Baseline Wa.Ter Quality Studies of Selected

BASELINE WA.TER QUALITY STUDIES OF SELECTED

1974 HOUSATO IC RIVER BASIN

inassachusetfs department of environmental qualify engineering DIVISION OF WATER POLLUTION CONTROL *thomas c. mcmahon, director BASELINE WATER QUALITY SURVEYS OF

SELECTED LAKES AND PONDS

IN THE HOUSATONIC RIVER BASIN

BERKSHIRE COUNTY 1974

Eben W. Chesebrough, M.S. Senior Chemist

and

Arthur J. Screpetis Biologist

Water Quality Section Division of Water Pollution Control

Westborough, Massachusetts

September 1975

-Cover

October Mountain overlooking the outlet to Woods Pond, Lenox/Lee, Massachusetts

PUBLICATION NUMBER: Approved by: 88585-76-131-10-75-CR Alfred C. Holland Purchasing Agent ACKNOWLEDGMENTS

The Division of Water Pollution control wishes to thank those whose efforts have made the 1974 Housatonic River Basin Baseline Lake Surveys and this report possible. The following groups and individuals have been particularly helpful:

George Minasian and the staff of the Lawrence Experiment Station who performed the analyses on the chemical san.ples from the lake studies.

Matthew Scott and the Maine Department of Environmental Protection for advice on methodology.

The Massachusetts Division of Fisheries and Game who provided much unpublished data included within the appendices.

The United States Department of Agriculture, Soil Conservation Service, who provided soils data for the study region.

The United States Department of the Interior, Geological Survey, for providing hydrological and water resources data.

Stephen Travis of the Massachusetts Division of Water Pollution Control, Water Quality Section, who performed the identification of the lake macroinvertebrates.

Raymond M. Wright of this Division whose intimate knowledge of the Housatonic River Basin proved invaluable.

2 TABLE OF CONTENTS

-ITEM PAGE 2 Acknowledgments 5 List of Tables

List of Figures 6

9 ti’ A Note on Limnology and the Lake as an Ecosystem 11 Eutrophication u Description of Terms 16 19 Housatonic River Basin Lake Surveys

Introduction 19 19 Berkshire County Geology 24 Lake Methodology 24 Morphology 24 Station Location 24 Data Collection 24 Physical and Chemical Data 24 Biological Data 24 Phytoplankton 25 Zooplankton 25 Macroinvertebrates 25 Aquatic Vegetation 26 Baseline Lake Surveys 26 Woods Pond 38 Stockbridge Bowl 51 Pontoosuc Lake 64 Laurel Lake 77 Lake Buel

3 TABLE OF CONTENTS (Continued)

-ITEM -PAGE Lake Garfield 94

Goose Pond and Upper Goose Pond 106

General Summary 119

Appendix A: Woods Pond Chemical and Biological Water Quality Data 120

Appendix B: Stockbridge Bowl Temperature and Dissolved Oxygen Data 123

Appendix C: Pontoosuc Lake Temperature and Dissolved Oxygen Data 124

Appendix D: Laurel. Lake Temperature and Dissolved Oxygen Data 125

Appendix E: Lake Buel Temperature and Dissolved Oxygen Data 126

Appendix F: Lake Garfield Temperature and Dissolved Oxygen Data 127

Appendix G: Goose Pond Temperature and Dissolved Oxygen Data 128

References 129

4 LIST OF TABLES

NUMBER -TITLE -PAGE 12 A Lake Trophic Characteristics 15 B Selected Data for two Hypothetical Lakes 29 1 Woods Pond Morphometric Data 33 2 Woods Pond Water Quality Data 35 3 Woods Pond Microscopic Examination 42 L Stockbridge Bowl Morphometric Data 46 5 Stockbridge Bowl Water Quality Data 47 6 Stockbridge Bowl Microscopic Examination 55 7 Pontoosuc Lake Morphometric Data 59 8 Pontoosuc Lake Water Quality Data 60 9 Pontoosuc Lake Microscopic Examination 68 10 Laurel Lake Morphometric Data 72 11 Laurel Lake Water Quality Data 73 12 Laurel Lake Microscopic Examination 81 13 Lake Buel Morphometric Data 85 14 Lake Buel Water Quality Data (Station 1) 87 15 Lake Buel Water Quality Data (Station 2) 88 16 Lake Buel Microscopic Examination (Station 1) 90 17 Lake Buel Microscopic Examination (Station 2) 98 18 Lake Garfield Morphometric Data 102 19 Lake Garfield Water Quality Data 103 20 Lake Garfield Microscopic Examination 110 21 Goose Pond and Upper Goose Pond Morphometric Data 114 22 Goose Pond and Upper Goose Pond Water Quality Data 116 23 Goose Pond Microscopic Examination

5 LIST OF FIGURES NUMBER -TITLE -PAGE A Eutrophication - The Process of Aging by Ecological 10 Succession

B Diagrammatic Sketch Showing Thermal Characteristics of 14 Temperate Lakes

Housatonic River and its Tributaries 20 21 Housatonic River Basin - Location of Major Lakes

Housatonic River Basin - Generalized Bedrock Geology 22

Woods Pond - General Watershed 27 30 Woods Pond - Location of Sampling Stations and Bathymetric Map

Woods Pond - General Soils Map 31

Woods Pond - Distribution of Aquatic Vegetation 37 39 Stockbridge Bowl - General Watershed

Stockbridge Bowl - Location of Sampling Stations and 41 Bathymetric Map

7 Stockbridge Bowl - General Soils Map 43 45 a Stockbridge Bowl - Deep Hole Temperature and Dissolved Oxygen Profile 49 9 Stockbridge Bowl - Distribution of Aquatic Vegetation 52 in Pontoosuc Lake - General Watershed 54 11 Pontoosuc Lake - Location of Sampling Stations and Bathymetric Map 56 12 Pontoosuc Lake - General Soils Map 58 13 Pontoosuc Lake - Deep Hole Temperature and Dissolved Oxygen Profile 62 14 Pontoosuc Lake - Distribution of Aquatic Vegetation 65 15 Laurel Lake - General Watershed

6 LIST OF FIGURES (Continued) NUMBER TITLE -PAGE 67 16 Laurel Lake - Location of Sampling Stations and Bathymetric Map

17 Laurel Lake - General Soils Map 69

18 Laurel Lake - Deep Hole Temperature and Dissolved 71 Oxygen Profile

19 Laurel Lake - Distribution of Aquatic Vegetation 75 20 Lake Buel - General Watershed 78

21 Lake Buel - Location of Sampling Stations and Bathymetric 80 Map 22 Lake Buel - General Soils Map 82

23 Lake Buel - Deep Hole Temperature and Dissolved Oxygen 84 Profile (Station 1) 24 Lake Buel - Deep Hole Temperature and Dissolved Oxygen 86 Profile (Station 2)

25 Lake Buel - Distribution of Aquatic Vegetation 92 26 Lake Garfield - General Watershed 95 27 Lake Garfield - Location of Sampling Stations and 97 Bathymetric Map

28 Lake Garfield - General Soils Map 100

29 Lake Garfield - Deep Hole Temperature and Dissolved 101 Oxygen Profile

30 Lake Garfield - Distribution of Aquatic Vegetation 104

31 Goose Pond and Upper Goose Pond - General Watershed 107

32 Goose Pond and Upper Goose Pond - Location of Sampling 109 Stations and Bathymetric Map

33 Goose Pond and Upper Goose Pond - General Soils Map 111

34 Goose Pond - Deep Hole Temperature.and Dissolved Oxygen 113 Profile

35 Upper Goose Pond - Deep Hole Temperature and Dissolved 115 Oxygen Profile

7 LIST OF FIGURES (Continued) - NUMBER -TITLE PAGE

36 Goose Pond and Upper Goose Pond - Distribution of 117 Aquatic Vegetation

8 A NOTE ON LIMNOLOGY AND THE LAKE AS AN ECOSYSTEM

Limnology is the study of inland fresh waters, especially lakes and ponds (lentic water VS. lotic water for streams and rivers). The science encompasses the geological, physical, chemical, and biological events that operate together in a lake basin and are dependent on each other (Hutchinson, 1957). It is the study of both biotic and abiotic features that make up a lake's ecosystem. As pointed out by Dillon (1974) and others before him, in order to understand lake conditions, one must realize that the entire watershed and not just the lake, or the lake and its shoreline, is the basic ecosystem, A very important factor, and one on which the life of the lake depends, is the gravitational movement of minerals from the watershed to the lake. Admittedly, the report contained herein concentrates mainly on the lake itself. Yet the foremost problem affecting the lakes and ponds today is accelerated cultural eutrophication, which origi- nates in the water shed and is translated into various and sundry non-point sources of pollution. A great deal of lake restoration projects will have to focus on shoreland and lake watershed management.

9 \ Mesotrophic Lake

Oligotrophic Lake

Pond, Marsh or Swamp

TIME IN THOUSANDS OF YEARS > Dry Land

EUTROPHICATION - the process of aging by ecological succession.

Source: Measures for the Restoration and Enhancement of Quality of Freshwater Lakes. !Jashington, D.C.: United States Environmental Protection Agency, 1973. EUTROPHICATION

The term "eutrophic" means well-nourished; thus, "eutrophication" refers to natural or artificial addition of nutrients to bodies of water and to the effects of added nutrients (Eutrophication: Causes, Consequences, and Correctives, 1969). The process of eutrophication is nothing new or invented by man. It is the process whereby a lake ages and eventually disappears. An undisturbed lake will slowly undergo a natural succession of stages, the end product usually being a bog and finally dry land (see Figure A). These stages can be identified by measuring various physical, chemical, and biological aspects of the lake's ecosystem. Man can and often does affect the rate of eutrophication. From a pollutional point of view, these effects are caused by increased population, industrial growth, agricultural practices, watershed development, recreational use of land and waters, and other forms of watershed exploitation.

For restorative or preservative purposes of a lake and its watershed, it is important to identify both a lake's problem and the cause of the problem. Problems associated with eutrophication include: nuisance algal blooms (especially blue-green algae) : excessive aquatic plant growth; low dissolved oxygen content; degradation of sport fisheries: low transparency; mucky bottoms: changes in species type and diversity; and others. The pollutional cause is identified as either point or non-point in origin. A point source of pollution may be an inlet to the lake carrying some waste discharge from upstream. Or it may be an industrial, agricultural or domestic (i.e., wash- ing machine pipe) waste discharge which can be easily identified, quantified, and evaluated.

Non-point sources of pollution, which are the more common type affecting a lake, are more difficult to identify. They include agricultural runoff, urban runoff, fertilizers, septic or cesspool leakage, land clearing, and many more. They are often difficult to quantify and thus evaluate.

An objective of a baseline survey is to measure a lake's trophic state, that is, to describe the point at which the lake is in the aging process. The measure most widely used is a lake's productivity. Technically, this involves finding out the amount of carbon fixed per meter per day by the primary producers. Since it is a rather involved procedure to do this, the baseline survey attempts to indirectly describe the lake's trophic state or level of biological productivity.

During the process of eutrophication, a lake passes through three major, broad stages of succession: oligotrophy, mesotrophy, and eutrophy. Each stage has its own characteristics (see Table A). Data from a baseline survey can be analysed for assessment of the lake's trophic state. Although the level of productivity is not quantified, the physical, chemical, and biological parameters measured go a long way in positioning the lake as to its trophic status. The perimeter survey helps locate and identify sources of pollution.

11 TABLE A

LAKE TROPHIC CHARACTERISTICS

1. Oligotrophic lakes: a. Very deep, themcline high; volume of hypolimnion large; water of hypolimnion cold. b. Organic materials on bottom and in suspension very low. c. Electrolytes low, or variable; calcium, phosphorus, and nitrogen relatively poor; humic materials very low or absent. d. Dissolved oxygen content high at all depths and throughout year. e. Larger aquatic plants scanty. f. Plankton quantitatively restricted; species many; algal blooms rare; Chlorophyceae dominant. g. Profunda1 fauna relatively rich in species and quantity; Tanytarsus type; Corethra usually absent. h. Deep-dwelling, cold-water fishes (salmon, cisco, trout) common to abundant. i. Succession into eutrophic type. 2. Eutrophic lakes: a. Relatively shallow; deep, cold water minimal or absent. b. Organic materials on bottom and in suspension abundant. c. Electrolytes variable, often high; calcium, phosphorus, and nitrogen abundant; humic materials slight. d. Dissolved oxygen, in deeper stratified lakes of this type, minimal or absent in hypolimnion. e. Larger aquatic plants abundant. f. Plankton quantitatively abundant; quality variable; water blooms common; Myxophyceae and diatoms predominant. g. Profundal fauna, in deeper stratified lakes of this type, poor in species and quantity in hypolimnion; Chironomus type; Corethra present. h. Deep-dwelling, cold-water fishes usually absent; suitable for perch, pike, bass, and other warm-water fishes. i. Succession into pond, swamp, or marsh. 3. Dystrophic lakes: a. Usually shallow; temperature variable; in bog surroundings or in old mountains. b. Organic materials in bottom and in suspension abundant. c. Electrolytes low; calcium, phosphorus, and nitrogen very scanty; humic materials abundant. d. Dissolved oxygen almost or entirely absent in deeper water. e. Larger aquatic plants scanty. f. Plankton variable; comonly low in species and quantity; Myxophyceae may be very rich quanfitatively. g. Profundal macrofauna poor to absent; all bottom deposits with very scant fauna; Chironomus sometimes present; Corethra present. h. Deep-dwelling cold-water fishes always absent in advanced dystrophic lakes; sometimes devoid of fish fauna; when present, fish production usually poor. i. Succession into peat bog.

SOURCE: Welch, P. S., Liumolo McGraw Hill Book Co., New York, 1952. (Reprinted with permission-+% rom t e publisher.)

12 Figure B shows the various zones of a typical stratified lake. In addition to the lake's life history mentioned above, a lake also has characteristic annual cycles. Depending on the season, a lake has a particular temperature and dissolved oxygen profile (see Figure B). During the summer season, the epilimnion, or warm surface water, occupies the top zone. Below this is the metalimnion which is characterized by a thermocline. In a stratified lake this is the zone of rapid temperature change with depth. The bottom waters, or hypolimnion, contain colder water. The epilimnion is well mixed by wind action, whereas the hypolimnion does not normally circulate. During the spring and fall seasons these regions break down due to temperature change and the whole lake circulates as one body. In shallow lakes (e.g., 10-15 feet maximum depth) affected by wind action, these zones do not exist except for short periods during calm weather.

The summer season (July-August) is the best time to survey a lake in order to measure its trophic status. This is the time when productivity and biomass are at their highest and when their direct or indirect effects can best be measured and observed. Some of the lakes included in this report were surveyed during June, or the early summer season. For this reason the thermocline had not yet strongly developed and the oxygen demand in the hypolimnion had only begun to assert itself. In each case, reference is made to this situation and described for each lake.

The oxygen concentration in the hypolimnion is an important characteristic for a lake. A high level of productivity in the surface waters usually results in low oxygen concentrations in the lake's bottom. Low oxygen in the hypolimnion can adversely affect the life in the lake, especially the cold water fish which require a certain oxygen concentration.

