured.
-229-
-------
2. Plans vs. Accomplishments
Phytoplankton was collected at each near-shore
and river mouth station at 1, 5, 20, 25, 35 and 50 m
meters below the surface (depth permitting) using
a 4.1 liter vertical Van Dorn (Alpha) Water Sampler.
One (1) liter of each sample was preserved with
Lugoi's solution. Fifty (50) milillters subsamples
of each are being examined for algae using the
inverted microscope method of Utermfihl. Species
composition as well as cell numbers and blovolume
are being calculated. This enumeration procedure
as well as the taxonomy being employed is being done
in cooperation with Dr. M. Munawar of the Canada
Centre for Inland Waters, who is conducting a similar
study of the phytoplankton collected in other sections
of Lake Ontario.
The initial plan was to count all the samples.
However, since the phytoplankton cannot be counted
in less than two (2) hours per sample, it was
necessary to limit the initial analyses to the
algae collected at depths of 1 and 5 meters at
near-shore stations 201, 202, 203, 207, 208, 209,
213, 214, 215,222, 223, 224, 231, 232, 233, 237,
-230-
-------
238, 239,.2JL3, 2^4, 2^5. In addition the
phytoplankton gathered at 20 s 25, 35 and 50 m also
is being counted at the stations whose numbers are
underlined in the above list. This reduction will
provide sufficient information for the near-shore model,
A preliminary examination also is being made
to ascertain if the number of river mouth stations
can be limited without having a negative impact on
the validity of the model.
Quantity and quality of phytoplankton vs. water
chemistry cannot be undertaken until the latter is
put in the STORET system by EPA.
3. Status
All 2600 samples were collected and preserved.
Analyses of the representative stations from the
April through July 1972 cruises have been completed.
Approximately five (5) weeks effort by two (2)
full-time individuals is necessary to complete the
examination of a cruise. Therefore the analyses
of the algae gathered during the ten (10) cruises
in 1972 will be completed in early December 1973.
The river mouth collections will be done by the
early spring 197^.
-231-
-------
4. Summary of Results
During Cruise I the diatoms comprised
approximately 5&% of algae at each station. The
dlnophyceans and cryptophyceans made up 22 and
respectively of the biomass, while Shlorophyta
comprise 2% and Cyanophyta less than 1%. By July
the diatoms decreased in number. They were replaced
by cryptomonads and colorless bi-flagellates. The
taxonomic composition of the summer flora will be
discussed in a later section of this report.
The dominant species in Cruises I and II are
shown in Table IV.
TABLE IV
DOMINANT PHYTOPLANTONIC SPECIES
Cruises I and II
Asterionella formosa Hasal.
Cryptomonas erosa Ehrenbg.
Gymnodinium helvitica Pennard.
Melosira binderana• Kg.
Melosira islandica ssp helvitica 0. Mtiller
Perldlnium aciculiferum Lemm.
Rhodomonas minuta Skuja
Scenedesmus bijuga- (Turpin) Langerheim
Stephanodis cus hantzschii Grun.
Stephanodiscus tenuis Hust.
Surirella angustata Kuetz
-232-
-------
The largest concentrations of algae by
biovolume observed In the 1 and 5 meter collections
from Cruise I and II collections were found inshore
of the thermal bar. This is shown in Table V.
TABLE V
AVERAGE PHYTOPLANKTON IN SURFACE WATERS
( #;a3 x 103/ml)
Cruise Dates Distance from Shore
I 15 Apr.-3 May
II 10-23 May
III 12-21 July
During Cruise I the thermal bar generally
was found from 1/2 to 3-1/2 km from shore; during
Cruise II the bar was observed primarily between
4 to 7 km from shore. By Cruise III the bar was
lakeward of the 8 km station. It should be noted
that while there appears to be a large number of
algae at the 4 km stations in Cruise III (Table V),
there was variation in the range of algal numbers
from transect to transect, which was not observed
in the Cruise I and II collections.
1/2 km
15^1
2866
569
4 km
9^6
2167
936
8 km
617
593
650
-233-
-------
The data from the vertical profiles from
Cruises I and II Indicated that higher concentrations
of algae were found in the waters having a temperature
higher than ^°C on the shoreward side of the thermal
bar.
Phytoplankton counts from the spring cruises
were fairly uniform throughout a given depth profile.
By Cruise IV a thermocline had become established.
The larger algal concentrations were found above the
thermocline, specifically in the collections from
depths of 5 meters. The distribution pattern of
algae with depth as measured on the Cruise IV samples
is shown in Table VI.
TABLE VI
ALGAL BIOMASS VS. DEPTH
FOR CRUISE IV
Depth Biomass
1 m 898 /i3xl03/ml
5 1115
20 558
35 653
50 618
-234-
-------
Unlike Cruises I, II and III, the species
composition varied with depth in Cruise IV. In
the latter diatoms were almost absent in the collections
from 1, 5 and 20 m below the surface, but at 35 and 50 m,
Meloslra islandica and M._ binderina were a substantial
fraction of the biomass.
The dominant species collected during Cruise IV
were Cryptomonas erosa, Rhodomonas minuta and a
variety of as yet unidentified colorless biflagellates.
These organisms were found in the epilimnion.
In the spring the Niagara River with 412 ju3xl03/ml
had considerably less phytoplankton than the receiving
o o
waters which averaged 1035 ju xlO /ml. Sampling along
the plume as it mixed with the lake, the algal
numbers and variety increase with distance from the
river mouth. By Cruise IV (12-21 July) the quantity
and quality of phytoplankton in the plume was very
similar to the collections from the 1/2 km stations.
The April collections from the Genesee River
q o o
mouth, which averaged 1206 ju^xlQ-vm , did. not
differ appreciably from the near-shore stations. Algal
biomass decreased with increased distance from the
mouth of the river. The shallowest stations yielded
the highest algal concentrations.
-235-
-------
B. Zooplankton
1. Objectives
The purposes of this aspect of the overall
study were to contribute to the understanding of
productivity and water quality in the Welland-
Rochester near-shore zone. This was to be
accomplished through the identification and
enumeration of planktonlc crustaceans utilizing
the techniques developed by Dr. Andrew Robertson.
2. Plans vs. Accomplishments
While a total of 825 zooplankton collections
were taken by means of a vertical haul of a 1/2
meter plankton net, at each near-shore and river-
mouth station on every cruise, the Project Director
and Mrs. Sharon Czaika, the individual doing the
analysis, believe that it is not possible to examine
every collection due to the time necessary to
accomplish this task. On the near-shore stations,
the zooplankton from every other transect is being
analyzed beginning with stations 201, 202 and 203.
This means that collections from a total of twenty-one
(21) stations per cruise will be quantitatively and
qualitatively analyzed. (It should be emphasized
that this type of examination is more than sufficient
-236-
-------
to provide the inputs necessary for the development
of the model. If time permits and/or if results
from the chemical analyses dictate, an examination
of the collections from the "in-between" stations
will be made.
The only change in techniques has been the use
of a Hansen-Stempel Pipette instead of a Folsom
Plankton Splitter.
3. Status
The zooplankton analysis was late in starting
due to the lack of agreement on taxonomy and
quantification procedures. However, this matter has
been remedied largely through conferences between
researchers at the Canada Centre for Inland Waters
and the Great Lakes Laboratory.
The zooplankton from Cruise I of the Genesee
River mouth is finished. Near-shore Cruises I and II
also are nearly complete with the exception that
bosminids will be saved and identified at the end
of the study when a sufficient variety of instars
will be available.
