quantitative analyses of periphyton biomass and ... - SUNY Oneonta

QUANTITATIVE ANALYSES OF PERIPHYTON BIOMASS 

AND 

IDENTIFICATION OF PERIPHYTON TAXA 

IN THE TRIBUTARIES OF OTSEGO LAKE, NY 

IN RELA-riON TO 

SELECTED ENVIRONMENTAL PARAMETERS 

Stefanie H. Komorowski 

Biological Field Station 

Cooperstown, New York 

Occasional Paper No. 26. July, 1994 

Biology Department 

State University College at Oneonta

THIS MANUSCRIPT IS NOT A FORMAL PUBLICATION 

The information contained herein may not be cited or 

reproduced without permission of the author or 

the S.U.N.Y. Oneonta Biology Department. 

This contribution has been modified from a 

NYSDEC Bureau of Fisheries, Safety and Health Manual 

provided by Mr. George Seeley, NYSDEC Fish Propagation Unit.

Introduction 

Methods 

Results 

TABLE OF CONTENTS 

Abstract i 

Table of Contents. . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . iii 

Nutrient Concentrations 1 

Water Quality 8 

Physical Parameters 10 

Macroinvertebrate Grazers 11 

Seasonality . . . . . . . . . .. . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 12 

Sampling 13 

Objectives . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . .14 

Selection and Characterization of Streams 14 

Description and Use of Artificial SUbstrates.. . 15 

Collection, Preparation, and Analysis of Samples 16 

Monthly and Seasonal Average Data for Biomass and Parameters 18 

Data Preparation . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 18 

Calculation of Bedrock and Soil Type Percents 19 

Stream Characterization . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . .. 20 

Biomass , 22 

Factors Affecting Periphyton Growth 27 

iii

Discussion 

Periphyton Taxa 31 

Identification of Bedrock and Soil Type in the Otsego Lake 

Watershed , 38 

Land Use 40 

Overview. . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . .. 42 

Stream Characterization , 42 

Affects of the Parameters on Periphyton Biomass 43 

Identified Periphyton Genera and Their Seasonal Succession 59 

Bedrock and Soil Correlations 62 

Affects of the Streams on Otsego Lake ..................•.........64 

References . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 66 

Appendices . • . . . . . . . . ... . . . . . . . . • . . . . . . . . . . . . . . . . . . . . . . . . . . . • . . . . . . . . 71 

iv

ABSTRACT 

Nine tributaries to Otsego Lake, Otsego County, NY; and the 

Susquehanna River, its outlet, were studied to gain an understanding of the 

nutrient concentrations, periphytic biomass and taxa, and macroinvertebrate 

grazer populations. Specific streams were chosen based on the land use 

practices in their drainage basins. Four streams had watersheds dominated by 

agricultural activities. They generally had the highest yearly average of 

nutrient concentrations and periphyton biomass. The combined yearly 

averages of T-P0 4 equaled .057 mgtl, N0 3 equaled 1.08 mgtl, chlorophyll a 

equaled .691 mglm 2 /d, and ash-free dry weight equaled 133.86 mgtm 2 /d. Four 

other streams had watersheds that were primarily forested. They generally had 

a lower yearly average of nutrient concentrations and periphyton biomass. 

The combined yearly averages of T-P0 4 equaled .037 mgtl, N0 3 equaled .46 

mgtl, chlorophyll a equaled .314 mgtm 2 /d, and ash-free dry weight equaled 

58.47 mgtm 2 /d. One stream 'flowed through an urban area. The T-P0 4 yearly 

average concentration was high in this stream (.334 mgtl). Nitrate and biomass 

yearly averages were low (N0 3 equaled .37 mgtl, chlorophyll a equaled .032 

mgtm 2 /d, and ash-free dry weight equaled 16.28 mg/m 2 /d). Other parameters 

that were measured in the streams were chlorides, turbidity, velocity, and 

temperature. 

Temporal patterns were considered important factors affecting stream 

ecology throughout the year because our seasons vary greatly. The change 

of seasons initiated variations of nutrient concentrations and periphyton 

biomass and taxa. The highest seasonal averages of T.P0 4 and N0 3 in the

agricultural streams occurred during the winter and in the forested stream in the 

summer. Periphyton biomass in the agricultural and forested streams was 

highest in spring. At the same time an increase in similar periphyton taxa 

communities and numbers of genera identified in each stream were found. 

The initiation of agricultural best management practices (BMP's) in the 

agricultural areas of the Otsego Lake Watershed will reduce the potential of soil 

erosion and high nutrient concentrations entering the lake. 

ii

INTRODUCTION 

In order to study the primary productivity, biomass, and diversity of 

periphyton taxa in streams, it is essential to learn what factors influence 

periphyton and how they effect their ecology. In this work, nine tributaries to 

Otsego Lake, NY; 42 Q 43'N - 73 Q 57'W (Iannuzzi 1991) and the Susquehanna 

River, its outlet, were studied (Figure 1). Factors that were considered 

influential to periphyton ecology included nutrient concentrations, water 

chemistry, physical variables, and macroinvertebrate population densities, all 

of which change seasonally throughout the year. 

The term periphyton has various definitions depending on the author. 

The meanings range 'from simple, •... microfloral growth upon substrata" (Wetzel 

1983) to more complex, .... zoogleal and filamentous bacteria, attached 

protozoa, rotifers, and algae, and also the free-living microorganisms found 

swimming, creeping, or lodged among the attached forms" (American Public 

Health Association (APHA)1989). The definition best suited for trlis study 

includes the filamentous blue-green algae, filamentous green algae, and 

diatoms attached to artificial and natural substrates. 

Nutrient Concentrations 

Nutrient concentrations varied between the ten study sites due to storm 

events, land use practices in the stream basins, and characteristics of bedrock 

and soil type including soil erodability. Fluctuations of nutrient concentrations 

have an effect on the growth of periphyton. 

Land use practices dominant in the Otsego Lake Watershed are

( 5 ) 

( 6) 

( 2 ) 

(9 ) 

(1) SUSQCEHANNA RIVER 

Figure 1. Map of the Otsego Lake Watershed showing the names, locations, 

and numbers of the studied streams. 

2

filaments from the substrate (Fuller 1987 and Bushong .e.t a.t.. 1989). Heavy 

rainfall causes the nutrient concentrations to increase by flushing the nutrients 

from the fields into the streams (Fuller 1987). This increase in nutrient 

concentration lasts for just a short time interval as described by McDiffett .e.t ai., 

(1989). As the storm continues, the nutrient concentrations increase followed 

by an increase in the discharge of the stream. The nutrient peak occurs before 

maximum discharge is reached. Once the peak is attained, the concentrations 

begin to decrease during the latter stages of the storm event because the 

nutrients, mostly from surface runoff, have been previously washed into the 

streams. 

Heavy rains cause strong currents and increase water velocities. In this 

situation algal mats are ripped away which results in a decrease in diatom 

populations and biomass of filamentous algae (Bushong .e.t ai., 1989; Horner .e.t 

at., 1990; Peterson .e.tai., 1990; and Dodds 1991). Biggs .e.tat., (1989) found 

that disruption of periphytic mats by floods occurred not only because of the 

shearing stress of the water velocity, but also from instability of the natural 

substrate, and scouring action of suspended solids. Algal species differ in 

attachment strength to the substrate depending on the current regime to which 

they are adapted (Horner .e.t ai., 1990). Diatoms can attach themselves to the 

substrate by a stalk, raphe, or mucilaginous pad to resist removal by strong 

currents (Stevenson 1982). The irregular surface of the natural rock substrate 

provides protection for diatoms and filamentous algae from the stress of water 

velocity (Nielson .e.t .al., 1984 and Peterson .e.t .al., 1990). Cladophora, a 

filamentous genus, has adapted to fast water velocities by exploiting the texture 

5

o'f rock in stream beds. Dudley.e.t ill., (1991) suggests that the pits and crevices 

in rocks serve as protection for algal basal filaments. Small propagules attach 

themselves in these microhabitats which create environments safe from 

scouring by fast currents and macroinvertebrate grazers. When ideal 

conditions exist, the propagules will grow into new mature filaments. 

The types of bedrock in the nine stream basins tributary to Otsego Lake 

include shale and limestone shown in Figure 3 (Rickard .e.t £1., 1964 and 

Iannuzzi 1991). A detailed description of each bedrock type is given in 

Appendix A. The water chemistry of streams with shale bedrock does not 

change greatly since shale does not readily dissolve (Graham 1992). 

Limestone is more easily dissolved. Calcium and magnesium ions are released 

from the limestone and act as buffering agents (Graham 1992). 

Soils can influence stream water quality most often by way of runoff. The 

land use practices and soil characteristics determine the amount of nutrients 

that may wash into streams, which is associated with erosion. 

Soil erosion is caused by rain, wind, and water freezing and thawing 

which results in high nutrient loss from the upper soils especially from farm 

lands (Brady 1974). The moisture content of soils in a stream1s basin before a 

storm event and the intensity of the storm event determine, in part, the amount of 

water, nutrients, and sediment that will reach the stream (Singer .e.t £1., 1975). 

Generally, during a storm of low intensity on dry soil there will be very little 

runoff, added nutrients, or sediment concentrations in the stream water (Singer 

.e.t £1., 1975). Conversely, high intensity storms for long periods on wet soils 

will cause an increase in runoff, nutrient concentrations, and sediment 

6

concentrations in the stream water (Singer m.a.l.. 1975). In correlation with land 

use practices, undisturbed, vegetated land surrounding a stream stores water 

and slowly releases it over time (Power m.al., 1988). Power m.a!., (1988) also 

stated. that land use disturbances, in which much of the vegetation has been 

removed, decrease the water-holding capacity of the soil allowing larger 

volumes of water to enter a stream at a faster rate. This, of course, depends in 

part on soil conditions before a storm event. Figure 4 shows the distribution of 

six general soil types that have been identified in the Otsego Lake Watershed 

(Morrrs 1993). The soils are characterized into two groups based on the pH 

range of each type, those "more" acidic (pH range of soil types 1, 8, and 2 = 

4.2 - 7.8) and those "less" acidic (pH range of soil types 11, 5, and 6 = 5.3 

8.4)(Morris 1990). Appendix B explains the calculation of the averaged pH 

ranges. 