Table B depicts concentrations of various substances and other data for two hypothetical lakes, one eutrophic, the other oligotrophic. It is intended as a guide for comparison to the lakes included in this report. Each lake, of course, is different from all others. There is no hard and fast rule as to critical concentrations for each lake. The morphology of a lake (e.g., mean depth) plays an important part in its general well-being. A small, deep lake will react differently to nutrient loading than a large, shallow lake. In the final analysis, each lake is found unique and must be evaluated on an individual basis.

13 Diagrammatic sketch showing thermal characteristics of temperate lakes

0- 5 - IO IS 20 25 30 35 40

* 45 48 2 50 .g 55 560 a 0" 65

Summer Spring - Fall Winter Dissolved Oxygen (mq/I) Dissolved Oxygen (mg/l) Dissolved Oxygen [mq/l) 0 2 4 6 8 1012 I4 0 2 4 6 a IO 0 2 4 6 8 1012 0 I I I I I 5 10 15 20 25 30

35 - --Temp. 40 D.0.- - 45 - % 50 - -0 ._c 55 - f 60 - m

2 65 ~ , , I , 32 39 47 54 61 68 75 a2 32 39 47 54 61 68 75 82 32 39 47 54 61 68 75 82 Temperature OF Temperature OF Temperoture OF Strotificotion ISothermol Inverse stratification

Source: Measures for the Restoration and Enhancement of Quality of Freshwater Lakes. Washington, D.C.: United States Environmental Protection Agency, 1973.

FIGURE 6

14 TABLE B SELECTED DATA FOR TWO HYPOTHETICAL LAKES Concentrations in mg/l

DISSOLVED TROPHIC* ' . OXYGEN AT TRANSPARENCY NO3 TOTAL PHYTOPLANKTON AQUATIC FISHERIES STATUS BOTTOM (Secchi level) NH3 P VEGETATION Lake A High High low low low High diversity, Sparse Coldwater (Oligotrophic) )5.0 <0.03 <0.03 eO.01 low numbers, types nearly complete absence of blue- c greens Lr Lake B Low Low high high high Low diversity, Abundant Warm water (Eutrophic) c5.0 >0.03 >0.03 >0.01 high numbers, types abundance of blue-greens. 'Not established as State standards. 201igotrophic - nutrient poor Eutrophic - high concentrations of nutrients DESCRIPTION OF TERMS

NAXIMIM LENGTH: Length of line connecting two most remote extremities of lake. Represents true open-water length; does not cross any land other thaa islands.

MAXIMUM EFFECTIVE LENGTH: Length of straight line connecting most remote extremities of lake along which wind and wave action occur without any kind of land interruption. Often identical with maximum length.

MAXIMUM WIDTB: Length of straight line connecting most remote transverse extremities over water at right angles to maximum length axis.

MAXIMUM EFFECTIVE WIDTB: Similar to maximum effective length only at right angles to it.

MAXIMUM DEPTH: Maximum depth known for lake. MTAN DEPTH: Volume of lake divided by its surface area.

MEAN WIDTB: Area of lake divided by maximum length, B: Refers to surface area of lake exclusive of islands. Determined by planimetry from outline of map.

VOLUME: Determined by computing the volume of each horizontal stratum as limited by the several submerged contours on the bathymetric &ydrographic) map and taking the sum of the volumes of all such strata.

SHORELINE: Length of lake's perimeter, measured from map with rotometer (map measurer).

DEVELOPMENT OF SHORELINE: Degree of regularity or irregularity of shoreline expressed as index figure. It is the ratio of the length of the ., shoreline to the length of the circumference of a circle of an area equal to that of the lake. It cannot be less than unity. The quantity can be regarded as a measure of the potential effect of littoral processes on the lake.

DEVELOPMENT OF VOLUME: Defined as the ratio of the volume of the lake to that of a cone of basal area equal to the lake's area and height equal to the maximum depth.

NEAN DEPTH - MAXIMLIM DEPTH RATIO: Mean depth divided by maximum depth. It serves as an index figure which indicates in general the character of the approach of basin shape to conical forms.

LENTIC: Relating to still or calm water, as lakes or ponds.

-LOTIC: Relating to moving water, as rivers or streams.

16 I

EPILIMNION: The circulating, auperfidal layer of a lake or pond lying above the metalhuion which does not exhibit thermal stratification.

HETALMNION: The layer of water ia a lake between the epilimnion and hypo- ltmuion in which the temperature exhibits the greatest difference in a vertical direction. f.

HPPOLIMNION: The deep layer of a lake lying below the metalimion and removed from surface influences (i.e., not circulating).

THEKHOtXINE: Coincident with metalimion; relates to lake zone vith greatest temperature change in a vertical direction.

CLINOGRADE: A stratification cume of temperature or of a chemical substance in a lake that exhibits a uniform slope from the surface into deep water.

ORTBOGRADE: A stratification cume for temperature or a chemical substance in a lake which has a straight uniform course.

WEROGRADE: A stratification curve for temperature or a chemical substance in a lake that exhibits a non-uniform slope from top to bottom. It can be positive (metalimnetic -mum) or negative (metalimetic minimum).

CULTURAL EUTROPHICATION: Enrichment or rapid increase in productivity of a body of water caused by man. It is an accelerated process as opposed to natural, slow aging of a body of water. Visual effects include nuisance algal blooms. low transparency, extensive aquatic plant growth, loss of cold water fisheries due to oxygen depletion, and others. It is caused by the rapid increase in nutrient additions to the lake.

AQUATIC PLANTS: bn aquatic can be defined as a vascular plant that germinates and grows vith at least its base An the water and is large enough to be seen with the naked eye. The following three broad categories are recognized: 1. EMERGENT: Those plants rooted at the bottom and projecting out of the water for part of their length. Examples: Arrowhead (Sagittaria sp.) Pickerelweed (Pontederia sp.) 2. FLOATII?G: Those which wholly or in part float on the surface of the water and usually do not project above it. Examples: Water shield (Bsasenia sp.1 Yellow water lily (Nuphar sp.) 3. SUEMERGED: Those-which are continuously submerged (except sometimes for floating or emergent inflorescences). Examples: Bladderwort (Utricularia sp.) Pondweed (Potamogeton sp.)

SESMN: All the particulate matter suspended in the water.

DIMICTIC LAKE: One Vith spring and fall turnovers (temperate lakes).

17 SILICA: Thin substance (Si02) is necessary for diatom growth. The concentration of silica is often cloaely llnked with the diatom population's growth. The limiting concentration in usually considered to be 0.5 mg/l.

....

18 HOUSATONIC RIVER BASIN LAKE SURVEYS

INTRODUCTION

Baseline lake studies were conducted on selected lakes and ponds within the Housatonic River Basin during June and August of 1974, These surveys were run concurrently with the ongoing river survey during each of the two weeks. The objectives of the baseline surveys were several: 1. Estimation of the lake's trophic level. 2. Data collection for the State's lake identification and classification program. 3. To satisfy the requirements of Section 314, PL92-500 of the Federal Lake Program (W2 included here). 4. To satisfy public demand for attention to lake problems.

The baseline survey is accomplished in one day. It generally consists of a perimeter survey and sampling the water column and sediments at the deep hole station. Inlets, outlets, and occasional special samples are also collected. The perimeter survey also includes the qualitative mapping of aquatic vegetation. Also noted are watershed characteristics including dominant tree type, land use, number and type of dwellings, and, of course, any direct discharges or septic tank problems. The results from a baseline survey enable the Division of Water Pollution Control to classify and identify the water quality of Massachusetts lakes. On the basis of such a survey, a lake may or may not be chosen for intensive, year-round study. The baseline surveys included in this report are of the following lakes and ponds:

NAME MUNICIPALITIES AREA VOLUME IN IN ACRES ACRE FEET

1. Woods Pond Lenox 122 500

2. Stockbridge Bowl Stockbridge 374 8,914

3. Pontoosuc Lake Pittsfield and 467 6,532 Lanesborough

4. Laurel Lake Lee and Lenox 165 4,310

5. Lake Buel New Marlborough 194 3,284 and Monterey

6. Lake Garfield Mont erey 262 4,150

7. Goose Pond Lee and Tyringham 225 5,593

BERKSHIRE COUNTY GEOLOGY

In consequence of the Paleozoic history, New England as a whole is of meta-

19 i? FIGURE C 20 I FIGURE D 21 VE

ana Water Resources of the Housatonic Source: R.F. Nowitch, sal., H droh River Basin, Massachusetts. -.: p-. 22 morphic terrain. Underlying the Great Valley of Vermont, which continues southward past Stockbridge, Massachusetts, and into northwest Connecticut, there is a narrow belt of Cambrian and Ordovician limestones, some of which are metamorphosed to marble. This area, merging northward with the Champlain Lowland, drains southward by the upper Housatonic River. New England's hard water lakes are largely confined to this belt due to the extensive limestone deposits (see Figure E).

Berkshire County itself is underlain by four major bedrock types: gneiss, quartzite, schist, and carbonate rocks (see Figure E). The gneiss and quartzite form the eastern hills, while the carbonate rocks underlie the low- lands in the central valley mentioned above. The carbonate rocks are very widespread in the Berkshires and, in places, produce a great deal of ground- water for wells.

The Berkshire lakes, as well as those in New England as a whole, owe their origin in part to Pleistocene glaciation. The majority appear to be in modi- fied rock basins darned by glacial drift. Stratified kame dams are more common than till alone, and kettle holes are quite numerous.

As any traveler can see, the outstanding feature of the Berkshires is the physiology of the region which produces the basis for the varied fish and wildlife resources. The hill and mountain ranges run predominantly north- south and fall between two major ecological zones: the chestnut-oak to the south and the northern hardwoods to the north.

23 LAKE METHODOLOGY

MORPHOLOGY

Bathymetric maps of the lakes were prepared either using an original from the Massachusetts Division of Fisheries and Game or constructing one in the field using a fathometer (Raytheon model DE 728A). Morphometric parameters were measured with a planimeter and rotometer according to Eutchinson (1957) and Welch (1948). Other pertinent map data were derived from U.S.G.S. topographic maps (7.5 minute series).

STATION LOCATION

For each lake surveyed, the following stations were established:

1. Deep hole station on the lake. 2. Inlet station(s). 3. Outlet station. Occasional special samples were also collected if any waste discharge was suspected or observed.

DATA COLLECTION

Physical and Chemical Data

Temperature profiles were made "in situ" with a Thermo Fishometer (Bright Radio Laboratories, Inc., Oceanside, N.Y.). Transparency measurements were made with a standard 20 cm secchi disc. Field pH tests were taken with a Hach model 17N Wide Range pH Test Kit. Water samples from the deep hole stations were collected with a standard type brass Kemmerer water sampler, while inlet and outlet samples were generally collected below the surface by hand. The sample method €or dissolved oxygen was collected in the manner prescribed by Welch (1948). The dissolved oxygen concentration was measured by azide modification of the Winkler technique (Standard Methods, APHA, 1971). Titrations were made within several hours after fixing in the field with the manganese sulfate and alkali-azide-iodide reagents. The sulfuric acid was added just prior to the titrations in the laboratory. Samples for chemical analyses were transported as soon as possible to the Lawrence Experiment Station of the Department of Public Health and analyzed according to Standard Methods (APHA, 1971). The following analyses were performed on each sample: pH, alkalinity, har.dness, conductivity, silica, ammonia-nitrogen, nitrate- nitrogen, and total phosphorus. In addition, many of the lakes were also tested for chloride, iron, and manganese. Wind, weather, and air temperatures were routinely recorded on every survey, along with any other pertinent observations,

Biological Data Phytoplankton

Phytoplankton samples were collected by a standard procedure prescribed by the

24 Maine Department of Environmental Protection, Division of Lakes and Biological Studies. The sample consisted of a composite core taken with a %-inch I.D. plastic tube with a weight attached to one end. The tube was lowered at the deep hole station close to the bottom, pinched below the meniscus, and raised into the boat. The sample was then allowed to drain into a clean and rinsed collection bottle. The procedure was repeated until a volume of 500 ml was collected. Samples were normally analyzed for phytoplankton on the same day of collection using a Whipple micrometer and Sedgewick-Rafter cell. Algae counts were reported as areal standard units/ml (Standard Methods, 1971).

Zooplankton

Zooplankton samples were collected with a simple conical plankton net (D= 5 inches: L=15 inches) with No. 20 mesh. The net was lowered at the deep hole station close to the bottom and then raised at a constant. semi-rapid rate (about 1 meterlsec.). The straining bucket was emptied into a clean and rinsed collection bottle and the procedure repeaced for a total of five times. The collection bottle was then diluted to a volume of 500 ml with lake surface water and preserved with 5% neutral formalin for later analysis.

Semi-quantitative analyses of the zooplankton samples were made by allowing the sample to settle for five minutes in a graduated cylinder and reading the volume in milliliters. Qualitative analysis under lOOX magnification was made according to Biological Field and Laboratory Methods for Measuring the Quality of Surface Waters and Effluents (EPA, 1973). The results were reported as relative frequency of species in the field.

Macroinvertebrates

Bottom invertebrate samples were collected at the deep hole station using a 6 x 6 inch Ekman dredge (0.25 ft2). A total of four samples were taken, emptied into a bucket and mixed, and then a one-quart volume subsample was taken and put in a plastic container, then sieved (1130 standard sieve) and "picked" within one week of collection and preserved in 70% ethyl alcohol for later identification.

Aquatic Vegetation

The aquatic vegetation in the lake was located and mapped by slowly examining the entire littoral zone of the lake by boat. Where the bottom was not visible, it was semi-quantitatively dragged for aquatic plants. Identification for the most part was made "in situ" except for a few samples which were taken back to the lab and identified according to Fasset (1957), Weldon --et al. (1973) or Hotchkiss (1972). Some aquatic macrophytes often could not be keyed to species because the plants were not in flower or fruit.

25 WOODS POND LENOX

-ITEM -PAGE I. Introduction 28

28 11. Morphometric Data 32 111. Water Quality Data Chemical 32

Biological 32

Phytoplankton 32

Zooplankton 32

Macroinvertebrates 36

Aquatic Vegetation 36

IV. Summary 36

WOODS POND I. INTRODUCTION

Woods Pond lies on the Housatonic River northeast of Stockbridge Bowl and about mo miles due west of Lenox Center. The general watershed of Woods Pond is shown in Figure 1. The drainage basin is small (4.36 square miles) covering portions of Lenox and Washington. The western boundary of the pond's drainage basin abuts that of Stockbridge Bowl. The drainage basin of the Housatonic River above Woods Pond is 161.40 square miles, and during the baseline survey (June 10, 1974) the inlet flow was recorded at about 190 cfs. Woods Pond is not used for recreational purposes other than canoeing. In short, the impoundment (a dam is located immediately below the outlet) is hypereutrophic with unsightly and undesirable water quality. The major causes of the water quality problems are the Pittsfield and North Lenox municipal wastewater treatment plants and the General Electric Com- pany, which is located in Pittsfield. In addition, the north and west shores are swampy and slowly encroaching on the pond's open water area.

