AN ENVIRONMENTAL EVALUATION

OF THE

LOWER WELLAND RIVER

JULY 1993

@ Ontario

Ministry of Environment and Energy

ISBN 0-7778- 1644-X

AN ENVIRONMENTAL EVALUATION OF THE LOWER WELLAND RIVER

JULY 1993

0

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Copyright: Queen's Printer for Ontario, 1993

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PIBS 2659

AN ENVIRONMENTAL EVALUATION OF THE LOWER WELLAND RTVER

Report prepared by:

R.J Pope, K.A Keenleyside, S.D Speller Tarandus Associates Limited

for

The Niagara River Improvement Project Ontario Ministry of the Environment

JULY 1993

DISCLAIMER

The content and conclusions of this report do not necessarily reflect the views and policies of the Ontario Ministry of Environment and Energy. The data as presented are regarded as valid and can be used in additional assessments.

Mention of trade names or commercial products does not constitute endorsement or recommendation for use.

Executive Summary

An environmental evaluation of the lower Welland River was conducted by Tarandus Associates Limited during the summer and fall of 1990. The study involved an assessment of water and sediment quality, as well as an examination of aquatic flora and fauna.

The objectives of the study were:

1) to obtain a database subset for the lower Welland River for use in assessing possible remediation options where appropriate and for determining the need for further environmental investigations and;

2) to provide information for use in evaluating the significance of the Welland River regarding environmental quality issues in the Niagara River Area of Concern.

After an initial reconnaissance of the study area, field trips to the lower Welland River were completed during August and November, 1990. A total of 25 stations were evaluated. Analyses of sediments and water from these stations were conducted by Beak Analytical Laboratories.

Water quality varied considerably among stations. At several sites, iron, copper, mercury, and total phosphorus exceeded the Provincial Water Quality Objectives (PWQO). Most water-quality parameters, however, including most metals, phenols, total cyanide, PCBs, polyaromatic hydrocarbons (PAHs), and organochlorine (OC) pesticides were below detection limits.

Data from regular MOE water-quality monitoring stations indicate that levels of zinc, copper, mercury, chromium, and lead have decreased in the Welland River from 1979 to 1987. A slight increase in aluminum concentrations in water, however, has been noted from 1981 to 1987.

Sediment quality was also variable throughout the study area. Concentrations of lead, chromium, mercury, cadmium, zinc, iron, nickel, copper, arsenic, total Kjeldahl nitrogen, total organic carbon, total phosphorus, and PCBs exceeded the MOE Provincial Sediment Quality Guidelines (PSQG) lower effect limit (LEL) at some stations." The PSQG - Severe Effect Limits (SEL) for chromium, mercury, nickel, iron, and copper were also exceeded at several stations in sections B and C of the study area. Concentrations of total cyanide and oil and grease exceeded the Open Water Disposal Guidelines (OWDG) at some stations. PAHs were also detected at several stations, most notably stations 9 and 10. All organochlorine pesticides were below detection limits.

Degraded sediment quality, as indicated by concentrations of several metals, oil and grease, total cyanide, and PAHs were found at stations 9, 10, 24, 11, and 12, in the lower Welland River between the syphons, as well as at stations 17, 18, 19 and 20 in the section east of Port Robinson. Sediments at station 7, located in the western portion of the City of Welland also had elevated concentrations of

several contaminants. A number of contaminant inputs are located in the vicinity of these stations, including storm sewers, a landfill site, a water pollution control plant (WPCP), and several industries.

Ninety benthic-invertebrate taxa were identified at the 25 sampling stations. The total is significantly higher than the 28 taxa reported previously (Johnson, 1964). The number of taxa varied among stations, rajiging from a low of 12 species at stations 6 and 25 to a high of 29 species at station 10.

Two invertebrate species were common to all the sampling stations; Procladius sp. and immature tubificids, although Chryptochironomus sp. , Limnodrilus hoffmeisteri , and Sphaerium sp. were found at 24 of the 25 sites. Johnson (1964) also noted Procladius and Limnodrilus throughout the Welland River. Sampling stations located upstream of the City of Welland were characterized by relatively high numbers of Hexagenia sp. and Coelotanyus sp. These species were generally absent from stations downstream of Welland, indicating degraded environmental conditions. Stations located below the urbanized areas were characterized by relatively high numbers of the more pollution-tolerant taxa, Spirosperma ferox and immature tubificids, as well as Valvata sp., and Hydrobiidae.

The total abundance of benthic invertebrates varied among stations in the study area, and ranged from a low of 634 individuals per square meter at station 12 to a high of 5900 individuals per square meter at station 22. Generally, stations located in and below the City of Welland had higher total abundances than those located in the rural area above Welland.

Benthic-invertebrate diversity (Shannon-Weaver and Brillouin) fluctuated considerably, especially in the river below the City of Welland. Diversities at all the stations upstream of Welland were relatively constant, ranging from 3.02 to 3.53. Shannon diversities ranged from a high of 3.96 at station 1 1 to a low of 2.52 at station 25. Similar trends were noted with the Brillouin diversity index. Diversities greater than 3.0 are generally indicative of unpolluted conditions.

Discriminant analysis of the stations, based on the results of cluster analyses, indicated that benthic- invertebrate communities below the City of Welland and above the Queenston-Chippawa Canal were associated with sediments characterized by elevated concentrations of several metals including chromium, copper, and arsenic. In contrast, benthic communities at stations above the City of Welland, occurred in an area characterized by sediments having relatively low levels of metals, and a high loss on ignition. Aluminum was also found at higher concentrations in this part of the Welland River than at stations further downstream.

The fish community of the lower Welland River was dominated by warmwater species, including catfish, white crappie, carp, suckers, and freshwater drum. Salmonid species were not found in the lower Welland River, although they are common in the Niagara River.

The Welland River shoreline was dominated by several emergent aquatic macrophytes, including Typha latifoUa and Sagiitaria laiifolia. A number of submerged aquatic macrophytes were also noted including Myriophyllum spicamm, Vallisneria americana, and Ceratophyllum demersum. These species have been previously reported in the study area by Johnson (1964) and Dickman et al. (1983). Previous authors have also noted areas devoid of higher aquatic plants below several industrial discharges (Dickman and Haynes, date unknown; Dickman eral, 1983). During this study, sparse macrophyte growth was only noted below the Thompson's Creek confluence.

Table of Contents

Page

Executive Summary i

List of Tables • v

List of Figures viii

List of Appendices x

Introduction 1

Study Methods 3

The Study Area

Water Quality 5

Sediment Quality

Benthic Invertebrates

Aquatic Macrophytes

Fisheries 9

Flow Measurements 10

Statistical Analyses H

1) Indices H

i) Shannon-Weaver Diversity Index 11

ii) Brillouin Diversity Index 12

2) Cluster Analysis 12

3) Principal Components Analysis 13

4) Discriminant Analysis 13

Results and Discussion 15

Water Quality 15

Sediment Quality . 27

Benthic Invertebrates 44

Table of Contents (continued)

i) Species Composition, Abundance, and Diversity 44

ii) Benthic Community Classification 51

iii) Environmental Quality Evaluation 54

Fisheries 60

Aquatic Macrophytes 62

Flow Measurements 64

Conclusions .65

Water Quality 65

Sediment Quality 65

Benthic Invertebrates and Environmental Quality 66

Fisheries 67

Aquatic Macrophytes 67

References 69

List of Tables

Table Page

1 The four sections of the study area 5

2 Analytical parameters - water 6

3 Analytical parameters - sediment 7

4 Sediment-quality parameters evaluated during the fall surv 8

5 Sediment-quality parameters used in discriminant analysis 14

6 Water-quality parameters below detection limits in all the

Welland River water Samples

7 Polycyclic aromatic hydrocarbons and their associated detection limits 23

8 Organochlorine pesticides and their associated detection limits 24

8b MOE results for concentrations of chlorinated organics in water

at stations 6 and 21. 25

9 A comparison of the water-quality of the Welland River with

selected river systems in the area 27

10 Provincial Sediment Quality Guideline levels and their significance 28

11 Concentrations of PAHs in Welland River sediments collected

during the summer survey 33

List of Tables (Continued)

Table Page

12 Concentrations of PAHs in Welland River sediments collected during the fall survey

34

12 b MOE results for concentrations of chlorinated organics at ^

sites 6, 9, 15 and 21. 35

13 Organochlorine pesticides and associated detection limits in sediment 38

14 Summary of sediment quality at all stations based on the PSQGs 40

15 Comparison of selected sediment-quality parameters at station 9 41

16 Comparison of selected parameters in sediments collected offshore

of the Atlas outfall . 41

17 A comparison of Welland River sediments with sediments from

Thompson's Creek, Lyon's Creek, and the Niagara River. 43

18 Number of taxa, total abundance, and diversity (Shannon and Brillouin)

for all stations 50

19 Correlations between the sediment parameters and the first two

discriminant functions for the benthic-invertebrate communities 56

20 Mean concentrations of the sediment parameters associated with the

benthic-invertebrate communities 56

21 Correlations between the sediment parameters and the first two discriminant functions for the three benthic communities in the Welland River 59

List of Tables (Continued)

Table , Page

22 Fish species caught in the Welland River during the summer and fall survey 61

23 Numbers of fish caught in hoop-net sets in sections A, B, and C 62

24 Species of submergent and emergent aquatic macrophytes found in the

study area during the summer survey 63

List of Figures

Figure Page

1 Welland River study area 2

2 Welland River sampling locations 4

3 Concentration of zinc, copper, chromium, mercury, and lead

in water samples collected at the Montrose Bridge from 1979 to 1987 18

4 Aluminum concentrations in water samples collected at the Montrose

Bridge and Port Robinson from 1981 to 1987 19

5 Total phosphorus levels in water samples collected at the Montrose -

Bridge, Port Robinson, and the Welland Airport from 1979 to 1987 20

6 Mean-yearly TKN levels in water samples collected at the Montrose

Bridge, Port Robinson, and the Welland Airport from 1979 to 1987 22

7 Tubificid abundances 45

8 Chironomid abundances 46

9 Hexagenia abundances 47

10 Total Oligochaete abundances 49

11 Cluster analysis results using Euclidean distance and Ward's method 52

List of Figures (Continued) Figure Page

12 PCA results of benthic-invertebrate abundance 53

13 Plot of benthic-invertebrate communities in discriminant space as defined by

the first two discriminant functions 55

14 Plot of the Welland River benthic-invertebrate communities in discriminant

space as defined by the first two discriminant functions 58

List of Appendices

Appendix Page

I Water Quality Graphics 73

II Sediment Quality Graphics 81

III Field observations of conductivity, dissolved oxygen,

and water temperature during the fall survey 97

IV Benthic-invertebrate species list 101

V Benthic-invertebrate species counts 107

VI Benthic-invertebrate species abundances 129

VII Taxonomic composition of benthic communities 139

VIII Component loadings for the PCA 145

IX Fish species found in the study area 149

X Flow calculations for sections A, B, and C 153

XI Water Quality Data 157

XII Sediment Quality Data 165

Introduction

In July, 1990, Tarandus Associates Limited was contracted by the Ontario Ministry of the Environment (MOE) to complete an environmental evaluation of the lower Welland River (Figure 1). The study included an assessment of water and sediment quality, as well as an evaluation of aquatic flora and fauna.

The objectives of the study were:

1) to obtain a database subset for the lower Welland River to allow assessment of remediation similar to that presently underway for the Niagara River as well as to determine the need for further environmental investigations and;

2) to provide information for use in evaluating the significance of the Welland River regarding environmental quality issues in the Niagara River Area of Concern.

A number of environmental studies have been completed on the Welland River, including sediment and water quality assessments (Kaiser and Comba, 1983; Brindle etal. , 1988; Johnson, 1964; Hart, 1986; Acres, 1990), fisheries studies (Johnson, 1964; Steele, 1981), benthic invertebrate surveys (Johnson, 1964), and aquatic-macrophyte surveys (Dickman et al., 1980; Dickman e[ al, 1983; Dickman and Hayes, date unknown). Much of the information in the earlier studies is appropriate only for historical purposes, given that the discharges to the river have changed significantly in recent years.