Water Quality 

Two parameters of water quality that were measured in this study include 

nutrient concentrations and turbidity. Two nutrients that are of most concern 

are phosphorus and nitrogen. Both are essential to periphyton in the synthesis 

of DNA, enzymes, vitamins, hormones, amino acids, and energy during 

photosynthesis (Wetzel 1983 and Keeton m .a.l.. 1986). Excess amounts of 

these nutrients can cause an overgrowth of periphyton which has unfavorable 

impacts on both economics and water quality. An abundance of periphyton 

growth, Cladophora, for example, can inhibit recreational activities such as 

fishing and boating, may decrease the concentrations of dissolved oxygen in 

8

the water during night-time respiration and during decomposition when the 

filaments die, and may give off foul odors during the decomposition process 

(Pitcairn m2.1., 1973). Periphyton are considered indicators of water quality 

because they can quickly respond to changes in their environment (Reisen m 

at., 1970; Nielson m .aJ,., 1984; and APHA 1989). Since these organisms 

readily incorporate nutrients, the study of biomass over a long period of time 

may indicate if the water is being polluted with excess nutrients (Nielson mgj., 

1984 and Welch mat., 1988). 

Turbidity is an optical property of water which measures the scattering 

and absorption of light by particulate matter (Monitek 1990). Particulate matter 

is com posed of u ••• discrete aggregations of matter... U wh ich vary in particle 

size, shape, and color (Monitek 1990). Turbidity may reduce the amount of 

light that reach periphyton. High turbidity measurements usually correspond 

with storm events. 

Physical Parameters 

Two important physical parameters to consider that influence the 

biomass and taxonomic structure of periphyton are solar light and water 

temperature (Stevenson 1982; Fuller 1987; Bushong mgj., 1989; and Munn m 

ill., 1989). It is the combination of both that impact periphyton seasonally. 

Biomass of periphyton may be higher in shallow streams in areas that have no 

vegetative canopy with warm water temperatures as compared to deeper 

streams with dense canopy cover, and lower water temperatures (Munn mgj., 

1989). Fuller (1987) states that streams without vegetative cover tend to have 

10

higher amounts of algal biomass than streams that are shaded. Jasper m.al., 

(1986) found a high correlation between light and photosynthetic rates; as light 

levels increased chlorophyil a measurements followed. Conversely, as light 

levels and water temperatures decreased, the growth rate slowed down 

because periphyton do not require as much energy in the winter as in the 

summer (Bushong mal.. 1989). Each of the ten sites studied in this experiment 

have different percentages of canopy cover. 

Blum (1957) and Whitford mai., (1963) found that changes in water 

temperature initiated succession in periphyton assemblages from season to 

season. 

Macroinvertebrate Grazers 

Periphyton are a food source for macroinvertebrate grazers (Robinson m 

ai., 1986 and Hill ftl ill., 1988a). Their feeding may have an effect on the 

biomass of periphyton. Studies by Hill .e1 ill., (1987, 1988a), Dudley ftl ill., 

(1991), and Steinman .e1 ai., (1991) indicated that grazing by invertebrates can 

reduce the biomass, distribution, primary productivity, and community structure 

of periphyton. Ungrazed substrates continue through normal succession of 

early diatom dominance to later dominance of filamentous algal tufts (Lamberti 

.e1 ai., 1983). However, grazed substrates remain in the early successional 

stages eXhibiting a single layer of diatoms and only propagules of filamentous 

algae (Lamberti .e1 ill., 1983). The once dominant, loosely attached species 

give way to the tightly attached prostrate species in an area that has been 

grazed by the macroinvertebrates (Hill.e1al., 1987 and Steinman .e.tal., 1991). 

11

Objectives 

The four objectives of this study were: 

1. To determine if streams flowing through agricultural 

areas have higher nutrient concentrations than streams 

f!owing through forested arisas. 

2. To determine if streams with high concentrations of 

nutrients support high periphyton biomass. 

3. To characterize the streams in the Otsego Lake 

Watershed based on nutrient concentrations and similar 

taxa present. 

4. To identify any impacts the streams may have on the 

water quality of Otsego Lake. 

METHODS 

Selection and Characterization of Streams 

There are over 20 streams tributary to Otsego Lake. Nine were chosen 

for this study because they represent the diversity of streams present in the 

Otsego Lake watershed and they flow throughout the year (Albright 1992). The 

Susquehanna River, the outlet from Otsego Lake, was also chosen to study. 

Stream diversity, for selection purposes, refers to the course of a stream flowing 

through either agricultural, forested, or urban areas and over limestone or shale 

bedrock. Criteria used to define a stream as agricultural, forested, or urban 

were the acreage of land use categories in the streams' basins and the yearly 

average nutrient concentrations. 

14

Description and Use of Artificial Substrates 

In order to compare the streams quantitatively, artificial substrates were 

used. By doing this, the area of each sample and texture of each substrate from 

the streams were identical. The artificial substra.te was plexiglass (Reisen .e.t al.. 

1970 and Peterson m. ill., 1990). Materials used to construct the plexiglass 

holder were slate, wood, coat hanger wire, and plastic tubing (Figure 6). 

PLEXIGLASS 

WIRE --tt'If] 

PLASTIC TUBING 

Figure 6. Sketch of artificial substrate holder. 

The slate base was approximately 20 cm x 15 cm. Two blocks of wood, 

approximately 8 cm x 2 cm x 6 cm were attached to the top of the slate. The 

blocks of wood were notched on the bottom so that thin pieces of wood could 

be placed under them to prevent the plexiglass plates from being set against the 

slate. The piece of coat hanger wire, approximately 23 cm long, was snugly 

fitted into plastic tubing to inhibit interference of metal ions. Four plexiglass 

15

plates, each 5 cm x 10 cm and having a designated area of 45 cm 2 on each 

side, were fed onto the plastic coated coat hanger wire. Plastic tubing, with a 

larger diameter, was cut into five pieces. Each piece fit tightly between each 

plate and between the blocks of wood and the nearest plate. This procedure 

was necessary to prevent the plates from scraping against each other when the 

water was turbulent. 

Each artificial substrate holder was piaced in an area of the stream that 

was deep enough to completely cover the plates and where the plates could 

receive as much incident light as possible. The holders were oriented so that 

the plates were parallel to the current. When necessary, heavy rocks were put 

near the sides of the holders for stabilization in faster currents. During the 

winter months, bricks were affixed to the bottom of the slate base to add weight 

to prevent the holders from being carried downstream by rapid currents and ice 

movements. This technique was not always successful. 

Collection, Preparation, and Analysis of Samples 

After 28 days of incubation in the streams, the plexiglass plates were 

removed and replaced with clean ones. After removal, the plates were placed 

in individual jars with stream water. As soon as the plates were brought back to 

the lab the periphyton was scraped off and prepared for chlorophyll a and ash 

free dry weight (AFDW) analysis. 

For chlorophyll a analysis, periphyton samples were ·filtered using glass 

fiber filters (APHA 1989). The filters were then placed in vials and frozen until 

analysis could be performed. The periphyton samples for AFDW analysis were 

16

also placed into vials and frozen until analysis could be performed. 

Procedures for both analyses were based on those found in APHA 

(1989). Procedures suggested by APHA and the procedures used in this study 

varied slightly. For chlorophyll a analysis, each filter paper disc was ripped 

into small pieces and placed in the tissue grinder with 2 ml of acetone, 

prepared as suggested by APHA. After grinding, the slu rry was poured into a 

centrifuge tube and 3 ml of acetone were used to rinse out the tissue grinder. 

More acetone was added to the centrifuge tube if the green color was too dark 

to be within the .1 - 1.00 Angstrom range APHA suggests. The slurry was 

clarified by centrifugation. The procedures then followed were those under 

"Spectrophotometric Determination of Chlorophyll" (APHA 1989). 

Before the AFDW analysis could be performed, 30 ITt I capacity fused 

quartz crucibles were placed in a muffle furnace at 550 QC for one hour to burn 

off any contaminants (Sohacki 1990). All other procedures were followed as 

written in APHA under "Dry and Ash-Free Dry Weight". When the crucibles 

were used several times, a build-up of residue developed on the inner surface. 

To thoroughly clean them, the crucibles were dipped in a potassium dichromate 

solution, set aside for about an hour, washed with hot water and Liqui-nox, and 

rinsed with glass distilled water, all the while being handled with gloved hands 

and stainless steel tongs (Sohacki 1990). The procedures for making the acid 

dichromate cleaning solution can be found in APHA (1989). 

17

Monthly and Seasonal Average Data for Biomass and the Parameters 

Biomass monthly averages were calculated from data collected 6 June 

1991 to 20 November 1991 and from 8 January 1992 to 24 June 1992. The 

beginning and ending dates of each collection (13 total) are shown in 

Appendix C. From February 1992 to June 1992, the monthly averages for the 

six parameters, total phosphorus (T.P0 4 ), nitrates (N0 3 ), chlorides (CI), 

turbidity (TRB), velocity (VEL), and water temperature (TMP), were calculated 

from 1991 data. The monthly temperature averages for streams 1, 2, 6, and 20 

were from 1992 data. Biomass and the other parameter data were also 

calculated seasonally. The collection months were divided into seasons as 

follows: summer = June· August, fall = September· November, winter = 

February and March, and spring =April· June. 

Data Preparation 

The baseline and storm event data for the six parameters collected in the 

nine tdbutaries and the Susquehanna River were recorded in spreadsheet 

format using Quattro Pro (Borland International, Inc. 1992). Measurements for 

T-P0 4 • N0 3 , and CI were then integrated, using Sigma Plot (Jandel Scientific 

1990) to accurately account for the differences in concentrations between 

baseline and storm event data during each month. By using integration, the 

concentrations of each parameter could be calculated for days when analysis 

of the parameters was not performed. The average monthly concentrations, 

therefore, include a concentration for every day of the sampling month. 

Monthly turbidity averages were obtained by averaging the turbidity for 

18

any storm events that occurred within the sampling months. Monthly velocity 

averages were calculated from center-stream velocity measurements and 

discharge data. The measured velocity and discharge readings were plotted 

against each other for each stream to create a regression line. Average 

monthly discharge for each stream was obtained by integration. These monthly 

discharge averages were plotted by hand on the x-axis of the graph. Average 

monthly velocity was estimated by drawing a line from each plotted discharge 

point to the regression line and then over to the center-stream velocity reading 

on the y-axis. See Appendix 0 for an example. Monthly temperature averages 

were calculated from stream water readings collected either once a week, once 

every two weeks, or once a month, depending on season and weather 

conditions. 

Calculation of Bedrock and Soil Type Percents 

A planimeter was used to measure the areas of the bedrock and soil 

types in the drainage basin of the nine tributaries in Figures 3 and 4. The areas 

were converted to percent acres in each drainage basin in order to easily 

compare bedrock and soil type within each basin and between basins. Also, 

representing the areas by percentages absorbed any inaccurate measurement 

of areas that occurred while the maps were being created. 

19

Stream Characterization 

RESULTS 

The formula used to calculate the trophic level index for each stream in 

order to characterize each as agricultural, forested, or urban is shown in Figure 

7. The data in Table 1 used in the formula were number of agricultural and 

forested acres and yearly average concentrations of T-P0 4 and N0 3 . 