Because of the upstream wastewater treatment plants, Woods Pond was selected for study by the National Eutrophication Survey of the U.S. Environmental Pro- tection Agency. The preliminary report of that study has been completed and reference will be made to portions of it in this report.

11. MORPHOMETRIC DATA

Morphometric data for Woods Pond are presented in Table 1 and Figure 2. The bathymetric map was constructed from field data using a fathometer (see Method- ology). Map data weret derived directly from either a USGS quadrangle map or a pantographic enlargement of same.

Woods Pond was the smallest lake surveyed (122 acres) in the Housatonic River Basin. The pond's shallowness is reflected in a mean depth of only four feet. The pond is actually an impoundment, and the bathymetric map shows evidence of the former river channel. The maximum depth recorded during the June survey was 15 feet in the southern basin where the deep hole station was sub- sequently located. The volume of the pond, as calculated from the bathymetric map, was some 500 acre feet.

Figure 3 depicts soils data for the immediate drainage basin. The entire eastern side is bedrock soils and well drained stony soil, with a steep slope. Included in this drainage portion are the very small Felton Lake and Halfway Pond water bodies (see Figure 1). The western drainage basin is composed of poorly drained organic and mineral soils (the swampy region) and well drained stony limestone soils.

In general, the morphometric data supports the statement that Woods Pond is more of a pond than a lake. That is, the majority of the pond's area is shallow with good light penetration to the bottom. Thus, with upstream municipal wastewater treatment plants discharging to the Housatonic River, Woods Pond may be expected to support a high productivity.

28 TABLE 1

IJOODS POND

MORPHOMETRIC DATA

Maximum Length 5,850 feet

Maximum Effective Length 5,350 feet

Maximum Width 1,850 feet

Maximum Effective Width 1,850 feet

Maximum Depth (June 1974) 15 feet

Mean Depth (June 1974) 4 feet

Mean Width 908 feet

Area With Islands 134 acres (0.2lmiles 2 )

Without Islands 122 acres (0.19miles2)

Volume (June 1974) 500 acre feet

Shoreline 8,700 feet

Development of Shoreline 1.06

Development of Volume (June 1974) 0.8

Mean to Maximum Depth Ratio (June 1974) 0.27

Drainage Area (includes Felton Lake, 4.36 miles2 Halfway Pond, and Sawmill Brook)

Uousatonic River Drainage Area Above Woods Pond Inlet 161.4 miles’

29 30 Excessivety drained and well Wined sandy and Well drained ond moderately welt droimd, stony, limestone soits with hardpons on uplonds with slopes less than 15 percent.

f5tEesssively-,droind md well drained sandy ond Shollow to bedrock &Is and deep, well droined ond moderately well droiwd stony soils with hardpans on uplonds with sbpes grerrtsr thon .l5 percent. Shollow to bedVOCk soils and deep, well droined Very poorly drained organic wip. .and modarutely keLI drained sfony soils wvrth bardpons on uplands with slopes less .than 15 percent,

W0UM POND

,GEMER.& SOIL MAP 111. WATER QUALITY DATA Water quality data for the June 10, 1974, survey are presented in Tables 2 and 3. Station locations are shown on Figure 2. Also included in Table 2 are data from the June 1974 river survey when the inlet and outlet of the pond were sampled. The complete data from the Housatonic River survey have been published by this Division under separate cover (Housatonic River: 1974 Water Quality Survey Data).

CHEMICAL Station 1 was located slightly west of the deep hole in the southern basin. The pond was not thermally stratified and showed good oxygen concentrations on the bottom (see Table 2 ). The pH (8.3), total alkalinity (107 mg/l), and total hardness (116 mg/l) were all in line with the region's geology and general water quality. As the soils data in Figure 3 show, part of the western drainage basin is composed of well drained stony limestone soils. It is a strongly buffered, hard water pond. The nutrient levels in the pond were very high as might be expected with two upstream treatment plants (Pittsfield and North Lenox). The river survey nutrient data for June and August (Table 2) show somewhat higher values at the inlet than at the outlet. The difference was most likely represented in algal and macrophyte growth with some loss to the sediments. The National Eutrophication Survey study found comparable nutrient values in the pond in 1972.

The suspended solids data from the June and August (especially August 8, 1974) river surveys were noteworthy. Observations at the time found floating solids all over the pond's surface with a distinguishable sludge odor present. The water appeared very turbid and had a secchi disc transparency of only two feet (at 1120 hours, sunny skies). The very high solids concentrations at the outlet on August 8 (33.0 mg/l) as compared to the inlet (9.0 mg/l was due to the algae present.

BIOLOGICAL

Phytoplankton With such high nutrient concentrations, one should expect heavy algal and plant growth in the pond. This is especially true for shallow depths which translate into good light penetration and warm water. The phytoplankton data from the June 10 lake survey did not show high algal counts (Table 3). The river survey phytoplankton results for June and August, although higher, also did not demonstrate very dense algal populations. The pond's flushing rate is high which prevented dense algal build-up. Both the National Eutrophication Survey study and personal communications with the local residents have shown that Woods Pond does support heavy algal blooms at times during the summer months.

Zooplankton

The zooplankton sample showed very low numbers of zooplankters. Cladocerons

32 w m N m

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34 Y

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h2 u were represented only by Daphnia sp. (water fleas), while other types were absent altogether.

Macroinvertebrates

The deep hole station revealed only three organisms of the family Tubificidae (Limnodrilus sp.) found during the June study. Severe environmental conditions caused by accumulations of sludge in Woods Pond limit a diverse population of organisms from becoming established.

Aquatic Vegetation

The distribution of aquatic vegetation for the June 10, 1974, study is shown in Figure 4. Although the survey was conducted early in the summer, the perimeter survey showed the onset of heavy macrophyte growth. Both milfoil (Myriophyllum sp. ) and yellow pond lily (msp. ) were widespread throughout the pond. Pickerelweed (Pontederia sp.) was also present in a few locations, and cattails (Typha sp.) were scattered all around the pond. The most notable and obvious plant, however, was duckweed (wsp.), which showed an extensive growth over the pond's surface. It is possible that the duckweed shaded out enough incident light to curtail algal growth in the pond.

1V. SUMMARY

Data from the June baseline survey, the June and August Housatonic River surveys, and general observations fully support the conclusion stated in the National Eutrophication Survey report: "...Woods Pond is a hypereutrophic impoundment which receives heavy loads of phosphorus (and nitrogen) from municipal and industrial sources. Heavy algal blooms and broad surface coverage by duckweed are recurrent phenomena."

The pond is also heavily populated with aquatic vegetation. The swampy sections of the pond appear to be filling in at a rapid rate, thus dimin- ishing the surface area of the pond. Floating solids and a malodorous smell are often present, discouraging recreational activities. In short, the pond has very little recreational asset and any restoration attempt would require a gargantuan effort.

36 AQUATIC VE ON

LEGEND

YY YY m mm

mmm mm WOODS POND LENOX 122 ACRES Dom .... FIGURE 4 STOCKBRIDGE BOWL

STOCKBRIDGE -ITEM -PAGE 40 I. Introduction 40 11. Morphometric Data 40 111. Water Quality Data 44 Chemical 48 Biological 48 Phytoplankton 48 Zooplankton 48 Macroinvertebrates 48 Aquatic Vegetation 48 Iv. sunrmary

STOCKBRIKE BOWL

I. INTRODUCTION

Stockbridge Bowl lies east of the West Stockbridge Mountain Range and only half a mile from the Tanglewood Auditorium. The entire drainage area is shown in Figure 5. The lake itself lies in the Town of Stockbridge and its watershed includes parts of Lenox, Lee, and a very small comer of Richmond. The lake drains south entering the Housatonic River between Stockbridge Center and Glendale. The lake has over 370 dwellings in its immediate area, only 20 of which are occupied year-round (Ludlam 5s.,1974). Stockbridge Bowl experiences very heavy recreational use, especially during the smer months. Nearby centers of population include Lenox, Lee, Stockbridge, and West Stockbridge. The lake is in a very attractive setting and is enjoyed by innumerable people every year. Unfortunately, however, the lake's water quality is undergoing accelerated cultural eutrophication.

11. MORPHOMETRIC DATA

Morphometric data for the lake are presented in Table 4 and Figure 6. The data were derived from a U.S.G.S. quadrangle map and relate to the main basin exclusive of the man-made outlet channel, except for the volume which pertains to the entire lake. The volume of the main basin has been calculated to be 8,833 acre feet (Ludlam -et _.a1 , 1974). The lake was the second largest studied in this series with a surface area of 374 acres. The maximum depth is 48 feet and the deep hole is located just about in the center of the lake. The mean depth is 24 feet, and the volume is 8,914 acre feet. The lake has a rather small watershed of about 11 square miles. The watershed area is composed mostly of well drained stony limestone soil, shallow to bedrock soils, and hardpans on slopes of less than 15 percent (Figure 7 ). According to a Water Resources Research Center study, I, ...the lake level has been controlled by various dams since the early 1800's." Presently the lake level is controlled by the Barker Dam which was constructed in or about 1869 and repaired in 1930 (Ludlam --et al., 1974). The lake is irregular in shape and of glacial origin. Its rather smooth shoreline is reflected in a low shoreline development index of 1.26.

111. WATER QUALITY DATA

The date of the survey (June 10, 1974) should be stressed because it represents early summer conditions in the lake. As the Water Resources Research Center report makes clear, the early smer conditions suggesting eutrophication grow progressively worse during the summer in Stockbridge Bowl. Where appropriate, further references and comparisons will be made to that report.

40 LOCATION OF SAMPLING STATtOMS and BATHYMETRIC MAP (contour intarvoi-five feet)

FIGURE 6 41 TABLE 4

STOCKBRIDGE BOWL

MORPHOMETRIC DATA

Maximum Length 6,750 feet

Maximum Effective Length 6,750 feet

Maximum Width 3,720 feet

Maximum Effective Width 3,720 feet

Maximum Depth 48 feet

Mean Depth 24 feet

Mean Width 2,414 feet

Area 374 acres

1 Volume 8,914.1 acre feet

Shoreline (main basin) 18,100 feet

Development of Shoreline 1.26

Development of Volume 1.5

Mean to Maximum Depth Ratio 0.5 2 2 Drainage Area 11.08 miles

1 Source: Ludlam et &. The Limnology of Stockbridge Bowl, Stockbridge, Massachusetts, Water Resources Research Center, Universitv of - Massachusetts, Amherst. Massachusetts, 1974. LSource: Curran Associates, Inc; Wastewater Collection and Disposal at Stockbridge Bowl, Stockbridge, Massachusetts, Northampton, Massachusetts, 1971.

42 GENERAL SOIL MAP

F CHEMICAL The water quality data from the baseline survey are presented in Table 5 and Figure 8. Station locations are presented in Figure 6. The smaller inlets (Shadow Brook, Mohican Brook, and Duck Pond Brook) were not sampled during the survey dk to a lack of flow. On June 10, a sunny, windless day (air temp. 8S°F), Stockbridge Bowl was stratified with a broad thermocline between the 5- and 25-foot level. The thermocline would, of course, become narrower with time as the epilimnion warmed up. Ice-out for the lake generally occurs at the end of April or beginning of May. Stratification of the lake normally does not begin until about mid-May. Despite this, the lake was found to be nearly anaerobic at 45 feet on June 10, 1974. This represents a high rate of dissolved oxygen demand in the hypolimnion which, in turn, is indicative of a high level of productivity. In fact, the University of Massachusetts study found the hypolimnion completely anaerobic from early July to the end of November as well as during the winter stagnation period.

The oxygen profile showed a broad maximum in the metalimnetic region of the lake. Two factors were responsible for this: first, the presence of Micro- coleus sp. (a blue-green algae), and second, the rapid decrease in tezture with depth. The University of Massachusetts study found Microcoleus the "most important net phytoplankton in the lake." Microcoleus is known to remain localized in a stratified lake's metalimion, thus capable of causing a positive heterograde oxygen profile.

The pH in the epilimnion was 8.5 and was measured as 9.0 at the 22- and 28-foot depths. At 45 feet it reached a low of 7.6.

The alkalinity and hardness concentrations were both on the high side, which is not unusual for a Berkshire lake. The soils on the northern shore of the lake are composed of well drained stony limestone material. Lily Brook inlet had a pH of 9.6, which for a natural water is very high. The epilimnion at eight feet had a phenolphthalein alkalinity of 15 mg/l and a total alkalinity of 112 q/l. The former (often called caustic alkalinity) is normally due to the carbonate fraction of total alkalinity. The Lily Brook inlet sawple had a phenolphthalein alkalinity of 35 mg/l, which again is very high for an un- polluted stream. At 45 feet, on the other hand, there was no phenolphthalein alkalinity and a total alkalinity of 117 mg/l. Thus, in the hypolimnion, the alkalinity was probably all due to bicarbonate.

Total hardness was measured at 128 mg/l in both the epilimnion and hypolimnion. This differs from the University of Massachusetts study, which showed an increase (inverse clinogradef in both calcium and magnesium ions with depth. The silica concentration, however, was observed to increase from 0.9 mg/l in the surface waters to 2.3 mg/l at 45 feet. This is normal behavior for silica, since the growth of diatoms and higher oxygen levels tend to keep the concentration lower in the trophogenic zone. The Lily Brook inlet was found to be a definite source of silica to the lake, with a concentration of 3.6 mg/l. The outlet had a surprisingly high value of 2.2 mg/l silica. One might expect the outlet to be more in line with the surface water concentration of 0.9 mg/l.

44 DISSOLVED OXYGEN (mg / I)

f I-

TEMPERATURE (" F)

I. m111u)iII I III IIIIIII imi \D N .Ill .IIIIIlIIIIIIIII .I 0 0 N m N

m m m 3 \D NIIINIIII 11 1 1 1 1 1III IN1 3 4 31 1 1 - 1 I I I I I I I I 1I I1 I131 3 4

N N u) U r? 0 0 0 0 0 .Ill .IIIIIIIIIIIIIII - 1 01 I 1 0 1 I I I I I I I I 1I Ill 101 0 0

0 0 0 0 0 -1 1 1 .IIIIIIIIIlIIIII .I w 01 1 1 0 1 1 1 1 1 1 1 I I1 I I1 I101 0 0 H H W & m 3 m WN dr? 01 I 1 0 1 1 1 I I 1 I I I I I I1 I Id 1 HO w -111 .IIIIIIlIIIIIIII .I69 2. wn o 0 0 HO 00 I N m

L. m m N r- m 31 1 1 3 1 1 1 1 1 1 1 1 1 1II1 1 1 3 1 3 2 -1 1 1 4 1 1 1I 11 1 IIIII 1 1 1 3 1 3 3

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~I~V~IININI I ~ IIII I I I 1 .I ..*I I .I .I .I INlu-ll I Iml I I 3 0-N N N N 333 333 mu) 0

m~mmm00m~0000~mmu-l~mm~u-l ...... I I m--u~~mmm~owmu)\~\~u~~~mm.. I I ~~r.u)~u)mmmmmuuuuuuuduud

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47 Ammonia-nitrogen was 0.03 mg/l at the surface and 0.48 mg/l at 45 feet. Nitrate-nitrogen was undetectable at the surface, eight-, and 45-foot levels. Total phosphorus concentrations increased slightly with depth from 0.02 mg/l at the surface to 0.06 mg/l at 45 feet. These concentrations of nitrogen and phosphorus are considered high for lake water and contribute to eutrophication. Nitrate-nitrogen was undetectable in the inlet sample, whereas the total phosphorus concentration was 0.04 mg/l.