Twenty six years ago, Johnson (1964) concluded that domestic sewage and industrial wastes led to serious water quality impairment in the lower Welland River. More recently, a number of sources of contaminants to the Welland River have been identified and investigated. Industrial sources include Atlas Specialty Steels, Cyanamid Canada Inc., B. F. Goodrich and Ford Motor Company. Various municipal sources such as the Welland Water Pollution Control Plant (WPCP), and a number of combined sewer outfalls and overflows also exist (NRTC, 1984).

Study Methods

The Study Area

The Welland River is approximately 70 kilometres long, and extends from just south of Hamilton to the Queenston-Chippawa Power Canal. The section of the Welland River from Chippawa westwards to the Queenston-Chippawa Power Canal is 6.4 km long and is locally known as Chippawa Creek. This portion of the Welland River now flows westerly carrying Niagara River water to the power-canal delta where it mixes with Welland River water and proceeds down the Queenston-Chippawa Power Canal. The Welland River drains an area of approximately 906 km' and has an average gradient of three feet per mile to the Chippawa- Queenston Power Canal. The Welland River is not navigable where it flows beneath the old and new Welland Ship Canals by way of inverted syphon systems.

The study area extends from O'Reilly's Bridge, which is located south of the Welland Airport, to the lighthouse in King's Bridge Park at Chippawa, excluding the Queenston-Chippawa Power Canal. The study area was separated into four sections: A, B, C, and D (Table 1) based on access, the various land uses, and the nature of developments in each section (Figure 1).

A total of 25 stations were selected for water and sediment analyses, and benthic-invertebrate collections (Figure 2). Fish were sampled at three net-set locations. Station locations were selected in consultation with MOE personnel. Sampling intensity was increased in sections B and C where industrial and municipal discharges are more common. Sampling was reduced in section A, where agricultural land uses are predominant, and in section D, where the flow consists of Niagara River water exclusively. The field work for this project was completed during the periods of August 20th to the 24th, 1990, and November 6th to the 9th, 1990.

Table 1 : The four sections of the study area.

Section (See Fig. 2)

General Description

A - O'Reilly's Bridge to the old Welland Canal

limited residential predominately rural agricultural activities common

B - old Welland Canal to the new Welland Canal

mostly residential

several municipal discharges

several industrial discharges

water diverted from the old Welland

Ship Canal

C - the new Welland Canal to the power canal

D - the power canal to the Niagara River

predominately rural several industrial discharges

Niagara River water diverted to the power canal through this section predominately rural

Water Quality

Water samples were collected at all stations with the use of a Van Dorn water-sampler. Each station sample was a composite of water taken at a depth of 1 meter below the surface at three locations: from the middle and from both sides of the river. All samples were placed in the appropriate labelled containers and were preserved as necessary. Samples were stored in a cooler on ice, until delivery to the laboratory for chemical analysis.

Water samples were collected from all 25 stations between August 20th and August 24th, 1990. These water samples were analyzed for either an "extensive list" or an "indicator list" of parameters (Table 2). Samples from stations 1, 9, 15, 21, and 23 were analyzed for the "extensive list" of parameters, and the remaining 20 stations were analyzed for the "indicator list". Water temperature, dissolved oxygen, and pH were determined in the field at all stations.

Table 2:

Analytical parameters in Appendix XI.

water. A glossary of parameter abbreviations is presented

Extensive List

Indicator List

Metals

Pb, Zn, Cd, Cr, Fe, Se, As, Sb, Ba, Be, Co, Cu, Mo, Ni, V, Ag, Hg, CN, Mn, Mg Al

Pb, Zn, Cd, Cr, Cu As, Hg, CN, Al

Organics

PCB/OC pesticide scan PAHs, Phenolics

PCB/OC pesticide scan Phenolics

Nutrients

NH4, TP, TKN, NO., NO3

TP, TKN

Miscellaneous

pH, conductivity, dissolved oxygen turbidity, colour, suspended solids temperature

pH, conductivity, dissolved oxygen turbidity temperature

A second set of water samples was collected from all stations during the period of November 6th to the 9th, 1990. All of these water samples were analyzed for phenolics. Water samples from stations 1-10, 15, 21, and 23 were analyzed for aluminum and copper, and samples from stations 1-5, 10, 15, 21 and 23 were analyzed for mercury. Water temperature, conductivity, and dissolved oxygen measurements were determined in the field, at most stations. Dissolved oxygen depth-profiles were also taken at some stations.

All water analyses were conducted by Beak Consultants Limited according to standard analytical methods approved by MOE. In addition, water samples were collected from stations 6 and 21 for subsequent analysis at the MOE laboratory in Rexdale. Chemical parameters included volatile organics, extractable organics, and organochlorine pesticides.

Spatial and temporal trends in water quality were examined throughout the study area. Data from previous studies, when available, were also incorporated in these analyses. Water-quality results were compared to the MOE Provincial Water Quality Objectives (PWQO) where .possible, and to the water quality of other river systems in the area.

Sediment Quality

Surficial sediments were collected with a stainless-steel ponar grab sampler, and consisted of composites of three sub-samples taken at the middle and both sides of the river. All sediment samples were homogenized and placed in appropriate labelled jars. Miscellaneous observations regarding sediment texture and colour, as well as the presence of any odour or oily sheen were also recorded where evident.

Sediment samples were collected at a total of 25 stations during the period of August 20th to the 24th, 1990. Samples from stations 1,9, 15, 21, and 23 were analyzed for an "extensive list" of parameters, and the remaining 20 samples were analyzed for an "indicator list" (Table 3).

A second set of sediment samples was also collected during the November survey. A modified set of chemical analyses based on the results of the August survey was conducted on each of these samples (Table 4).

Table 3: Analytical parameters - sediments

Extensive

Indicator

Metals

Pb, Zn, Cd,.Cr, Fe, Se, As, Sb, Ba, Be, Co, Cu, Mo, Ni, V,

Ag, Hg, CN, Mn, Mg Al

Pb, Zn, Cd, Cr, Cu As, Hg, CN, Al

Organics

PCB/OC pesticide scan PAHs, Phenol

PCB/OC pesticide scan Phenol

Nutrients ' TP, TKN, TOC, LOI LOI

Miscellaneous pH, SAR, Oil and Grease pH, Oil and Grease

Table 4: Sediment-quality parameters evaluated during the fall survey.

Parameter(s)					Stations
Zn, Cd, Mn, Co, Cu, Total Cyanide (CN) Mercury (Hg) Arsenic (As) PAH Scan PCB Oil and Grease	Fe,	Pb,	Cr,	Ni	5-19,20 17-22 7-13 7-10,11-20 1,3,5,7-10, 15 1, 3, 5, 7-10, 15, 19a, 21, 23 1-23

All sediment analyses were completed by Beak Consultants Limited according to standard methods approved by MOE.

In addition, sediments were collected from stations 9, 15 and 21 at the request of MOE for subsequent analysis at the MOE laboratory in Rexdale. Parameters determined included volatile organics, extractable organics, organo-chlorine pesticides, and dioxins.

Trends in sediment quality were examined throughout the study area. Data from previous studies, when available, were also used for these analyses. Sediment-quality results were compared to Provincial Sediment Quality Guidelines (PSQG), and to the sediment quality of other local river systems such as Thompsons Creek, Lyons Creek and the Niagara River.

Benthic Invertebrates

Benthic-invertebrate samples were collected from the middle and both sides of the river at each of the 25 stations in August, for a total of 75 samples. All samples were collected with the use of a ponar grab sampler, and the sediments were sieved through a 200-u mesh sieve-bucket. Residual materials were placed in appropriately labelled jars, and preserved in 10% buffered formalin.

All samples were manually washed, picked, and sorted to separate all organisms from associated debris. All samples were picked in their entirety with the use of a stereomicroscope. The organisms found in each sample were sorted into similar taxonomic groups and placed in separate labelled vials for subsequent identification.

All benthic invertebrates were identified to the lowest practical taxonomic level by Dr Richard Vineyard and Mr Brad Hubley of the firm Original Insect Ideas. Prior to identification, tubificids and chironomids were cleared and mounted on labelled microscope slides with the use of polyvinyl lactophenol. In cases where the immature forms of some invertebrates prevented identification to species, classification was usually completed to the genus level.

All sorted invertebrate samples were provided to MOE at the completion of the project. In addition, a reference collection was prepared for use in confirming identifications and to ensure the repeatability of the benthic invertebrate classification in future studies. Slides were labelled with species identification, date, location, taxonomist and station.

All species counts were tabulated by sample and station, and were converted to abundance counts (number/m^) for use in subsequent statistical analysis.

Aquatic Macrophytes

A visual qualitative assessment of the aquatic-macrophyte community was completed at all stations in the study area. Assessments of both submergent and emergent macrophytes were completed, including observations regarding species present, dominant species, and the presence of any unusual or rare plants. Photographs of existing aquatic-macrophyte communities in the study area were also taken where possible to supplement the community descriptions.

A species list of aquatic macrophytes was prepared for the study area. Trends in species composition and species association were noted, and any atypical occurrences were recorded. Unusual community patterns, particularly those that may result from anthropogenic disturbances were also described.

Fisheries

Fish were collected during both field trips to evaluate community composition in the study area. A Scientific Collector's Fish Permit was obtained from the Ministry of Natural Resources in Fonthill before the field work for the fish survey was initiated.

Sampling methods included the use of hoop nets, a seine net, and minnow traps. The identity of all species sampled during the survey was recorded, and any observations of abnormalities, disease, or parasites were noted. All fish were released alive if possible.

The hoop nets used during the study had a rectangular opening of approximately 47 by 38 inches (190.5 by 96.5 cm) and hoops measuring about 36 inches (91.4 cm) in diameter. The hoop-net enclosure measured approximately 20 feet (6.1 m) in length, and had an attached lead of 100 feet (30.5 m). At all sets, the lead was attached to trees or rocks at the shore, and the trap was positioned in deeper water at an angle that varied from about 45° to 90° to the shoreline. Water

depths in which the hoop net was set ranged from 1.0 to 2.5 meters. This fish survey was intended to provide general overview information only and was not designed to be a detailed assessment of the fish populations in the Lower Welland River.

A total of 5 hoop-net sets were completed during the summer and fall surveys. The hoop net was set once in sections A, B, and C during the August survey and once in sections A and C during the November survey. Each hoop-net set was placed overnight for a period of approximately 24 hours. All net-set locations are illustrated in Figure 2.

Fish were also collected with the use of a 5-meter beach seine at a number of locations in sections A, C, and D during the August survey. The steep banks of section B prevented the completion of any seining in that part of the river.

A total of 8 minnow traps were also set in sections A, B, and C. The traps were baited with bread and set overnight.

Flow measurements

Water velocity was measured with the use of a Montedoro-Whitney portable velocity meter at 5-meter intervals across several sections of the river. Velocity measurements were taken at 0.2 and 0.8 times the water depth at each measuring point as recommended by Arseneault (1976). Individual velocity measurements consisted of the average instantaneous velocity measured during a 20 second time interval. A number of surface spot velocities were also recorded at several stations.

Flow calculations were completed using the Velocity-Area Method. This technique involves dividing a cross-section of the river into a number of segments, each bounded by imaginary vertical lines from the water surface to the stream bed. The area of each segment is determined and the mean velocity of water flowing through it is determined from velocity measurements. The discharge for each segment is computed by multiplying the area of the segment by the corresponding mean velocity, and these individual discharges are added to obtain the total discharge.

10

Statistical Analyses

Several methods of data analysis were used to evaluate water and sediment quality, and selected biotic communities in the study area. Statistical methods were generally selected because of their recognized utility in delineating spatial and temporal variation, or ability to quantitatively summarize associations and trends. A brief summary of the rationale and application, and the mathematical formula for each analysis is presented below.