# agricultural acres yearly ave of yearly ave of 

+ + 

# forested acres rr· P04] [NOs] 

TROPHIC 

LEVEL 

AGRICULTURAL STREAMS: STREAM # INDEX 

17 3.94 

16 2.88 

20 2.62 

6 2.09 

FORESTED STREAMS: 15 1.23 

5 1.02 

9 0.97 

4 0.91 

URBAN STREAM: 2 1.18 

Figure 7. The general trophic condition of each stream basin was calculated 

by using the above formula. In this way, the stream basins were characterized 

as agricultural or forested by comparing the individual stream indices. Higher 

trophic values indicate more agricultural acres than forested acres in the 

stream basin and higher yearly average total phosphorus (T-P0 4 ) and nitrate 

(N0 3 ) concentrations.. Stream 2 was characterized as urban because the last 

type of environment the stream flows through before reaching the lake is 

residential which is highly influential to water quality of Otsego Lake. 

20

STREAM STREAH AGR'L FOR'D P04 H03 Cl TRB VEL THP CHL A AFOW 

, TYPR ACRES ACRES .gll IIgtl ag/1 ntu I/S °C Ig/112/d IIg/1I2/d 

20 A 5380,68 4392.45 0,090 1. 31 8.07 

------------------------------------- 

24. 94 0.97 10.75 0,363 109.42 

16 A 5202.46 2976.12 0.051 1. 08 6.13 7.58 2.22 12,15 I. 264 193.93 

17 A 4502.10 1924.88 0.056 1. 55 9,84 18.45 1. 75 11. 26 0.833 183.32 

6 A 1005.53 602.14 0.031 0.39 6.98 14. 30 1. 35 9.37 0.305 48, ?7 

I'\) 15 F 1103.60 1529.99 0.035 0.47 5.49 7. 22 1. 75 9.80 0.653 91. 55 

....... 

5 F 530.49 683.99 0.023 0.22 3.80 4. 31 l. 22 9.52 0.130 26.23 

9 F 388.71 460.68 0.058 0.69 10,73 29,16 l. 75 9,45 0.228 45 .64 

4 F 430.26 1015.88 0.031 0.46 4. 70 9.24 I. 59 9,82 0,255 70,45 

2 u 237.98 501.15 0.334 0.37 33.42 396,48 1.24 9.64 0.032 16.28 

Table 1. The values listed in this table for the agricultural and forested acres and the total phosphorus and nitrate 

concentrations were used in the equation in Figure 7. The yearly averages of chloride, turbidity, velocity, water 

temperature, chlorophyll a, and ash-free dry weight are also listed for comparison.

Streams 17, 16, 20, and 6 were characterized as agricultural, streams 

15, 5, 9, and 4 were characterized as forested, and stream 2 was characterized 

as urban. The Susquehanna River, the main outlet of the lake, was not 

characterized as the other streams were because this study focused mainly on 

the land use practices and water quality in the watershed that affect Otsego 

Lake. 

Biomass 

Biomass of periphyton in each stream was collected monthly over a one 

year period from 6 June 1991 - 24 Juna 1992. However, there is a gap in the 

data. Measurements from the end of November 1991 to the beginning of 

January 1992 could not be collected at any of the sampling sites due to high 

water levels, fast water velocities, and ice cover on the streams. These 

conditions made it impossible to find and/or keep the artificial substrate holders 

in the streams. There were a total of 13 collections during the year. 

In some streams the monthly collections are widely spaced, temporally, 

due to weather conditions or at other times, the artificial substrates may have 

been vandalized. Streams with a total of 13 monthly collections for ci-liorophyll 

a and ash-free dry weight (AFDW ) include 16, 17, and 20. Stream 6 had 13 

monthly collections for AFDW only (see map in Figure 1 for location and name 

of the streams and Figure 8 for number of collections for each stream). The 

other streams vary in number of collections. The calculated monthly averages 

of chlorophyll a and AFDW for each stream during each collection period are 

shown in Appendix E. 

22

Number of Number of 

chlorophyll a AFDW 

Stream # Collections Collections 

1 9 9 

2 3 4 

4 10 9 

5 10 11 

6 11 13 

15 9 9 

16 13 13 

17 13 13 

20 13 13 

Rgure 8. Total number of collections of chlorophyll a and ash-free dry weight 

for each stream over the collection year. There was a maxim um of 13 

collections. 

The yearly averages of periphyton biomass for each stream are shown in 

Table 2. Stream 16 had the highest yearly averages of chlorophyll a (1.264 

mg/m 2 /d) and AFDW (193.93 mg/m 2 /d). The lowest yearly averages of 

chlorophyll a and AFDW were found in stream 2 (.032 mg/m 2 /d and 16.28 

mg/m 2 /d, respectively). 

23

CHL a STREAM AFDW STREAM 

mglm21d # mglm2ld L 

1.264 16 193.93 16 

0.833 17 183.32 17 

0.643 15 109.42 20 

0.363 20 91.55 15 

0.305 6 48.77 6 

0.228 9 47.65 1 

0.130 5 45.64 9 

0.054 1 26.23 5 

0.032 2 16.28 2 

T-P04 STREAM N0 3 STREAM CI STREAM 

mgll # mgt! # mgt! # 

0.334 2 1.55 17 33.42 2 

0.090 20 1.31 20 10.73 9 

0.058 9 1.08 16 9.84 17 

0.056 17 0.69 9 8.07 20 

0.051 16 0.61 1 7.18 1 

0.035 15 0.47 15 6.98 6 

0.031 4 0.46 4 6.13 16 

0.031 6 0.39 6 5.49 15 

0.023 5 0.37 2 4.70 4 

0.020 1 0.22 5 3.80 5 

TRB STREAM VEL STREAM TMP STREAM 

ntu # mls # ?C # 

396.48 2 2.26 15 12.15 16 

29.16 9 2.22 16 11.36 1 

24.94 20 1.75 17 11.26 17 

18.45 17 1.75 9 10.75 20 

14.30 6 1.59 4 9.82 4 

9.24 4 1.53 1 9.80 15 

7.58 16 1.35 6 9.64 2 

7.22 15 1.24 2 9.52 5 

4.31 5 1.22 5 9.37 6 

3.76 1 0.97 20 9.22 9 

Table 2. The yearly averages of biomass and the remaining parameters for 

each stream in order from highest to lowest values are shown. (Chi a = 

chlorophyll a, AFDW = ash-free dry weight, T-P0 4 = total phosphorus, N0 3 = 

nitrate. C! = chloride, TRB = turbidity, VEL = velocity, and TMP = water 

temperature) 

24

Table 3a shows the seasonal averages of periphyton biomass for the 

individual streams, seasonal averages for the streams during each season, and 

the overall seasonal averages for these streams. The chlorophyll a seasonal 

averages were highest during spring for both the agricultural (1.845 mg/m 2 /d) 

and forested streams (.627 mg/m 2 /d) and highest during summer in the urban 

stream (.045 mg/m 2 /d). Chlorophyll a seasonal averages were lowest during 

fall for the agricultural (.148 mglm 2/d) , forested (.151 mg/m 2 /d), and the urban 

streams (.006 mg/m 2 /d). The AFDW seasonal averages were highest during 

spring for both the agricultural (150.15 mg/m 2 /d) and forested streams (64.18 

mg/m 2 /d) and highest during fall in the urban stream (25.63 mg/m 2 /d). AFDW 

seasonal averages were lowest during summer in -the agricultural streams 

(124.22 mg/m 2 /d), winter in the forested streams, (3.16 mg/m 2 /d) and spring in 

the urban stream (1.39 mglm 2 /d). The overall seasonal averages of chlorophyll 

a and AFDW in the agricultural streams (.729 mg/m 2 /d and 135.45 mg/m 2 /d, 

respectively) were more than twice as high as the overall seasonal averages in 

the forested streams (.300 mg/m 2 /d and 47.04 mg/m 2 /d, respectively). In the 

urban stream, the overall seasonal averages of chlorophyll a and AFDW were 

low (.026 mglm 2 /d and 15.36 mg/m 2 /d, respectively). 

25

CHLOROPHYLL a- mglm 2 /d OVERALL 

SEASONAL 

Stream # Summer Fall Winter Spring AVERAGE 

17 0.537 0.204 0.713 2.036 

Agricultural 16 0.451 0.037 0.980 4.035 

Streams 20 0.390 0.175 0.128 0.661 

6 0.260 0.177 0.234 0.646 

seasonal average 0.410 0.148 0.514 1.845 0.729 

15 0.443 0.149 1.638 

Forested 5 0.106 0.036 0.331 

St-reams 9 0.251 0.079 0.413 

4 0.248 0.341 0.159 0.124 


Urban Stream 2 0.045 0.006 0.026 

ASH-FREE DRY WEIGHT - mglm 2 /d OVERALL 

SEASONAL 


17 164.30 259.07 105.67 191.03 

Agricultural 16 148.21 80.90 386.93 254.52 

Streams 20 134.70 122.12 25.90 110.27 

6 49.65 73.04 16.17 44.78 


15 67.08 106.26 138.02 

Forested 5 37.45 16.43 2.38 24.80 

Streams 9 63.05 31.59 3.94 70.08 

4 63.03 98.36 23.81 


Urban Stream 2 19.05 25.63 1.39 15.36 

Table 3a. Shown are the seasonal averages and overall seasonal averages of 

biomass for the individual streams as well as the characterized streams. 

Seasonal average is the average of the four streams for a particular season. 

Overall seasonal average is the result of averaging the seasonal averages to 

compare agricultural, forested, and urban streams through the seasons. 

26

Factors Affecting Perlphyton Growth 

Appendices F and G list the monthly averages for each parameter 

monitored; total phosphorus (T-P0 4 ), nitrates (N0 3 ), chlorides (GI), turbidity 

(TRB), velocity (VEL), and temperature (TMP) in all the streams during the year. 

The yearly average of the parameters for each stream is shown in Table 2. 

Stream 2 had the highest concentrations of T-P0 4 (.334 mg/l) and CI (33.42 

mgtl) as well as the highest TRB average (396.48 ntu) during the year. Stream 

17 had the highest concentration of N0 3 (1.55 mg/l), stream 15 had the highest 

average VEL (2.26 m/s), and stream 16 had the highest average TMP (12.15 

QC) during the year. Stream 1 had the lowest yearly averages of T-P0 4 (.020 

mg/l) and TRB (3.76 ntu) measurements during the year. Stream 5 had the 

lowest yearly averages of N0 3 and CI concentrations (.22 and 3.80 mg/l, 

respectively). The lowest yearly average VEL was in stream 20 (.97 m/s) and 

stream 9 had the lowest yearly average TMP (9.22 QC). 

Tables 3b, 3c, and 3d show the seasonal averages of the T-P0 4 , N0 3 , 

CI, TRB, VEL, and TMP measurements during the year between the 

agricultural, forested, and urban streams. For each parameter the seasonal 

averages in the individual streams, seasonal averages for the streams during 

each season, and the overall seasonal averages for these streams are given. 