BIOLOGICAL

Phytoplankton

The phytoplankton sample (Table 6) from the deep hole station showed a far greater proportion of Cyanophyceae (blue-greens) than either Bacillariophyceae (diatoms) or Chlorophyceae (greens). Of the Cyanophyceae, Microcoleus sp. was by far the dominant genus, with some Aphanizomenon sp. present. In view of the adequate amount of silica present and the time of year (early summer), it is curious that a greater proportion of the phytoplankton were not diatoms as was found in the University of Massachusetts study. The dominant position of Micro- coleus sp., however, does agree with the University of Massachusetts study.

Zooplankton

In the zooplankton sample (Table 6 ), Cladocerons (Daphnia sp.) were most numerous, followed by Copepods (Canthocamptus sp., Cyclops sp.) and Rotifers (Kellicottia sp. and Keratella sp.). An interesting aspect of the zooplankton sample was the presence of Ceratium sp. and a huge number of Dinobryon sp., although neither was observed in the phytoplankton sample.

Macroinvertebrates

The deep hole station sampled for benthic fauna revealed only one type of organism, that being a Diptera (Chaoborus punctipennis). Ten of these phantom midges were found, despite the nearly complete absence of dissolved oxygen. Hydrostatic organs on their body allow these insect larvae to move about freely, where they migrate to upper levels of the lake in order to obtain oxygen. During these movements, they actively feed on microcrustacea, rotifers, and algae.

Aquatic Vegetation

The June survey found sp., Potamogeton crispus (pondweed), p. pectinatus and Nymphaea sp. (white water lily) all present in the littoral zone of the lake. Chars sp. was the dominant type followed by Potamogeton crispus. Accord- ing to the University of Massachusetts study, Myriophyllum sp. (milfoil) later becomes the dominant vascular plant in the lake. They also found Chars sp. and Potamogeton crispus very numerous in late summer. The distribution of these types in Stockbridge Bowl is presented in Figure 9.

IV. SUMMARY

On the basis of the baseline survey, earlier data (see Appendix B) and the Water

48 8. ..I. .* , .... ix :'.. Y-5 ,. . . A,.

s 3'

Olga 0seiUotak w. . DISTRIBUTION OF . AQUATIC VEGETATION JUNE IO, 1974 BARK€R W FIGURE 9

~~ ~

1- ~ 49 Resources Research Center study, Stockbridge Bowl is a eutrophic body of water. The baseline survey indicates an early and rapid loss of dissolved oxygen from the hypolimnion. It also indicates an increase of ammonia-nitrogen, phosphorus, and silica in the hypolimnion, most likely concomitant with the oxygen depletion. The Water Resource Research Center study further demonstrated an increase in calcium and magnesium in the hypolimnion. The baseline survey found that nitrate-nitrogen was undetectable at those depths sampled as well as at the inlet and outlet. The phytoplankton was dominated by the blue-green algae Microcoleus sp., which concentrates in the metalimion region. The lake's water is certainly hard and an aquatic vegetation problem exists in the littoral zone.

The Water Resources Research Center study states that enrichment of the lake's water followed shortly after development of the watershed. This is not surprising and definitely not unique to Stockbridge Bowl. At the present time, the major nutrient contributions appear to be non-point in origin. Future lake management planning will have to seriously face the problems of property zoning, fertilizer use, phosphate detergents, septic tank locations, street drains, and other known nutrient sources.

50 PoNToosuc -LAKE

PITTSFIELD-LANESBOROUGH

ITEM -PAGE 53 I. Introduction 53 11. Morphometric Data 53 111. Water Quality Data Chemical 57

Biological 61

Phytoplankton 61

Zooplankton 61

Macroinvertebrates 61 61 Aquatic Vegetation

61 I??. sunrmaly

51 PITTSFIELD- LANESBORO

FIGURE IO 52 PONTOOSUC LAKE

I. INTRODUCTION

Pontoosuc Lake is located in Berkshire County and lies divided between Lanes- borough and Pittsfield. The drainage basin of Pontoosuc Lake is shown in Figure 10. The lake is in a beautiful setting surrounded by many mountains. The lake's watershed touches the towns of Hancock, New Ashford, Cheshire, and Pittsfield, but it is mostly contained within Lanesborough. Pontoosuc Lake is enjoyed by more people than any other singular lake or pond in the Berkshires. The lake is a major attraction, both summer and winter, for such recreational activities as power and sail boating, ski-dooing, skating, swimming, auto racing, and, of course, fishing. The lake is a Great Pond and the Massachusetts Division of Fisheries and Game manages the lake for yellow perch and trout. There is a public boat ramp, beach, and access off Route 7.

Development around the lake is very dense and not confined to the immediate shoreline. There are several summer camps, a park, and commercial develop- ments such as Pontoosuc Gardens and Lakeview Terrace. In view of the extremely high density of development around the lake, it is not surprising that the water quality shows the lake to be in a eutrophic condition.

11. MORPHOMETRIC DATA

Morphometric data for Pontoosuc Lake are presented in Table 7 and Figure 11. The lake's long axis is oriented in a north-south direction with a maximum length of 8,050 feet (1.52 miles). The maximum width is nearly two-thirds its length, or 4,800 feet (0.91 miles). The lake's area is fairly large at 467 acres and has one major basin with a maximum depth of 35 feet. There are two small islands and several other erratic features in the southern section of the lake (see Figure 11). The mean depth for the lake is 14 feet, and the volume is 6,532 acre feet. The development of the shoreline and volume are 1.59 and 1.20, respectively. The drainage area for the lake is 21.35 square miles of mostly mountainous terrain in Lanesborough. Pontoosuc lake was the largest of the seven lakes surveyed in the Housatonic Basin during the 1974 sampling season.

The general soils description is shown in Figure 12. Most of the immediate drainage area is composed of moderately well drained limestone soils. The northern section contains some very poorly drained organic soils, mostly restricted to the inlet areas. There is also a section of well drained sandy and gravelly soils on the northern immediate watershed.

111. WATER OUALITY DATA The water quality data for Pontoosuc Lake indicate an early eutrophic condition. The locat,ion of sampling stations is shown in Figure 11. The northern inlets, located in swampy sections, were not sampled due to lack of flow. The water quality data are presented in Table 8 (chemical and physical), Figure 13 (temperature and dissolved oxygen profile), Table 9 (microscopical analysis), and Figure 14(aquatic vegetation map). The date of the survey,

53 FIGURE II

54 TABLE 7 PONTOOSUC LAKE

MORPHOMETRIC DATA

Maximum Length 8,050 feet

Maximum Effective Length 7,250 feet

Maximum Width 4,800 feet

Maximum Effective Width 4,800 feet

Maximum Depth 35 feet

Mean Depth 14 feet

Mean Width 2,806 feet 2 Area 467 acres (0.73 miles ) Volume 6,532 acre feet

Shoreline 25,400 feet (4.81 miles)

Development of Shoreline 1.59

Development of Volume 1.20

Mean to Maximum Depth Ratio 0.40 2 Drainage Area 21.35 miles

55 FIGURE 12

56 .: June 11, 1974, should be kept in mind because it represents an early stage in the lake's productive season and stratification period.

CHEMICAL Pontoosuc Lake was found to be stratified with the thermocline located between the 5- and 15-foot levels. This represents a rather shallow epilimnion; however, it would be expected to increase as the summer continued. That is, the thermocline would be driven downward as the upper waters increased in temperature. The dissolved oxygen profile was of the clinograde type, nearing anaerobic conditions on the bottom. Presuming the lake experienced a turnover in early spring, this would represent a high rate of oxygen demand in the hypolimnion. The oxygen profile also showed a metalimetic maximum (positive heterograde curve), probably caused by algal photosynthesis below the lake's surface.

The pH of the water was above neutrality at all depths, with a high of 9.2 at the surface. The alkalinity and hardness data indicate well-buffered, hard water in the lake. The surface and 10-foot depths showed phenolphthalein alkalinity (11.0 and 8.0 mg/l, respectively) indicative of carbonate alkalinity. These values for pH, alkalinity, and total hardness are typical for a lake with limestone soils in its watershed, which is the case for many of the Berkshire lakes.

The nutrient content of the surface waters (trophogenic layer) was found to be quite low, due in part to early summer biological activity (i.e., diatom growth). The ammonia-nitrogen was significantly higher (0.41 vs. 0.01 mg/l) at the bottom of the lake (tropholytic layer). This was due to the near- anaerobic conditions found at 32 feet. Ammonia-nitrogen accumulates as part of the end-products from bacterial decomposition of organic matter. Nitrate- nitrogen was undetected in the lake except for 0.01 mg/l at 32 feet. The data indicate that nitrate was being biologically utilized as fast as it was made available. Analysis of the other lakes in this report reveals similar nitrate uptake.

The silica (orthosilicate) also was found to have a higher concentration at 32 feet than in the surface waters (0.2 mg/l vs 5.0 q/l). This is not unusual for stratified lakes with an oxygen depletion in the hypolimnion (Soukup, 1974). Experimental studies indicate that this is regulated by redox potential, possibly by the reduction of ferric silicate previously formed in the superficial layers of mud when in contact with oxygenated water (Hutchinson, 1957). The lower concentration in the epilimnion was due to the development of a diatom bloom (often called a diatom pulse-see Table 9). Diatoms use silica in the formation of their frustules (skeletons).

Although phosphorus IS also known to accumulate in the hvDolimnion of lakes under low oxygen concentrations, in Pontoosuc Lake it was low both in the surface (0.01 mg/l) and bottom (0.03 mg/l) waters.

The secchi disc reading (measure of transparency) was 12 feet, coincident with the maximum of the positive heterograde oxygen curve (Figure 13).

57 DISSOLVED OXYGEN (mg /I)

w 035 30 35 40 45 50 55 60 65 70 75 TEMPERATURE F) TABLE 8

PONTOOSUC LAKE

WATER QUALITY DATA (mg/l)

STATIONS 1 & 2 - JUNE 11, 1974 DEPTH TEMP. D.O. pH TOTAL PHTH. NH -N N03-N TOTAL TOTAL SILICA 3 (feet) OF ALK . ALK . P HARD.

STATION 1 - DEEP HOLE

Surface 68.0 10.0 9.0 2 68.0 10.0 9.2 4 67.0 __ __ 6 66.0 10.1 9.0 62.5 __ __ 60.0 11.1 8.8 12 58.0 -- -_ 14 55.5 11.4 9.0 16 52.5 __ -- 18 51.0 8.5 __ 20 50.0 __ __ 22 49.0 8.0 8.0 24 48.0 _- __ 26 47.5 __ __ 28 47.5 3.5 __ 30 46.5 __ __ 32 46.5 0.5 7.6

STATION 2 OUTLET

Mid-depth 74.0 10.1 8.8 12 0.02 0.0 0.02 0.2 TABLE 9

PONTOOSUC LAKE

MICROSCOPIC EXAMINATION

STATION 1

June 11, 1974

PHYTOPLANKTON AND PROTOZOA^ ZOOPLANKTOK’

ALGAE CLADOCERONS

Bacillariophyceae 3,865 Bosmina common

Cyanophyceae 50 Daphnia occasional

Chlorophyceae 260 Diaphanosoma occational m 0 PROTOZOA COPEPODS

Sarcodina -- Diaptomus common Mastigophora -- Cyclops common Infusoria 5 ROTIFERS

1Expressed in Areal Standard Units/ml. P loesoma very common

Testudinella common ’Relative frequency of genus in field;perCent: 60-100 ...... abundant Kellicottia occasional 30-60 ...... very common 5-30...... common Platyias occasional 1-5 ...... occasional

(I ...... rare Conochilus occasional An oxygen curve such as this is normally produced by a concentrated band of algae. The algae would, to some degree, also impede light transmission. BIOLOGICAL

Phytoplankton

The phytoplankton data for Station 1 are presented in Table 9. At the time of the survey, Pontoosuc Lake was experiencing a diatom bloom, which is normal for lakes in late spring or early summer. The bloom consisted mainly of Fragilaria sp. and, to a lesser extent, Tabellaria sp. This bloom was the cause of the oxygen maximat 15 feet. Also present were green and blue-green algae. Following the diatom bloom, the green and blue-green algae would be expected to increase rapidly.

Zooplankton

Cladocerons. Copepods, and Rotifers were all present in the zooplankton sample from Station 1. Of the Cladocerons, Bosmina sp. was most numerous, while the Copepods were represented by Diaptomus sp. and Cyclops sp. Rotifers were very numerous, with Ploesoma sp. being very common.

Macroinvertebrates

There were a total number of 26 Diptera (Chaoborus punctipennis) larvae found in Pontoosuc Lake in June. As was mentioned previously, these phantom midge migrate from the oxygenless profunda1 regions to upper levels of the lake to obtain oxygen and food.

Aquatic Vegetation

Aquatic vegetation was very ah-undant in Pontoosuc Lake during the June sampling. The distribution can be seen iq PFgure 5. Particularly abundant plants were pondweed (Potamogeton crispus) and water milfoil (Mydophyllum sp.). Very knse growths of these types occurred throughout the’cove and littoral areas of the lake. Yellow water lily (Nuphar varlegatum) and stonewort (gsp.) were also foid during the study, although they were both very sparsely distributed.

IV. SUMMARY The baseline survey on June 11, 1974, of Pontoosuc Lake revealed some of the classic symptoms of eutrophy. Although it was only early June, the bottom hypoliumion showed 0.5 mg/l dissolved oxygen. The situation undoubtedly grew progressively anaerobic as che summer.stagnation period continued.

The lake’s littoral or s’hore zone was plagued with heavy aquatic plant growth.

61 62 Pondweed and milfoil were the dominant types at the time of the survey. Wide- spread plant growth can cause nuisance conditions from an aesthetic and recreational point of view.

The phytoplankton data revealed a vernal diatom pulse. The dominant diatoms were Fragilaria sp. and Tabellaria sp., with Asterionella sp. also present. It is known from personal communications and public complaints that the algae shifts to green and blue-green genera during the summer, causing unsightly conditions.

Pontoosuc Lake is otherwise a typically well-buffered, hard water lake in the Berkshire region. The lake's surrounding watershed is very heavily developed. The major contributing cause to the accelerated cultural eutrophication is believed to be non-point in origin. There are no known point waste discharges to the lake or its tributaries. It is suggested that the process of eutrophication will continue unless lakeshore and watershed management undertakes to control the non-point sources of pollution.

It should be mentioned that on the basis of the baseline survey, heavy recreational use, and public interest, Pontoosuc Lake has been selected for intensive study during 1975-1976.