1) Indices

Indices provide a simple method of summarizing complex data. They are derived variables such as a ratio of one variable divided by a standard variable. When applied to invertebrate data, such indices generally involve ratios of numbers of taxa and numbers of individuals in the collected samples. These indices have interpretive value as data summaries.

i) .Shannon-Weaver (or Shannon-Weiner) Diversity Index (H')

Diversity is a measure of the distribution of observations among categories (e.g. species). When applied to communities of invertebrates, diversity calculations incorporate counts of organisms within each taxonomic group. A low diversity is the result of a concentration of invertebrates in few categories; and conversely, a more uniform distribution of organisms among all categories results in a high diversity. Diversities greater than 3.0 are indicative of an unpolluted environment, whereas diversities less than 1.0 indicate severely polluted conditions ( Weed and Rutschlcy, 1972). The formula for the Shannon-Weaver diversity index, H' is:

N. N.

n -^ n

where n = the total number of individuals in the sample N , = the number of individuals in the "i"th sample S = the number of categories (taxa) with known proportional abundance

ii) Brillouin Diversity Index

Brillouin's Diversity H, is "the species diversity per individual of a collection in which all n specimens have been assigned to one of s species, and counted to give the N,'s" (Kaesler et al. , 1978). Unlike Shannon's index, it can give the actual diversity of a fully censused collection of invertebrates. In addition, it is an actual measurement of the diversity of the sample, and is not just a statistical estimate. The formula used to determine Brillouin's index of diversity is given below:

H=— (logi2! -^ logN^

where n = the total number of individuals in the sample N i = the number of individuals in the "i"th sample S = the number of categories (taxa) with known proportional abundace

2) Cluster Analysis

Benthic invertebrate communities were defined with the use of cluster analysis, which reduces the species abundance data to a graphical summary. The resultant groups or clusters characterize relatively homogeneous species assemblages (Green, 1979). The significance of group separation relative to environmental variables can be evaluated by multiple discriminant analysis, which is discussed on the following page.

In order to confirm the robust nature of the results, several cluster analysis techniques were used, including:

i) Minimum Variance Clustering (Ward's Method) ii) Group Average Clustering iii) Centroid Clustering

Cluster analysis was completed on abundance data and presence/ absence data with use of' SYSTAT software (Wilkinson, 1988).

Some problems may be encountered in the use of cluster analysis, including: (i) the subjective choice of clustering method and similarity measure will affect the outcome; and (ii), clusters may be produced when they do not exist (Jackson er ai, 1989). The patterns revealed by the cluster analyses were confirmed with the use of Principal Components Analysis (PCA).

3) Principal Components Analysis

Principal components analysis (PCA) was used to analyze the benthic invertebrate data and to verify station groupings defined by cluster analysis. PCA is a technique for deriving linear combinations of the original variables, called principal components, that are orthogonal to one another, and that successively account for the largest portion of the residual sample variance (Rogers, 1971). This method, as with most multivariate statistics that reduce the dimensionality of multivariate observations, is used to generate a smaller number of variables that summarize most of the information contained in the original variables.

The "factor loadings" produced during principal components analysis are correlation coefficients between each original variable and each principal component. Since species abundance data rarely conform with the linearity assumptions associated with the use of correlations and covariances in PCA (Ludwig and Reynolds, 1988), we chose to use rank correlations in the PCA's (Rising and Somers, 1989). The data were ranked prior to completing the PCA, and the first two or three factors were graphed for presentation in this report.

The PCA's were calculated with use of the SYSTAT computer program and were presented graphically with use of SYGRAPH software (Wilkinson, 1988).

4) Discriminant Analysis

Discriminant analysis was used to evaluate differences among the defined benthic communities with respect to environmental conditions (sediment parameters). Discriminant analysis is a multivariate technique used to distinguish groupings (e.g. communities) on the basis of a series of quantitative descriptors (e.g. sediment chemistry). The resultant discriminant axes (functions) are linear combinations of the sediment chemical variables that maximize differences between the groups of communities. Each axis is mterpreted with the use of correlation coefficients (r) between the discriminant functions and the original sediment parameters.

Eleven sediment variables were used to discriminate between benthic communities (Table 5). Grain (particle) size data was not available and could not be used in the analysis.

Table 5 : Sediment-quality parameters used in discriminant analysis.

METALS	NUTRIENTS	OTHERS
Zinc	Loss on Ignition	Oil and Grease
Cadmium		pH
Copper
Lead
Chromium
Aluminum
Mercury
Arsenic

All variables were logarithmically transformed prior to use in discriminant analysis. Concentrations below detection limits were set equal to the detection limit.

Discriminant analysis was completed on the benthic communities defined by cluster analysis, as well as on individual sampling stations. Discriminant analysis was conducted using SYSTAT computer software. Double precision was used during the analysis, as discriminant analysis is particulariy sensitive to rounding errors (Green, 1979).

Results and Discussion

Water Quality

Water quality was evaluated at a total of 25 sites on the Welland River (Appendix I and Appendix XI). Water quality varied among stations, with concentrations of several parameters (including iron, copper and mercury) exceeding Provincial Water Quality Objectives (PWQO's) at some stations. Several water-quality parameters were below detection limits. A list of metals and other parameters which were below detection limits is presented in Table 6.

Table 6: Water-quality parameters below detection limits in all the Welland River water samples.

	Chemical
Parameter	Symbol	Detection Limit
Cadmium	Cd	0.002 mg/L
Cobalt	Co	0.005 mg/L
Lead	Pb	0.01 mg/L
Chromium	Cr	0.005 mg/L
Nickel	Ni	0.005 mg/L
Beryllium	Be	0.005 mg/L
Molybdenum	Mo	0.005 mg/L
Vanadium	V	0.005 mg/L
Arsenic	As	0.005 mg/L
Antimony	Sb	0.002 mg/L
Selenium	Se	0.001 mg/L
Silver	Ag	0.005 mg/L
Phenolics		0.001 mg/L
Total Cyanide	CN	0.002 mg/L

Following is a summary of the water-quality results. Concentrations of water-quality parameters are illustrated in Appendix I. ^

Iron

Iron concentrations exceeded the PWQO at stations 1, 15, and 21 (Appendix I); and levels of iron ranged from a low of 0.06 mg/L at station 23 to a high of 2.1 mg/L at station 1. Iron levels reported by Hart (1986) near the Queenston-Chippawa Power Canal ranged from 0.420 mg/L to 0.840 mg/L respectively. A study by Johnson (1964) throughout the river noted levels between 0.62 mg/L and 6.16 mg/L.

Copper

During the summer survey, copper levels exceeded the PWQO at all stations with the exception of stations 3, 10a, 15, 19a, and 23. Levels of copper were reduced during the fall survey; however stations 2, 4, 10, 15, and 23 exceeded the PWQO. Copper concentrations ranged from below detection limits to 0.05 mg/L. Concentrations reported by Hart (1986) were within this range.

Mercury

Mercury concentrations ranged from a low of <0.05 fxg/l at most stations to a high of 0.30 /xg/1 at station 1 (Appendix 1). Mercury levels exceeded the PWQO at stations 1,2, and 3 during the summer survey; however all the stations had concentrations below detection during the fall survey.

The high concentrations of mercury in water samples from stations 1 - 3 may be due to the bacterial methylation of mercury in an upstream reservoir (Lake Niapenco). Mercury levels may have been lower during the fall survey because of lower water temperatures which reduce the metabolic activity of bacteria. Mercury concentrations reported by Hart (1986) near the Queenston-Chippewa Power Canal ranged from below detection to 0.02 mg/L.

Aluminum. Magnesium, and Zinc

Aluminum levels ranged from a low of 0.09 mg/L at station 9 to a high of 3.4 mg/L at station 3, and concentrations were found to be higher in those water samples taken during the fall survey. The MOE guideline for total aluminum in clay-free samples is 0.075 mg/L. All stations exceeded this guideline. Elevated aluminum concentrations may be due to the high suspended clay content in the water column rather than the influence of any specific contaminant sources.

Magnesium concentrations at the "extensive" stations were between 8.4 mg/L and 14.1 mg/L (Appendix I). There is currently no PWQO for this parameter in water.

16

Zinc levels were below detection limits in all water samples except those from stations 1 and 24 (Appendix I). Concentrations noted at stations 1 and 24 were below the PWQO. Zinc concentrations reported by Hart (1986) ranged between 0.005 mg/L and 0.01 mg/L, and were all below the PWQO.

Long Term Monitoring

Water quality has also been monitored on an ongoing basis by MOE at a number of sites on the Welland River, including the Montrose Bridge (station 21). Temporal trends of zinc, copper, chromium, mercury, and lead concentrations at the Montrose Bridge between 1979 and 1987 are illustrated in Figure 3. There is generally a reduction over time in levels of these metals in the Welland River water at this site.

The Ministry has also monitored aluminum levels at the Montrose Bridge and at a site near Port Robinson (Figure 4). There appears to be a slight increase in mean aluminum concentrations between 1981 and 1987, with the highest levels noted during 1985 at both stations. As discussed on the previous page, the high aluminum concentrations may be due to high levels of suspended clay in the water, rather than a specific contaminant source.

Phosphorus

Total Phosphorus (TP) at the 25 stations ranged from 0.013 mg/L to 0.25 mg/L (Appendix I). The PWQO for TP was exceeded at all stations except for stations 9, 10, 22, 23, and I9a. Low levels of TP were found at stations 22 and 23, which receive water from the Niagara River that is diverted to the Queenston-Chippewa Power Canal. Water samples from stations 1 through 6, had high levels of TP, probably due to the influence of agricultural activities in and above section A.

Total phosphorus data during the period 1979 to 1987 at the MOE water quality stations are illustrated in Figure 5. The concentration of total phosphorus in the water varied among years; however, the Welland Airport station had consistently higher levels of total phosphorus than those found-at the downstream stations. This pattern was most likely due to dilution of water in the lower reaches of the river from the Welland Ship Canal, and to assimilation of phosphorus by biota.

17

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Total Kieldahl Nitrogen

Total Kjeldahl Nitrogen (TKN) levels during the August 1990 survey ranged from 0.28 mg/L to 2.6 mg/L (Appendix I). As with TP, higher levels of TKN were found at sampling stations located in section A, most probably due to the influence of agricultural activities. The highest level of TKN was noted at station 21 located below the Montrose Bridge.

Mean yearly TKN levels for the period 1979 to 1987 at MOE water quality stations are presented in Figure 6. TKN levels at MOE stations located at the Welland River Airport and at Port Robinson have remained fairly constant over the years, whereas TKN levels at the Montrose Bridge station have decreased dramatically. The decrease in TKN at the Montrose Bridge is most likely due to improvements in effluent quality from Cyanamid. The main nitrogen treatment system became operational in 1985.

Ammonia concentrations ranged from 0.008 to 0.333 mg/L, and levels of nitrite and nitrate ranged from 0.003 to 0.04 mg/L and 0.16 to 0.56 mg/L, respectively. Station 21, at the Montrose bridge, had the highest levels of these parameters due to the discharge of nitrogen species from Cyanamid to Thompson's Creek.

PAHs. PCBs. and PC Pesticides

All PAHs, OC pesticides and PCBs were below detection limits (Tables 7 and 8 respectively). The Ministry of the Environment has also monitored OC pesticide levels from 1981 to 1989 (MOE-unpublished data (1981-1989)). Most pesticides were below detection limits; however alpha-BHC and gamma-BHC were detected in trace quantities for all years. Endosulfan sulfate, beta-BHC, 4,4'-DDE, and 4,4'-DDT were also detected in trace amounts for some years.

Organic compounds ifrom sites 6 and 21, which were analyzed at the MOE laboratory, were also below detection limits (Table 8b).