In Table 3b, the highest seasonal averages of T-P0 4 were during winter 

in the agricultural streams (.068 mgtl) and during summer in the forested streams 

(.047 mg/l) and the urban stream (.680 mg/l). The lowest· seasonal averages of 

T-P0 4 were during spring in the agricultural streams (.045 mg/l), fall in the 

forested streams (.026 mgll), and winter in the urban stream (.095 mgtl). The 

27

overall seasonal average of T-P0 4 was approximately 2.5 times greater in the 

urban stream (.256 mg/I) than in the agricultural (.057 mg/I) or forested streams 

(.035 mg/I). The highest seasonal averages of N0 3 were during winter in the 

agricultural streams (1.96 mg/I) and in the forested streams the same N0 3 

average was measured during summer, winter, and spring (.54 mg/I). In the 

urban stream, the highest seasonal average of N0 3 was during summer (.49 

mg/I). The lowest seasonal averages of N0 3 were during summer in the 

agricultural streams (.70 mg/I) and during fall in the forested streams (.21 mg/I) 

and the urban stream (.24 mg/I). The overall seasonal average of N0 3 was 

highest in the agricultural streams (1.22 mg/I) which was 2.5 times greater than 

the value in the forested streams (.46 mg/I) and the urban stream (.35 mg/I). 

Table 3c shows that the highest seasonal average of CI in the 

agricultural (10.69 mg/l) and forested streams (8.06 mg/I) occur-red in fall. In the 

urban stream, the highest seasonal average of CI occurred in winter (87.71 

mg/I). The lowest seasonal averages of CI occurred in spring for all the 

characterized streams; agricultural 5.69 mg/I, forested 4.76 mg/I, and urban 

16.91 mg/1. The overall seasonal average of CI in the urban stream (38.82 mg/I) 

was approximately five times greater than the overall seasonal average of CI in 

the agricultural (7.77 mg/I) and forested streams (6.27 mg/I). Seasonal turbidity 

averages in the agricultural streams (20.87 ntu), forested streams (21.43 ntu), 

and the urban stream (815.10 ntu) were highest during summer and lowest 

during the fall (9.92 ntu, 2.49 ntu, and 78.82 ntu, respectively). The overall 

seasonal average of TRB in the urban stream (306.09 ntu) was approximately 

20 times greater than the overall seasonal averages in the agricultural (15.58 

29

ntu) and forested streams (10.70 ntu). 

The highest seasonal average water velocities were found during spring 

in the agricultural streams (2.13 m/s) and during winter in the forested streams 

(2.26 m/s) and in the urban stream (1.46 m/s)(Table 3d). Summer was the 

season of the slowest water velocities; agricultural streams (1.25 m/s for both 

summer and fall), forested streams (1.38 m/s), and the urban stream (1.13 m/s). 

The typical seasonal water temperature variations found in this climate were 

represented in the streams; warmest water temperatures during summer and 

coldest water temperatures during winter. The overall seasonal averages of 

both velocity and temperature were similar between the characterized streams. 

Periphyton Taxa 

Most periphyton were identified from the plexiglass plates in the artificial 

substrate holders. Identification in some streams was incomplete due to the loss 

of the substrate holders from the streams or ice cover. Cladophora glomerata, 

Oscillatoria spp., and Vaucheria spp., were identified from the natural rock 

substrates or concrete spillways in the streams. 

Table 4 lists the genera of periphyton that were identified, the collection 

period and stream number in which they were found, and the total number of 

streams in which they were found. A total of 15 genera were identified in' the 

nine tributaries and the Susquehanna River from May 1991 through June 1992. 

Gomphonema olivaceum was the most common species, found in eight of the 

nine streams and in the Susquehanna River, especially in the spring. The most 

diverse month was April in which 11 different taxa were identified. Also evident 

31

VELOCITY - mls 

Stream # 

17 

Ag ricu Itural 16 

Streams 20 

6 

Summer 

1.55 

1.60 

0.70 

1.16 

Fall 

1.56 

1.57 

0.73 

1.15 

Winter 

2.00 

3.05 

1.35 

1.67 

Spring 

2.08 

3.37 

1.41 

1.66 

OVERALL 

SEASONAL 

AVERAGE 


15 1.74 1.97 3.25 2.77 

Forested 5 1.01 1.05 1.58 1.53 

Streams 9 1.50 1.59 2.00 2.13 

4 1.28 1.26 2.21 2.01 


Urban Stream 2 1.13 1.15 1.46 1.35 1.27 

TEMPERATURE - 2C OVERALL 

SEASONAL 


17 18.33 9.05 0.91 8.57 

Ag ricultu ral 16 19.80 10.01 1.01 8.99 

Streams 20 18.45 9.27 0.73 6.10 

6 15.26 8.55 1.01 6.02 


15 16.01 7.51 0.12 8.19 

Forested 5 15.36 7.62 0.70 7.55 

Streams 9 14.79 7.61 0.41 7.44 

4 15.64 7.98 1.24 7.66 


Urban Stream 2 15.00 9.10 1.16 6.92 8.05 

Table 3d. Shown are the seasonal averages and overall seasonal averages of 

velocity and temperature for the individual streams as well as the characterized 

streams. Seasona.l average is the average of the four streams for a particular 

season. Overall seasonal average is the result of averaging the seasonal 

averages to compare agricultural, forested, and urban streams through the 

seasons. 

32

was the seasonal succession of the identified genera. The number of taxa 

identified in each season were 13 in spring and summer, 9 in fall, and 6 in 

winter. Although spring and summer had the same .number of identified taxa, the 

genera were common to more streams during spring than in summer. 

Tables 5a, 5b, and 5c list the stream numbers and the names of 

periphyton identified during each season. Of all the streams, stream 17 was the 

most diverse having 13 periphyton taxa identified during the year. In terms of 

periphyton diversity in each stream during the seasons, streams 5 and 6 were 

the most diverse in summer with six genera, stream 4 was most diverse in fall 

with six genera, the Susquehanna River (stream 1) was most diverse in winter 

with four genera, and streams 16 and 20 were most diverse in spring with ten 

taxa. Communities of periphyton taxa found in agricultural streams were also 

found in forested streams. These tables show the general pattern of the spring 

season being dominant in the number of identified periphyton taxa and the 

number of streams in which they were found. 

34

AGR'L 

STREAMS SUMMER FALL WINTER SPRING 

17 (13) Cocconeis Oscillatoria Meridion Gomphonema. 

spp. spp. circulare olivaceum 

Diatoma Fragilaria Cladophora 

vulgare spp. glomerata 

Osci/latoria Meridion 

spp. circulars 

Spirogyra Cocconeis 

spp. spp. 

Vaucheria Navicula 

spp. spp. 

Oiatoma 

vulgare 

CyrrtJella 

spp. 

Ulothrix 

spp. 

Diatoma 

elongata 

16 (12) Cladophora Cladophora Meridion Gomphonema 

glomerata glomerata circulare olivaceum 

Cocconeis Spirogyra Diatoma Cladophora 

spp. spp. vulgare glomerata 

Oiatoma Meridian 

vulgare circulare 

Oscillatoria Cocconeis 

spp. spp. 

Navicula 

spp. 

Synedra 

ulna 

Diatoma 

vulgare 

Achnanthes 

spp. 

Diatoma 

elongata 

Vaucheria 

spp. 

Table 5a. Listed are the agricultural streams and the genera of periphyton 

found during the seasons. The number in parentheses indicates the number of 

taxa identified in that stream. 

35

AGR'L 


6 (12) Cladophora Meridion Meridion Gomphonema 

glomerata circulare circulare olivaceum 

Cocconeis Cocconeis Synedra Cladophora 

spp. spp. ulna glomerata 

Navicula Synedra Oscil/atoria Merldion 

spp. ulna spp. circulare 

Synedra Synedra 

ulna ulna 

Diatoma Diatoma 

vulgare vulgare 

Closterium CyntJella 

moniliforme spp. 

Ulothrix 

spp. 

Diatoma 

elongata 

20 (11) Cocconeis Cladophora Meridion Gomphonema 

spp. glomerata circulare olivaceum 

Oscillatoria Oscillatoria Cladophora 

spp. spp. glomerata 

Spirogyra Meridion 

spp. circulare 

Cocconeis 

spp. 

Navicula 

spp' 

Synedra 

ulna 

Diatoma 

vulgare 

CyntJella 

spp. 

Ulothrix 

spp. 

Osciliatoria 

spp. 

Table 5a continued. Listed are the agricultural streams and the genera of 

periphyton found during the seasons. The number in parentheses indicates the 

number of genera identified in that stream. 

36

FORESTED 


5 (10) Cladophora Meridion Me ridion Gomphonema 


Cocconeis Cocconeis Synedra Cladophora 

spp. spp. ulna glomerata 

Navicula Synedra Meridion 

spp. ulna circulare 

Synedra Gscillatoria Cocconeis 

ulna spp. spp. 

Diatoma Synedra 

vulgare ulna 

Cymbella Achnanthes 

spp. spp. 

4 (9) Cladophora Cladophora Cladophora 

glomerata glomerata glomerata 

Meridion Meridion Me ridion 

circulare circulare circulare 

Cocconeis Cocconeis Navicula 

spp. spp. spp. 

Achnanthes Synedra 

spp. ulna 

Vaucheria Spirogyra 

spp. spp. 

Fragilaria 

spp. 

15 (8) Cladophora Cladophora Gomphonema 

glomerata glomerata olivaceum 

Cocconeis Meridion Cladophora 

spp. circulare glomerara 

Cocconeis Meridion 

spp. circulare 

Ulothrix Cocconeis 

spp. spp. 

Synedra 

ulna 

Oiatoma 

vulgare 

Cymbella 

spp. 

Ulothrix 

spp. 

9 (6) Cladophora Meridion Mendion Gomphonema 


Cocconets Cocconets CiaC1ophora 

spp. spp. glomerata 

Vaucheria Ulothrix Mendion 

spp. spp. circulare 

Cocconeis 

spp. 

Ulothrix 

spp. 

Table 5b. Listed are the forested streams and the genera of periphyton 

found during the seasons. The number in parentheses indicates the 

number of taxa identified in that stream. 

37

URBAN 

STREAM SUMMER FALL WINTER SPRING 

2 (4) Gomphonema Navicula 

olivaceum spp. 

Achnanthes Ulothrix 

spp. spp. 

Navicula 

spp. 

SUSQUEHANNA 

RIVER SUMMER FALL WINTER SPRING 

1 (10) Diatoma Synedra Synedra Gomphonema 

vulgare ulna ulna olivaceum 

Cymbella Cymbella Diatoma Navicula 

spp. spp. vulgare spp. 