4. Summary of Results
A summary of these initial results from the
Genesee River Cruise I are as shown in Table
There was little difference between the stations
with respect to the quality and quantity
-237-
-------
TABLE VII
ZOOPLANKTON - CRUISE I - Genesee
Genesee River
Taxonomic Group - Comments % of Individuals
COPEPODS: 1.^
Calanoids:
Diaptomus siclloldes - dominant species
Diaptomus oregone'nsis
Diaptomus reighardi
2 anomalous groups
Cyclopoids: 15.0
immatures - most abundant
Cyclops bicuspidatus thomasi - dominant species
Tropocyclops prasinus mexicanus
Cyclops vernalis
Eucyclops prinophorus
Herpacticoids: Canthocamptus robertcokeri 1.2
Nauplii 76.5
CLADOCERANS: 6'°
bosminids - dominant species
Chydorus sphaericus
Daphnia (2 species) - rare and in only 1/2 samples
galeata mendotae
retrocurva
Alona costata - rare and in only 1 sample
Alona guttata - rare and in only 1 sample
100.0%
-238-
-------
of organisms. The only quantitative difference
was the fact that twice as many individuals
were found at station #35^, which is approximately
700 meters northeast of the river entrance and
in the middle of the Genesee River plume.
A list of species was submitted to EPA
in Gaithersburg, Maryland, for their use in setting
up the STORET system to accept these data.
C. Benthos
1. Objectives
The objectives of the quantitative and
qualitative analyses of benthlc macroinvertebrates
essentially was the same as those for phytoplankton
and zooplankton.
2. Plans vs. Accomplishments
Benthos was collected durinz; 1972 on Near-shore
Cruises I (18 April - 3 May), III (19 - 28 June),
VI (5 - 13 September) and IX (6 - 22 November).
Genesee River mouth samplings occurred on Cruises I
(30 May - 1 June), V (12-13 June), VI (22 - 2^ August)
and VIII (27-28 November);'benthos from Niagara River
mouth sites were collected during Cruises I (29 May -
5 June), III (12 - 16 June), IV (21 - 26 August) and
-239-
-------
VI (5-12 December). While attempts were made
to obtain a sample at each collection site the
rocky nature of the bottom precluded collections
being made at near-shore stations 201, 204, 207,
210, 213, 216, 219, 222, 225 and 237- While each
of the Genesee River mouth sites were collected,
no benthos could be gathered at stations 366, 369,
371, 375, 378, 379, 380, 382 and 383 in the Niagara
River mouth. A total of 310 stations were sampled.
One (1) Ponar grab was taken at each on the
collections through August, 1973. After August
three (3) separate Ponar hauls were made at each site.
The use of an Ekman Dredge was terminated after
the initial cruise due to the fact that collections
with this device could be gathered at less than at
a third of sites where Ponar collections could be made.
3. Status
The 1972 samples will be completed by December,
1973- The necessity of splitting the samples due
to the large volume of organisms has delayed the
project by approximately three (3) weeks.
*J. Summary of Results
The majority of organisms found at the 1/2
and 4 km stations in the near-shore zone are
tubificids, sphaerids and chironomids which are found
-240-
-------
In nearly equal abundance but average less than
a fifth of the number of sludge worms. A few
gastropods and some crustaceans also were observed.
There was relatively little difference between
the collections at the 1/2 and A km stations.
The most abundant organisms at the 8 km
stations were Mysis and Pontoporela. Oligochaetes
and sphaerids also were present.
The benthic environment of the river mouths
were dominated by oligochaetes. There was substantial
differences between both stations in a single cruise
and between the same stations sampled during
different cruises.
D. Cladophora
1. Objectives
Purpose of this aspect was to ascertain the
mass, in terms of wet, dry and ash weights, of
Cladophora collected at different depths (1, 2, 3,
4, 5 and 6 meters) along five (5) transects
extending from the shore into the lake. Another
objective was to provide ground truth for the
quantification of this attached alga by remote sensing.
2. Plans vs. Accomplishments
Six (6) samplings of up to six (6) collection
sites along five (5) transects had been planned.
-241-
-------
These transects were adjacent to stations
207, 216, 22, 228 and 237. However, high winds
and waves, which made collecting the Cladophora
by SCUBA techniques impossible, resulted in the
cancellation of some of the Cladophora runs. The
dates when collections were made per station is
shown in Table VIII.
TABLE VIII
CLADOPHORA COLLECTIONS
Transect Julian Date Remarks
207 172 No Cladophora at 1 and 2 m
» 179 t, ,« it I m
n 193 .. •• " 1 m
11 209 " " " 1, 2 and 3 m
" 221 " " 21, 2 and 3 m
292 " " "1 and 2 m
216 173-175 High wind + waves - no
collection
„ 177-178 " " " " "
" 195 No Cladophora at 1 m
11 223 " " " 1,2",4,5 and 6m
" 297 " " " 1,2,5 & 6 m
222 178
" 196
-242-
-------
Table VIII continued
Transect Julian Date Remarks
" 209
" 223 No Gladophora at 1,2 &
3 m
" 230 " " at 1 & 2 m
301 " "1m
228 179-180 High winds + waves,
no collection
" 201
" 213 No Cladophora at 1 in
" 225-277 High winds + waves,
no collection
it 302-305 " " " " "
237 173-175 High winds + waves,
no collection
" 180 No Cladophora at 1 & 2m
" 202 " " at 1,2 and 4 m
" 214 " " 1,2 and 3 m
230 " " 1 ra
" 303 High winds + waves, no
collection
Sand comprised the sediment of depths
at which Cladophora consistently did not grow.
During the latter collection dates wave action had
swept away.
-243-
-------
3. Status
The Cladophbra collections and analyses
(dry, ash and wet weights) have been completed.
Directions for entering these data in STORET are
being awaited.
4. Summary of Results
Cladophora growth was not found on sand
or other unconsolidated strata. Also development
was limited in depths of 1 to 2 meters due to wave
action which broke the filaments and/or held fasts.
The changes in the percent dry, fixed and
volatile weights of the Cladophora collected on
different dates in randomly selected square foot
sections of the -bottom is shown in Table IX. The
dry weight was observed to generally increase in
the spring, reached a maximum in late July-early
August and decrease again in the fall. The fixed
and dry weight, on the other hand, showed no consistent
pattern.
Cladophora growth will be correlated with the
nutrient levels when the latter data becomes available.
-244-
-------
TABLE IX
CLADOPHORA WEIGHTS
Station
207
tt
u
11
ft
II
216
M
ii
it
222
it
ii
it
ii
ii
228
11
237
it
ii
Date
172
179
193
209
221
292
195
209
223
297
178
196
209
223
230
301
201
213
180
202
214
Dry Weight
13.79?
13.17
18.76
18.92
35. 94
15.72
22.95
19.16
34.80
19-50
29.30
13.44
20.65
29.52
22.98
24.77
21.54
24.90
18.67
22.12
22.67
Fixed Weight
42.85*
52.40
47.72
42.91
73.. 91
82.96
57.55
49.68
26.80
61.30
65.02
35.11
45.71
64.89
36.83
68.77
43.16
46.31
41.02
47.24
28. lb
Volatile Weight
57.1535
47.60
52.28
57-09
26.09
17.04
42.45
50.32
73.20
38.70
34.98
64.89
58.29
35.11
63.17
31.21
56.84
53.69
58.98
52.76
71.85
230 14.09 22.65 77.35
-245-
-------
E. Chlorophyll-a
1. Objectives
The chlorophyll-a data were gathered in order
to augment the phytoplankton data regarding primary
productivity in the near-shore and river mouth study
areas.
2. Plans vs. Accomplishments
As proposed samples for chlorophyll-a analyses
were collected at each time and depth that a
phytoplankton sampling was made.
3. Status
The samples have been collected.
At the request of EPA, the raw data from the
spectrophotometric analysis of chlorophyll-a were
forwarded to Grosee lie for entry into STORET. Once
the latter was complete the final values for chlorophyll-a
were to be calculated by the STORET computer. To dat
these data were not retrievable.
4. Summary of Results
Awaiting print-out of raw data from STORET.
-246-
-------
III. CHEMICAL STUDIES
A. Sediments
1. Objectives
The purposes of this phase of the study were
to ascertain the chemical quality of the sediment
in the Welland-Rochester near-shore zone and in the
mouths of the Genesee and Niagara Rivers and to
measure changes that occur in those benthic environments
during the duration of the Field phase of IAGLR.
These data were to be contrasted with the quantity
and quality of benthos as well as the chemical
conditions of the water above the bottom.