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Table 7: Polycyclic aromatic hydrocarbons and associated detection limits

PAH Detection Limit (/xg/L)

Naphthalene	0.1
Acenaphthylene	0.1
Acenaphthene	0.1
Fluorene	0.1
Phenanthrene	0.2
Anthracene	0.2
Fluoranthene	0.2
Pyrene	0.2
Benzo(a)anthracene	0.2
Chrysene	0.2
Benzo(b)fluoranthene	0.5
Benzo(k)fluoranthene	0.5
Benzo(a)pyrene	0.5
Perylene	0.5
Indeno(l,2,3-c,d)pyrene	2
Dibenzo(a,h)anthracene	5
Benzo(g,h,i)peryIene	1

23

Table 8: Organochlorine pesticides and associated detection limits

OC Pesticide Detection Limit (/xg/L)

Hexachlorobenzene	0.003
alpha-BHC	0.003
gamma-BHC	0.003
Heptachlor	0.003
Aldnn	0.003
beta-BHC	0.003
Oxychlordane	0.003
Heptachlor epoxide	0.003
Endosulfan I	0.003
gamma-Chlordane	0.003
alpha-Chlordane	0.003
4,4'- DDE	0.003
Dieldrin	0.003
Endrin	0.003
2,4'- DDT	0.003
4,4'- DDD	0.003
Endosulfan II	0.003
4,4'-DDT	0.003
Mirex	0.003
Endosulfan Sulfate	0.005
Methoxychlor	0.005
PCB's (Total)	0.050

24

Parameter	D. L. (ng/L)	6 21
Extractable Org.	N.A.	no numeric result
Volatile Org.	N.A.	no numeric result
Octachlorostyrene	N.A.	no suitable sample
PCB, Total	20	below detection limit
Hexachlorobenzene	1	below detection limit
Heptachlor	1	below detection limit
Aldrin	1	below detection limit
PP-DDE	1	below detection limit
Mirex	5	below detection limit
A-BHC Hexachlorocyclohex	1	below detection limit
B-BHC Hexachlorocyclohex	1	below detection limit
G-BHC Hexachlorocyclohex	1	below detection limit
A-Chlordane	2	below detection limit
G-Chlordane	2	below detection limit
Oxychlordane	2	below detection limit
OP-DDT	5	below detection limit
PP-DDD	5	below detection limit
PP-DDT	5	below detection limit
DMDT Methoxychlor	5	below detection limit
Heptachlorepoxide	2	below detection limit ■
Endosulfan I	2	below detection limit
Dieldrin.	• 4	below detection limit
Endrin	4	below detection limit
Endosulfan II	4	below detection limit
Endosulfan Sulphate	4	below detection limit

D.L. is detection limit. N.A. means no numeric value was reported.

25

Water temperature, conductivity, and dissolved oxygen as determined in the field are presented in Appendix III. All values are within ranges considered normal.

A comparison of the water quality in the study area of the Welland River with several of its tributaries and the Niagara River is presented in Table 9. Water quality of the Welland River is generally similar to that of Thompson's Creek, Lyons Creek, and the Niagara River, with the exceptions of TKN and total phosphorus. Concentrations of these parameters are higher in Thompson's Creek than in the lower Welland River, probably because of the influence of Cyanamid. Levels of iron and aluminum are also slightly elevated in the lower Welland River compared with concentrations in the other river systems. This phenomenon is probably due to the influence of metal industries located on the Welland River, and the high suspended cay load in the water column.

26

Table 9: Comparison of water quality of the Welland River with selected river systems in the area. All parameters are in mg/L unless otherwise specified.

Parameter	Welland River	Thompson's Creek'	Lyon's Creek'	Niagara River ^
Fe	0.06-2.1	0.510-0.720	0.120-1.20	ND-0.3.2
Al	0.09-3.4	0.370-0.440	0.110-0.950	ND-2.6
Ni	ND	0.007-0.016	0.002-0.004	ND-0.04
Zn	ND-0.02	0.020-0.030	0.004-0.036	ND-0.03
Cu	ND-0.04	0.020-0.032	0.003-0.019	ND-0.029
Cr	ND	0.005-0.054	ND-0.002	ND-0.260
Pb	ND	ND-0.006	ND-0.011	ND-0.005
Cn	ND	NA	NA	ND
Cd	ND	0.0002-0.0003	ND-0.0005	ND-0.0004
Hg	ND-0.0003	0.040-0.050	ND-0.010	ND-0.0006
As	ND	0.001	ND	ND-0.003
TP	0.013-0.149	0.60-1.26	0.015-0.039	NA
TKN	0.28-2.6	97.5-485	0.020-0.310	NA

ND - not detected NA - not analyzed

1 - Hart (1986)

2 - Kauss (1983); from stations in the Lower River, the Tonawanda Channel, and the Chippawa Channel.

Sediment Quality

Sediment quality was extremely variable throughout the study area (Appendices II and XII). When compared with the Draft Provincial Sediment Quality Guidelines (PSQG) and in some cases the existing Open Water Disposal Guidelines (OWDG), concentrations of a number of metals, nutrients, and oil and grease exceeded the criteria at several stations.

The OWDG's (Persaud and Wilkins, 1976) were originally intended for use in assessing the suitability of soils and dredged material proposed for open-water disposal. Until recently, these guidelines have also been used to evaluate contaminant levels in existing aquatic sediments. The Draft PSQGs (Persaud ei ai, 1990) are recently developed guidelines which are specifically

27

intended to protect aquatic biological resources. These guidelines are based on three levels of ecotoxic effects: a no-effect level (NOEL), a lowest effect level (LEL), and a severe effect level (SEL) (Table 10).

Table 10: Provincial Sediment Quality Guideline levels and their significance (Persaud et al, 1990 - Draft)

Guideline Level

Sediment Quality

Potential Impact

> SEL

Grossly Polluted

Will significantly impair use of sediment by benthic organisms

< SEL > LEL

Significantly Polluted

Will impair sediment use by some benthic organisms

< LEL > NOEL

Clean - Marginally Polluted Potential to impair some sensitive water uses

< NOEL

Clean

No Impact on water quality, water uses, or benthic organisms anticipated

Lead

Lead levels in sediments exceeded the PSQG-LEL of 3 1 ^g/g at all stations during the summer survey, except for stations 2, 4, 11, 13, 14, 15, 16, 19a, 21, 22, and 23 (Appendix II). Stations 13 and 14 were the only stations having sediment lead levels below the LEL during the fall survey. The highest lead concentrations were found at stations 9 and 12 (138 /ig/g and 91 ^g/g, respectively) during the fall survey, whereas stations 22 and 23 had the lowest levels during the summer survey.

All sediment samples had lead levels less than the SEL of 250 /xg/g.

28

Chromium

Chromium concentrations exceeded the PSQG-LEL of 26 ^g/g at most stations (95%) with the exception of stations 22 and 23 located in Chippawa Creek (Appendix II). Extremely high chromium levels were noted in sediments collected from stations 10, 12, and 17 during both the summer and fall surveys. Chromium concentrations in sediments at stations 10 and 12 were approximately 26 and 18 times the LEL, respectively.

The SEL of 1 10 /^g/g was only exceeded at stations located in sections B and C of the study area. Sediments from stations 12, 13, 15, 17, and 18 during the summer survey, and stations 10, 10a, 11, 12, 13, 14, 15, 16, 17, 18, and 19 during the fall survey were characterized by chromium concentrations in excess of the SEL.

Sediment mercury levels exceeded PSQG-LEL of 0.2 yug/g at stations 8, 9, 10a, 12, 16, 18, and 19 during the summer survey, and at stations 7, 8, 9, 10, 11, and 12 during the fall survey (Appendix II). Sediments collected from station 9 had the highest mercury concentrations during both surveys (approximately 16 and 21 times the LEL).

The SEL of 2 ;ag/g was only exceeded at station 9 during both the summer and fall surveys.

Cadmium

Cadmium levels were extremely variable throughout the study area, and exceeded the PSQG- LEL of 0.6 /ig/g at stations 9, 10, 12, 19, and 22 during the summer survey, and at stations 7, 9, 10, 10a, 11, 12, 17, and 19 during the fall survey (Appendix 11).- Station 12 was characterized by the highest cadmium levels during both the summer and fall surveys (1.4 /xg/g and 1.5 /xg/g, respectively).

All sediment samples had cadmium levels well below the SEL of 10 pLg/g.

Arsenic

Arsenic levels exceeded the PSQG-LEL of 6 fxg/g at stations 3, 9, 10, 10a, 12, 18, 19, and 20 during the summer survey and at stations 10, 12, 14, 15, 17, 19, 19a, and 20 during the fall survey (Appendix II). The highest concentrations were found in sediments at stations 10 and 12, and the lowest levels were found at stations 22 and 23.

All sediment samples had arsenic levels below the SEL of 33 /xg/g.

29

Zinc

Zinc concentrations exceeded the PSQG-LEL of 120 ^J.glg at stations 7, 9, 10, 10a, 12, 17, 18, 19, and 19a during the summer survey, and at stations 5, 7, 8, 9, 10, 10a, 11, 12, 14, 15, 16, 17, 18, 19, 19a, and 20 during the fall survey (Appendix II). Sediments collected from stations 10 and 12 had the highest zinc levels; 555 /^g/g and 620 /xg/g respectively.

The SEL of 820 /^g/g was not exceeded at any of the stations.

Iron

All sediment samples collected in the study area exceeded the PSQG-LEL of 20 mg/g (2%) for Iron, with the exception of station 23 during the summer survey (Appendix II). Of the five "extensive" stations evaluated during the summer survey, only station 15 had iron levels exceeding the SEL of 40 mg/g (4%).

Iron levels in excess of the SEL were found at stations 10, 10a, II, 12, 13, 14, 15, 16, 17, 18, 19, and 20 during the fall survey, with the highest concentration from station 10 (118 mg/g).

Nickel

The PSQG-LEL of 16 /xg/g for nickel was exceeded at the five "extensive" stations sampled in the summer, and at all the stations evaluated m the fall. Nickel concentrations ranged from highs of 390 ixgig and 270 p.glg at stations 10 and 12 respectively to a low of 19.5 /xg/g at station 23 (Appendix II).

The SEL of 75 ^g/g was exceeded at station 15 during the summer survey, and at all stations in sections B and C (with the exception of station 9) during the fall survey.

Copper

Most sediment samples had copper levels in excess of the PSQG-LEL of 16 /xg/g, with the exception of stations 22 and 23 during the summer survey (Appendix II).

The SEL of 1 10 /xg/g was exceeded at station 19 during the summer survey, and at stations 10, 19, 19a, and 20 during the fall survey. The highest copper concentrations were noted at station 10 and station 20.

30

Other Metals

Concentrations of several other metals were also evaluated during the summer survey, including aluminum and magnesium (Appendix II). Aluminum concentrations varied a great deal throughout the study area with the highest levels occurring stations 3, 12, and 19. Stations 22 and 23 had the lowest aluminum concentrations.

Magnesium levels were evaluated at the five "extensive" stations, and ranged from alow of 9.9 mg/g at station 1 to a high of 17.2 mg/g at station 23.

Nutrients

Loss on ignition (LOI) was measured at all the stations in the study area, whereas total kjeldahl nitrogen (TKN), total phosphorus (TP), and total organic carbon (TOC) were evaluated at all the "extensive" stations during the summer survey.

LOI is a measure of the particulate organic matter (leaves, bark, sewage, fibres) in the sediment. LOI for sediments ranged from a low of 2 percent at stations 11, 13, 14, and 15, to a high of 14 percent at station 1 (Appendix II). Sediment samples collected from section A of the river were also characterized by higher LOI levels.

Total kjeldahl nitrogen levels exceeded the PSQG-LEL of 550 /xg/g at stations 1, 9, 21, and 23 (Appendix II). Concentrations ranged from a low of 290 /xg/g at station 15 to a high of 2800 /Lig/g at station 1. All sediment samples had TKN levels below the SEL of 4,800 jxglg. Similarly, TOC values exceeded the PSQG-LEL of 1 percent at stations 1, 9, 21, and 23 (Appendix II). TOC levels ranged from a low of 0.92 percent at station 15 to a high of 7.4 at station 1. The SEL of 10 percent was not exceeded at any station.

Total phosphorus concentrations exceeded the PSQG of 600 /xg/g at all stations, and ranged from 620 ixgig at station 23 to 1300 /xg/g at station 21 (Appendix II). All sediment samples had TP levels below the SEL of 2000 /xg/g.

Total Cyanide

Total cyanide was determined at all stations during the summer stirvey and at a subset in the fall. Concentrations were below detection limits in most instances (Appendix II). The OWDG of O.I /xg/g (no existing PSQG) was exceeded at station 1 and station 20 during the summer survey, and at stations 2, 17, 18, 19a, 20, and 21 during the fall survey. Sediments collected from station 20 had the highest cyanide level of 1.67 /xg/g,

Oil and Grease

Concentrations of oil and grease ranged from a low of 195 /xg/g at station 13 to a high of 1 1 ,800 /xg/g at station 12 (Appendix II). Oil and grease levels exceeded the OWDG of 1,500 jxg/g (no existing PSQG) at a number of stations during both the summer and fall surveys, predominantly in the urban area of the City of Welland and the industrial section east of Port Robinson.