Achnanthes Oscillatoria Cymbella Synedra 

spp. spp. spp. ulna 

Spirogyra CyrrtJel/a Achnanthes 

spp. spp. spp. 

Fragi/aria Diatorna 

spp. elongata 

Table 5c. Shown are the urban stream and the Susquehanna River and the 

genera of periphyton found during the seasons. The number in parentheses 

indicates the number of taxa identified in that stream. 

Identification of Bedrock and Soli Type in the Otsego Lake Watershed 

General bedrock types identified in the Otsego Lake Watershed were 

shale and limestone (Figure 3). The percentage of each type in each stream 

basin is indicated on Table 6. Shale bedrock was dominant on the West side of 

the lake in stream basins 2, 4, 5, 6, 9, and 15. Limestone bedrock was 

dominant North of the lake in stream basins 16, 17, and 20. Six soil types were 

identified in the watershed (Figure 4). The average pH range of each soil type, 

varying in depths from 0-18 inches to 0-80 inches, was used to categorize the 

soil types. Low pH ranges were calculated in soil types 1 (4.2 -7.8), 2 (4.5 

6.2), and 8 (4.4 - 7.8) (Figure 4). Slightly higher pH ranges were calculated in 

38

BEDROCK BEDROCK %OFEACH % OF CMBN 

SmEAM # NAME TYPE BDRK TYPE BDRK TYPE 

2 Opm shale 83.83 100 S 

Oso shale 16.17 

4 Opm shale 74.82 100 S 


5 Opm shale 91.41 100 S 


6 Dpm shale 70.61 100 S 

Dso shale 29.39 

9 Dpm shale 37.62 100 S 


Dot shale 3.67 

15 Dpm shale 5.03 98.79 S 



Dch shale 2.78 

Duc limestone 0.52 1.21 L 

Don limestone 0.69 

16 Dso shale 0.96 15.32 S 



Due limestone 526 59.23 L 


Dec limestone 5.49 

Dk limestone 1.70 

Glacial Overburden 25.45 25.45 G.O. 

17 Dot shale 1.86 11.20 S 

Sby shale 2.01 


Due limestone 3.58 86.39 L 


Dec limestone 9.60 


Ddb limestone 12.82 

Ddj limestone 6.02 

Glacial Overburden 2.44 2.44 G.O. 

20 Dpm shale 2.15 35.60 S 




Duc limestone 3.82 64,40 L 


Dcc limestone 5.83 


Ddb limestone 4.75 

Ddj limestone 6.37 

Dr limestone 9.65 

Dct limestone 5.97 

Table 6. Listed are the bedrock types, percent of each bedrock type, and the 

percent of the combined bedrock types .in each stream basin. The combined 

bedrock type was derived from adding the shale percentages and limestone 

percentages to obtain one overall percentage of each bedrock type. S = shale, 

L = limestone, and G.O. = glacial overburden. 

39

soil types 5 (5.3 - 8.4), 6 (5.4 - 8.0), and 11 (5.3 - 8.2). Percentage of each soil 

type for each stream basin is indicated in Table 7. The "more N 

acidic soils were 

generally dominant on the West side of the lake in stream basins 2, 4, 5, and 9. 

The Niess· acidic soils were generally dominant at the North end of the lake in 

stream basins 16, 17, and 20. Stream basins 6 and 15 also had "less" acidic 

soil, but are located on the West side of the lake. 

Land Use 

By viewing aerial photographs of the watershed, it was possible to identify 

the types of land use the streams and their tributaries flowed through (Figure 2). 

Streams on the West side of the lake, 2, 4, 5, 6, 9, and 15, flow mostly through-. 

forested land. Streams North of the lake, 16, 17, and 20, flowed through a 

mixture of agricultural and forested land, the former being more common. 

Streams 15, 16, and 20 have wetland areas in their basins. 

40

%OFEACH % OF CMBN 

STREAM # SOIL TYPE SOil TYPE SOil TYPE 

2 1 72.70 100.00 A 

8 27.30 

4 1 20.60 50.00 A 

2 5.90 50.00 B 

5 50.00 

8 23.50 

5 1 18.92 62.16 A 

2 40.54 37.84 B 

5 37.84 

8 2.70 

6 1 31.71 60.98 B 

2 2.44 39.03 A 

5 60.98 

8 4.88 

9 1 39.13 60.87 A 

2 21.74 39.13 B 

5 39.13 

15 1 15.15 81.83 B 

2 3.03 18.18 A 

5 75.76 

6 1.52 

11 4.55 

16 5 3.00 97.50 B 

6 92.50 2.50 A 

8 2.50 

11 2.00 

17 5 10.56 85.72 B 

6 65.22 14.29 A 

8 14.29 

11 9.94 

20 1 6.85 77.63 B 

2 15.53 22.38 A 

5 14.16 

6 59.82 

11 3.65 

Table 7. Listed are the soil types, percent of each soil type, and the percent of 

the combined soil types in each stream basin. The combined soil types means 

the soils with similar pH ranges were combined to obtain a percentage in each 

stream basin. Refer to Figure 4 for formal soil names. A = "more" acidic soil 

types 1, 2, and 8. B = "less" acidic soil types 5, 6, and 11. 

41

Overview 

DISCUSSION 

This study was unique to Otsego Lake in that nine tributaries and one 

outlet were studied simultaneously, over a year, to characterize them in terms of 

land use, nutrient concentrations, periphyton biomass, and periphyton taxa. 

The study of periphyton ecology can be difficult since so many factors 

contribute to variations in periphyton biomass seasonally. To measure each 

continuously for the purpose of defining trends would have required more work 

than was possible for us. The parameters measured for this study represent 

only a few of the many that could be monitored. Seasonality is an important 

parameter to consider. Locally, in the temperate zone, it is the ultimate regulator 

of fluctuations in the other environmental factors. Figure 5 shows a way in 

which physical parameters, weather, and water chemistry can be regUlated by 

seasonality and how periphyton biomass is effected by several factors at the 

same time. 

Stream Characterization 

The calculation of a trophic level index for each stream was used to 

characterize them as either agricultural, forested, or urban. The use of indices 

was an unbiased approach to group the streams based on a combination of 

data specific for each stream. As seen in Figure 7, the pertinent information 

used in the formula to calculate the indices were number of agricultural and 

forested acres and the yearly average concentrations of T-P0 4 and N0 3 . 

Table 1 shows the values of the variables in the formula. 

42

Streams 16, 17, 20, and 6 were characterized as agricultural streams. 

Based on the indices, higher values indicate more agricultural land and 

generally higher nutrient concentrations. 

Streams 15, 5, 9, and 4 were characterized as forested streams based 

on the trophic level indices (Figure 7). The lower values indicate more forested 

land than agricultural and generally lower nutrient concentrations. 

Stream 2 was characterized as urban because it flowed through the 

Village of Cooperstown. Of the ten sampling sites, the highest yearly average 

concentrations of T.P0 4 (.334 mg/l) and CI (33.42 mg/I) were recorded for this 

stream, which is typical of urban streams (Wetzel 1983). 

Affects of the Parameters on Periphyton Biomass 

The 'first two objectives of this study were to determine (1) if streams 

flowing through agricultural areas have higher nutrient concentrations than 

streams flowing through forested areas and (2) if streams with high 

concentrations of nutrients supported high periphyton biomass. 

Streams 16, 17, and 20, located in the Northern section of the Otsego 

Lake Watershed, flow mostly through agricultural land. The reduced amount of 

vegetated areas between the fields and stream banks allow more nutrients from 

runoff to enter the stream and incident light to reach the stream which 

provides energy for photosynthesis and warms the water. This situation 

provides an ideal environment for periphyton growth. Figure 9 shows the 

monthly averages of T-P0 4 and N0 3 concentrations during the collection year 

in the agricultural streams. Appendix F lists the monthly average values. The 

43

and wastes between the water and periphyton which then can enhance algal 

growth. With the slower velocities in stream 20, an efficient exchange of 

nutrients and water was not occurring. 

Stream 6 was an exception because this agricultural stream did not 

have high yearly averages of nutrient concentrations (T-P0 4 =.031 mg/I and 

N0 3 = .39 mg/I) or biomass (chlorophyll a =.305 mg/m 2 /d and AFDW =48.77 

mg/m2/d, Table 1). Although the trophic level value for stream 6 was higher 

than those for the forested streams, the yearly average nutrient concentrations 

were lower than those in some forested streams. Even though there were more 

agricultural acres than forested acres in the basin, most of stream 6 was 

bordered by forest areas (Harter 1993). Nutrient runoff from the agricultural 

areas in this basin may have been taken up mostly by the vegetation before the 

nutrients were able to reach the stream. Low nutrient concentrations, lack of 

sunlight, and cooler water temperatures (yearly average = 9.37 QC) -could 

cause periphyton biomass in stream 6 to be low. Hill Sll gj., (1988b) and 

DeNicola .e1 gj., (1992) stated that shaded streams usually limit periphyton 

biomass. 

The West side of Otsego Lake is mostly forest land that streams 4, 5, 9, 

and 15 flow through. Nutrient concentrations were generally low due to the 

vegetative canopy along the banks. Monthly averages of T-P0 4 and N0 3 in 

the forested streams are shown in Figure 15. In contrast to the agricultural 

streams, the forested streams generally had low yearly averages of nutrient 

concentrations, biomass, and water temperature (Table 1, Figures 10, 12, and 

14). Mostly vegetated basins and tree canopies along the banks incorporate 

50

nutrients, shade the streams, and maintain cooler water temperatures. 

Periphyton biomass measurements were low, in part. due to these conditions. 

Considering all the measurements taken from stream 5, it represents a 

typical forested stream. The low yearly averages of chlorophyll a and AFDW 

(. 130 mg/m 2 /d and 26.23 mg/m 2 /d, respectively) where probably due to the low 

yearly averages of T-P0 4 and N0 3 (.023 mg/I and .22 mg/I, respectively) as 

well as the low yearly average water temperature (9.52 QC) caused by the 

vegetative canopy (Table 1). 

Stream 4 was the only forested stream that was not shaded at the 

sampling site. The yearly average water temperature was 9.82 QC, just .93 QC 

below the yearly average for an agricultural stream. With light not a limiting 

factor, then the low chlorophyll a and AFDW measurements (.255 mg/m 2 /d, and 

70.45 mg/m 2 /d, respectively) may have been due to the low yearly average 

concentrations of T-P0 4 and N0 3 (.031 mg/I and .46 mg/I, respectively,Table 

1). 