A total of thirty-three (33) parameters were
to be measured on each sample including: nitrate,
ammonia, organic and total nitrogen; suspended
and dissolved phosphorus; total, fixed and volatile
solidsj total organic carbon (TOC) and total
inorganic carbon (TIC); pesticides (DDT, DDE, ODD,
lindane, aldrin, dieldrln, toxaphene, chlordane,
endrin, heptochlor and heptochlor expoxide); heavy
metals (iron, manganese, copper, zinc, lead, mercury,
magnesium, chromium, nickle and cadmium);
polychlorobiphenyls (PCB's)
-247-
-------
2. Plans vs. Accomplishments
Sediment samples were collected with a Ponar
Dredge during near-shore Cruises I (18 April - 3 May),
III (19-28 June), VI (5-13 September ) and IX (6-
22 November). Niagara River mouth samples were taken
during Cruise I (29 May - 5 June), IV (21-26 August)
and VI (5-12 December). The Genesee River mouth
sediment was gathered during Cruise I (30 May - 1 June),
V (12-13 June), VI (22-2*1 August), and VIII (27-28
November ). An attempt was made to obtain a sediment
sample at every station. However, the nature of the
bottom (rock or hard-pan) prevented material from
being taken from Near-shore stations 204, 207, 210,
213, 216, 219, 222, 225 and 237, as well as Niagara
River stations .366, 369, 371, 375, 378, 379, 380,
381, 382 and 383.
With regards to chemical analysis, a measurement
of dry weights were added to the test for solids.
Samples for pesticide and PCB analyses were sent to
the Lake Ontario Environmental Laboratory (LOTEL)
of the State University College at Oswego. In
exchange the GLL made quantitative and quantitative
tests for the ten (10) heavy metals listed above on
sediment samples collected by LOTEL.
-248-
-------
3. Status
All sediment samples gathered during 1972
In the Welland-Rochester Near-shore zone as well
as in the mouths of the Genesee and Niagara Rivers
have been analyzed with the exception of pesticides
and PCB's, which are being done by LOTEL. These
data have been sent to EPA for input to the STORET
system. The GLL plans to utilize the capacity of the
latter computer system to plot and analyse these
data.
^. Summary of Results
The analysis of sediment data from the Welland-
Rochester Near-shore zone showed a definite influence
from the Niagara River on the benthic chemistry
(Figure 1-30).
The nature of the sediment downstream from the
Niagara and Genesee Rivers was quite sandy especially
at stations 208, 211, 2^3 and 245- The percent
volatile solids were highest at the 4 and 8 km
stations near the Niagara River plume (stations
205, 206, 208 and 209) and decrease steadily moving
east towards Rochester. Generally the percent dry
weights decreased and the percent volatile solids
-249-
-------
Figure 1
MEAN VALUES
PERCENT DRY WEIGHTS
and
PERCENT VOLATILE SOLIDS
NEAR-SHORE SEDIMENTS
-250-
-------
203
206 209 212
1972 IFYGL
3 Dry
% Volatile Sol
218 221 22'f
DEEP LAKE STATIONS
2l»5
20-,
202
203
211
211*
217 220 223 226
MID LAKE STATIONS
229
232
235
230
LdO
2k it
2'0
-o
1(1
_J
rj;
CJ
9
2
LU
;*
4
e:
LU
ex
c;
C3
•V
A
\/M
LU
LU
0 —
LU
_J
—
CO
rH ^
.^~M_^— •
»w/ ^x^ £
l/'\l^^ >
- c;
LU
LU
LU
LU
Lf., « o
^^ -^ «•
•no
.70 £
60
-------
Figure 2
MEAN VALUES
NITRATE NITROGEN (rag/g)
and
ORGANIC NITROGEN (mg/g)
NEAR-SHORE SEDIMENTS
-252-
-------
.20"
.00
203
1072 IFYGL
Hi trate
Organic-!! nr:/.'C(av.';.)
206
209 .212
215
»'"' ' f
218 221 221} 227
DEEP LAKE STATIONS
236 23D
2.0
1.4
ro
tn
\-f°
2'(2 2!f5
n.O
.20,
217 220 223 22C
HID LAKE STATIONS
•2.0
i
(£
to
t;
u
o
0.0
i.10
4->
rc
<
K.
LJ
c:
t:
C3
207 210
Yl3
216 219 222
HEAR SHORE STATIOflS
-------
Figure 3
MEAN VALUES
AMMONIA NITROGEN (mg/g)
and
TOTAL NITROGEN (mg/g)
NEAR-SHORE SEDIMENTS
-254-
-------
.00
203
1972 IFYGL
Atvmon i n-!!
otal-.'!
.20"
i
(_n
01
1
_Uo*
. 00 '
/S
_j e: / f
~ > ftjflfd/ /
0 K / /
1 ^Jtr A? i
\ I .....__ __r__
202 205 208 211
.20*
*
_.
T. 10*
K.
"S:
*~ •
_i c:
e£ UJ
^r »
cJ r.:
CJ <
~ ^?
i o
Zj <
w —
| t
o A .. .
nn » T'i T l~~" — ^* ~ * — — —
•°°201 201* 207 210
^^^^vx-^X^ X\
^^*- >n>C. "^^ \ \
iu X \
L'J \\
K. \\
o >A
L'J ^k
CO
r-l
2Ht 217 220 223 22G
II ID LAKE STATIONS
~'
1:1
IU
{.•-.
O
UJ
-J
~
CO 1
r-l
|
\f
217- 216 219 222 225
229
232
T—
235
233
7.0
a
LU
F2.0
^t-^*i iT.im •^JTM^^.. t-^-t ^.,,.-... j"--fj
2 28 251 23'j
•M
O
r-
jj'/jy o. o
HEAD SHORE STATIOII3
-------
Figure 4
MEAN VALUES
DISSOLVED PHOSPHORUS (mg/g)
and
TOTAL PHOSPHORUS (mg/g)
NEAR-SHORE SEDIMENTS
-256-
-------
••> ft
203
1972 IFYGL
niGSOI.VF.n-P ms/
Total-P m£/g
-------
Figure 5
MEAN VALUES
PERCENT TOTAL ORGANIC CARBON
and
PERCENT TOTAL INORGANIC CARBON
NEAR-SHORE SEDIMENTS
-258-
-------
203
1972 IFYGL
";T.O.C. (nv-. )
J.T. I .C. (avr.)
213
DEEP
L0.0
22U
STATIOMi
n .
20
V
~r-
205
20G
211
21'}
217 220 223
HID LAKE STATIONS
235 233
21*1
2.0
c
•rt- <*• 0. 0
2k k
(.ft
o
O.SSrV-
201
c.'.
<
t5
v',
207 210
U.)
UJ
C.C
o
UJ
e:
219 222 22'5
NEAR SHORE GTATIOIfG
u.n
.2.0
2V3
h-
*.'
n.o
-------
Figure 6
MEAN VALUES
IRON (;ig/g)
and
MAGNESIUM
NEAR- SHORE SEDIMENTS
-260-
-------
1972 IFYGL
233 236 239 2'i2 2^5
218 221 221'.
DEEP LAKE STATION
1
Is)
0\
h- '
i
1] f.^
It *••-
K <
K.
c
":" •
:
' t
0
CJ
<
—1
>r! ^
?^*r
-•TX.
L'J
^
«.
£^r
<;
rj
C;
T
20:
205 200
211
2 Ih
217 220 223 22C
MID LAKE STATIONS
229
232 ?35 2T3
-' 201
219 222 221
NEAR SHORE STATIONS
2UO 2V3
-------
Figure 7
MEAN VALUES
MANGANESE
and
ZINC
NEAR-SHORE SEDIMENTS
-262-
-------
203
1972 IFYGL
Manganese
Zinc ue/c(avc.
218 221 22/;
DEEP LAKE STATIONS
o
r-i
2 x
c
i
1-0
ON
LO
I
O*-?-1
202
20G
211
211;
217 220 223 ' 22C
MID LAKE STATIONS
229 232,
"T
233
(T
"
L7
M /}•
X
_c
Ow
._»
•--
<*
(J
c
2
L'.!
x'/
201
LJ
^>
M_
\
\A
^NS.
219 222 22*5 22S
V.