Polycyclic Aromatic Hydrocarbons

The polycyclic aromatic hydrocarbon (PAH) analytical results for all sediment samples collected in the summer and fail are presented in Table 1 1 and 12 respectively. Station 9, in downtown Welland, had extremely high levels of all the PAHs relative to those found at other stations during the summer and fall surveys. Station 10, located near the McMaster Avenue outfall, also had high levels of some PAHs during the fall survey.

Total PAH levels at stations 1 and 9 exceeded the PSQG-LEL of 2,000 ng/g during the summer survey. SEL levels were not exceeded at any of the stations tested during the summer survey. Total PAHs exceeded the PSQG-LEL at stations 7, 8, 9, 10, and 15 during the fall survey. SELs for organic compounds are dependent on the amount of organic carbon in the sediment (MOE 1991). SELs could not be calculated for the fall survey because TOC concentrations were not measured.

PAH concentrations were extremely variable, both between surveys, and between duplicate samples collected from the same station. This phenomenon probably reflects the uneven distribution of the contaminants within the sediments.

Polychlorinated Biphenyls

Polychlorinated biphenyls (PCBs) were not detected in any sediment samples collected during the summer survey; however they were detected in several fall samples. Total PCB levels ranged from <0.05 ^g/g to 0.13 /xg/g, and exceeded the PSQG-LEL of 0.07 /xg/g at stations 7, 8, 9, and 15 (Appendix IÏ). The SEL could not be calculated as TOC levels were unavailable for the fall survey.

Results from detailed chemical analyses conducted by MOE on sediments from stations 6, 9, 15 and 21 indicated total PCB concentrations at station 21 also exceeded the LEL (Table 12b). The laboratory report noted that PCB congeners detected at site 21 resembled a mixture of Aroclor 1254 and 1260. PCBs were not detected at the other stations 6, 9 or 15.

32

Table 1 1 : Concentrations of PAHs in Welland River sediments collected during the summer survey. All concentrations are in ng/g.

1 PAH	Stn 1	Stn 9 *	Stn 15	Stn 21	Stn 23
Naphthalene	22	129 (290)	19	<10	16
Acenaphthylene	<10	<10(15)	<10	<10	<10
Acenaphthene	13	200 (880)	<10	<10	<10
Fluorene	33	270 (710)	<10	<10	12
Phenanthrene	200	1630 (4100)	24	52	63
Anthracene	95	490 (1590)	14	25	55
Fluoranthene	400	2100(7200)	82	210	210
Pyrene	370	2200 (7200)	104	240	210
Benzo(a)anthracene	125	1050 (4000)	30	79	126
Chrysene	148	1020 (3700)	35	101	175
Benzo(b)flouranthene	260	1600 (5700)	90	220	300
Benzo(k)flouranthene	260	1600(1900)	90	220	116
Benzo(a)pyrene	69	1470 (5400)	61	140	170
Perylene	680	570 (1490)	31	97	101
Indeno(123,cd)pyrene	<100	1150(5200)	<100	83	<100
Dibenzo(ah)anthracene	<100	1390 (4800)	<100	<100	<100
Benzo(ghi)perylene	<50	470(1500)	<50	35	<50
Total PAH's'	2 '125	16774 (54185)	689	1475	1487

1 - Total PAHs is the sum of all the PAHs listed except for perylene. Concentrations of PAHs below detection limits were taken as equal to half the detection limit.

* - Value in brackets is the PAH concentration in a duplicate sample taken from the three ponar samples taken at each station

33

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Table 12 b: MOE results for concentrations of chlorinated organics at sites 6, 9, 15 and 21.

Parameter

Units

D.L.

Station

21

T4CDD

P5CDD

H6CDD

H7CDD

08CDD

T4CDF

P5CDF

H6CDF

H7CDF

08CDF

Ex tractable Org.

Volatile Org.

PCB, Total

Hexachlorobenzene

Heptachlor

Aldrin

Mirex

a-BHC

/3-BHC

7-BHC

A-Chlordane

G-Chlordane

Oxychlordane

PP-DDE

OP-DDT

ppt	*
ppt	*
ppt	N.A
ppt	N.A,
ppt	N.A,
ppt	*
ppt	*
ppt	N.A,
ppt	N.A.
ppt	N.A,
N.A.	N.A.
N.A.	N.A.
ng/g	20
ng/g	1
ng/g	1
ng/g	1
ng/g	5
ng/g	1
ng/g	• 1
ng/g	1
ng/g	2
ng/g	2
ng/g	2
ng/g	1
ng/g	5

ND

ND(4)	ND(7)	ND(6)
ND(7)	ND(12)	ND(9)
793	31^	60^
230^	,230^	420^
1900'	2300'	3100'
ND(5)	ND(8)	ND(7)
14>	ND(12)	ND(7)
30^	12'	28^
160-	922	140'
63'	36'	81'

2(T)

no numeric result no numeric result ND ND

below detection limit below detection limit below detection limit below detection limit below detection limit below detection limit below detection limit below detection limit below detection limit below detection limit

2(T) ND

below detection limit

85 (T)

4(T)

35

Table 12 b: Continued

Parameter	Units	D.L.	Station
		6 9 15 21
PP-DDD	ng/g	5	below detection limit
PP-DDT	ng/g	5	below detection limit
DMDT Methoxychlor	ng/g	5	below detection limit
Heptachlorepoxide	ng/g	1	below detection limit
Dieldrin	ng/g	2	below detection limit
Endrin	ng/g	4	below detection limit
Endosulfan I	ng/g	2	below detection limit
Endosulfan II	ng/g	4	below detection limit
Endosulfan Sulphate	ng/g	4	below detection limit
Octachlorostyrene	ng/g	1	below detection limit

D.L. is the parameter detection limit.

Asterisks (*) indicate parameter detection limits may be found in brackets ( ) for each station.

N.A. indicates a numeric value or result was not reported.

A superscript denotes the number of isomers of that parameter detected at that station.

ND indicates that parameter exists at a concentration below D.L. at that station.

(T) means the parameter was measured in trace amounts at that station. Interpret with caution.

36

Pesticides

Organochlorine (OC) pesticides were not detected at any of the sampling stations. A list of all OC pesticides and their detection limits is presented in Table 13. The Ministry of the Environment has also routinely determined OC pesticides in Welland River sediments from 1981 to 1988 (MOE-unpublished' data (1981-1988)). Alpha-BHC, alpha-chlordane, dieldrin, hexachlorobenzene, 4,4'DDE and gamma-chlordane were detected in some years. Concentrations were consistently low. With the exception of PP-DDE, which was detected in trace amounts at stations 6, 9 and 21, pesticides analyzed by MOE for the preSent study were below detection limits (Table 12b).

Dioxins and Furans

Polychlorinated dibenzo-p-dioxins were found at stations 9, 15, and 21 (Table 12b). Concentrations ranged between 31 and 79 ppt for hexachlorinated forms, 230 to 420 for the heptachlorinated forms, and 1,900 and 3, 100 for the octachlorinated congener. Polychlorinated dibenzofurans were also detected at the same stations. A pentachlorinated congener was found only at station 9 and at a concentration of 14 ppt. The hexa, hepta, and octachlorinated forms were found at stations 9, 15, and 21 at levels ranging from 12 to 30, 92 to 160, and 36 to 81 ppt respectively.

The more highly chlorinated dioxin and furan congeners such as the octachlorinated forms are generally believed to be less of an environmental concern than are the tetrachlorinated isomers because of the relatively large size of the molecules. The larger molecules tend to bind tightly to sediment particles and have a high octanol-water partition coefficient; and because of the large size, they cannot cross cell membranes easily. The toxicity of these contaminants to aquatic biota is poorly understood at present; however, it is acknowledged that they can affect growth, reproduction, and hormonal processes in some organisms.

37

Table 13 : Organochlorine pesticides, PCBs and associated detection limits in

sediments.

OC Pesticide Detection Limit (/xg/g)

Hexachlorobenzene	0.003
alpha-BHC	0.003
gamma-BHC	0.003
Heptachlor	0.003
Aldrin	0.003
beta-BHC	0.003
Oxychlordane	0.003
Heptachlor epoxide	0.003
Endosulfan I	0.003 .
gamma-Chlordane	0.003
alpha-Chlordane	0.003
4,4'- DDE	0.003
Dieldrin	0.003
Endrin	0.003
2,4'- DDT	0.003
4,4'- DDD	0.003
Endosulfan II	0.003
4,4'-DT	0.003
Mi rex	0.003
Endosulfan Sulfate	0.003
Methoxychlor	0.003 - 0.005
PCBs	0.050-0.100

38

Sediment Contamination by Station

Sediment quality in the study area with respect to the PSQGs for metals, and OWDGs for oil and grease and total cyanide, is summarized in Table 14.

Sediments at stations 9, 10, 10a, 11, and 12, located in the upstream portion of section B, along with those at stations 15, 16, 17, 18, 19 and 20 in section C are the most contaminated, as indicated by the levels of several metals and oil and grease. Concentrations of chromium, mercury, iron, nickel, and copper also exceed the SEL's at several stations in sections B and C.

Station 7, which also has relatively contaminated sediments, is located in the eastern downstream portion of section A below a large storm sewer. Storm water is a known source of heavy metals and oil- and grease. Inputs to this storm drain may be the cause of contaminants accumulating in sediments at this site.

Sediments at station 9 are characterized by high concentrations of metals, oil and grease and a number of PAHs. A large storm drain located upstream of this station is the suspected source of contaminants. Elevated levels of several metals have also been found in sediments at this location during previous studies (Acres 1990). A comparison of results from the Tarandus and Acres studies is presented in Table 15. Concentrations are also compared with PSQG lowest effect and severe effect levels.

Sediments at stations 10 and 10a, situated a short distance downstream from the Atlas Steel outfall and downstream from the old McMaster Avenue combined sewer outfall also have elevated levels of several metals, and oil and grease. A reef-type deposit of industrial waste was first noted off the Atlas outfall by Brindle and Dickman in 1980 (Acres, 1990). Acres (1990) examined this deposit in detail and also discovered two areas of further contamination, one at the outfall from the McMaster Avenue combined sewer, and one approximately 400 meters downstream from the Atlas outfall. The reef sediments contained elevated levels of copper, chromium, iron, lead, manganese, nickel, zinc, and oil and grease. A comparison of sediment quality results from the 1990 Tarandus survey and the Acres study is presented in Table 16.

The discharge outfall from Atlas Steel has been well documented as a source of contaminants to the Welland River (COA, 1981; NRTC, 1984). The industrial effluent was also documented as exceeding effluent guidelines for several parameters including chromium, copper, lead, nickel, zinc, iron, phosphorus, nitrogen, and sulphate (NRTC, 1984; Dalrymple in Dickman and Hayes, 1985).

39

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Parameter	Tarandus (1990)	Acres (1990)	PSQG LEL	PSQG SEL
Chromium	50.0-320.0	14.0-79.0	26	110
Copper	79.0-126.0	33.0-146.0	16	110
Lead	49.0-138.0	24.0-339.0	31	250
Manganese	400.0-750.0	269.0-794.0	460	1100
Nickel	37.0-195.0	25.0-140.0	16	75
1 Zinc	158.0-460.0	242.0-2236.0	120	820

Table 16: Comparison of selected parameters in sediments collected offshore of the Atlas outfall. All results are in>g/g.