Stream 15 had low yearly average T-P0 4 (.035 mg/I) and NOs (.47 mg/I) 

concentrations and cooler water temperatures (yearly average =9.80 QC, Table 

1). The latter caused by the surrounding vegetation. Despite the low nutrient 

concentrations, the yearly average of chlorophyll a (.643 mg/m 2 /d) was higher 

than stream 20 (an agricultural stream) and the yearly average of AFDW 

(91.55 mg/m 2 /d) was comparable to the yearly averages for the agricultural 

streams. The higher yearly average chlorophyll a in stream 15 may have been 

due to VEL and TRB, the same parameters that may have caused the lower 

chlorophyll a yearly average in stream 20. In stream 15, the yearly average 

52

VEL was faster (2.26 m/s) and the yearly average TRB was lower (7.22 ntu) 

than in stream 20 (Table 1). 

Stream 9 is an exception to forested stream trends. Although the trophic 

level value was low, the yearly average concentrations of T-P0 4 and N0 3 

(.058 mg/I and .69 mg/I, respectively) were much higher than those in the other 

forested streams (Table 1 and Figure 10). The yearly average of T.P0 4 in 

stream 9 was higher than three agricultural streams. Aerial photographs show a 

long section of stream 9 as having forest land on the North side and agricultural 

land on the South side. The higher nutrient concentrations, especially T-P0 4 , 

apparently result from the stream flowing adjacent to this working farm. 

Phosphorus ions tend to adsorb onto sediment particles (Meyer .e.t sil., 1988). 

As sediment is eroded from the land surface and stream banks during a storm, 

the adsorbed phosphorus ions are transported to the stream. Runoff could enter 

the stream since the land does slope in that direction. Strip farming began in 

1993, which helps to reduce the amount of runoff and sediment that could 

potentially reach the stream (Harter 1993). Two more possible sources of runoff 

are the nearby condominiums and the road, which occasionally borders the 

stream. 

Even though nutrient concentrations were high, the biomass yearly 

averages were quite iow in stream 9 (chlorophyll a =.228 mg/m 2 /d and AFDW 

= 45.64 mglm 2 /d, Table 1 and Figure 12). This could be due to the coolest 

yearly average of water temperature (9.22 QC). The low biomass measurements 

may also be caused by the high yearly average turbidity (29.16 ntu). 

The yearly average concentrations of T-P0 4 and CI in stream 2, the 

53

During storm events the rainwater transports nutrients from the various 

sources in the village directly to the stream. In Cooperstown, there are fewer 

vegetated areas, in contrast to forested and agricultural stream banks, to 

reduce the amount of nutrients getting into the stream, therefore, stream 2-reacts 

differently than the other streams during a storm event. Nutrient concentrations 

and stream discharge quickly increase and then peak shortly after a storm 

begins, sometimes within minutes, and then they decrease at a bit slower rate 

as the storm continues (Albright 1993). The other streams, having more of a 

buffering area near the stream banks, do not respond to storm events as 

quickly; the increases and decreases are-more gradual (Albright 1993). 

Without vegetated areas along the banks (of stream 2 in the village) to absorb 

excess water and nutrients, nutrient concentrations and stream discharge 

increase rapidly and to a greater degree than the other streams. 

Stream 2 had the lowest yearly average of chlorophyll a (.032 mglm 2 /d) 

and AFDW (16.28 mg/m 2 /d, Table 2 and Figure 12). The cool water 

temperatures (yearly average = 9.64 QC) and shade probably inhibited some 

periphyton growth, but the most important factor may have been storm events. 

As previously mentioned, the discharge increased rapidly, especially with no 

buffering zone. The current can become so swift at times that periphyton may 

have been torn away from the plexiglass plates or the arti'ficial substrate holder 

was carried downstream by the current. These conditions in this stream are not 

favorable for periphyton growth. 

Only broad generalizations can be made based on the explanations 

given for the high and low yearly averages of the biomass measurements in the 

55

agricultural, forested, and urban streams. The use of nutrient concentrations to 

only roughly estimate what the periphyton biomass could be seems 

acceptable, but should not be based solely on them. This statement is derived 

from a study done by Biggs .e1 al.. (1989). They suggest periphyton be 

analyzed simultaneously with hydrological factors and not base the periphyton 

changes on nutrient concentrations alone. Each stream is unique in the way 

periphyton reacts to the influences of limiting factors. These influences either 

enhancing or inhibiting periphyton growth, vary seasonally. Therefore, 

seasonality, in this geographic location, seems to be the regulator of periphyton 

biomass changes. Nutrient concentrations, incident light, and water 

temperatures, velocity, and turbidity are influential parameters, but there are 

many more (such as oxygen and silicon concentrations, type of natural 

substrate in the stream bed, and depth of stream) in a stream environment and 

as many as possible shou Id be considered when estimating periphyton 

biomass. 

Regression analyses of biomass and the parameters in each stream 

shown in Tables 8 and 9 support the above statement by Biggs msil., (1989). 

Chlorophyll a as weli as AFDW were compared to the individual parameters 

(Table 8). The low regression values indicate no strong relationships between 

the biomass and these factors. Biomass changes cannot be explained by just 

one parameter. Table 9 shows the regression values between chlorophyll a as 

well as AFDW and the combination of all the parameters studied in each 

stream. The increased r 2 values are evidence that periphyton biomass 

changes are influenced by several factors simultaneously. Other parameters, 

56

in addition to those measured in this study, must be influencing biomass 

changes, indicated by the r 2 values not being 100%. Since stream 2 lacks 

sufficient monthly biomass measurements, regression analysis could not be 

calculated. 

Regression Analyses for Chlorophyll a and Each Parameter 

Stream # .1_._4 L_._L-_a 15 16 17 2.Q 

T- P04 0.118 0.331 0.023 0.008 0.363 0.093 0.106 0.056 0.017 

N0 3 

0.258 0.067 0.015 0.195 0.108 0.218 0.049 0.088 0.004 

CI 0.140 0.183 0.084 0.213 0.362 0.083 0.169 0.051 0.301 

TRB 0.012 0.060 0.020 0.065 0.040 0.024 0.132 0.402 

VEL 0.110 0.048 0.209 0.565 0.102 0.269 0.543 0.142 0.062 

TMP 0.027 0.028 0.040 0.117 0.001 0.046 0.144 0.033 0.003 

Table 8. Shown are the results (r 2 values) of regression analyses between 

chlorophyll a and the individual parameters in each stream. Low r 2 values 

indicate no single parameter can explain the changes in biomass during the 

collection year. Monthly averages 'from Appendices E, F, and G were used in 

these analyses. 

57

Regression Analyses for AFDW and Each Parameter 

Stream # 1 4 5 6 9 15 16 17 20 

T-P0 4 

0.246 0.003 0.009 0.051 0.039 0.026 0.047 

NOa 0.348 0.113 0.039 0.008 0.404 0.237 

CI 0.110 0.028 0.203 0.560 0.016 0.008 0.095 0.004 

TRB 0.070 0.264 0.003 0.031 0.187 0.009 0.007 0.183 

VEL 0.235 0.303 0.157 0.086 0.061 0.179 0.249 0.022 0.049 

·rMP 0.379 0.002 0.331 0.007 0.225 0.158 0.178 0.205 

Table 8 continued. Shown are the results (r2 values) of regression analyses 

between ash-free dry weight and the individual parameters in each stream. Low 

r 2 values indicate no single parameter can explain the changes in biomass 

during the collection year. Monthly averages from Appendices E, F, and G 

were used in these analyses. 

Stream # Chi a AFDW 

1 0.522 0.676 

4 0.570 0.885 

5 0.478 0.582 

6 0.660 0.309 

9 0.978 0.491 

15 0.832 0.848 

16 0.795 0.625 

17 0.390 0.133 

20 0.599 0.395 

Table 9. The regression analyses of chlorophyll a as well as ash-free dry 

weight and the six parameters combined (total phosphorus, nitrates, chlorides, 

turbidity, velocity, and water temperature) are shown. Higher r2 values indicate 

that several parameters, collectively, influence periphyton biomass changes. 

Monthly averages from Appendices E, F, and G were used in these analyses. 

58

Cladophora glomerata, Meridion circulare, and Diatoma vulgare. Clearly, more 

periphyton genera will appear in spring and similar combinations of genera will 

appear in the streams despite the variation in nutrient concentrations between 

the streams. 

In general, ttle same trends described for the agricultural streams were 

found in the forested streams. T2ble 5b shows the identified periphyton genera 

in each forested stream during each season. Table 3b shows the seasonal 

average concentrations of T-P0 4 and N0 3 for the forested streams. Periphyton 

were identified from the plexiglass plates in the artificial substrate holders. 

During some seasons, especially winter, the artificial substrate holders were 

either unretrlevable or lost (see Appendix E for dates of missing data). 

Therefore, the trends are not as. clear as in the agricultural streams. An 

increase in the number of genera in spring is seen in streams 9 and 15, the 

same number of genera found in summer were also found in spring in stream 5, 

and stream 4 had the least number of genera in the spring. Again, nutrient 

concentrations varied between the streams in spring (T-P0 4 = .021 - .042 mg/I 

and N0 3 = .20 - 1.10 mgll) and the same genera were found. In stream 5, 9, 

and 15, similar identified genera included G. olivaceum, C. glomerata, M. 

circulare, and Cocconeis spp. Cladophora glomerata and M. circulare were also 

common to stream 4. 

Although the overall seasonal averages of nutrient concentrations were 

higher in the agricultural streams than forested streams, several genera were 

common to them. For example, stream 20 had one of the highest seasonal 

averages of T-P0 4 and N0 3 concentrations and stream 5 had the lowest 

60

Sm ith (1965) fall is the season of active vegetative growth for Spirogyra spp. 

Fragilaria spp. were identified during late summer and early winter in this study. 

Correlating with these results are findings by Nielson §;.1 ai., (1984) in which 

Fragilaria spp. were also identified during the same seasons and on artificial 

substrates, but in the Spokane River, WA. Identified genera that did not appear 

frequently were Closterium moniliforme , (only in stream 6), Achnanthes spp., 

Cymbel/a spp., Diatoma elongata, and Vaucheria spp. 

Bedrock and Soil Correlations 

The correlations between bedrock and soil types found in the individual 

basins of the agricultural streams were quite consistent (Table 10). Streams 16, 

17, and 20 had a greater proportion of limestone than shale bedrock and a 

greater proportion of soil type B ("less" acidic). This correlation was not 

consistent in the basin of stream 6. Although soil type B was dominant as for 

the other agricultural streams, the basin was composed of 100% shale bedrock. 

Bedrock and soil type correlations found in the forested stream basins 

were also quite consistent (Table 10). Streams 4, 5, and 9 had 100% shale 

bedrock and had a greater proportion of soil type A ("more" acidic) in their 

basins. An exception to this correlation was stream 15. Although shale 

bedrock was dominant, a greater proportion of soil type B ("less" acidic) was 

identified in this basin. 

The bedrock and soil types in the basin of stream 2 were similar to those 

in the forested stream basins. The entire basin was shale and the only soil type 

was type A, the "more" acidic soil. 