2Ti
HEAR SHORE
-------
Figure 8
MEAN VALUES
COPPER (oig/g)
and
LEAD (jig/g)
NEAR-SHORE SEDIMENTS
-264-
-------
100
203
1072 IFYGL
Copper u^
i
218 221 22'f
DEEP LAKE STATIONS
see
2'iS
inn-
= 50
o
0'
^
j ., » .
202
f
20S
Ni^
208
211
21'!
A
"n
" ' i '••-
217
220
22
22C
MID LAKE STATIOMS
229
232
235
23T
21*1
100
. 0
100
50 ~
— !
<*"
r~
..„ ,..
2'OJf' 207 210
N.X
UJ
L.l
c;
o
UJ
•— J
E
CO
r-l
\v
2*13 216 210 222
^ &
^^k ^^
ys«^^ v^C*i
^^» gjjT^^'i^^***
225 228 231 2Tl>
237
L'J
U'l
to
HEAR SHORE
-------
Figure 9
MEAN VALUES
CADMIUM
and
CHROMIUM (jig/g)
NEAR-SHORE SEDIMENTS
-266-
-------
203
1972 IFYGL
CoHnium
fhromiun
212 221 22';
DEKP LAKE STATIC!15
o
•me
2U5
I
ho
202
205
211
217 220 225
HID LAKE STATIONS
r-
22G
229
232
235 233
2U1
200
140
20
S
CJ
^
_J
_J
I1..1
A
201
c:
L-J
r.:
<
204
207 210
213
CO
r-l
216 219 222
NEAR SHORE *'•
,200
L-
CJ
,100
-------
Figure 10
MEAN VALUES
NICKEL (jug/g)
and
MERCURY (jig/g)
NEAR-SHORE SEDIMENTS
-268-
-------
2 0 0~
loo:
203
202
1972 IFYGL
!'ic!;cl un/
I'ercury u^
2*05
20D
212
215
r
213 221 22'; 227
DEEP LAKE STATIONS
230
205
203
211 21'f 217 220 .223 22G 229 232
MID LAKE STATIONS
2lT
233
2kl
0
.7.
ca
4+
2k i;
2UU
100 *
.
1
<
cJ
c
_l
_J
t'J
.(i
bi
w
C.'
c:
o
A
20^' 207 210
213
UJ
5 219 222
IIJIAR SHORE STATIONS
51»0 ' 2V3
-------
Figure 11
MEAN VALUES
PERCENT DRY WEIGHTS
and
PERCENT VOLATILE SOLIDS
GENESEE SEDIMENTS
-270-
-------
1972 IFYHI.
orvy
I I I » I
555 3GC 3G1 353 357
TRANSECT #1 TRANSIICT
35H
351
352
350
TRANSECT #3
359
TRANSACT A LAi'.E
3
—I
3fi2
w
T!
!i Dry UoF^
*Volati le Gol idsCnvr-
'( o
80 1
•M
ti
O
50
351 352
CLOSE SHORE
353 35'i 355
HIP- SHORE
35G
157
353 3G2
FAR SHORE
359
300
361
•c
o
0!
, +J
3 ra
o
i-:>
-------
Figure 12
MEAN VALUES
NITRATE NITROGEN (mg/g)
and
ORGANIC NITROGEN (mg/g)
GENESEE SEDIMENT
-272-
-------
1072
IIIVMR)
o
.004-7
—7
355 3GO 3G1 353 357 355
351
352 35'* 353
TRANSECT -53
TR.M'!S!-:CT ."i LAKE
Mitratc n
Organic-!' •:
1.2
359 3G2
t- 0.0
LO
I
.OS
NY
O
i)
Q f^..
31S1 352
CLOSH SiiOI^
353 35!>
MID SHORE
350 357
350 3G2 359
FAR SHORE
1.2
c
c
bi
SSO 351
-------
Figure 13
MEAN VALUES
IMMONIA NITROGEN (mg/g)
and
TOTAL NITROGEN (mg/g)
GENESEE SEDIMENTS
-274-
-------
1Q72 IFYGLCGEMflSIZE KIVj-R)
-':•-. 10
355 3GO 301
TRANSACT*!
353 357
TRANSECT
35G
r^
351
THACSL-CT rt. LAK
352 55k 353
TRANSECT "3
359 3G2
2.0
- ,
To^al-f! m,T/.f:
l.n-
o
4J
o
t-
.0.0
i
ho
351 352
CLOSE Si!0.".I:
353 35i}
HID SHORE
35G
i.* -in*.; «•_'. t
357
'•^•-*
353
302 359-
FAR 5110RI:
360
-•-«•-»•"
3G1
1.5
.75 .1
ra
*j
c
- 0.0
-------
Figure 1*4
MEAN VALUES
DISSOLVED PHOSPHORUS (mg/g)
and
TOTAL PHOSPHORUS (mg/g)
GENESEE SEDIMENTS
-276-
-------
355 300 301 353 357 35G
TRANSECT*1 TRAilSECT ;?2
351 • 352 351* j
THAMSECT i?3
j .-iHi ssol v?d-P mrlrAn
'Totnl-P m";/;-: (?v;O
o
i--
'»-—-—-7
359 302
I. 0.0
N) . "'i.'i
tn
•£. OCV!
i
c.
To-mt-P
"* i M *: rr c* s
553 35l> 355
t!! n ^i
302 359
PAR SNORE
C
I-
3GO 3G1
-------
Figure 15
MEAN VALUES
PERCENT TOTAL ORGANIC CARBON
and
PERCENT TOTAL INORGANIC CARBON
GENESEE SEDIMENTS
-278-
-------
1972
ENrsni: UIVI-IR)
TRANSACT fi LAKE
"'T.O.C. (nv::)
ST. I.C. (av.O
73»<
3G1
353 357 35G
TRAiiSilCT #2
1.0
352 35d :
TRANSECT -53
359 3G2
h-
0 I,-™.-..-.
35T 352
CLOSE SMOKE
353
35/1
GilORE
n™. AV— *
357
353
3G2
FAR SHORE
359
350 361
1.5
-------
Figure 16
MEAN VALUES
IRON (jug/g)
and
MAGNESIUM (jug/g)
GENESEE SEDIMENTS
-280-
-------
I"'
c
Lu
351
CLOSE SHORE
355 3GO 3G1
TKAMSSCT01
3 357 35G
TRAiiSECT i?2
/~Vtf<
7^'
/ ***
353 35/>
HID SIIOR!-
3
151 352 35!; ;
TRAMSECT "3
1072 irYGKcuiir
THA!!3!-CT u LAK
0 I ron u^/.^
Ma^nc s i un
302
3GS 3G2
FAR SIIORf:
3GO 351
.s ( a V5' )
-------
Figure 17
MEAN VALUES
MANGANESE (jug/g)
and
ZINC (>ig/g)
GENESEE SEDIMENTS
-282-
-------
1972 IFYGUGENITSEII P.IVI-RJ
C-J
o
TRANSECT A LAKE
v. 2-
3GO
TRAUSECTi'l
53 357
TRANSECT
356
»-^—
351
352 35'*
TRANSECT #3
Zinc un/^
c
N
359 3G2
oo (v
l
'•/'•*-
351 352
CLOSE SHORE
353
HID
35G 357 35S 3G2 359 360 3(51
FAR SHORE
'1.5
c
M
-o
-------
Figure 18
MEAN VALUES
COPPER (jug/g)
and
LEAD (jig/g>
GENESEE SEDIMENTS
-284-
-------
1972
iMV.'-fi)
301 353 357 356
TRAHSECT #2
•v-
THAI!.';.!•:CT ." LA;;;;
r(j,n Copper u-i/.