Parameter	Tarandus (1990)'	Acres (1990)'
Chromium	91.0-670.0	21.0-5,000
Copper	50.0-168.0	17.0-860.0
Iron	11,800	20,000-420,000 1
Lead	38.0-87.0	15.0-870.0
Manganese	1,210	470.0-6,600
Nickel	390	37.0-11,000
Zinc	270.0-550.0	36.0-690.0
PCBs	< 0.05-0.045	< 0.2-0.3^

1 - sediment quality results for stations 10 and 10a

2 - sediment quality results for 18 samples taken from an area 20 meters upstream and 20

meters downstream of the Atlas outfall

3 - PCBs analyzed at 3 stations directly off the outfall

Sediments at station 11, located downstream from the Welland Water Pollution Control Plant (WPCP) also exceed PSQG-LELs for several metals, and oil and grease. These sediments also exceeded SEL's for chromium, iron, and nickel. The WPCP effluent has also been documented as exceeding effluent guidelines for copper, lead and zinc (NRTC, 1984).

Solid waste (primarily slag) and liquid waste from Atlas Steel (primarily slag) has been deposited since 1930 at the company's landfill located on the east bank of the river and has in the past been documented as a source of contaminants to the Welland River through surface runoff (NRTC, 1984). Contaminants include aluminum, arsenic, cadmium, chromium, copper, mercury, nickel, lead, selenium, zinc, and cyanide.

All stations located in section C were also characterized by elevated levels of several metals, total cyanide, and oil and grease. The Cyanamid Canada plant located along this section of the Lower Welland River is considered a source of several contaminants found in the river sediments. Cyanamid formerly discharged at a point just upstream of station 18, but now discharges to Thompson's Creek. Thompson's Creek enters the Welland River slightly upstream of station 20. Cyanamid' s discharge has been reported as a source of several contaminants including chromium, nickel, zinc, copper, and cyanide (NRTC, 1984). Hart (1986) also reported elevated sediment concentrations of silver, chromium, mercury, nickel, lead, zinc, and iron at the mouth of Thompson's creek.

A comparison of selected sediment contaminant concentrations found in several nearby river systems in the area is presented in Table 17. Means and ranges for the Welland River were calculated using data for all sites except sites 22 and 23, which are in Chippawa Creek. Mean sediment concentrations of lead, chromium, mercury, cadmium, arsenic, zinc, nickel and copper in the Welland River were higher than levels in sediments collected from the Upper Niagara River or, with the exception of cadmium, from Lyon's Creek. Niagara River sediments had higher PCB concentrations than Welland River sediments. Elevated levels of several contaminants in the sediments from Thompson's Creek may be the result of discharges from industrial processes. The Cyanamid effluent has been reported to be approximately 90 percent of the average annual flow in Thompson's Creek.

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Benthic Invertebrates

i) Species Composition. Abundance, and Diversity

In total, 90 benthic invertebrate taxa were identified at the 25 sampling stations in the study area (Appendix IV). The total number of taxa was higher than the number of genera (28) Johnson in 1964. As might be expected because of the range of habitat types and environmental quality, the number of taxa at each station varied. It ranged from a low of 12 taxa at stations 6 and 25 to a high of 29 taxa at station 10 (Table 18). The abundance of taxa at stations 9 and 10 may reflect the diversion of relatively cleaner water from the Welland Canal at the inverted syphon. The distribution of the various invertebrate species, by number/sample and number/m^ for each station are presented in Appendix V and VI respectively.

Only two invertebrate species were common to all the sampling stations; Procladius sp. and immature tubificids, although Chrypiochironomus sp., Limnodrilus hoffineisreri, and Sphaerium sp. were found at 24 of the 25 sites. Similarly, Johnson (1964) found that Procladius and Limnodrilus were common throughout the Welland River system.

Tubificids have been used extensively as indicator organisms (Lauritsen ei ai, 1985; Cook and Johnson, 1974). Limnodrilus hoffineisreri, for example, is a species known to be characteristic of organically enriched sediments and is generally tolerant of high concentrations of some heavy metals (Winner et al. 1980). It should be noted, however, that Limnodrilus spp. are not necessarily confined to polluted waters (Hynes, 1971; Brinkhurst and Cook, 1974). The abundance of several tubificids, including L. hoffineisreri at all the sampling sites is illustrated in Figure 7. Relatively high numbers of this species were found at station 9 and station 16.

The chironomids, Procladius sp. and Chironomus sp. are usually common in polluted conditions (Cook and Johnson, 1974). The relative abundances of Chironomus chironomus and Procladius sp, at all sampling sites in the study area are illustrated in Figure 8. High numbers of Chironomus sp. were found at station 9. High abundances of Procladius sp. were found at stations 10, 11, 15, and 22.

Mayflies, such as Hexagenia sp. are considered intolerant of polluted conditions (Schloesser, 1988; Fremling, 1964; Winner er al., 1980), and as a result, their presence is usually indicative of uncontaminated conditions. Mayflies were relatively abundant in Section A (stations 1-8), but were generally absent from the rest of the study area (Figure 9). Johnson (1964) also noted an absence of mayflies from the same sections of the Welland River.

44

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Zebra mussels {Dreissena polymorpha) are a recent addition to the benthic community in the study area. Adult Zebra mussels were noted at several stations in sections B, C, and D, most likely the result of veligers introduced to the Welland River from the Welland Canal at the upper syphon by the diversion structures. The mussel was not found in section A, probably because of its inability to move upstream into this section of the river. Zebra mussels found in sections B, C, and D were attached to rocks and other solid debris as well as to aquatic macrophytes. Station 9 had the highest density of zebra mussels (1013/m^).

The total abundance of benthic invertebrates ranged from a low of 634 individuals per square meter at station 12 to a high of 5900 individuals per square meter at station 22 (Table 18). Station 9 also had a relatively high mean total abundance of 4013 invertebrates per square metre. Generally, stations located in sections B, C, and D had higher total abundances than those found in section A, primarily due to higher densities of oligochaetes. Johnson (1964) observed total invertebrate densities between 97/m^ and 3,757/m^ and also noted higher densities in the eastern sections of the Welland River.

Figure 10 illustrates the total Oligochaete abundances throughout the study area. The reduction in the density of oligochaetes at stations below the Atlas Steel discharge and Cyanamid Canada may be due to the toxicity of the high metal concentrations in these sediments.

The Shannon-Weaver and Brillouin diversity indices for all stations are presented in Table 18. Benthic-invertebrate diversity fluctuated a great deal, especially in sections B, C, and D. Diversities at all the stations in section A, were relatively constant. Shannon-Weaver diversities ranged from a high of 3.96 at station 1 1 to a low of 2.52 at station 19a. Similar trends were noted with the Brillouin diversity index. Benthic invertebrate diversities (Shannon-Weaver index) calculated from Johnson's (1964) data ranged from 0.34 to 3.48. Weed and Rutschky (1972) considered Shannon-Weaver diversities greater than 3.0 to represent unpolluted conditions, a diversity of 1.0-2.0 moderately polluted, and a diversity of less than 1.0 severely polluted.

48

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Number of taxa, total abundance (#/m^), and diversity indices (Shannon and Brillouin) for all stations.

	# of Taxa	Total Abundance	Diversity
Station	Shannon	Brillouin
1	18	1,387	3.45	2.36
2	20	1,447	3.50	2.39
3	18	1,387	3.53	2.42
4	19	1,140	3.49	2.38
5	21	1,473	3.30	2.25
6	12	666	3.02	2.05
7	21	1,240	3.20	2.18
8	18	1,113	3.30	2.25
9	26	4,013	3.34	2.30
10	29	2,407	3.84	2.64
10a	28	2,093	3.91	2.68
11	27	1,394	3.96	2.70
12	16	634	3.08	2.10
13	22	1,300	3.49	2.38
14	23	1,447	3.07	2.09
15	24	2,360	3.29	2.26
16	19	2,380	3.10	2.13
17	22	1,793	3.17	2.17
18	24	2,793	2.57	1.76
19	22	2,700	3.16	2.17
19a	12	1,367	2.52	1.73
20	14	1,147	3.18	2.17
21	20	1,607	3.03	2.07
22	,27	5,900	2.83	1.95
23.	26	2,407	3.14	2.16

50

ii) Benthic-Commiinity ClassiFication

The benthic invertebrate communities were defined by means of cluster analysis. Based on the total species composition at each station, the cluster analysis split the twenty-five sampling locations into four groups or communities (1, 2, 3, and 4). The taxonomic composition of the four communities is presented in Appendix VII. The cluster analysis using euclidean distance and Ward's Method produced the best defined clusters (Figure 11).

Principal components analysis (PC A) was used to verify station groupings revealed by cluster analysis (Figure 12). The PC A was completed on all the benthic invertebrate genera. The component loadings and percent total variance for the principal components are presented in Appendix VIII. Approximately 24 percent of the variation is explained by the first two factors. Although the percent variation explained is relatively low, the PCA results generally confirm those of the cluster analysis. All the stations from section A of the study area form a fairly distinct group (community 1) in the PCA diagram. This group is characterized by relatively high numbers of the Hexagenia, and the Coeloranypus sp. Communities 2, 3, and 4 revealed by the cluster analysis is also fairly distinct in the PCA diagram. The stations found these communities are influenced by the relative abundances of Hirudinea, Spirosperma ferox, and immature tubificids, as indicated by their positive correlation with the first axis of the PCA axis. Community 4 is separated from the other communities along the second PCA axis and is influenced by the relative abundances of Polypedelium (Polypedelium) sp. and planaria.

51

Figure 11: Cluster analysis results using Euclidean distance and Ward's method. Large numbers indicate groups of sites (small numbers) with similar benthic invertebrate

communities.

20- 19a- 12- 13- ,14- 16- 19- 18- 21- 17- 15- 11- 10a- 10- 9- 23- 22-

DIS.TANCES

5.00C

52

Figure 12; Scatterplot of sample locations on tiie first two principal components. Sites grouped together have similar benthic invertebrate communities

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53

iii) Environmental Quality Evaluation

Figure 13 illustrates the separation in discriminant space of the four groups of stations defined by cluster analysis and PC A. Correlations between sediment parameters and the first two discriminant functions are given in Table 19.

The first discriminant axis (DA I) separates the communities characterizing the Welland River sites (communities I, 2, and 3) from community 4, located in Chippawa Creek (Figure 13). The axis indicates that communities 1, 2, and 3 are found in sediments with high concentrations of metals such as chromium, copper, aluminum, lead, mercury, and arsenic relative to those associated with community 4. The sediments of community 1, however are characterized by lower levels of these metals relative to communities 2 and 3.

The second discriminant axis (DA II) separates community 1 from the remaining communities in discriminant space (Figure 13). This axis indicates that community 1 is found in sediments with slightly higher levels of aluminum and LOI relative to the sediments in communities 2, 3, and 4.

This analysis suggests that the separation of communities is due to differences in concentrations of sediment parameters. It indicates that communities 1, 2, and 3, located in the Welland River, reflect degraded environmental conditions, relative to community 4 located in Chippawa Creek. Of the Welland River communities, 2 and 3 are more degraded than 1. This observation is not surprising, given the fact that communities 2 and 3 are located in urbanized sections of the river which receive inputs from various industrial and municipal sources. Community 1, which consists of all the stations in Section A of the river, may be in more organically enriched sediments, as is illustrated by the relatively high loss on ignition (LOI). The only exception to the general pattern of correspondence between contamination and community type is aluminum, which is found in higher amounts in community 1 than in communities 2 and 3. The mean concentrations of all sediment parameters associated with each community are presented in Table 20.

54

Figure 13: Plot of the benthic invertebrate communities in discriminant space as defined by the first two discriminant functions.

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55

Table 19: Correlations between sediment parameters and the first two discriminant functions for benthic invertebrate communities.

Parameter

Discriminant Function I II

Zinc

Cadmium

Copper

Lead

Chromium

Aluminum

Mercury

Arsenic

Loss on Ignition

Oil and Grease

m

0.163	-0.031
0.004	-0.064
0.218	0.121
0.142	-0.134
0.220	-0.258
0.244	-0.256
0.120	0.040
0.184	0.092
0.093	-0.453
0.014	-0.048
0.091	0.264

Table 20: Mean concentrations of sediment parameters associated with benthic invertebrate communities. All units are expressed as //g/g, dry weight unless otherwise stated.