62

% OF CMBN % OF CMBN 

STREAM # BEDROCK TYPE SOIL TYPE 

2 100.00 S 100.00 A 

4 100.00 S 50.00 A 

50.00 B 

5 100.00 S 62.16 A 

37.84 B 

6 "iOO.OO S 60.98 B 

39.03 A 

9 100.00 S 60.87 A 

39.13 B 

15 98.79 S 81.83 B 

1.21 L 18.18 A 

16 59.23 L 97.50 8 

5.32 S 2.50 A 

25.45 G.O. 

17 86.39 L 85.72 B 

11.20 S 4.29 A 

2.44 G.O. 

20 64.40 L 77.63 B 

35.60 S 22.38 A 

Table 10. Listed are the percentages of the combined bedrock types and 

percentages of the combined soil types to show correlations in the stream 

basins. Shale stream basins tend to be common under soil type A ("more" 

acidic) and limestone stream basins tend to be common under soil type B 

("less" acidic), however, there are exceptions. S = shale, L = limestone, and 

G.O. = glacial overburden. 

63

Affects of the Streams on Otsego Lake 

The fourth objective of this study was to identify any impacts the streams 

may have on the water quality of Otsego Lake. Concentration of nutrients that 

enter the lake from its tributaries are of great concern. Nutrients can originate 

from non-point sources such as agricultural lands and urban areas. Movement 

of T-P0 4 , NOs, CI , and sediment into the streams by soil erosion can be 

controlled by soil conservation practices and proper landscaping techniques. 

The two working farms on the West side of Otsego Lake and approximately 80% 

of the farms in the northern section of the watershed do follow soil conservation 

methods (Harter 1993). 

Examples of conservation practices are 1) conservation til/age 2) strip 

cropping and 3) establishment of vegetated strips. The purpose of 

conservation tillage is to allow some crop residue to remain on the field after 

harvesting it. This natural land ·cover Y 

reduces the impact of rain drops, 

increases soil moisture holding capacity, and reduces soil compaction by 

lesser use of machinery on the field, aI/ of which decrease the possibility of soil 

erosion (Anonymous 1988 and Harter 1993). Strip cropping is done on 

hillsides to reduce erosion by altering rows of crops with sad which slows water 

flow from the fields to the stream (Anonymous 1988). Vegetative filter strips are 

established on areas of crop land that are alongside streams, ponds, or other 

water sources (Anonymous 1988). Grass, trees, and other vegetation are 

planted to reduce soil erosion and runoff of nutrients and pesticides 

(Anonymous 1988), Water quality is improved by this method. If these 

practices are continued the concentrations of nutrients and sediment entering 

64

the lake will be heid at a minimum. 

Streams on the West side of the lake pose less threat to the lake since 

most of the basins are undisturbed forest land and hayfields. However, the 

potential exists for these forested lands to be logged. If harvested in a way as to 

clear-cut an area, soil erosion during storm events may alter a stream 

ecosystem and eventually the proximity of the lake near the mouth of the 

stream. 

Stream 2, the urban stream, does contribute to pollution in Otsego Lake. 

The phosphorus and chloride loading into the lake were very high in this stream 

compared to the other streams in the study (Table 2). As explained earlier, the 

T-P0 4 and NOs concentrations were high during certain seasons due to few 

buffer zones, storm events, and use of de-icing salts. 

Preventative measures can be taken by residents in the Village of 

Cooperstown and around Otsego Lake to reduce urban runoff into the streams 

and lake. Yards can be landscaped by planting trees and grass to prevent soil 

erosion. Rainwater from driveways and rooftops can be re-directed to grassy 

areas to increase absorption into the soil. Decks or sidewalks should be 

constructed of materials that will allow rainwater to soak in and direct it down 

into the soil. Drainage water from paved areas should be collected by building 

trenches made of gravel to filter the water into the soil (Harman 1991). 

65

REFERENCES 

Albright, M. 1992-1993. Personal Communication. Biological Field Station,R.D. 

#2, Box 1066, Cooperstown, NY 13326 

Anonymous. 1978. Stevens Water Resources Data Book srd ed. Leupold and 

Stevens, Inc., OR. 

Anonymous. 1988. Conservation System Workshop Manual. University of 

Illinois College of Agriculture, Cooperative Extension Service. Pp. 5-4, 5 

6, and 5-8. 

APHA, AWWA, WPLF. 1989. Standard Methods for the Examination of Water 

and Wastewater. American Public Health Association, NY. 

Biggs, B.J.F. and M.E. Close. 1989. Periphyton biomass dynamics in gravel 

bed rivers: the relative effects of flows and nutrients. Freshwater Biology 

22: 209-231. 

Blum, J.L. 1957. An ecological study of the algae of the Saline River, MI. 

Hydrobiol. 9: 361-408. 

8th Brady, N.C. 1974. The Nature and Properties of Soils. ed. Macmillan 

Publishing Co., Inc., NY. 

Bushong, S.J. and R.W. Bachman. 1989. In situ nutrient enrichment 

experiments with periphyton in agricultural streams. Hydrobiol. 178: 1-10. 

DeNicola, D.M., K.D. Hoagland, and S.C. Roemer. 1992. Influences of canopy 

cover on spectral irradiance and periphyton assemblages in a prairie 

stream. J.N. Am. Benthol. Soc. 11: 391-404. 

Dodds, W.K. 1991. Micro-environmental characteristics of filamentous algal 

communities in flowing freshwaters. Freshwater Biology. 25: 199-209. 

Dudley, T.L. and C. M D'Antonio. 1991. The effects of substrate texture, 

grazing, and disturbance on macroalgal establishment in streams. Eco!. 72: 

297-309. 

Ertl, M. 1971. A Quantitative Method of Sampling Periphyton from rough 

substrates. Limnol. Oceanogr. 16:576-577. 

66

Fuller, A.L. 1987. A study of nutrient loading/limitation in the four main 

tributaries to Otsego Lake. in 20 th Ann. Rep., S.U.N.Y. Oneonta Bio. Fld. 

Sta., S.U.N.Y. Oneonta, Oneonta, NY 

Graham, S. 1992. Personal Communication. Biological Field Station,R.D. #2, 

Box 1066, Cooperstown, NY 13326 

Harman, W.N. 1990. Otsego Lake Watershed Geographic Information System 

Poster. S.U.N.Y. Oneonta Bio. Fld. Sta., Cooperstown, NY 

Ibid., 1991; 2 nd printing. The Lake Book: a guide to reducing water pollution at 

home. Otsego Lake Watershed Planning Report #1. Dccas. Pap. No. 22. 

S.U.N.Y. Oneonta Bio. Fld. Sta., S.U.N.Y, Oneonta, Oneonta, NY 

Harter, J. 1993. Personal Communication. USDA Soil Conservation Service, 

R.D. #4, Box 430, Cooperstown, NY 13326. 

Hill, W.A. and A.W. Knight. 1987. Experimental analysis of the grazing 

interaction between a may fly and stream algae. Eco!. 68: 1955-1965. 

Ibid., 1988a. Concurrent grazing effects of two stream insects on periphyton. 

Limnol. Oceanogr. 33: 15-26. 

Ibid., 1988b. Nutrient and light limitation of algae in two Northern California 

streams. J. PhycoL 24: 125-132. 

Horner, R.A., E.B. Welch, M.A.Seeley, and J.M. Jacoby. 1990. Responses of 

periphyton to changes in current velocity, suspended sediment and 

phosphorus concentration. Freshwater Biology. 24: 215-232. 

Iannuzzi, T.J. 1991. A model land use plan for the Otsego Lake watershed. 

Phase II: the chemical limnology and water quality of Otsego Lake, New 

York. Occas. Pap. No. 23. S,U.N.Y. Oneonta Bio. Fld. Sta., S.U.N.Y 

Oneonta, Oneonta, NY 

Jasper, S. and M.L. Bothwell. 1986. Photosynthetic characteristics of lotic 

periphyton. Can. J. Fish. Aquat. Sci. 43: 1960-1969. 

Keeton, W.T. and J.L. Gould. 1986. Biological Science 4 th ed. W.W. Norton & 

Company, NY. 

67

Lamberti, G.A. and V.H. Resh. 1983. Stream periphyton and insect herbivores: 

an experimental study of grazing by a caddisfly population. Eco!. 64: 

1124-1135. 

McDiffett, W.F" AW. Beidler, T.F. Dominick, and K.D. McCrea. 1989. Nutrient 

concentration-stream discharge relationships during storm events in a 

first-order stream. Hydrobiol. 179: 97-102. 

Meyer, J.L., W.H. McDowell, T.L. Bott, J.W. Elwood, C. Ishizaki, J.M. Melack, 

B.L. Peckarsky, B.J. Peterson, and P.A Rublee. 1988. Elemental dynamics 

in streams. J.N. Am. Benthol. Soc. 7: 410-432. 

Monitek. 1990. Operating and Maintenance Instructions. Hayward, CA. 

Morris, D. 1993. Personal Conversation. USDA Soil Conservation Service, 

A.D. #4, Box 430, Cooperstown, NY 13326. 

Ibid., 1990. Otsego Lake Watershed Soils Survey, Soil Interpretations Records. 

Otsego Soil and Water Conservation District, Cooperstown, NY 

Munn, M.D., L.L. Osborne, and M.J. Wiley. 1989. Factors influencing 

periphyton growth in agricultural streams of Central Illinois. Hydrobiol. 

174:89-97. 

Nielson, T.S., W.H. Funk, H.L. Gibbons, and R.M. Duffner. 1984. A comparison 

of periphyton growth on arti'ficial and natural substrates in the upper 

Spokane River. Northwest Science. 58: 243-248. 

Peterson, e.G. and R.J. Stevenson. 1990. Post-spate development of epilithic 

algal communities in different current environments. Can. J. Bot. 68: 2092 

2102. 

Pitcairn, C.E.R. and H.A Hawkes. 1973. The role of phosphorus in the growth 

of Cladophora. Water Research. 7: 159-171. 

Power, M.E., R.J. Stout, C.E. Cushing, P.P. Harper, F.R. Hauer, W.J. Mathews, 

P.B. Moyle, B. Statzner, and I.R. W. DeBadgen. 1988. Biotic and abiotic 

controls in river and stream communities. J.N. Am. Benthol. Soc. 7: 456 

479. 

Reisen, W.K. and D.J. Spencer. 1970. Succession and current demand 

relationships of diatoms on artificial substrates in Prater's Creek, South 

Carolina. J. Phyco!. 6: 117-121. 

68

Rickard, L. V. and D. H. Zenger. 1964. Stratigraphy and paleontology of the 

Richfield Springs and Cooperstown Quadrangles, N.Y. New York State 

Museum of Science Service, Bulletin No. 396. 

Robinson, C.T. and G.W. Minshall. 1986. Effects of disturbance frequency on 

stream benthic community structure in relation to canopy cover and 

season. J. N. Am. Benthol. Soc. 5: 237-248. 