Lone) u,T/^(
351 352 35't 35G 359 3G2
TRANSECT #3
kio
Ui
30-
ft-
Q .ii.j™,,™,^...^ »
351 352
CLOSE SHORE
353
HID SHORE
'CO
30
355 302
FAR SHORE
359- 3GO 3S1
-------
Figure 19
MEAN VALUES
CADMIUM (jug/g)
and
CHROMIUM (jug/g)
GENESEE SEDIMENTS
-286-
-------
355 3GO 3G1
353 357 358
TRAi.'SECT «!2
351 352 35'* :
TRANSECT #3
359
1972 I
THAflSilCT u LAKH
Cadmium
Chromium
i: HIV.'-iR)
-7-
3G2
CLOSE SHORE
353
HID S!!OR£
mj.J ft-i- E
357
•60
'30
358 302 359
FAR SHORE
360 301
-------
Figure 20
MEAN VALUES
NICKEL Oug/g)
and
MERCURY -(jig/g)
GENESEE SEDIMENTS
-288-
-------
1972
El: RIVI-IR)
1 nn
TRAMSECT*1
3G1
353 357 356
TRAiiSliCT $2
351
352 35/i j
TRANSECT #3
TRAUGI-CT u LA
, ,, f.'ickel i
' " Mercury
359 3G2
i
NJ
00
00
3.50*
0 ^
yjl 352
CLOSE SHORE
353 351}
DID SHORE
357 358 302 359
FAR SHORE
B-O.
3GO 351
* Q Q
-------
Figure 21
MEAN VALUES
PERCENT DRY WEIGHT
and
PERCENT VOLATILE WEIGHT
NIAGARA SEDIMENTS
-290-
-------
T172 I FYCL( IIIAGARA RIVER)
;
*?
\:r:!.';!it
*•***»
PRY
TRANSECT ,"t LAKE
TSDry Weight fi Z Volatile SolidsCavO
-1?.
V«t
\
\
V4I4
V
10
TJ
369 307 3G5 3GG 373 370 371 372 37't 375 37G 377 373 330 331 33't 379 332 333 335 326
TRANSECT t-7. TRANSECT #3- TRANSECTn TRANSECT #5 TRANSECT #G
n
vat
3/7" 3 70
MOUTH
05 370 37;
CLOSE SHORE
till) SHORE'
303 3*o5 s'cTD? 37G 3 ifl 3
-FAR SHORE
12
VI
-a
o
-------
Figure 22
MEAN VALUES
NITRATE NITROGEN (mg/g)
and
ORGANIC NITROGEN (mg/g)
NIAGARA SEDIMENTS
-292-
-------
W. I FYCLC! I ACAKA III '/*,'>
Tn*tim:pT « I Ai/rr
I i\<\ lOi.L I ct L/\i\il
Ultrato-M ft Organic-!! m?./?, Cnv:)
I
o
u:
5CO 30G 'i
^TRANSECT
3G3 3G9 3G7 365 3GS 373 370 371 372 37'i 375 37G "77 373 380 331.33*> 379 332 333 335 38G
L TRANSECT tZ TRANSECT ?3 TRAMSECT^t TRANSECT *5 TRAHSI-CT *G
i:o3-f! r, in"
"37 3 3")T 377 37^)
MOUTM
:J5 370 37« 3?? 3
CLOSE SIIORII
0.0
0.3^
-------
Figure 23
MEAN VALUES
AMMONIA NITROGEN (mg/g)
and
TOTAL NITROGEN (mg/g)
NIAGARA SEDIMENTS
-294-
-------
1972 IFYGLOMAGARA RIVER)
TRAIISI-CT u LAKE
Ammonia-M ft Total-t! tig/^
\
I
ro
o
3Gd 3G3 3G9 3G7 365 3G8 373 370 371 372 37tt 375 376 377 378 3.10 331- 33'i 379 332 3G3 385 386
TRAMSIiCT H TRANSECT *2 TRANSECT -53 TRAHSECTfii TRANSECT *5 TRANSECT #6
MOUTH
G/Q 37.1
CLOSR SIIOUI-
3G*7
HID SHORE'
0.6
'0.3
FAR SHORE
-------
Figure 24
MEAN VALUES
DISSOLVED PHOSPHORUS (rag/g)
and
TOTAL PHOSPHORUS (mg/g)
NIAGARA SEDIMENTS
-296-
-------
1 '.) 72 I F Y C L ( ! ! I AC', A F> A H ! V r R )
x ic
TKA'IGIiCT ." LAKE
Pi scol vex!-? ''; Totol-P m.t/^(avr.)
£>
^v
<$*
IB
o
5C<) 3(i
C9 3G7 365 303 373 370 371 372 37U 375 37G 377 373 3SO 331.3GI> 379 332 333 335 38(='
TRANSECT £2 TRANSECT #3 TRAIISECTS'i TRANSACT #5 TRAHSGCT #6
x 10'
Dis.
V««»-P
01*. f*
/
. • I9
3o9~373 jfii 377 370 3*36 370 3
3.'/3
o.n
0.3
1C
c.
3'C,
(K)UTil
CLOSiL SHORE
111!) SHORE'
376
FAU SHORE
3C5 335
~> 0
-------
Figure 25
MEAN VALUES
PERCENT TOTAL ORGANIC CARBON
and
PERCENT TOTAL INORGANIC CARBON
NIAGARA SEDIMENTS
-298-
-------
l'.)72 II-'YQLCIIAGARA RIVKR)
0
T.O.C,
T
TRADSMCT fi LAKE
"JT.O.C. .'. r.-T. I .C. CavO-
=*3ttW^ jw—Mjroa^—
-3.0
2.0
o
l.n1""
3C9 3GG 3d> 303 369 367 365 3G8 373 370 371 372 37l> 375 37G 377 373 3HO 331 33h 37J) 30?. 333 335 386'
rPxAi.'GIICT n TRANSECT ^2 TRAIIGECT #3 TRAIir>ECT*U TRANSECT #5 . TRANSACT #G
TIC
T*<
359 :i73 374 l>TT~il^
MOUTil
336 370 y/
CLOSi: SIIORC
30*7
1111) SHORE'
3*G 3 "J'o
? 2 3 7 G 3 d
FAR SlinilE
3.0
1.0
-------
Figure 26
MEAN VALUES
IRON (jag/g)
and
MAGNESIUM Cug/g)
NIAGARA SEDIMENTS
-300-
-------
1!) 72 1 FYCL(1! I AGARA III V^R
TRAMGMCT A LAKE
ron ": !'a.-;nesiun u?J:r. (ay;)
V
•- 10
t;
re
5C9 TfiG 30U 303 3C9 3G7 365 302 373 370 371 372 37U 375 37G 377 373 3150 381 .32/> 379 332 303 335 38G'
TRAf.'SECT »l TRAM3ECT «?. TRAMGECT i'3 TRAIIGECTflj TRAMSIICT «5 TRANSECT #G
u>
o
Fe x 10J
ft,
f
-------
Figure 27
MEAN VALUES
MANGANESE (jig/g)
and
ZINC (jug/g)
NIAGARA SEDIMENTS
-302-
-------
\'.n x 10"
y**
1!)72 IFYCLCMAGARA RIVER)
TRAIISECT i" LAKE
.Mannctnose ft Zinc un/.i (avr:)
/KM
\
60
c.
M
30
U-'1 ™.r~.~_~^=orc«r, r-^^ary*^***?^-^* > —«——"J™"—=1 » "" I » «~~ »" * '"•'» » < '—"V" • «y—="5"""""^
3CD 3fiC 3GU 3G3 369 367 365 3GC 373 370 371 372 37H 375 37G 377 373 3fiO 331'33'j 379 332 333 335 38C
TRAIiSf-CT *1 TRANSECT *7. TRAIiGECT #3 TRAIISECT*U TRAHSI-CT ?5 TRAHSECT *G
(In x 10'
I':
." "5 . _y ~~—_,
369 37- 3711 377
COUTH
3iio 370
CLOSE SIIORL:
35307 3?
MIR SHORE'
3^3~?o5 3(38 31TT7G 3
FAR SHORE
'60
I 30
c.
t-t
I". 10
-------
Figure 28
MEAN VALUES
COPPER
and
LEAD (jig/g)
NIAGARA SEDIMENTS
-304-
-------
l'.)72 ll:YCL(i!IAGARA RIVER)
Cu
p"*~ v
5c<) :;GG
TPwMISI-CT C( LAKE
Copper & Lead u"-./", (nvr;)
. 10
3G5 3G9 3G7 3G5 3G8 373 370 371 372 37'j 375 370 377 373 3flO 301 33'; 379 332 333 335 38C
'
TPw\MS!ZCT $?.