63 LAUREL LAKE LEE-LENOX

ITEM -PAGE

I. Introduction 66

I€. Morphometric Data 66

111. Water Quality Data 70 70 Chemical 74 Biological 74 Phytoplankton 74 Zooplankton 74 Macroinvertebrates 74 Aquatic Vegetation 76 IV. summary

64 G ENERAL WATERSHED

0 mm LAUREL LAKE -FEET LEE and LENOX

FIGURE 15 65 LAUREL LAKE

I. INTRODUCTION

Laurel Lake straddles the town line between Lenox and Lee in Berkshire County. Its watershed lies mostly in those two towns, with only a minor fringe touch- ing on the Town of Stockbridge (see Figure 15). The drainage area is quite small (2.68 square miles) and borders the Stockbridge Bowl drainage area to its west and Woods Pond drainage area to the north. The outlet stream flows less than a mile into the Housatonic River in Lee.

The lake is classified as a Great Pond and has a public access area off Route 20. It experiences moderate recreational use, mainly swimming, boating, and fishing. The Massachusetts Division of Fisheries and Game annu- ally stocks the lake with rainbow trout, and the bass fishing is also good. The lake is developed mainly along its northern shore, where some thirty dwellings are located. The south and west shorelines are, for the most part, totally undeveloped. A breakdown of the watershed has been done by Soukup (1974) who reports the area as 51%forest, 32% farmland, and 17% residential.

Laurel Lake, although comparatively undeveloped with other lakes in the Housatonic River Basin, is showing signs of eutrophy. Drainage from farmland and leaching from subsurface sewage systems have contributed to this situation. During the height of the summer, however, the lake is enjoyed by swimmers and boaters without a great deal of complaint.

The lake level is enhanced by a dam constructed by the Schweitzer Paper Com- pany, which also controls the lake level (Soukup, 1974). In addition to a spillway, the paper company controls a 12-inch intake pipe at the outlet.

11. MORPHOMETRIC DATA

Morphometric data for the lake are presented in Table 10 and Figure 16. The lake's long axis runs in an east-west direction. The maximum effective length, or longest wind fetch, is about 4,550 feet. The depth contours found in Figure 16have been drawn from that of Soukup, 1974. Likewise, some of the morphometric data have been taken from that same report. The lake has three shallow coves and the depth contours are fairly concentric with the lake's shoreline. The lake has a centrally located maximum depth of 53 feet and a mean depth of 26 feet. The development of volume index (1.46) and the mean to maximum depth ratio (0.49) indicate a regular rate of depth increase as regards the volume and surface area of the lake. Although the lake is rather small (165 acres), it has a volume of 4,310 acre feet, due to its morphometry.

A general soils map for the lake's immediate watershed has been included in Figure 17. There are five major soil types located around the lake, with limestone, bedrock, and stony soils predominant. Most of these soils appear to have good drainage characteristics.

66 LOCATION OF w SAMPLING STATIONS

(contour interval- five feet)

01 U

LAUREL LAKE. LEE and LENOX 165 ACRES

.J . . TABLE 10 LAUREL LAKE

MORPHOMETRIC DATA

Maximum Length 5,300 feet

Maximum Effective Length 4,550 feet

Maximum Width 2,450 feet

Maximum Effective Width 2,450 feet

Maximum Depth 53 feet

Mean Depth * 26 feet

Mean Width 1,356 feet

Are& 165 acres

Volume * 4,310 acre feet

Shorelin& 16,040 feet

Development of Shoreline * 1.7 1.46 Development of Volume* 0.49 Mean to Maximum Depth Ratio 2.68 miles 2 Drainage Area

*Source: Soukup, M. Dissolved Silica in Laurel Lake: Influx, Uptake, and Differential Accumulation During Summer Stratification. Water Resources Research Center, University of Massachusetts, Amherst, 1974.

68 GENERAL SOIL MAP

KEY TO WATERSHED SOIL TYPES

0 1ooomJa LAUREL LAKE -Feet LEE and LENOX FIGURE 17 69 111. WATER QUALITY DATA

The August baseline survey on Laurel Lake revealed that the lake is undergoing nutrient enrichment. Location of the sampling stations is shown in Figure 16 . The water quality data for the August 6, 1974, survey are presented in Tables 11 and 12 and in Figure 18.

CHEMICAL

The deep hole station was located near the center of the lake with a 53-foot maximum depth. On August 6 the lake was strongly stratified (see Figure 18) with the thermocline located between 10 and 25 feet, The oxygen profile was clinograde or, more precisely, positive heterograde. This means the lake showed its maximum oxygen concentration in the metalimnetic region and was anaerobic in the hypolimnion. The day of the survey was sunny and calm, and the lake showed a secchi disc transparency of 12 feet at Station 1.

The total alkalinity and hardness data from Station 1 showed that the lake water was well buffered and hard. Carbonate alkalinity was present at the 5- and 20-foot levels, as indicated by the phenolphthalein alkalinity. The pH of the surface water was high at 8.4 and was 7.7 at 50 feet.

Sargent Brook inlet, which drains through limestone soil, had a very high pH of 9.3, a phenolphthalein alkalinity of 22 mg/l, and a total hardness of 94 mg/l. Another indication of the high alkalinity and hardness of the water was the presence of calcium carbonate on some floating, emergent, and submerged aquatic vegetation.

The silica profile showed a minimum concentration at 20 feet (0.4 mg/l) and a maximum at 50 feet (3.5 mg/l). The low concentration at 20 feet was due to diatom metabolism and growth.

The nutrient concentrations showed a slight accumulation of ammonia-nitrogen and total phosphorus in the anaerobic hypolimnion. The concentrations of these two nutrients was low in the upper layers (0.02 mg/l). As was found with some of the other Berkshire lakes, nitrate-nitrogen was undetectable at all depths sampled and at Sargent Brook inlet and the outlet. It would appear that of those nutrients measured, nitrate was perhaps the limiting nutrient, although the evidence for this is not conclusive.

During the sampling procedure, hydrogen sulfide was detected by smell at the 50-foot depth. This was another indication of anaerobic conditions on the lake bottom. Manganese and iron were also tested for at the %-foot level and were found present at concentrations of 1.20 and 0.33 mg/1, respectively. Under anaerobic conditions these two metals, along with ammonia-nitrogen, phosphorus, and silica, often accumulate over surface level concentrations. Soukup (1974), who studied the 1972 silica cycle in Laurel Lake, found concentrations of around 5 mg/l on the lake's bottom during anaerobic periods. The release from sediments and sedimentation from surface waters of various dissolved chemical species was reflected in a higher specific conductivity in the hypolimnion of 370ymho/cm as compared to 300&mho/cm in the surface waters.

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73 BIOLOGICAL

Phytoplankton

The dominant sector of the phytoplankton found in Laurel Lake was the blue- green algae (Cyanophyceae). These were mostly Gomphosphaeria sp., Anabaena sp., and Microcystis sp. Green algae (Chlorophyceae) were also present, dominated by Protococcus sp. and Phacus sp. Although not counted during the analysis, the diatom (Bacillariophyceae) Melosira sp. was identified as being present.

Ceratium sp. (Mastigophora) was also present in the phytoplankton sample. Despite this flagellate's rather low count of 60 a.s.u./ml in the phytoplankton sample, it was identified as being very numerous in the zooplankton sample. Zooplankton

Cladocerons, Copepods, and Rotifers were all present in healthy numbers in Laurel Lake. The Cladocerons were dominated by Daphnia a?.; the Copepods were dominated by Diaptomus sp. and Cyclops sp.; and the Rotifers were completely dominated by Brachionus sp. During the analysis, many of the Copepods were observed with egg sacs and there were many loose eggs in the sample.

Macroinvertebrates

There were no benthic fauna found at the deep hole station in Laurel Lake during the August study.

Aquatic Vegetation

As mentioned earlier, the lake has three shallow areas. These coves were all found to bear very heavy aquatic plant growth, with minor growth around the remainder of the lake (see Figure 19). The dominant plants were of two types, milfoil (Myriophyllum sp.) and pondweed (Potamogeton robbinsii). These two plants were intermixed and very abundant, especially in the north and west coves. Other aquatic vegetation identified was smartweed (=- gonum natans), bushy pondweed (+ sp.), and wild celery (Vallisneria americana). The aquatic vegetation, especially the milfoil, was oaserved to be encrusted with a coating of calcium carbonate. This lent an off-white appearance under the water and gave it a brittle feeling to the touch. This phenomenon is known as biogenic calcium carbonate precipitation and is caused by the aquatic vegetation itself through photosynthesis in hard, alkaline water. Chemically, it may be represented as the following:

Ca(HC03)2-) CaC03 + H20 + CO2 Increased growth of the aquatic vegetation over Laurel Lake will not occur to any appreciable extent due to either unfavorable substrate or the water depth. Portions of the shore are too rocky, and the remainder of the open water in the lake is too deep to afford growth of the rooted aquatics.

IV. SUMMARY Laurel Lake is a rather small (165 acres) but deep (53 feet) lake in Berk- shire County. Its shoreline includes three major coves which support very heavy and thick aquatic vegetation growth during the summer. The lake's hypolimnion becomes anaerobic during the summer with hydrogen sulfide genera- tion and nutrient accumulation occurring. The phytoplankton during August was dominated by blue-green algae, although not in nuisance quantities. Secchi transparency during August was measured at 12 feet. The lake water is typical of the Berkshire lakes in that it is hard and alkaline. An interesting result was the undetectable concentration of nitrate in the lake water and the inlets.

Laurel Lake is experiencing a period of enrichment and shows the beginning signs of eutrophication. This conclusion is in agreement with Soukup (1974). It should be pointed out that the lake is still fairly undeveloped and the lake water remains acceptable for swimming throughout the summer months. The only inconvenience is the extensive aquatic vegetation in tne shallow regions.

76 LAKE BUEL

MONTEREY - NEW MRLBOROUGH -ITEM PAGE 79 I. Introduction 79 11. Morphometric Data 83 111. Water Quality Data 83 Chemical 89 Biological 89 Phytoplankton 91 Zooplankton 91 Macroinvertebrates 91 Aquatic Vegetation 93 IV. Summary

77 U m LAKE BUEL

I. INTRODUCTION

Lake Buel is located in the southwest corner of Monterey with its southern end extending into New Marlborough near Hartsville. The small watershed (3.89 square miles) is spread over three towns: Monterey, Great Barrbngton, and New Marlborough (the latter to only a minor extent; see Figure 20). The lake is classified as a Great Pond and has a public access located off Route 57 on its northwest shore. The perimeter of the lake is densely crowded with houses and summer cottages except near the outlet and inlet, where swampy conditions apparently prevent construction. This development extends back farther than the immeduate shoreline. The Massachusetts Division of Fisheries and Game manages the lake for rainbow trout. Bass, yellow perch, and pickerel fishing also exists. During the summer season, the lake experiences very heavy recreational use, with boating heading the list. Lake Buel also has the distinction of having a portion of the Appalachian Trail cross the northwest corner of its drainage basin. Northeast of Lake Buel about one-half mile is Stevens Pond (44 acres) which drains into it via an unnamed brook (here called Stevens Brook). Stevens Pond has a very small drainage area of 264 acres.

The outlet of Lake Buel flows almost immediately into the Konkapot River, a tributary of the Housatonic River. The drainage basin of the lake is mostly forested with conifers and mixed hardwood vegetation. There are some nine farms located throughout the watershed, two of which are within the drainage of Stevens Pond. According to McCann and Daly (1972), Stevens Pond is a private lake with no public right-of-way.

During the August baseline survey, the water quality of Lake Buel did not appear degraded. Despite its general appearance, however, the chemical and biological data indicate a mesotrophic-eutrophic condition. Because of the absence of sewering and the peripherally dense development around the lake, it is expected that the lake will experience continued enrichment. Dense aquatic growth in the littoral areas exists and restricts recreational activities to some extent.

11. MORPHOMETRIC DATA

Morphometric data for Lake Rue1 are presented in Table 13 and Figure 21. The lake's long axis is oriented in a northeast-southwest direction and the maximum length is 6,900 feet (1.3 miles). The lake is composed of two separate basins located at the northeast and southwest ends of the lake (see Figure 21). The northeast basin is the deeper of the two, with a maximum depth of 43 feet; the southwest basin is about 33 feet deep. The center stretch of the lake has a fairly shallow depth of 5-10 feet. The mean depth for the whole lake is 17 feet, and the mean width is 1,225 feet. Lake Buel has an area of 194 acres, which is comparable to Laurel Lake's 165 acres. Due to the shallow

79 LOCATION OF I SAMPLING STATIONS 0 500 lo00 1 FeSt and

- ''LAKE~ BUEL MONTEREY and NEW MARLBOROUGH

194 ACRES

FIGURE 21

80 TABLE 13

LAKE BUEL

MORPHOMETRIC DATA

Maximum Length 6,900 feet

Maximum Effective Length 6,900 feet

Maximum Width 2,100 feet

Maximum Effective Width 2,100 feet

Maximum Depth 43 feet

Mean Depth 17 feet

Mean Width 1,225 feet

Area 194 acres

Volume 3,284 acre feet

Shoreline 17,500 feet

Development of Shoreline 1.7

Development of Volume 1.20

Mean to Maximum Depth Ratio 0.40 2 Drainage Area 3.9 miles

81 MONTEREV and NEW MARLBOROUGH mid-section, Lake Buel's volume is 3,284 acre feet, or about 1,000 acre feet less than Laurel Lake. The development of shoreline is 1.7 (same as Laurel Lake), and the development of volume is 1.20.

The general soils map (Figure 22) shows predominantly well drained soils in the lake's watershed. Only the northern inlet is composed of poorly drained mineral soils. The soils map also shows the absence of limestone soils, with most of the area composed of bedrock soils and sandy, gravelly, or stony soils.

111. WATER QUALITY DATA

Because of the morphology of the lake, two central stations were established in each of the main basins. The location of these stations and the inlet- outlet stations are shown in Figure 21. The water quality data are presented in Tables 14 and 15 (physical and chemical), Tables 16 and 17 microscopic analysis), Figures 23 and 24 (temperature and oxygen profiles), and Figure 25 (aquatic vegetation).

CHEMICAL

The two surface stations compared favorably with each other, and thus the major discussion will cover both stations. Although not identical, due to maximum depth differences, the temperature profiles indicated strong stratification. The thermocline was located between the 10- and 20- or 25-foot levels (see Figures 23 and 24). Both stations had clinograde oxygen profiles, tending toward anaerobic conditions on the bottom. Station two indicated a metalimnetic oxygen maximum (called positive heterograde) due to algal photosynthesis. The oxygen data indicated a high oxygen demand in the hypolimnion (see Tables 14 and 15).

The secchi disc reading was 9 feet at both ends of the lake. This indicated a rather high turbidity and low transparency.

The pH was between 7.8 and 8.6 in the surface waters and around 7.4 on the bottom. The alkalinity and hardness were high, showing well buffered, hard water which is the norm for the Berkshire lakes. Station 2 had a phenolphthalein alkalinity of 1.0 mg/l at the surface, which suggested the presence of carbonate alkalinity.