Singer, M.J. and R.H. Rust. 1975. Phosphorus in surface runoff from a 

deciduous forest. J. Environ. Qual. 4: 307-311. 

Sohacki, L.P. 1974. Limnologica! studies on Otsego Lake. In]1h Ann. Rep., 

S.U.N.V: Oneonta Bio. Fld. Sta., S.U.N.V: Oneonta, Oneonta, NV: 

Ibid., 1990-1992. Personal Communication. Biological Field Station,R.D. 

#2, Box 1066, Cooperstown, NY 13326 

Steinman, AD., P.J. Mulholland, D.B. Kirschtel. 1991. Interactive effects of 

nutrient reduction and herbivory on biomass, taxonomic structure, and 

phosphorus uptake in lotic periphyton communities. Can. J. Fish. Aquat. 

Sci. 48: 1951-1959. 

Stevenson. R.J. 1982. How currents on different sides of substrates in 

streams affect mechanisms of benthic algal accumulation. Int. Rev. Ges. 

Hydrobiol. 69: 241-262. 

Welch, E.B., J.M. Jacoby, R.R. Horner, and M.R. Seeley. 1988. Nuisance 

biomass levels of periphytic algae in streams. Hydrobiol. 157: 161-168. 

Wetzel, R.G. 1983. Limnology 2 nd ed. Saunders Publishing Co., Philadelphia, 

PA. 

Whitford, L. A and G.J. Schumacher. 1963. Communities of algae in North 

Carolina streams and their seasonal relations. Hydrobiol. 22: 133-186. 

Whitton, B.A 1970. Biology of Cladophora in freshwaters. Water Research. 4: 

457-476. 

69

COMPUTER SOFTWARE PACKAGES 

Borland International, Inc. 1992. Quattro Pro software. Version 4.0. 

Claris Corporation, Inc. September,1989. MacWrite II Release 1.1. 

Jandel Scientific. 1990. Sigma Plot software used for integration. Version 4.1. 

WordPerfect Corporation. 1990. Version 5.1, Orem UT. 

PERIPHYTON IDENTIFICATION SOURCES 

Anonymous. 1966. A Guide to the Common Diatoms at Water Pollution 

Surveillance System Stations. U.S. Department of the Interior, Federal 

Water Pollution Control Administration, Cincinnati, OH. 

Hohn, M. 1951. A study of the Distribution of Diatoms (Bacillariceae) in Western 

New York State, Cornell University Agricultural Experimental Station, 

Ithaca, NY: 

Prescott, G.W. 1962. Algae of the Western Great Lakes.Wm.C. Brown 

Company Publishers, DuBuque, IA. 

2nd Smith, G.M. 1950. The Fresh-water Algae of the United States ed. 

McGraw-Hili Book Company Inc., NY: 

70

APPENDIX A 

Explanation of Bedrock Types 

Dpm • Panther Mountain Formation 

Dark, bluish-gray shale, arenaceous shale, and flaggy fine-grained argillaceous sandstone. 

Dso • Solsville Sandstone 

Upper part: fine-grained sandstone and arenaceous shale. Middle part: dark gray, thin and unevenly bedded 

arenaceous shale. Lower part: very dark gray to black fissile shale. 

Dot - Otsego Shale 

Gray, irregularly bedded, lumpy siltstone overlying brownish-gray, fissile, soft shale. 

Dch • Chittenango Shale 

Black, fissile shale with limestone septaria and calcareous concretions. 

Sby - Brayman Shale 

Crumbly green shale overlying dark gray thin-bedded shale, argillaceous and dolomitic limestone. 

Due· Cherry Valley Limeatone and Union springs Shale undifferentiated 

Cherry Valley: black, argillaceous limestone, weathers rusty-orange. Union Springs: fissile, black shale with 

calcareous concretions and thin limestone beds. 

Don • Onondaga limestone 

Fine-grained, medium gray limestone with shaly partings and black chert. Basal member of massive, gray, 

coarse-grained crinoidallimestone with white-weathering chert and coral reefs. 

Dee - Rickard Hill (Schoharie), Limestone, Carlisle Center Shale, Esopus Shale, and Oriskany 

Sandstone undifferentiated 

Mainly buff-weathering, calcareous siltstone and shale assigned to the Carlisle Center Shale. Sporadic 

occurrence of arenaceous limestone, gray siliceous shale, and brown orthoquartzite assigned to remaining 

units. 

Ok - Kalkberg Limestone 

Medium grained, thin to medium bedded dark blue limestone with interbedded calcareous shale and black 

chert. 

Ddb • Deansboro (Coeymans) Limestone 

Coarse-grained, crinoidallimestone with massive, irregular bedding. 

Ddj • Jamesville, Clark Reservation, and Elmwood (all Manlius) and Dayville (Coeymans) Limestone 

Upper part: fine to medium grained, thin and evenly bedded limestone, stromatoporoid biostrome at top. 

Lower part: coarse-grained, crinoidallimestone, some interbedded fine-grained limestone. 

Oct - Thacher (Manlius) Limestone, Chrysler (Rondout) Dolomite, and Cobleskill Limestone 

undifferentiated 

Thacher: dark blue-black, fine-grained limestone with stromatoporiod biostromes. Chrysler. argillaceous 

shaly to thinly bedded dolomite and dolomitic limestone. Cobleskill: argillaceous mottle calcitic and dolomitic 

limestone. 

Dr - Ravena (Coeymans) Limestone 

Massive and irregularly bedded, coarse-grained crinoidallimestone. 

(Rickard et aI., 1964) 

72

APPENDIX B 

Explanation of Soil Type pH Values 

AVERAGED 

SOIL MAJOR DEPTH IN pH pH RANGE OF pH RANGE OF 

TYPE SOILS INCHES RANGE MAJOR SOilS SOIL TYPES 

1 Lordstown 0-5 4.5 - 6.5 4.5 - 6.5 4.2 - 7.8 

5 - 26 4.5 • 6.0 

26 - 30 5.1 - 6.0 

Mardin o - 8 3.6 - 6.5 3.6 - 8.4 

8 - 15 3.6 - 6.5 

15 - 60 4.5 . 7.3 

60 • 70 5.1 - 8.4 

o - 9 4.5 < 6.0 4.5 - 8.4 

9 ·29 4.5 - 6.0 

29 ·46 4.5 • 6.5 

46 - 60 5.1 - 8.4 

8 Chenango o - 8 4.5 - 5.5 4.5 - 7.8 4.4 - 7.8 

8 - 30 4.5 - 6.0 

30 - 72 5.1 - 7.8 

Valois 0-7 3.6 - 6.0 3.6 - 7.3 

7 - 30 3.6 - 6.0 

30 - 47 3.6 - 6.0 

47 - 60 4.5 • 7.3 

Howard o - 9 5.1 - 7.3 5.1 - 8.4 

9 • 24 5.1 - 7.3 

24 - 45 5.1 - 7.3 

45 - 72 6.6 - 8.4 

2 Mongaup o . 12 4.5 - 5.0 4.5 - 5.5 4.5 - 6.5 

12 - 22 5.1 - 5.5 

Wiildin 0-7 4.5 • 6.0 4.5 • 6.5 

7 - 14 4.5 - 6.5 

17-44 4.5 • 6.5 

44 - 80 5.1 - 6.5 

Lewbath o - 8 4.5 - 6.0 4.5 - 6.5 

8 - 21 4.5 - 6.0 

21 . 52 4.5 - 6.0 

52 - 80 4.5 • 6.5 

Formal name of each soil type and the pH at specific depths are shown. The 

pH range of each soil type was obtained by averaging the three lowest pH 

values of the major soils and averaging the highest pH values of the major soils. 

This overall range was calculated to be able to categorize the soil types. 

73

SOiL 

TYpe 

MAJOR 

SQILS 

APPENDIX B CONTINUED 

Explanation of Soil Type pH Values 

DEPTH IN 

INCHES 

11 Wayland o . 7 

7 . 38 

38 - 60 

Raynham 0-6 

6 . 22 

22 . 72 

Canandaigua 0-8 

8 . 30 

30 - 60 

5 Lansing 0-6 

6 . 17 

17 . 42 

42 . 65 

Conesus 0-9 

9 • 36 

36 - 60 

Honeyoye 0-8 

8 . 26 

26 - 60 

6 Honeyoye o . 8 

8 - 26 

26 . 60 

Farmington 0-8 

8 - 18 

Wassaic D 

10 

- 10 

- 28 

pH 

RANGE 

5.1 · 7.8 

5.1 · 8.4 

5.6 - 8.4 

5.1 - 

5.1 - 

5.6 · 

5.2 - 

6.1 - 

6.6 · 

5.1 · 

5.1 · 

5.1 · 

6.6 - 

5.1 · 

5.1 · 

6.6 · 

7.3 

7.3 

7.8 

7.8 

7.8 

8.4 

7.3 

7.3 

7.3 

8.4 

7.3 

7.3 

8.4 

5.6 - 6.5 

5.6 - 7.8 

7.4 · 8.4 

5.6 · 6.5 

5.6 - 7.8 

7.4 - 8.4 

5.1 - 6.5 

5.6 · 7.8 

5.6 

5.6 

74 

- 

- 

7.3 

7.8 

AVERAGED 

pH RANGE OF 

MAJOR SOILS 

5.1 - 8.4 

5.1 - 7.8 

5.6 - 8.4 

5.1 · 8.4 

5.1 · 8.4 

5.6 - 8.4 

pH RANGE OF 

SOIL TYpes 

5.3 . 8.2 

5.3 • 8.4 

5.6 . 8.4 5.4 . 8.0 

5.1 - 7.8 

5.6 · 7.8

APPENDIX C 

Collection Dates 

Collection # CQllection Dates Abbreviation 

1 9 May 1991·6 June 1991 = Jun 191 

2 6 June 1991 - 3 July 1991 = Jul 1 

92a 

3 3 July 1991 - 31 July 1991 = Jul'92b 

4 31 July 1991 -28August. 1991 = Aug '91 

5 28 August. . . . .. 1991 - 25 September 1991 = Sept'91 

6 25 September ... 1991 - 23 October 1991 = Oct '91 

7 23 October. . . .. 1991 - 20 Novem ber 1991 = Nov '91 

8 8 January..... 1992 - 5 February 1992 = Feb '92 

9 5 February.... 1992 - 4 March 1992 = Mar '92 

10 4 March 1992 - 1 April 1992 = Apr '92a 

11 1 April 1992 - 29 April 1992 = Apr 192b 

12 29 April 1992 - 27 May 1992 = May '92 

13 27 May '" .1992 - 24 Ju'ne 1992 = Jun'92 

Beginning and ending dates of each collection month. 

75

quantitative analyses of periphyton biomass and ... - SUNY Oneonta

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