TRAMCEC
TRAIIGECT^U TRAi-ISIICT #5 '
TRAMSMCT
CM-
fr 30
20
10
MOUTH
3 Go 370 37.7
ciosr SHORE
3VT?7 37^*77*5
HID SHORE'
303 3t 5 3}j8 3 f 2~ ~3~7TT?i 3
FAR SHORE
-------
Figure 29
MEAN VALUES
CADMIUM Oig/g)
and
CHROMIUM (jug/g)
NIAGARA SEDIMENTS
-306-
-------
l'.)72 I!:YCL(!!IAGARA RIVER)
.fr
TRA!IG::CT a LAKE
Cadmium A Chromium UJT/,": (avr;)
100
3C<) 3GG 3GK 3G3 3G9 3G7 3C5 3GG 373 370 371 372 37'> 375 37G 377 373 3150 331-331! 379 332 333 335 38(fn
TRA:;:;I:CT n TRANSECT t?. TRAIIGECT *3 TRANSECTS TRANSECT #5 TRAMSMCT #G
i
•150
'100
5/7 370
MOUT:
o
CLOSE SIIORL-
371
lill) SHORE
FAR SHORE
-------
Figure 30
MEAN VALUES
NICKEL (yg/g)
and
MERCURY (jug/g)
NIAGARA SEDIMENTS
-308-
-------
II:YCLC!IAGARA R
'iicl-.cl .';
TRA:IS:-:CT n LAKE
I'ercury u?,/Z (<~>vr;)
\ M
•r, r
•O.I*
510 3G9 3G7 363 303 373 370 371 372 37'i 375 37G 377 373 3HO 331 3G!( 37
21 TRANSECT $2 TRAIIGECT S3 TR/MISECTn TRANSECT *5
9 332 333
fRAMSKCT
3S5 381?
#G
0.0
' O.li
MOUTH
/O 37;:
CL05I- SIIORII
________ ,p_r-,..- __ m — ,„
351; 3C7 371 37*5
HID SHORE'
G3 39 375
FAR SHORE
-------
Increased in distance from the shore. The nitrate
and ammonia nitrogen values ranged greatly but
were consistently higher at the 8 km stations.
The organic'nitrogen and total nitrogen were higher
at the 8 km stations and between the Niagara and
Genesee River plumes at the 4 km stations. The
dissolved phosphorus concentrations of the 4 km
stations were lower than the 8 km sites. Dissolved
and total phosphorus values were relatively constant
at 0.005 mg/g and 0.5 mg/g respectively. The TIC-TOG
contents of the sediment were highest at the 4 km
stations except at the Niagara River. Apart from
the Niagara River the TIC-TOG concentrations were
relatively constant at about 1.055 at the *J km stations,
approximately 0.5% TIC and 1.2/5 TOG at the 8 km
stations.
In terms of metals, the Influence of the
Niagara River was greatest at stations 205 and 268.
In general, all the metals had high concentrations
at the 8 km stations decreasing slightly to the
east. At the 4 km stations the concentrations were
low near the Niagara River, increased sharply just
east of the Niagara River and decreased slowly towards
the Genesee River. The near-shore stations showed
-310-
-------
little influence from the Genesee River since
all the sampling points, with the exception of
one transect were taken on the west side of the
river. East of the Genesee River, there was a
slight increase at station 2^4 for all parameters
measured. Zinc concentration increased sharply
at this near-shore station.
Discussion of the 1/2 ion stations is
difficult since only five-(5) of the proposed fifteen
(15) stations yielded any analyzable sediment. Of
these 5 stations, the 3 west of the Genesee River
were sampled only once.
No temperature correlation can be attempted
since the maximum temperature variation is only 3°C.
During the first sampling the water was isothermal at 3°C,
During the other samplings the lake was stratified
and the sediment water interfact temperature were 5-6°C.
The only areas which would show temperature
variations wfeire the 1/2 km stations (being above the
thermocline) but unfortunately all of these sites
could not be sampled.
The only seasonable variation observed was the
phosphorus content between the spring and fall
samplings. During the spring and fall the phosphorus
-311-
-------
Figure 31
GENESEE RIVER MOUTH SAMPLING SITES
357 „-•
353
West Transect
54 X355
mid shore
.361
East Transect
352 close
shore
hannel Transect
Genesee
River
close, mid and far shore
. transect lines
-312-
-------
concentrations were considerably higher.
For the sake of discussion the stations at
the mouth of the Genesee River have been grouped
into three (3) zones - West Transect, Channel
Transect and East Transect - on an East-West plain
and three (3) zone-close shore, mid-shore and
far-shore - on a north- south plain. This is shown
on Figure 3^.
The benthic chemical conditions at the mouth
of the Genesee River (Figure 31 ) were quite
similar to those of the near-shore zone. The sediment,
unlike that of the Niagara River area, was a sandy
ooze. Percent dry weights were all being 60-70% except
for one station, 355, which was considerably higher.
The percent volatile solids are quite consistent in the
channel transect and in the far shore stations.
Percent volatile solids were lower on both sides of
the channel transect and at the mid-shore stations. The
nitrate nitrogen concentrations ranged from station
to station but except for station 356 the values all fell
between 0.2-0.4 mg/g. The organic and total nitrogen
content was high at the far-shore stations and in the
channel transect. The east transect had a high value
at station 360 but the other two were low. The
-313
-------
organic nitrogen content in the west transect
Increased with depth of water. The ammonia nitrogen
concentrations were highest in the channel transect
especially at the close shore. The other ammonia
values were relatively constant at 0.15-0.20 mg/g.
The totaU phosphorus concentrations were also
relatively constant (.5-.75 mg/g). The dissolved
phosphorus content was quite high (.003 -.006 mg/g)
in channel transect, particularly at the mid and far
shore stations.
Seasonable variations were observed in the
phosphorus concentrations. The phosphorus values
were 25 to 5Q% higher in the spring and fall,
especially in the close and mid shore stations,
than in the summer. TOG concentrations were highest
in the far shore stations. The content was relatively
constant at all stations around the Genesee River.
The TOC concentrations were particularly high in
the east transect. These east transect sediment samples
contained small amounts of what appears to be coal.
The iron concentrations were quite variable
throughout the entire Genesee River sampling area.
The far shore stations showed a decreased iron content
from west to east. The highest Iron concentration was
-314-
-------
Figure 32
NIAGARA RIVER MOUTH SAMPLING SITES
Transect #if
Transect #3
Transect #5
Transect #2
Transect
336'
Transect
farshore
mid shore"
Niagara
River
-315-
-------
noted at station 352, a close shore station.
Magnesium concentrations were highest in the
close shore and again in the channel transect at the
far shore stations. The magnesium concentrations
were quite low in the west transect and increased
steadily in the east transect away from the Genesee River,
Manganese and zinc showed a relatively constant
concentration over the entire sampling area. Copper
and lead also were constant over the entire sampling
area with the exception of quite high values (30;ug/g Cu,
40 ;ug/g Pb) in the middle of the channel transect at
the mid and far shore stations. The same was true of
cadmium and chromium except for high concentrations
of stations 352, 35^, 356 and 358 (all in the channel
transect). N concentration was low, except In the
channel transect. Stations 352 and 358 were especially
high. The mercury concentrations were quite low
(^0.2 ug/g) except in the west portion of the channel
transect at the mid and far shore lake stations.
For purposes of discussion the Niagara River
stations also have been grouped into four (4) east-west
and six (6) north-south transects (Figure 32).
One must realize that any conclusions of the following
-316-
-------
data must be general at best, since eleven (11)
of the twenty-four (24) proposed stations all
of a transect 6 had a rock bottom.
The sediment collected from the Niagara River
were all sandy; with high percent dry weights.