The ammonia-nitrogen data showed only trace amounts in the surface waters with accumulation in the hypolimnion (0.95 mg/l at Station 1). Nitrate- nitrogen was undetectable at all depths as well as at both inlets and the outlet. This curious phenomenon was also observed at Laurel Lake, Lake Garfield, Stockbridge Bowl, Lower and Upper Goose Pond, and Pontoosuc Lake, except for 0.1 mg/1 observed at 32 feet in the latter lake.

Total phosphorus was 0.02 mg/l in the surface waters of Lake Buel, with accumulation of up to 0.16 mg/l in the hypolimnion (Station 1). This accumulation of phosphorus and amonia-nitrogen in the near-anaerobic bottom is caused by a combination of sedimentation, bacterial degradation, and release from the sediments.

83 DISSOLVED OXYGEN (mg / I) TABLE 14

LAKE BUEL

WATER QUALITY DATA (mg/l) STATION 1 - AUGUST 7, 1974

SPEC. DEPTH TEMP. D.O. pH TOTAL PHTH. NH3-N N03-N TOTAL TOTAL SILICA COND. Mn Fe (ft.) OF ALK. ALK . P HARD UmhO 1Cm Surface 71.0 -- -- _------_

5 71.0 8.8 7.8 0.02 3.0 240 0.02 0.04 lo 71.5 -- __ 15 61.5 9.1 --

20 51.0 9.0 8.2 0.02 4.0 250 0.03 0.03 m Ln 25 47.0 4.2 -- __

30 43.0 0.2 --

35 41.5 0.6 -- -_ _- ______

40 41.0 0.3 7.2 0.16 9.4 260 1.30 0.22 DISSOLVED OXYGEN (mg /I)

. . TABLE 15

LAKE BUEL

WATER QUALITY DATA (mg/l) STATIONS 2, 3, 4, & 5 - AUGUST 7, 1974

~~ ~~ SPEC. DEPTH TEMP. D.O. pH TOTAL PHTH NH3-N N03-N TOTAL TOTAL SILICA COND. Mn Fe (feet) OF ALK . ALK . P HARD. umho/cm. STATION 2 - DEEP HOLE Surface 74.0 -- __ __ -_ __ ------_- __ __

5 74.0 9.4 8.6 112 1.0 0.01 0.0 0.02 109 2.8 215 0.04 0.02

lo 73.0 8.8 ------______- ______15 67.0 10.1 ______-_ -- -- m -- ______u 20 57.0 6.6 7.8 126 00 0.01 0.0 0.04 119 5.4 235 0.06 0.04

25 51.0 1.6 ------______30 49.5 1.3 7.5 108 __ 0.34 0.0 0.10 121 8.2 240 0.85 0.12

STATION 3 - NORTH INLET Mid-dep th 77.0 13.0 8.0 122 ___ 0.04 0.0 0.05 135 7.6 270 -- -- STATION 4 - STEVENS POND INLET Mid-depth 76.0 12.5 7.6 107 __ 0.00 0.0 0.05 114 2.0 215 -- --

STATION 5 - OUTLET Mid-dep th 77.0 9.7 8.3 100 __ 0.02 0.0 0.11 104 2.6 205 -- -- TABLE 16

LAKE BUEL

MICROSCOPIC EXAMINATION

STATION 1 - AUGUST 7, 1974

PHYTOPLANKTON AND PROTOZOA 1 ZOOPLANKTON2

ALGAE CLADOCERONS Bacillariophyceae 265 Bosmina occasional

Cyanophyceae 150 Daphnia very common

Chlorophyceae 18 Ceriodaphnia abundant

m PROTOZOA COPEPODS m Sarcodina ___ Diaptomus abundant

Mastigophora 198 Cyclops common 3 Infusoria _-_ Nauplius occasional

ROTIFERS none ‘Expressed in Areal Standard Units/ml.

2Relative frequency of genus in fields; percent: 60-100 ...... abundant 30-60 ...... very common 5-30 ...... common 1-5...... occasional < I...... rare 3 Immature Copepod stage. Silica was found to be plentiful in the surface waters (3.0-5.0 mg/l) and also showed accumulation in the hypolimnion (9.4 mg/l at Station 1). The north inlet water was found rich in silica with 7.6 mg/l. Lake Buel definitely possessed an adequate supply of silica for diatom growth. This was also the case in the other Berkshire lakes included in this report.

Manganese and iron were shown to have high concentrations in the hypolimnion relative to the epilimnion. Under very low oxygen concentrations (reducing concentrations) these chemical species are reduced to a soluble form. Under these conditions they are released from the sediments and accumulate in the overlying water, sometimes to a high degree. At Station 1 in Lake Buel, the manganese concentration (manganous ion) was 1.30 mg/l and the iron (ferrous ion) was 0.22 mg/l. Normally, because of its chemical properties, the ferrous ion is released ahead of the manganous ion and is usually found in a higher concentration. In Lake Buel, however, hydrogen sulfide was present in the hypolimnion (detected by smell). When hydrogen sulfide comes in contact with ferrous iron, ferrous sulfide is formed which quantitatively precipitates out of the system. For this reason, manganese was found in higher concentrations than iron at both stations in Lake Buel. In fact, with hydrogen sulfide present in the bottom waters of Lake Buel, it was surprising to find even 0.22 mg/l iron. Although manganous sulfide can also be formed and precipitate out, it does so only under a very high manganous ion concentration. This same situation occurred in Laurel Lake where manganese was found in a higher concentration than iron in the presence of hydrogen sulfide (see Laurel Lake, Table 11).

The specific conductivity was rather high and increased slightly from surface to bottom (240 VS. 260 umholcm).

Of the two inlets, the north end brook showed higher concentrations in all chemical parameters measured except for total phosphorus, which was equal to Stevens Brook inlet (0.05 mg/l). In neither case was there evidence of contamination. The data for the outlet was similar to the 5-foot depth data at Stations 1 and 2 except for a high phosphorus concentration of 0.11 mg/l.

BIOLOGICAL

Phytoplankton

The phytoplankton data (see Tables16 and 17) showed a high diversity of types present. Both lake stations were found very similar in their phytoplankton content. At each station there were high numbers of Bacillariophycea (diatoms), Cyanophyceae (blue-green algae), Mastigophora (flagellates), and a smaller number of Chlorophyceae (green algae).

Important in terms of water quality were the blue-green algae. The dominant genera at each station were Anabaena sp. and Aphanizomenon sp. Station 2 also had a high count of Microcystis sp. Also, although unobserved in the phytoplankton sample, the zooplankton sample showed a high number of Lyngbya sp. present at both stations. This filamentous blue-green algae has been known to cause nuisance conditions in many lakes. TABLE 17

LAKE BUEL

MICROSCOPIC EXAMINATION

STATION 2 - AUGUST 7, 1974

2 PHYTOPLANKTONAND PROTOZOA^ ZOOPLANKTON

&GAE CLADOCERONS Bacillariophyceae 118 Bosmina occasional

Cyanophyceae 295 Daphnia very common

Chlorophyceae 24 Ceriodaphnia abundant

PROTOZOA COPEPODS Sarcodina Diaptomus abundant

10 0 Mastigophora Cyclops very common 3 Infusoria Nauplius common

ROTIFERS none

'Expressed in Areal Standard Units/ml. 'Relative frequency of genus in fields; percent; 60-100 ...... abundant 30-60 ...... very common 5-30 ...... common 1-5 ...... occasional

31mature Copepod stage. The diatom genus Fragilaria was numerous at both stations, and the dominant green algae were Protococcus sp. The flagellates were represented by Cera- -tium sp., Dinobryon sp., Mallomonas sp., Peridinium sp., and Phacus sp.

Lake Buel was shown to have diverse, well-represented flora. Stevens Pond inlet (Station 4), which was channeled inland so as to give boating access to several dwellings located off-shore, was almost completely covered with filamentous algae. The water quality appeared degraded, probably from subsurface sewage system contamination. There were many gas bubbles apparent under the filamentous algae, due to gas formation under anaerobic conditions.

It should be noted that the phytoplankton data for Lake Buel were conserva- tive because the analysis noted the apparent dying-off of the algae. This was due to a 24-hour lag time between collection and analysis.

Zooplankton

The zooplankton data for Stations 1 and 2 are shown in Tables 16 and 17. Both Cladocerons (water fleas) and Copepods were abundant, while the Rotatoria (rotifers) were unobserved at both stations. The Cladocerons were dominated by Ceriodaphnia sp. and the Copepods by Diaptomus sp. Some immature Copepods (nauplius) were also common. The zooplankton data for Stations 1 and 2 were very similar as they also were for the phytoplankton data. An interesting observation was the presence of the blue-green algae Lynnbya sp. in the ZOO- plankton sample but not in the algae sample.

Macroinvertebrates

Station 1 in Lake Buel revealed one Diptera larva (Family Chironomidae). There were no benthic fauna found at Station 2 during this study.

Aquatic Vegetation

The aquatic vegetation data gathered from the perimeter survey of Lake Buel are presented in Figure 25. The macrophytes around Lake Buel were extremely dense, with many genera represented. The small coves along the north shore were especially crowded with plants. With so many types and numbers of plants, it becomes difficult to accurately represent them on a map. The map should thus be considered a general representation rather than a specific guide.

The most widespread genera include Myriophyllum sp. (water milfoil), 3- charis sp. (Elodea or waterweed), Nymphaea sp. (white water lily), Nuphar sp. (yellow water lily), Brasenia sp. (watershield), and Potamogeton sp. (pondweed). Also present in dense patches were Pontederia sp. (pickerelweed), Ceratophyllum sp . (coontail), and sp. (bushy pondweed).

Both inlets were choked with aquatic plant growth. In addition to those plants noted in Figure 25, the north inlet was blanketed with duckweed (m sp.). As mentioned in the phytoplankton section, Stevens Pond inlet had dense growths of filamentous algae. Cattails, bur reeds, and bulrushes were also scattered around the lake's perimeter.

91 TRlBUTlO AQUATIC VEGET I AUGUST 7,

LAKE BUEL MONTEREY and NEW MARLBOROUGH

194 ACRES

FIGURE 25

92 IV. SrnY Lake Buel is composed of two major basins connected by a shallow central region. The water quality of both basins was found to be similar. On the basis of those parameters measured, Lake Buel can be said to be undergoing eutrophication. Although nutrient levels were not excessive, other parameters indicated enrichment. At the time of the survey (August 1974), most of the available nutrients were tied up in the biomass.

Lake Buel showed near-anaerobic bottom conditions with the concomitant release and accumulation of various chemical species from the bottom sediments in the two basins (see Tables 14 and 15). The water in Lake Buel was both hard and alkaline with above neutral pH values.

Phytoplankton was abundant and diverse at both stations sampled. Several blue-green algae types were present and well established. The future problem of nuisance blue-green algal blooms is a possibility.

Most noticeable to the recreational observer, however, would be the luxurious aquatic vegetation growth along the littoral areas of the lake. In places it was very dense with several species intermixed. Increased growth may be expected except where excessive depth inhibits the rooted aquatic plants.

The absence of nitrate-nitrogen at all depths and stations sampled was noteworthy but not peculiar to Lake Buel in the Housatonic Basin.

Despite the foregoing summary, Lake Buel at the time of the survey was experiencing heavy recreational use, especially boating. The actual appearance of the water quality was not bad. It is believed that the major cause for the water's enrichment is the peripheral development around the lake. There are no known point waste discharges. Faulty subsurface sewage systems contribute to the degradation of the water quality. This is especially noticeable in the artificial canals at Stevens Pond inlet where dense filamentous algal growth was observed.

93 LAKE GARFIELD

MONTEREY

-ITEM -PAGE 96 I. Introduction 96 I€. Morphometric Data 96 111. Water Quality Data 99 Chemical 99 Biological 99 Phytoplankton 99 Zooplankton 99 Macroinvertebrates 99 Aquatic Vegetation 105 IV. sunwlary

LAKE GARFIELD I. INTRODUCTION

Lake Garfield is located in Berkshire County. The lake and its drainage area (3.62 square miles) lie entirely within the bounds of the Town of Monterey. The lake watershed is headwaters of the 61.30 square-mile Konkapot River Basin, a large tributary stream to the Housatonic River. The lake is used for a variety of recreational activities including boating, fishing, ice fishing, swimming, and camping. There are three summer camps, a public beach, and portions of the Beartown State Forest located within the lake's watershed. The Massachusetts Division of Fisheries and Game periodically stocks the lake with trout. Fishing pressure is moderate to high with warm water species dominating the creel.

Degradation of water quality in Lake Garfield appears to be from failing subsurface sewage systems by individual homeowners. Evidence of this stems from the August baseline study in which heavy growths of rooted aquatic vegetation and filamentous algae were found near concentrations of dwellings on the lake.

11. MORPHOMETRIC DATA

Morphometric data are presented in Table 18 and Figure 27. Lake Garfield is a 262-acre lake having a maximum depth of 31 feet. Mean depth is 16 feet, and the lake has a volume of 4,150 acre feet. The watershed is mostly forested and the banks of the lake are relatively steep.

Lake Garfield is of glacial origin, having formed during the last period of glaciation which left Berkshire County between 10 and 12 thousand years ago. The lake watershed is underlain by three major bedrock types: gneiss (granite biotite gneiss with some micaceous schist and quartzite), quartzite (quartzite, quartzite conglomerate, feldspathic quartzite, and some mica schist), and carbonate rocks (limestone, dolomite, and marble).

There are six major soil areas located within the lake watershed (see Figure 28 ). The till is a heterogeneous mixture of clay, silt, sand, gravel, and boulders deposited directly by the glacial ice. The general characteristic which is common to most of these soil types is that they are well drained and stony and most of them have hardpan layers which have a moderately slow peme- ability that restricts the downward movement of water.

111. WATER QUALITY DATA

In general, water quality and biological data collected in Lake Garfield indicate the lake to be in an early eutrophic condition. The location of sampling stations can be seen in Figure 27. Complete chemical and biological data on Lake Garfield for the August baseline survey are presented in Tables 19 and 20 and Figures 29 and 30.

96 LOCATION OF SAMPLING STAT1ON S and BATHYMETRIC MAP (contour interval- five feet)

-Contour A Sample Stution

0 500 1000 i feet TABLE 18

LAKE GARFIELD MORPHOMETRIC DATA

Maximum Length 9,200 feet

Maximum Effective Length 7,900 feet feet Maximum Width 3,000

Maximum Effective Width 3,000 feet

Maximum Depth 31 feet

Mean Depth 16 feet

Mean Width 1,240 feet

Area 262 acres

Volume 4,150 acre feet

Shoreline 24,000 feet

2.0 Development of Shoreline Development of Volume 1.5

Mean to Maximum Depth Ratio 0.52 2 Drainage Area 3.62 miles

98 CHFNICAL

Station 1 was located at the deep hole on the eastern end of the lake. The temperature and oxygen concentrations for this station are graphically presented in Figure 29. As can be seen, the lake was in a state of stratification at this time. A strong thermocline extended from approximately 15 feet to 25 feet during the August sampling. Dissolved oxygen concentrations ranged from 9.1 mg/l at a depth of 5 feet to a low of 0.2 mg/l at the 30-foot level. Total hardness and alkalinity values indicate the lake to be of moderately soft water origin. Nutrient concentrations were generally low at all sampling stations, including both the inlets and the outlet. Particularly interesting was the complete absence of nitrate-nitrogen from all the samples, a phenomenon common to several lakes in the Housatonic Basin. There is one significant point which should be mentioned. At the 30-foot level at the deep hole station, ammonia-nitrogen and total phosphorus concentrations increased significantly, indicating the nutrients were accumulating in the bottom layer of the lake. The accumulation of silica also occurred here.