		Benthic	Community
	1	2	3	4
Parameter
Zinc	112.5	176.9	313.3	65.3
Cadmium	0.48	0.40	0.58	0.49
Copper	33.5	58.3	62.1	17.0
Lead	42.0	34.9	55.9	18.3
Chromium	43.1	156.8	73.6	20.8
Aluminum	32375	29182	30438	14075
Mercury	0.116	0.175	0.955	0.065
Arsenic	5.38	7.36	7.50	3.50
Loss on Ign.	10.09	4.00	5.25	5.50
Oil/ Grease	1500.6	1399.6	2198	1455
pH	6.98	7.23	7.08	7.00

56

To evaluate the Welland River environment by itself, community 4 was removed from the data set and discriminant analysis was again performed. Figure 14 illustrates the separation in discriminant space of the three Welland River communities. Correlations between sediment parameters and the first two discriminant functions are given in Table 21. Results confirm patterns observed in the discriminant analysis on the whole data set. However, they reveal differences between conditions in which communities 2 and 3 are found.

The first discriminant axis (DA I) separates community 1 from communities 2 and 3 (Figure 14). The axis indicates that communities 2 and 3 are found in sediments with higher concentrations of metals such as chromium, copper, mercury, zinc, and arsenic relative to the sediments in which community 1 exists. The sediments of community 1, however, are characterized by lower levels of these metals, and higher LOI than those associated with communities 2 and 3. The absence of high numbers of pollution-sensitive species such as the mayfly, Hexagenia sp. and the presence of large numbers of Spirosperma ferox and immature tubificids in communities 2 and 3 could be due to high concentrations of various metals in the sediments.

The second discriminant axis (DA II) separates communities 2 and 3 in discriminant space (Figure 14). This axis indicates that community i is found in sediments with slightly higher levels of chromium, as well as a higher sediment pH, relative to community 3. Similarly community 3 is found in sediments with higher mercury, lead, zinc, and LOI levels relative to community 2.

The analysis suggests that communities 2 and 3 reflect degraded environmental conditions with respect to various metals, relative to community 1. Community 2 and community 3 are located in urbanized sections of the river which receive inputs from various industrial and municipal sources. Community 1 , which consists of all the stations in Section A of the river, may be more organically enriched, as illustrated by the high loss on ignition. Mean concentrations of all sediment parameters associated with each community are presented in Table 20.

57

Figure 14: Plot of the Welland River benthic-invertebrate communities in discriminant space as defined by the first two discriminant fiinctions.

2 0

4 -2 0 Cr,Cu,Hg,As,Zn,pH <

58

Table 21: Correlations between the sediment parameters and the first two discriminant functions for the three benthic invertebrate communities in the Welland River.

	Discriminant Function.
	I	II
Parameter
Zinc	-0.144	0.186
Cadmium	0.033	0.128
Copper	-0.210	-0.013
Lead	0.009	0.192
Chromium	-0.282	-0.256
Aluminum	0.099	0.041
Mercury	-0.148	0.275
Arsenic	-0.169	-0.013
Loss on Ignition	0.402	0.200
Oil and Grease	0.031	0.088
m	-0.226	-0.240

59

Fisheries

The fish community of the Welland River is characterized by warmwater fish species including catfish, carp, suckers, and freshwater drum (Appendix IX, Table 22). Salmonids are not endemic. to the Welland River but are common in the Niagara River. Appendix IX also compares the Welland River fish community with those of 12-Mile Creek and the Niagara River area. All fish species caught in the Welland River during this survey are also found in the Niagara River.

The most common fish species caught during the field surveys were channelcatfish (fall survey) and white crappie (summer survey), both warmwater species. Substantially more fish were caught in the hoop nets in section A than in Sections B and C (Table 23). A fisheries study by Johnson (1964) found that the more! common fish included brown bullhead and sunfish (including crappies). The author also noted a decrease in the number of fish in the area covered by sections B, C, and D of the river.

During a twelve month survey by Steele (1981) on the Welland River, 25 species and two- hybrids were caught (Appendix IX). Dominant fish species included white crappie, brown bullhead, and channel catfish. Most of the species observed by Steele were tolerant of low dissolved oxygen concentrations, and high turbidity.

60

Table 22: Fish species caught in the Welland River during the summer and fall surveys.

HOOP NET	Summer'	FalP
White Crappie^	25	2
White Bass	2	0
White Perch	0	10
Channel Catfish	0	59
Gizzard Shad	0	7
Freshwater Drum	0	8
White Sucker^	0	1
Yellow Bullhead	0	2
Shorthead Redhorse	0
Caip	0	1
Pumpkinseed"*	0	1
Rock Bass'	0	3
Seine net/Minnow traps	Summer	Fall'
Smallmouth Bass	-
1 Spottail Shiner	-
Emerald Shiner	*
Johnny Darter	-
Brook Silverside	-
Sculpin	¥
Banded Killifish	-	J

* - Fish species present (no numbers available)

1 - Three hoop-net sets - summer survey

2 - Two hoop-net sets - fall sur\'ey

3 - Fish species also caught in the seine net.

4 - No seining was conducted during the Fall Survey.

61

Table 23: Numbers of fish caught in hoop-net sets in sections A, B, and C.

HOOP NET	A	■ " B	C	Total
White Crappie	23	2	0	27
White Bass	7	0	0	2
White Perch	10	0	0	10
Channel Catfish	59	0	0	59
Gizzard Shad	6	0	1	7
Freshwater Drunn	8	0	0	8
White Sucker	1	0	0	1
Yellow Bullhead	2	0	0	2
Shorthead Redhorse	1	0	1	2
Carp	1	0	0	1
Pumpkinseed	1	0	0	1
Rock Bass	0	0	3	3
Total	114	2	5	121

Aquatic Macrophytes

The Welland River shoreline throughout the study area was characterized by the presence of several emergent aquatic macrophytes, particularly Typha latifolia and Sagiiiaria latifoUa (Table 24). Johnson (1964) and Dickman ei al. (1983) also noted an abundance of these species during previous surveys.

Several studies have been completed regarding effects of industrial discharges on the macrophyte community (Dickman and Haynes, date unknown; Dickman et al. , 1983). Dickman and Haynes (date unknown) noted areas devoid of higher aquatic plants downstream of the previous 36" Cyanamid outfall to the Welland River, as well as below the Thompson's Creek confluence. The summer Tarandus survey also revealed an area below the Thompson's Creek confluence that had sparse macrophyte growth; however the area below the previous outfall to the Welland River now has a relatively luxuriant growth of macrophytes; this outfall was sealed in 1985. Dickman and Haynes (Date unknown), also noted a similarly impacted zone downstream of the Atlas Steel outfall. This impacted area was not observed during the summer survey by Tarandus personnel. Several submerged aquatic macrophytes were also noted including Myriophyllum spicatum, ValUsneria ame ricana, Ceratophyllum denwrsum, and Hcreramhera dubia (Table 24).

62

Submerged macrophytes noted by Johnson (1964) included Ceratophyllum demersum and Potamogeton spp.. Dickinan et al. (1983) found that the submerged aquatic macrophytes were dominated by Elodea canadensis, MyriophylUim sp. , Potamogeton pectinatus, and Ceratophyllum sp. .

Table 24: Species of submergent and emergent aquatic macrophytes found in the study area during the summer survey.

Common Name	Scientific Name	Abundance
Water Lily	Nymaphaea vaiiegatum	Common
Cattail	Typha latifolia	Common
Eurasian Milfoil	Mynophyllum s pi cat u m	Common
Smartweed	Polygonum sp.	Occasional
Wild Celery	Vallisneria amehcana	Common
Duckweed	Lemna sp.	Occasional
Bulrush	Scirpus sp.	Occasional
Arrowhead	Sagittaria latifolia	Common
Spiked Loosestrife	Lythrum salicaria	Occasional
Mud Plantain	Heteranthera dubia	Common
Pondweed	Potamogeton crispus	Rare
Pondweed	Potamogeton ricbardsonii	Rare
Coontail	Ceratophyllum demersum	Rare
Sedge	Carex sp.	Rare
Joe-Pie Weed	Eupatorium maculatum	Rare
Wild Rice	Zizania aquatica	Rare
Bushy Pondweed	Najas fle.xiUs	Rare
Waterweed	Elodea canadensis	Rare

63

Flow Measurements

Water velocities and depth were determined at cross-sections of the river in sections A, B, and C. The flow calculations ranged from 19.24 mVs in section A to 37.12 mVs in section B, and are presented in Appendix X. The flow estimate for section C was 25.09 mVs. Welland River flow estimates cited in Acres (1990) ranged from 0 to 48 mVs.

The increased flows observed in section B are mainly the result of diversion of water from the old Welland Ship Canal to the Welland River. The amount of water diverted from the old ship canal has been estimated at 14.2 mVs (Acres 1990).

Flow in section C would normally be expected to be higher than that in section B because of added diversion of canal water at Port Robinson and inputs from natural sources. During the survey on November 9, 1990, however, the flow was found to be 25.09 mVs in this section, a significant drop from that noted the previous day in section B. This apparent reduction in flow may be the result of fluctuations of water flows in the Queenston-Chippawa Power Canal. Reductions in flow in this facility have been known to temporarily "back up" and/or reduce the flows in the lower sections of the Welland River (P. Odom, MOE, pers. com.).

64

Conclusions

Water Quality

1) Water quality parameters, including iron, copper and total phosphorus frequently exceeded the PWQOs. Mercury concentrations at stations 1 and 2 exceeded the PWQO for this metal. Between stations 1 to 5 there was a distinct and progressive decrease in mercury levels in water. The elevated concentrations of mercury in the most upstream stations may originate in the reservoir located upstream of the study area.

2) Most other water-quality parameters, including most metals, phenolics, total cyanide, PCBs, PAHs, and organo-chlorine pesticides were generally below detection limits.

3) MOE monitoring data from several stations indicate that levels of zinc, copper, mercury, chromium, and lead in Welland River water appear to have decreased from 1979 to 1987. However, there has been a slight increase in the concentration of aluminum in the water from 1981 to 1987.

Sediment Quality

1) Concentrations of several parameters including lead, chromium, mercury, cadmium, zinc, iron, nickel, copper, arsenic, total kjeldahl nitrogen, total organic carbon, total phosphorus, and PCBs exceeded the PSQG Lowest Effect Level at some stations. Consistently, stations 9, 10, 12, 18 and 19 had the most elevated concentrations of most of these parameters. Station 9 is situated at a major storm water discharge, stations 10 and 12 are located in the vicinity of the Atlas Steel plant and the Welland WPCP respectively, and stations 18 and 19 are located downstream of the Cyanamid Canada plant. Severe Effect Levels (SELs) were also exceeded for chromium, iron, nickel and copper in the river from station 10 through at least station 19a. Mercury was only above the SEL at station 9; however, mercury concentrations in the fall sediment sample at station 11 were equal to the SEL. Levels of total cyanide and oil and grease also exceeded the QWDGs at some stations.

2) PAHs were also detected at several stations in the study area, with particularly high concentrations noted at station 9. With the exception of trace amount's of PP-DDE, which were detected at stations 6, 9 and 21, all organo-chlorine pesticides were below detection limits. The more highly chlorinated furans were detected at stations 9, 15 and 21. Concentrations of hexa- and hepta-chlorinated furans were highest at station 9. Sediments at station 21 had the highest concentration of octachloro-dibenzofuran. Although the more highly chlorinated dioxin and furan congeners such as octachlorinated forms are generally believed to be less of an environmental concern than are the tetrachlorinated isomers, the toxicity of these contaminants to aquatic biota is poorly understood at present.

65

3) Sediments in section D are relatively uncontaminated. The only water in this section is diverted from the Niagara River to the Queenston-Chippawa Power Canal.

4) Sediments located in the western portion of section A are characterized by high levels of total phosphorus, total kjeldahl nitrogen, and loss on ignition, probably due to the influence of agricultural activities.

Benthic Invertebrate Community and Environmental Quality

1) Stations in section A, located upstream of the City of Welland, were characterized by relatively high numbers of the pollution sensitive species Hexagenia sp. and Coelotanyus sp. . These taxa were generally absent from stations in downstream sections. Stations in sections B, C, and D were characterized by relatively high numbers of the more pollution tolerant taxa Spirosperma ferox, Valvutu sp. , and Hydrobiidae, further substantiating the relatively poorer quality of the sediments.