The percent volatile solids in the center of the
mouth of the Niagara River were the highest of any
station in the project. The far shore volatile
solids were consistently between 2-^%. Nitrate
nitrogen content was high (.02 mg/g) in the center
of the river mouth and low on either side. To the
west of the Niagara River (Transect 1) the nitrate
nitrogen concentration was high but decreased towards1
the river mouth and increased again on the east side
of the mouth. The nitrate nitrogen concentration
at Station 381 (a far shore station) was particularly
high. The organic, ammonia and total nitrogen
values were high in the center of the river mouth and
on the west side of the river but relatively low at
the other sites.
Total phosphorus concentrations at the river
mouth were low but increased with greater depth of water
The values of the far shore stations directly north
of the river mouth were quite high and decreased on
-317-
-------
either side of these stations. The dissolved
phosphorus contents were high in the center of the
mouth of the Niagara River and relatively low at
all the other sampling sites.
TIC-TOG concentration varied over the sampling
area.. The highest observed TOO contents were west
of the Niagara River and decreased steadily to the
east. TIC values were particularly high at the
river mouth (37^ and 377). These were the highest
TIC values measured during the study. TIC values also
were high in the far shore stations directly north
of the river mouth.
Iron concentrations were low at the mouth of
the river and increased on all transects with greater
depth of water. Magnesium concentrations also were
low in the Niagara River sampling area.
Zinc ,and manganese also were low in this area
except for the stations directly north of the mouth.
Copper and lead contents were high at the mouth
of the river, particularly in the center but decreased
sharply in the deeper waters.
Cadmium and chromium were low in this area with a
few exceptions. Cadmium was high at station 377 (at
the mouth of the river) and chromium was high at
-318-
-------
station 376, a far shore station directly north
of the mouth. The other values for cadmium and
chromium were relatively constant.
Nickel concentrations were high at the center of
the mouth of the Niagara River and to the west of
the river. Station 372, a far shore station, north
of the mouth also was quite high.
Mercury concentration also was low in this area
except for those stations west of the Niagara River.
Little seasonable variation in ion concentration
was noted in the Niagara River area.
More intensive analysis of these data, including
contrasting sediment and water chemistry and biological
measurements will be made when the information has
been entered into STORET.
-319-
-------
B. Water
1. Objectives
The objectives of this phase of the
project essentially were the same as those
described above for sediment.
2. Plans vs. Accomplishments
As stated in the proposal by the GLL to EPA,
water samples were gathered with a 4.1 liter Van
Dorn Collection Bottle from one (1) meter below the
surface, mid-depth and one (1) meter above the bottom
during each near-shore and river mouth cruise for a
total of more than two thousand (2000) collections.
The pH, ammonium ion content and total alkalinity of
each sample were determined immediately after the
water was collected. The water samples were
preserved in order that the quantity of each of the
following proposed parameters could be ascertained
at EPA's Rochester Field Station: nitrate, nitrite,
organic and total nitrogen; suspended, soluble and
total phosphorus; total organic carbon; sulfates;
chlorides; silicon dioxide; phenols; calcium; sodium;
potassium; heavy metals (iron, magnesium, mercury,
lead, zinc, chromium, selenium, cadmium, nickel,
manganese and copper); pesticides (DDT, DDE,1 DDD,
lindane, aldrin, dieldrln, toxaphene, endrln,
-320-
-------
toxaphene, chlordane, heptochlor and heptochlor
expbxide).
The ammonium measurements were abandoned
when It was determined that they could not be
measured with any degree of confidence with a
specific ion electrode.
3. Status
The alkalinity and pH values were forwarded
to EPA for Insertion into the IPYGL data bank.
The status of the water analyses being conducted
by EPA-Rochester is unclear. No data has been entered
into STORET.
4. Summary of Results
Few conclusions can be drawn due to the fact
that the results of the analyses concerning those
parameters measured by EPA-Rochester area were not
available at this writing.
Examination of the results of tests made in
the field showed that the alkalinity ranged from
95-113 ppm with no consistent pattern in the
vertical or horizontal profiles or between the values
observed at the same station on different cruises,
in the near-shore zone or at the mouth of the
Niagara River. However, at the mouth of the Genesee
-321-
-------
River the surface waters had an alkalinity
of up to 124 ppm while the measurements of
about 100 ppm were found at the mid and bottom
waters.
The pH differed by as much as 0.5 units between
the 1/2 and 8 km stations with the lower values
found at the latter collection sites. During the
spring there was little difference in the pH with
depth at the near-shore and Niagara River stations.
However, when the lake was stratified, the pH
was higher above the thermocline than below. After
the stratification was destroyed, there again was
little difference between the pH from the surface
to the bottom.
The pH of the Genesee River surface was consistently
lower than lower depths irregardless of the season.
-322-
-------
IV. PHYSICAL STUDIES
A. Ship-Board
1. Objectives
This phase of the survey was designed to
determine the changes in oxygen concentrations,
temperature and light transmission, each measured
on vertical and horizontal plains. From the above
the location and duration of the thermal bar and
thermocline was to be calculated along with the
nature and extent of the plumes from tributaries
discharging into the Welland-Rochester near-shore
zone.
2. Plans vs. Accomplishments
The proposed measurements to be made at
each station on every cruise included: oxygen-
temperature profile, light (transmission) profile,
pH and conductivity at the surface, mid-depth and
bottom. All of the above was accomplished with the
exception that the light meter (submarine photometers)
malfunctioned on the second Genesee River mouth
sampling and was not repaired until the last cruise
in 1972 (27-29 November).
-323-
-------
3. Status
All data has been calculated (i.e., percent
transmission, conductivity adjusted to 25°C, etc.)
and sent to EPA, Grosse lie, for entering in STORET.
At this time, this information Is not ready for
retrieval.
4. Summary of Results
The GLL has been awaiting the entry of the
data in STORET in order to use the capacity of the
latter system to plot the mean, median, standard
deviation, co-efficient of variance, variance and
standard error via the Invent Program. Hence,
extensive analysis of this information has not been
done. However, some generalizations can be drawn
from the raw information.
A thermal bar was present during the 18 April
through 3 May 1972 period. It extended between
stations 202 (4 km) and 203 (8 km) and 204 (1/2 km)
and 205 (4 km) to the mouth of the Niagara River.
To the east it reappeared to the shoreward-side of
station 210 (1/2 km), extended between stations 213
(1/2 km) and 21*4 (^ km) and again to the shore south
of station 216 (1/2 km). From the latter, it was
-324-
-------
present between the 1/2 and 4 km stations through
219 (1/2 km) and 220 ( 4 km). East of the 234 (1/2 km),
235 (4 km) and 236 (8 km) chain it Intersected the
shore to the south of station 337 (1/2 km). To
the east the thermal bar again was found between
the 1/2 and 4 kilometer stations.
On the 10-23 May 1972 cruise the bar had
moved lakeward. It was observed between stations
202 (4 km) and 203 (8 km). However, instead of
moving to the shore, it extended to the north of
stations 206 (8 km) and 209 (8 km). To the east
it stretched Just below the 4 km stations 211, 214, 217 and
220 from which it was found between the 4 and 8 km
stations through 238 and 239. It was north of 8 km
stations 243 (8 km) and 245 (8 km).
A thermal bar was not observed again in 1972.
With respect to vertical temperature
stratification, isothermal conditions were observed
on the 18 April through 3 May and 10 through 23 May
1972 cruises. During the 19-28 June cruise a
thermocline was present between 10 and 15 meters at
all stations. The stratification was found between
15 and 20 meters on both Cruise IV (12-2-1 July) and
V (25 July - 2 August). On the 5-13 September cruise
-325-
-------
the thermocline was observed between twenty (2)
and twenty-five (25) meters at the 4 and 8 km
stations. However, the thermocline had risen to
15 meters at the *J and 8 km stations on cruise
VII (21 September - 4 October). On Cruise VIII
the thermocline had sunk below ^5 meters. The last
stratification was noted at station 220 and 30
October. On Cruise IX (6-22 November) and X (ll-l1!
December) the water was isothermal with slightly
warmer conditions found at the 4 and 8 km stations.
No significant difference was observed in the
dissolved oxygen profiles between the 1/2, 4 and 8 km
stations on any single cruise. This includes the
period when thermal stratification was present.