BIOLOGICAL Phytoplankton

Phytoplankton samples from Lake Garfield showed significant numbers of diatoms (Bacillariophyceae) and blue-green algae present during the August study. Most abundant were the blue-greens (Cyanophyceae) which were dominated by Anabaena sp., Lyngbya sp., Microcystis sp., Aphanizomenon sp., and Oscilla- toria sp. Many diatoms were also abundant. Some of these included Tabellaria sp., Synedra sp., Navicula sp., and Melosira sp. There were two "blooms" noted in the samples, the blue-green Anabaena sp. and the diatom Synedra sp. In general, most of the phytoplankton collected are considered indicators associated with enriched water.

Zooplankton

Cyclops sp. was the most common zooplankton type collected in Lake Garfield during August. Another Copepod, Diaptomus sp., was also very common. Among the Rotifers, Ploesoma sp. and Kellicottia sp. were common. Ceriodaphnia sp. and Daphnia sp. were representatives of the relatively small numbers of Cladocerons collected.

Macroinvertebrates

There were only two types of benthic organisms collected at the deep hole station in Lake Garfield. The phantom midge larvae (Chaoborus punctipennis) and aquatic worms (Tubifex tubifex) were found in relatively small numbers. Both types are able to survive under anaerobic conditions.

Aquatic Vegetation

Aquatic vascular vegetation was abundant in Lake Garfield during the August

99 i DISSOLVED OXYGEN (mg /I)

TEMPERATURE (OF) r. m m rD N u) 3 3 r. 4 3 TI

N m -3 U .D N m m 3 m m 0 3 3

N N N N N N -3 -3 m U -3 -3

m m m U U m 0 0 3 0 0 0 0 W 0 0 0 0 0 cl 0m ffi W 0 0 0 0 0 0 H 0 0 0 0 0 0 3U pi 3 3 W u3 3 nW 0 0 m 0 0 0 I 0 0 0 0 0 0

8H F- 0 m m W 0 m U U m trl m 2m trl

0 m 0 0 \D m r. r. r. m W m

3 0 0 N N m u3 I m m m N 0 m m I

m m 0 m 0 0 0 0 r. r. r. \D N N m m r. r. r. u) u) m e if

.c +J 5 e a 5a a, a, IcfW 0 0 m 0 aI N N m aI I u! 3 a4 .da a.rl c s c

102 TABLE 20

LAKE GARFIELD

MICROSCOPIC EXAMINATION STATION 1 - AUGUST 8, 1974

PHYTOPLANKTON AND PROTOZOA' ZOO PLANKTON^ ALGAE CLADOCERONS Bacillariophyceae Daphnia occasional Tabellaria sp. 118 cyanophyceae Ceriodaphnia occasional Lyngbya sp. 118 Anabaena sp. 1235 Microcystis sp. 60 COPEPODS Diaptomus common

PROTOZOA Cyclops common Mastigophora Euglena sp. 30 Peridinium sp 47 ROTIFERS Kellicottia common

AMORPHOUS MATTER 1765 Ploesoma common

NOTE: Melosira sp., Navicula sp., Synedra sp., Aphanizomenon sp., and Oscillatoria sp. 'Relative frequency of genus in fields; percent: were found in the zooplankton sample. 60-100.....abundant 30-60 ...... very common 'Areal Standard Units/ml 5-30 ...... common 1-5 ...... occasional <1...... rare KONKAPOT RIVER OISTRlBUTlON OF OmET AQUATIC VEGETATION & AUGUST 8, 1974 IFI LEGEND r Potomweton richorbnil (pondweed) b Momageton robbimi (pondwed) 8-K INLET m M)riophyllum sp. (m#e nilfO//) W NymWma sp (wbif# wf#rti&) CT A-ris CmOdwiE (WUtWnWd)

w*mdm 0 Sagittorio btif0#o (8rmwkwd) Typho latlfolio (cuttuiil) t -- Potamopston sp. and airpur ep. (Mrush) Myrioohyllun 0. 0 e NOTE: MyrlaphyTb sp strands floating in wetor over entire lake.

n r

LAKE GARFfELD R richordsonli ond MONTEREY 262 ACRES

FIGURE 30

-. . sampling period (Figure 30). Two species of pondweed (Potamogeton richardsonii and P. robbinsii) and water milfoil (Myriophyllum sp.) were the most abundant vascxar plants encountered. The thickest growths of these occurred in the northwestern cove of the lake where the water depth was relatively shallow, affording favorable conditions. Other macrophytes were much more limited in their distribution. These included white water lily (Nymphaea sp.), water weed (Anacharis canadensis), smartweed' (Polygonum natans), bushy pondweed (wflexilis), arrowhead (Sagittaria latifolia), cattails (Typha latifolia), and bulrush (Scirpus sp.). In general, the cove areas throughout the lake contained the heaviest growths of aquatic vegetation, particularly pondweeds and milfoil. The shallow water depths in these coves and good light penetration aided these plants to literally "take over" the area.

IV. SUMMARY

Chemical and biological data from the August baseline survey point to the fact that Lake Garfield is in an early state of eutrophication. Dense growths of aquatic vegetation, significant numbers of algal species, and oxygen depletion in the lower strata of the lake support this statement.

The morphometric character of the watershed plays an important role in the lake's present condition, particularly on the amount of nutrients entering the lake and the distribution and types of aquatic plants. The general shape of the lake basin, the bottom composition, and certain physical features are significant factors influencing the distribution of aquatic plants. Hardpan is a general characteristic of the soil composition in the lake watershed. This condition tends to restrict downward movement of water which severely limits the use of the soils for septic tank sewage disposal systems.

105 GOOSE POND AND UPPER GOOSE POND LEE-TYRINGHAM

ITEM - -PAGE 108 I. Introduction 108 11. Morphometric Data 108 111. Water Quality Data 112 Chemical 112 Biological 112 Phytoplankton 112 Zooplankton 112 Macroinvertebrates 112 Aquatic Vegetation 118 Iv. summary

. .

106 GOOSE POND

LEE-TYRING)IA,, . ,, ..

FIGURE 31

107 GOOSE POND

I. INTRODUCTION

Goose Pond is a raised Great Pond located in Berkshire County. Its water level is controlled by Westfield River Paper Company, Lee, Massachusetts. The pond and its drainage area (3.66 square miles) lie within the towns Of Lee and Tyringham. This also includes the upper Goose Pond drainage system, a 1.11 square mile area of mostly forested, mountainous terrain (see Figure 31). Goose Pond is used for a variety of recreational activities which include boating, swimming, fishing, and ice-fishing. A portion of the Appa- lachian Trail, a well-known hiking trail from Mount Katahdin in Maine to Springer Mountain, Georgia, some 2025 miles, transects the watershed. Goose Pond is managed for trout by the Massachusetts Division of Fisheries and Game. Fishing pressure is moderate to high during the season. Permanent and seasonal dwellings located within the watershed are few in number. General water quality conditions in Goose Pond during the August study appeared good. Aquatic macrophyte and algal populations were relatively low, indicative of low productivity.

11. MORPHOMETRIC DATA

Morphometric data are presented in Table 2land Figure 32. The Goose Pond watershed contains two main waterbodies, Goose Pond and Upper Goose Pond. Goose Pond is the main basin and the larger of the two, with an area of 225 acres and a maximum depth of 48 feet. Mean depth is 25 feet, and the pond has a volume of 5,593 acre feet. Maximum length and width are 7,500 feet and 2,125 feet, respectively, with a shoreline of 20,000 feet. In contrast, the smaller Upper Goose Pond has an area of 45 acres and a maximum depth of 32 feet. The mean depth is 16 feet with a volume of 727 acre feet. Most of the watershed is wooded and sparsely populated with the banks of both ponds relatively steep. Both Goose Pond and Upper Goose Pond are of glacial origin, similar to other waterbodies in the Housatonic Basin, having been formed during the last period of glaciation. Underlying bedrock in the Goose Pond watershed is of one type, gneiss (granite biotite gneiss with some micaceous schist and quartzite).

There are four major soil types located within the watershed (see Figure 33 ). Shallow bedrock soils and deep well-drained stony soils with hardpans on the upland slopes characterize the drainage area. Most of the clay, silt, sand, gravel, and boulders were deposited as till by the glacial ice.

111. WATER QUALITY DATA General water quality conditions in Goose Pond during the August survey appeared relatively good. Although the pond is not in an eutrophic condition, both the chemical and biological data appear to indicate slightly enriched conditions. The location of sampling stations is shown in Figure 32 Complete chemical and biological data on Goose Pond for the baseline survey are Presented in Tables 22 and 23 and in Figure 34. Chemical data for Upper Goose Pond are shown in Table 22 and Figure 35.

108

TABLE '21

GOOSE POND AND UPPER GOOSE POND

MORPHOMETRIC DATA

GOOSE POND UPPER GOOSE POND

Maximum Length 7,500 3,800 feet

Maximum Effective Length 6,500 3,800 feet

Maximum Width 2,125 850 feet

Maximum Effective Width 2,125 850 feet

Maximum Depth 48 32 feet

Mean Depth 25 16 feet

Mean Width 1,307 516 feet

Area 225 45 acres

Volume 5,593 727 acre feet

Shoreline 20,000 9,400 feet

Development of Shoreline 1.8 1.9

Development of Volume 1.6 1.5

Mean to Maximum Depth Ratio 0.52 0.50 2 Drainage Area 2.55 1.11 miles

110 GOOSE POND LEE-TYRINGHAM

FIGURE 33 CHEMICAL

Station 1 on Goose Pond was located at the deep hole towards the north- eastern end of the pond. Temperature and oxygen concentrations for this station are graphically presented in Figure 34, Therma1,stratificationwas evident with a strong thermocline starting at 19 feet and extending through to the 30-foot level. Nutrient concentrations were relatively low throughout the epilimnion and thermocline layers with increased ammonia-nitrogen levels in the lower hypolimnion. Total phosphorus was present at 0.03 mg/l. As in other lakes and ponds within the Housatonic River Basin, there was no nitrate-nitrogen at any of the sampling stations. Silica, manganese, and iron concentrations also accumulated in the bottom strata. Water quality conditions in both the inlets, Higley Brook and Cooper Brook, appeared to be free of any contamination. The outlet (Goose Pond Stream) was also relatively free of any adverse degradation in general water quality.

BIOLOGICAL

Phytoplankton

Flagellates (Mastiogophora) dominated the phytoplankton samples from Goose Pond collected during the August study. Most abundant were Ceratium sp., Mallomonas sp., Peridinium sp., and Synura sp. The diatom Fragilaria sp. and the blue-green algae Microcystis sp. were also present. Tabellaria sp., Melosira sp., and Dinobryon sp. were collected in the zooplankton sample. The relative numbers of these algal types were not great enough to have a pronounced effect on water quality conditions in Goose Pond.

Zooplankton

Cladocerons, Copepods, and Rotifers were the common groups of organisms collected in Goose Pond during August. Among the Cladocerons, Daphnia sp. and Latonopsis sp. were common. Diaptomus sp. and Cyclops sp. were common Copepods. The Rotifer Kellicottia sp. was common, and there was a small number of Keratella sp. present. Nauplius, the immature stage of Copepods, was also quite common.

Macroinvertebrates

The deep hole station sampled for benthic fauna revealed a total of 15 organisms. Of these, Chaoborus punctipennis (phantom midge) was most abundant. Another Diptera, Chironomus sp., was also present.

Aquatic Vegetation

Macrophytes were not particularly abundant in Goose Pond during August (see 36). Figure A good diversity of types was found, indicating a stable commun- ity, with Potamogeton sp. dominating the flora. The two species E. richardsonii and P. robbinsii were very common, particularly near the outlet region ofeporia and where Cooper Brook enters. This area of Goose Pond is relatively shallow, affording favorable light conditions. Other macrophytes were more

112 DISSOLVED OXYGEN (mg / I)

I 2 3 4 5 6 7 8 9 I' 5 GOOSE POND IO TEMPERATURE and Temperature 15 OXYGEN PROFILE

20 Cloudy I J> STATION 25 / AUGUST 7, 1974 -3 30

45,

30 35 40 45 50 55 60 65 70 75

TEMPERATURE (OF) TABLE 22

GOOSE POND AND UPPER GOOSE POND

WATER QUALITY DATA

STATIONS 1, 2, 3, 4, & 5 - AUGUST 7, 1974

SPEC. DEPTH TEMP. D.O. pH TOT& NH3-N N03-N TOTAL TOTAL COND . SILICA Mn Fe feet OF ALK . P m. fimholcm. STATION 1 GOOSE POND - DEEP HOLE Surface 68.5 5 68.0 7.9 0.0 0.03 10 68.0 8.3 _- -_ 15 68.0 7.8 __ _- 20 59.0 8.0 __ __ 25 49.0 9.4 0.0 0.03 30 45.0 7.8 __ __ 35 43.0 3.3 __ __ 40 42.0 0.6 __ -_ 45 42.0 0.0 0.32 0.02 STATION 2 UPPER GOOSE POND - DEEP HOLE ______Surface 69.0 __ __ 5 68.5 7.7 ______10 68.0 7.7 ______15 54.0 7.2 7.0 15 0.0 0.0 0.02 20 47.5 2.0 ______25 44.5 1.6 30 43.0 0.1

STATION 3 HIGLEY BROOK INLET Mid-dep th 72.0 5.8 6.9 16 0.03 0.0 0.05 STATION 4 COOPER BROOK INLET Mid-depth 62.5 7.6 7.2 19 0.03 0.0 0.03 STATION 5 GOOSE POND STREAM OUTLET Mid-depth -- __ 7.4 19 0.0 0.0 0.02 DISSOLVED OXYGEN (rng / I)

I 2 3 4 5 6 7 -8

Temper,

Secci DISC at 1150 --___-______- - -_ - -- -_ - 15. Cloudy

Dissolved Oxygen

UPPER GOOSE POND TEMPERATURE and c 0) OXYGEN PROFILE .c0) Y STATION 2 AUGUST 7, 1974 Q w n 30 35 40 45 50 55 60 65 70 TEMPERATUR E F TABLE 23

GOOSE POND

MICROSCOPIC EXAMINATION

STATION 1 - AUGUST 7, 1974

PHYTOPLANKTON AND PROTOZOA' ZOOPLANKTON2

ALGAE CLADOCERONS Bacillariophyceae Daphnia common Fragilaria sp. 118 Cyanophyceae ~atonopsis3 common Microcystis SE. 60

COPEPODS PROTOZOA Diaptomus common Mastigophora Ceratium sp. 60 Cyclops common Mallomonas sp 24 Nauplius Peridinium sp 24 4 common Synura sp. 47

ROTIFERS APK)RPHOUS MATTER 1175 Kellicottia common

Keratella occasional NOTE: Tabellaira sp., Melosira sp., and Dinobryon sp. were found 3rentative genus identification. in the zooplankton sample. 41mmature Copepod stage 'Relative frequency of genus in fields; percent: 'Areal Standard Units/ml. 60-100.....abundant 30-60...... very common 5-30...... common 1-5...... occasional (1...... rare AQUATK VEGETATION

Wvy growth8 of C. demersum, N. flexiliu, A. canadensis, and 5

Wavy prawths of richon)s0nii ad p- robblwli limited in their distribution. These included bushy pondweed (wflexilis), waterweed (Anacharis canadensis), stonewort (wsp.), yellow water lily (Nuphar sp.) , wild celery (Vallisneria americana) , smartweed (Polygonum natans), and coontail (Ceratophyllum demersum). Upper Goose Pond, where Higley Brook enters, also contained many types. Particularly dominant in this area were bladderwort (Utricularia sp.), stonewort, and coontail. In general, the absence of excessive nutrient concentrations and the steep slope of the lake basin tended to limit the distribution and abundance of aquatic plants in both ponds.