Contrasting the changes with the seasons, the
dissolved oxygen decreased from 13-1** ppm in the
spring to 10-11 ppm in the summer. It Increased to
11-12 ppm in the fall and 12-13 ppm by the winter.
Conductivity (300-310 jumohs) was fairly uniform
from the surface to the bottom prior to stratification,
There also was little variation between the 1/2, 4
and 8 km stations or from one end of the near-shore
zone to the other. However, after stratification
the epilimnetic waters had a conductivity of
-326-
-------
280-300 ^mohs while the hypolimnion was 300-325
jumohs. This condition persisted until Cruise XIII
at which time the vertical mixing occurred and
the conductivity returned to 300-310 jumohs.
B. Other Physical Measurements in Study Area
1. Objectives
Other researchers in the IAGLR Program also
made measurements and collections in the same regions
as the GLL. Each of these studies had individual
objectives, which can be obtained from the Project
Director of each project, in addition to providing
information that could be used by other researchers.
2. Plans vs. Accomplishments
The direction, duration and intensity of currents
in the Welland-Rochester near-shore area were to
be made by scientists at the Rochester Field Office
of the Environmental Protection Agency and the
University of Rochester. The GLL has contacted these
researchers and is awaiting inputs on the nature and
extent of their data.
The discharges from the Niagara and Genesee
River also were measured. These data also are being
sought as is the information from the meterological
towers in and near the near-shore zone.
3. Status
Unknown.
lJ. Summary of Results
Unknown.
-327-
-------
V. BUDGET VS. ACCOMPLISHMENTS
The sediment chemistry and physical phases of the
study are on schedule. The analyses of benthos is somewhat
behind but should be completed by the termination of the grant.
The phytoplankton and zooplankton identification and
quantification will not be finished by the end of the grant
due to the problems explained above. A three (3) month
extension is being requested. There should be sufficient
funds left in the 1973-74 grant to-cover the estimated costs of
$6324 (1 Research Assistant for three months @ $833/month plus
fringe benefits of $450 and overhead of $374.00; one consultant •
Mrs. Sharon Czaika - 3 months @ $1000/month).
The above savings in the 1973-7** grant come as a result
of the fact that the consultant, proposed to be hired under
the 1973-74 award, to assist with the development of a
«c +
mathematical model ef the near-shore zone was added to the
A
GLL staff. This was due to the fact that one of the major
inputs to the proposed model - specifically the results
of the 1972 and 1973 water chemistry - has not become available.
Until this Information, along with the results of the
measurements in the GLL's study area by other IFYGL researchers,
Is completed, a comprehensive model cannot be constructed.
Since these data may not be available by the end of the period
of 1973-74 award, a 1974-75 grant proposal (for approximately
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$10,000) to support the modeling will have to be made
or the model will have to be abandoned by the GLL.
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A REMOTE SENSING PROGRAM FOR THE DETERMINATION
OF CLADOPHORA DISTRIBUTION IN LAKE ONTARIO (IFYGL)
Grant Number 800778
F. C. Polcyn
Environmental Research
Institute of Michigan
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A REMOTE SENSING PROGRAM FOR THE DETERMINATION
OF CLADOPHORA DISTRIBUTION IN LAKE ONTARIO (IFYGL)
GRANT NUMBER 800778
A. REVIEW OF THE SUBJECT UNDER STUDY
This investigation is designed to contribute to the U. S. Biological
and Chejnical program in Lake Ontario (IFYGL) by providing data regarding
the distribution of Cladophora along the U. S. shoreline of the lake.
Any attempt to delineate the distribution of Cladophora on a large
scale basis must face the issue that conventional methods of data acquisition
are totally inadequate for this purpose. Therefore, the present study is
designed to exploit the capabilities of remote sensing technology for
mapping submerged aquatic vegetation. The program includes multispectral
and photographic data collection, using the ERIM remote sensing aircraft,
and computer processing of the multispectral scanner data to map the dis-
tribution, calculate areas, and estimate biomass of Cladophora.
B. PLANNED OPERATION VERSUS ACTUAL OPERATION
The original program provided for one multispectral aircraft data
collection mission during the month of June 1972 along the entire shoreline
of Lake Ontario. The intent was to acquire approximately 500 miles of data
along a flight track 1500 feet wide for subsequent processing on a sampled
basis. The program also provided for limited data processing to establish
the computer techniques best suited for routinely processing the data set.
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Data were collected on June 20, 1972 along the U. S. shoreline from
Niagara to Stony Pt. at the eastern end of the lake. Poor weather conditions
forced cancellation of the plan to collect data over Canadian portions of
the lake. Because of very unfavorable field conditions in June along
portions of the flight line, particularly between Rochester and Stony Pt.,
a second mission was recommended for the month of July. Upon consultation
with the EPA project monitor, the original plan for data collection over
Canadian waters was abandoned in favor of a second mission along the U. S.
shore. This mission was carried out^ on July 31, 1972. A Canadian decision
to collect data over Canadian waters provided added justification for
restricting activities to U. S. portions of the lake.
C. COST TO PROGRAM BECAUSE OF STUDY DEVIATION
The modification described above had no effect in terms of cost
to the contract. The original plan of operations provided for one data
collection mission consisting of 500 data miles. The subsequent modification
resulted in two missions for a total of approximately 500 miles. Likewise
the modification will have no effect on the current data processing phase
of the program.
D. STATUS OF THE PROGRAM
The first year of the program was devoted to multispectral data
collection and the determination of the most suitable computer-implemented
Cladophora mapping procedures.
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Two multispectral data collection missions were completed along the
U. S. shoreline, June 20, 1972 and July 31, 1972, from altitudes of 1300 ft
and 2000 ft respectively. Twelve channel multispectral scanner data were
recorded in addition to black-white and color photography. Four scanner
channels have been reproduced on film strips. These are: 0.43 - 0.48 vim,
0.52 - 0.57 urn, 0.61 - 0.70 urn, and 9.3 - 11.7 urn.
Preprocessing of the scanner data had been undertaken at selected
areas, and computer processing of a section of the New York shoreline was
completed.
A request was forwarded to EPA for ground truth data at a number of
locations in the study area. This information is required in the data
processing phase of this investigation. To date, this information has not
been received.
The objectives of the program for the first year were to collect
multispectral data and to demonstrate the ability to map Cladophora.
These objectives have been realized.
E. AREAS OF PROGRAM WHICH ARE BEHIND SCHEDULE
None
F. SUMMARY OF RESULTS TO DATE
In view of the fact that the second year of the program is devoted
to computer processing of the data, the results of the first year effort
presented herein are necessarily limited to selected examples.
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Shown in Figures 1 and 2 is a portion of the New York shoreline in
the vicinity of North Hamlin, New York. The dark areas visible in the
0.52 - 0.57 pm band are Cladophora beds. The upper band, 9.3 - 11.7 ym,
depicts surface temperature variations at the time of the overflight.
Computer processing of a section of shoreline was completed and the
area extent of Cladophora was calculated. Shown in Figure 3 is a digital
map of a portion of the study area illustrated in Figure 2. The area shown
is 470 meters by 1220 meters. Within this area, 430,344 sq meters or 75%
of the bottom is covered by Cladophora. Ground truth data provided by EPA
will be used to calculate standing crop expressed as weight per unit area.
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9.3-11.7 /«m
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**
0.52-0.57 //m
MULTISPECTRAL IMAGERY-LAKE ONTARIO NEAR NORTH HAMLIN, N. Y.
20 JUNE 1972
Sheet 1 of 2 Sheets
FIGURE I
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9.3-11.7
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0.5210.57 //m
MULTISPECTRAL IMAGERY-LAKE ONTARIO NEAR NORTH HAMLIN, N. Y.
20 JUNE 1972
Sheet 2 of 2 Sheets
FIGURE 2
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1220 meters
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I:::::::::::::::::::::::::::::::::::::::::::::::
HHl iii&iMi
5?Ilf5:SU
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3
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2
5°
CLADOPHORA DISTRIBUTION
LAKE ONTARIO NEAR NORTH HAMUN, N. Y.
Scene Date - 20 lune 1972
FIGURE 3
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