IV. SUMMARY

The chemical and biological data collected during the August baseline survey indicate that both Goose and Upper Goose Ponds are relatively free of any serious water quality conditions associated with a eutrophic state. Relatively diverse and low numbers of algal and zooplankton types and the absence of any significant growths of aquatic vegetation support this.

The limited amount of nutrients (except perhaps phosphorus) and the sparsely populated area within the watershed should keep Goose Pond from any serious degradation of water quality. The morphometric character of the watershed with its relatively sharp, sloping banks should keep the present water quality conditions from altering significantly. Significant development of the watershed should be carefully planned to avoid future degradation of the water quality.

118 HOUSATONIC RIVER BASIN LAKES REPORT

GENERAL SUMMARY

1. The majority of the Housatonic River Basin lakes are hard, alkaline water lakes with high pH values. This property is in consequence of the widespread carbonate rocks in the Berkshires.

2. The waters of the Housatonic River Basin lakes appear nitrate-deficient. In all the lakes included in this report except Woods Pond, Lenox, nitrate- nitrogen was undetectable in the lakes as well as at the inlets and outlets. There are basically three mechanisms for nitrate removal from a lake's water:

a. assimilation by green plant cells; b. bacterial denitrification; C. physical phenomena, e.g., adsorption onto particulate matter followed by sedimentation,

Because of the high productivity in the Berkshire lakes, it is suggested that assimilation by green plant cells (especially the littoral macrophytes) accounts for the nitrate disappearance. In any event, the lack of nitrate-nitrogen in the lakes studied is important in that it may act as a limiting factor for further plant growth (both phytoplankton and rooted aquatics). Thus, any addition of nitrate-nitrogen via sewage, fertilizer, etc., would increase the lakes' productivity and accelerate the process of eutrophication.

3. There is considerable aquatic plant growth in the Housatonic River Basin lakes. The littoral areas of the lakes are covered with thick beds of aquatic macrophytes. Particularly abundant and widespread are species of Potamogeton, Myriophyllum, Anacharis, Nymphaea, Nuphar, Pontederia, and Ceratophyllum with many other types.. well represented. The hard, alkaline water supports a diverse and heavy aquatic flora.

4. The Berkshire lakes appear to be undergoing accelerated eutrophication. Supporting data for this statement include anaerobic hypolimnion, presence of blue-green algae, low transparency, extensive aquatic plant growth, and deep, black ooze sediments. The extensive shoreline development around the lakes is a contributing factor to this process.

119 APPENDIX A

WOODS POND

CHEMICAL AND BIOLOGICAL WATER QULITY DATA^

CHEMICAL (10/8/72) Station 1

PARAMETER MINIMUM MAXIMUM MEAN MEDIAN

Conductivity @mhos) 250 250 250 250 PH 7.3 7.3 7.3 7.3 Alkalinity (mg/l) 79 79 79 79 Total P (mg/l) 0.309 0.309 0.309 0.309 Dissolved P (mg/l) 0.238 0.238 0.238 0.238 NO2 + NO (mg/l) 0.440 0,440 0.440 0.440 NH3 (mg31) 0.700 0.700 0.700 0.700 Secchi (inches) 24 68 43 36 b- N 0 CHLOROPHYLL a* PKYTOPLANKTON

DATE STATION** CONCENTRATION (mg/l) DATE DOMINANT GENERA NUMBER PER ML.

6/5/72 1 3.2 6/4/72 Asterionella 470 8/1/72 1 12.1 Navicula 265 1018172 1 19.0 Fragilaria 90 Dinobryon 72 * All values plus or minus 20 percent. Synedra 72 ** Station number corresponding to this Other 429 report, TOTAL 1,398 8/1/71 Flagellates 3,002 Anabaena 778 Dinobryon 651 Cyclotella 380 Svnedra 325~~ Other 1,121 'SOURCE: U.S. Environmental Protection Agency, TOTAL 6,257 Preliminary Report on Woods Pond, Berkshire County, Massachusetts, National Eutrophication Survey, PNEFiL, Corvallis, Oregon, August, 1974. APPENDIX A (Continued)

WOODS POND MICROSCOPIC EXAMINATION

JUNE 11, 1974

PHYTOPLANKTON AND PROTOZOA! ZOOPLANKTON3

INLET OUTLET^

ALGAE CLADOCERONS None

Bacillariophyceae 37 Present COPEPODS None Cyanophyceae 121 Abundant

Chlorophyceae 199 Abundant ROTIFERS None

PROTOZOA

Sarcodina --- Present

Mastigophora lo Absent

Infusoria 10 Absent

3Relative frequency of genus in fields; percent: 'Expressed in Areal Standard Units/ml. 60-100 ...... abundant 'A direct count was not possible. 30-60...... very common 5-30...... common 1-5 ...... occasional <1...... rare

Source: Commonwealth of Massachusetts, Water Resources Commission, Division of Water Pollution Control, Housatonic River: 1974 Water Quality Survey Data. APPENDIX A (Continued)

WOODS POND

MICROSCOPIC EXAMINATION

AUGUST 6, 1974

1 PHYTOPLANKTON AND PROTOZOA ZOO PLANKTON^

INLET OUTLET

ALGAE CLADOCERONS None

Bacillariophyceae __ 29 Cyanophyceae 88 COPEPODS None +. N 153 47 N Chlorophyceae ROTIFERS None PROTOZOA

Sarcodina

Mastigophora

Infusoria

2Relative frequency of genus in fields; percent: inAreal Standard Units/ml. 60-100 ...... abundant 30-60...... very common 5-30 ...... common 1-5...... occasional

STOCKBRIDGE BOWL

TEMPERATURE (OF) AND DISSOLVED OXYGEN (mg/l) CONCENTRATIONS

DEEP HOLE STATION

7130147" 9/2/65* 8/14/70* 8/8/72" 8/16/73* 11/7/73 1131174 DEPTH (ft.) TEMP. D.O. TEMP. D.O. TEMP. D.O. TEMP. D.O. TEMP. D.O. TEMP. D.O. TEMP. D.O. 46.0 --- Surface 78.0 8.0 76.0 --- 72.5 8.6 76.0 9.9 34.0 --- 5 76.0 8.6 76.0 --- --_ __- 76.0 9.8 46.0 9.0 35.5 11.9

45.0 10 75.0 8.2 75.0 ------76.0 9.6 --- 35.5 --- 15 70.0 8.4 73.5 8.6 69.8 11.0 76.0 9.4 45.0 --- 35.5 11.8

20 --- ___ 61.0 10.6 53.6 5.0 63.0 14.6 45.0 9.0 35.5 ---

57.0 9.0 50.0 0.6 51.8 1.3 54.0 0.5 45.0 --- 35.5 11.8

30 48.0 8.0 45.5 0.5 --_ --- 49.0 0.2 45.0 --- 35.5 11.5

35 47.0 0.6 -__ --- 45.5 --- 47.0 0.2 45.0 --- 36.0 9.2

40 46.0 0.0 -__ ___ 45.5 0.4 --_ _-- 45.0 8.9 37.5 10.0

45 46.0 0.0 ______--_ _-- --_ -_- 45.0 6.1 ______

*SOURCE: Massachusetts Division of Fisheries and Game, Westborough Field Headquarters, Westborough, Massachusetts. APPENDIX C

PoNToosuc LAKE

TEMPERATURE (OF) AND DISSOLVED OXYGEN (mg/l) CONCENTRATIONS

DEEP HOLE STATION*

8/18/47 9/3/54 8110155 9/1/65 8/19/74 DEPTH (ft) TEMP. D.O. TEMP. D.O. TEMP. D.O. TEMP. D.O. TEMP. D.O.

Surface 77.0 7.2 67.5 --- 76.5 6.7 ------77.0 8.0 5 74.0 7.2 67.5 -__ 76.5 --- 64.7 8.9 76.0 7.8 10 73.0 7.8 67.3 --- 76.5 --- -_- __- 74.0 7.2 15 72.0 7.6 67.0 --- 76.0 6.3 --- __- 72.0 4.8

20 69.0 7.6 65.5 --- 63.8 0.6 ------67.0 0.0

25 59.0 7.2 65.1 7.0 57.0 --- 55.0 0.4 59.0 0.0

30 54.0 7.2 59.0 3.4 53.2 ------56.0 0.0

35 53.0 7.2 53.1 1.2 52.0 0.0 51.8 0.1 ------

*SOURCE: Massachusetts Division of Fisheries and Game, Westborough Field Headquarters, Westborough, Massachusetts.

124 APPENDIX D LAUREL LAKE

TEMPERATURE (OF) AND DISSOLVED OXYGEN (mg/l) CONCENTRATIONS DEEP HOLE STATION^

8/9/55 8/21/74 DEPTH TEMP. n.0. TFXP. n.0. (ft .)

Surface 76.2 --- 76.0 8.8 5 76.0 -_- 76.0 8.7

10 76.2 --- 75.0 8.4 15 75.1 _-- 74.0 8.6

20 66.3 _-- 63.0 10.4

25 53.5 7.8 59.0 9.9

30 47.3 1.7 51.0 2.2

35 -_- __- ___ _--

40 44.2 0. I ------

45 -__ -_- --_ ---

50 ______---

52 43.2 0.0 46.0 0.0

'Source: Massachusetts Division of Fisheries and Game, Westborough Field Headquarters, Westborough, Massachusetts.

125 APPENDIX E LAKE EUEL

TEMPERATURE (OF) AND DISSOLVED OXYGEN (mg/l) CONCENTRATIONS 1 DEEP HOLE STATIONS

STATION 1 STATION 2 7/13/47 8/21/74 9/2/54 8/21/74 DEPTH (ft.) TEMP. D.O. Tm. D.O. TEMP. D.O. TEMP. :D.O.

Surf ace 77.0 7.8 78.0 8.7 67.2 79.0 10.0 5 76.0 8.0 77.0 8.6 66.6 79.0 8.5

10 72.0 7.2 75.0 8.3 66.6 75.0 8.4

15 59.0 12.4 71.0 11.2 66.4 73.0 9.0

2c 50.0 10.2 58.0 3.4 62.5 62.0 0.0

25 47.0 2.2 52.0 0.0 51.8 62.0 0.0

30 45.0 0.6 48.0 0.0 48.6 56.0 0.0

35 44.0 0.2 46.0 0.0 ___ 55.0 0.0

40 43.0 0.2 ______

45 43.0 0.1 45.0 0.0

kource: Massachusetts Division of Fisheries and Game, Westborough Field Headquarters, Westborough, Massachusetts.

126 APPENDlX F

LAKE GARFIELD

TEMPERATURE (OF) AND DISSOLVED OXYGEN (mall) CONCENTRATIONS DEEP HOLE STATION^

7/9/47 9/2/54 8/7/57 8/ 21174 DEPTH (ft.) TEMP. D.O. TEMP. D.O. TEMP. D.O. TEMP. D.O.

Surface 75.0 8.0 70.7 --- 74.4 --- 78.0 8.5 5 75.0 8.0 68.3 --- 74.0 --- 76.0 8.5

10 73.0 7.6 67.0 --- 73.9 --- 74.0 8.2

15 72.0 7.6 65.0 --- 73.6 7.8 73.0 6.7

20 58.0 7.8 65.3 --- 65.1 4.2 66.0 0.0

25 51.0 7.8 62.3 7.8 58.2 0.0 56.0 0.0

30 49.0 7.6 56.5 0.2 55.5 --- 53.0 0.0

'SOURCE: Massachusetts Division of Fisheries and Game, Westborough Field Headquarters, Westborough, Massachusetts.

127 APPENDIX G

GOOSE POND

TEMPERATURE (OF) AND DISSOLVED OXYGEN (mg/l) CONCENTRATIONS

DEEP HOLE STATION^

8/18/11 7/17/47 9/3/54 8/21/74 DEPTH (ft.) TEMP. D.O. TEMP. D.O. TW. D.O. TEMP. D.O.

Surface 74.0 74.0 7.4 66.8 75.0 8.3 5 72.0 72.0 7.4 ___ 74.0 8.2

_-- 10 72.0 74.0 7.4 74.0 8.0 15 70.0 71.0 7.4 --_ 73.0 7.7

20 58.0 60.0 7.4 65.0 67.0 8.0

25 49.0 52.0 7.6 64.5 57.0 6.4

30 47.0 47.0 6.0 53.0 50.0 1.6

35 _-- -_- ___ 50.0 48.0 0.0

40 ___ 46.0 7.2 49.0 47.0 0.0

45 ___ 46.0 7.0 ______

'Source: Massachusetts Division of Fisheries and Game, Westborough Field Headquarters, Nestborough, Massachusetts

128 REFERENCES

1. American Public Health Association, Standard Methods for the Examination of Water and Wastewater, New York, 1971.

2. Commonwealth of Massachusetts, Water Resources Commission, Division of Water Pollution Control, Housatonic River: 1974 Water Quality Survey Data, Westborough, Massachusetts, 1975.

3. Commonwealth of Massachusetts, Water Resources Commission, Division of Water Resources, Special Report of the Water Resources Commission Relative to: The Water Supply of Berkshire County, Boston, Massa- chusetts, 1967.

4. Commonwealth of Massachusetts, Division of Fisheries and Game, Stocked Trout Waters in Massachusetts, Westborough, Massachusetts, 1973.

5. Curran Associates, Inc., Wastewater Collection and Disposal at Stock- bridge Bowl, Stockbridge, Massachusetts, Northampton, Massachusetts, 1971.

6. Dillon, P.J., A Manual for Calculating the Capacity of a Lake for Develop- e,Ontario, Canada: Ontario Ministrv of the Environment. Mater Resources Branch, 1971. 7. Edmondson, W.T., (Ed.), Ward and Whipple, Fresh-Water Biology, New York: John Wiley and Sons, 1959.

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