2) The total abundance of benthic invertebrates varied throughout the study area, ranging from a low of 634 individuals per square meter at station 12 to a high of 5900 individuals per square meter at station 22. Generally, stations located in sections B, C, and D had higher total abundances than those found in section A, and in most cases were also characterized by large number of oligochaetes.

3) Benthic invertebrate diversity (Shannon-Weaver and Brillouin Indices) varied more in sections B, C, and D than in section A, where the indices were relatively constant. Almost all diversity indices were greater than 3, which suggests that the study area represents conditions that are relatively unpolluted.

4) Statistical analyses identified four separate benthic invertebrate communities, corresponding to the four sections of the study area. The structure of each community was governed by concentrations of certain sediment parameters. The benthic communities located in sections A, B, and C (Welland River) were distinguished by their association with sediments which had elevated concentrations of several metals (i.e. aluminum, chromium, copper, arsenic, zinc, lead, mercury) relative to those in section D (Chippawa Creek). . The benthic community of section A occurred in sediments with lower metal levels and higher loss on ignition (organic content) relative to the other two Welland River communities (sections B and C).

66

Fisheries

1) The fish community of the Welland River is dominated by warmwater fish species including catfish, white crappie, carp, suckers, and freshwater drum. No salmonid species were found, although they are common in the Niagara River. The fish community in section D was not sampled.

2) Higher numbers of fish were caught in hoop-net sets in section A than in sections B and C.

Aquatic Macrophytes

1) The Welland River shoreline is dominated by several emergent aquatic macrophytes, particularly Typha larifolia and Saginaria lafifolia. A number of submerged aquatic macrophytes were also noted including Myriophyllum spicarum, VaUisneria americana, and Cerarophyllum demersum. Sparse macrophyte growth was noted only below the Thompson's Creek confluence.

67

References

Acres International Limited. 1990. Welland River Reef Study (Draft). Report prepared for Atlas Steel, Welland -Office.

Arseneault, J. S. 1976. A Field Guide to Streamflow Measurement by Gauging and Metering. Department of Fisheries and the Environment, Vancouver, British Columbia, Technical Bulletin Series PAC/T-76-2.

Brinkhurst, R. O. and D. G. Cook. 1974. Aquatic Earthworms (Annelida:01igochaeta). In Hart, C. W. and S. L. H. Fuller (Eds.). Pollurion Ecology of Freshwater Invertebrates. Academic Press, New York, pp 143- 156.

Brindle, I., A. Wei-chu, X. Li and C. L. MacLaurin. 1988. Study of in Place Pollutants in the Twelve Mile Creek and Welland River. Proceedings Technology Transfer Conference, November 28 and 29, 1988, Royal York Hotel, Toronto, Ontario. ppl75-188.

COA-Canada-Ontario Agreement on Great Lakes Water Quality. 1981. Environmental Baseline Report of the Niagara River. Environment Canada and the Ontario Ministry of the Environment.

Cook, D. G. and M. G. Johnson, 1974. Benthic Macroinvertebrates of the St. Lawrence Great Lakes. J. Fish Res. Bd. Can. 3:763-782.

Department of Commerce and Development. 1960. Twelve Mile Creek Conservation Report. Conservation Branch.

Dickman, M., C. Prescott, and K. L. E. Kaiser. 1983. Variations in the Aquatic Vegetation of the Welland River (Ontario, Canada) Above and Below an Industrial Waste Discharge. J. Great Lakes Res. 9:317-325.

69

Dickman, M. and P. Hayes, date unknown. Evaluation of the Impact of Shock Loading on the Microbiota of the Welland River. Department of Biological Sciences, Brock University, St. Catharines, Ontario.

Dickman, M., J. Smol and P. Steele. 1980. The Impact of Industrial Shock Loading on Selected Biocoenoses in the Lower Welland River, Ontario. \Maier Poll. Res., 15:17-31,

Fitchko, J. 1986. Literature Review of the Effects of Persistent Toxic Substances on Great Lakes Biota. Report prepared for the Great Lakes Science Advisory Board. 255pp

Fremling, C. R. 1964. Mayfly Distribution Indicates Water Quality on the Upper Mississippi River. Science, 146:1164-1166.

Green, R. H., 1979. Sampling Design und Siaiisiical Methods for Environmental Biologists. John Wiley and Sons Inc., New York. 257pp.

Hart, C. J. 1986. 1983 Niagara River Tributary Survey. Report prepared for the Great Lakes Section, Water Resources Branch, the Ontario Ministry of the Environment.

Hynes, H. R. N., 1971. The Biology of Polluted Waters. University of Toronto Press, Toronto. 202pp.

Jackson, D. A., K. M. Somers and H. H. Harvey, 1989. Similarity Coefficients: Measures of Co-Occurrence and Association or Simply Measures of Occurrence. Am. Nat. 133:437-453.

Johnson, M. G. 1964. Ontario Water Resources Commission Report on the Biological Survey of the Welland River - 1964. Ontario Water Resources Commission.

70

Lauritsen, D. D, S. C. Mozley and D. S. White, 1985. Distribution of Oligochaetes in Lake Michigan and Comments on Their Use as Indices of Pollution. J. Great Lakes Res., 11:67-76.

Ludwig, J. A. and J. F. Reynolds, 1988. Siaiisiical Ecology. John Wiley and Sons, New York. 337pp.

Kaesler, R. L., E. E. Herricks and J. S. Grossman. 1978. Use of Indices of Diversity and Hierarchical Diversity in Stream Surveys. In Dickson, K. L., J. Cairns, Jr., and R. J. Livingston (Eds.), Biological Data in Water Pollution Assessment; Quantitative and Statistical Analyses, American Society for Testing and Materials, pp92-112.

Kaiser, K. L. E. and M. E. Comba. 1983. Volatile Contaminants in the Welland River Watershed. J. Great Lakes Res., 9:21 A-2Z{).

Kauss, P. B. 1983. Studies of Trace Contaminants, Nutrients, and Bacteria Levels in the Niagara River. J. Great Lakes Res., 9:249-273.

Mudroch, A., L. Sarazin and T. Lomas. 1988. Summary of Surface and Background

Concentrations of Selected Elements in the Great Lakes Sediments. J. Great Lakes Res.

14:241-251.

Nalepa, T. F. and N. A. Thomas. 1976. Distribution of Macrobenthic Species in Lake Ontario in Relation to Sources of Pollution- and Sediment Parameters. J. Great Lakes Res., 2:150-163. '

Niagara River Toxics Committee. 1984. Report of the Niagara River Toxics Committee, October 1984.

Ontario Ministry of the Environment, 1983. Handbook of Analytical Methods for

Environmental Samples. Laboratory Services and Applied Research Branch, Toronto, Ontario.

Ontario Ministry of the Environment, 199 1 . The Provincial Sediment Quality Guidelines (Draft). Water Resources Branch, Toronto, Ontario.

71

Persaud, D., R. Jaagumagi and A. Hayton. 1990. The Provincial Sediment Quality Guidelines - Draft. Water Resources Branch, Ontario Ministry of the Environment.

Persaud, D. and W. D. Wilkins. 1976. Evaluating Construction Activities Impacting On Water Resources. Ontario Ministry of the Environment.

Rising, J. D. and K. M. Somers, 1989. The Measurement of Overall Body Size in Birds. The Auk, 106:666-674.

Rogers, A., 1971. Matrix Methods in Urban and Regional Analysis. Holden-Day: San Francisco. 508pp.

Schloesser, D. W. 1988. Zonation of Mayfly Nymphs and Caddisfly Larvae in the St. Mary's River. J. Great Lakes Res. , 14:227-233.

Steele, P. O. 1980. Water Quality and Fish Populations of the Welland River, Ontario.

Master of Science Thesis, Department of Biological Sciences, Brock University, St. Catharines, Ontario.

Weed, C. E. and C. W. Rutschky. 1972. Benthic Macroinvertebrate Community Structure in a Stream Receiving Acid Mine Drainage. Proc. Pa. Acad. Sci., 1972: 4641-47.

Wilkinson, L., 1990. SYSTAT: The System Jar Statistics. Systat Inc., Evanston, IL. Wilkinson, L., 1990. SYGRAPH. Systat Inc., Evanston, IL.

Winner, R. W., M. W. Boesel and M. P. Farrell. 1980. Insect Community Structure as an Index of Heavy-Metal Pollution in Lotie Systems. Can. J. Fish. Aquat. Sci., 37:647-655.

72

Appendix I

Water-Quality Graphics

Parameter		Page
Copper		74
Mercury		75
Aluminum		76
Iron, Zinc		77
Magnesium		78,
Total Phosphorus and
Total Kjeldahl	Nitrogen	79
Ammonia, Nitrite and Nitate	80

Parameter concentrations at each station sampled are indicated with shaded bars for summer and fall sampling periods. Existing Provincial Water Quality Objectives (PWQOs) are indicated with horizontal lines.

73

Copper (Summer)

PWQO

Station

Copper (Fall)

Station

Detection Limit = 5.0 ug/L PWQO = 5.0 ug/L

Mercury {Summer)

0.35 0.30 0.25

_l 0.20

■>^ O) ^ 0.15

0.10

0.05

0.00

FI '

i:n

In il

1 :V ■ ! -

PWQO

Station

Mercury (Fall)

PWQO

Station

Detection Limit = 0 . 05 ug/L PWQO = 0.2 ug/L

Aluminum (Summer)

PWQO

Station

Aluminum (Fal

PWQO

■^c\JCo^^locû^^oocDO

Station

PWQO = 0 . 075 mg/L

Iron (Summer)

PWQO

Detection Limit = 0.01 mg/L PWQO = 0.3 mg/L .

Station

Zinc (Summer)

PWQO

Station

Detection Limit = 10 ug/L PWQO = 30 ug/L

Magnesium (Summer)

	16.0
	14.0
	12.0
-I	10.0
E	8.0
	6.0
	4.0
	2.0
	0.0

-|

1 1 é

m

\ m

C\( 00 Tf «o

station

no PWQO available

Total Phosphorus (Summer)

Station

Detection limit = 0 . 001.4 PWQO = 0.03mg/L

Total Kjeldahl Nitrogen (Summer)

Station

no PWQO available

o

E E

CO

c o

O)

o

CD 03

■a

c: CO

CD

CO "c o E E <

JO

> CO

<0

o a

Appendix II Sediment Quality Graphics

Parameter		Page
Lead		82
Chromium		83
Mercury		84
Cadmium		85
Arsenic		86
Zinc		87
Iron		88
Nickel		89
Copper		90
Aluminum ana	Magnesium	91
Loss On Ignition and
Total Organic	Carbon	92
Total Kjeldahl :	Nitrogen and
Total Phosphorus	93
Total Cyanide		94
Oil and Grease		95
Total PCBs		96

Parameter concentrations at each station sampled are indicated with shaded bars for summer and fall sampling periods. Provincial Sediment Quality Guideline lowest effect levels (LELs) are indicated with horizonal lines. Where concentrations approach or exceed severe effect levels (SELs), these levels are also graphed. Open Water Disposal Guidelines are indicated where Provincial Sediment Quality Guidelines are not available.

Lead (Summer)

140 120 100 -

CD 80

^ 60

1 In i H L . .	pn	V-1-n	T	lfl..B.-,-._-
■p^jn4-	-i 1 - !	nnP^ ;.i	< ;-; j :J

LEL

y- c\t CO -rt m

Station

Lead (Fall)

140 120 100 80 60 40 20 0

LEL = 31 ug/g SEL = 250 ug/g

-
-	l-]	I	1 (~j		m
-	n		- 1	\		rannn	\	^hS
	r 1 1	1	--i-	"1	-'	- -i ;l-^-	-,\-	1 i""l		__j
		J --I : 1	-1	J	1	ni i ■Mi 1	-A 1 "	1 i	A.	1 ,

LEL

Station

Chromium (Summer)

700

600

500

CD 400

=5 300

200

100

0

F^ni^FlF^f^FH^Hme

n

a

Hi

\m

ir'r-H-.JT-Ti

LEL

SEL

Station

Chromium (Fall)

f\JU

fïm

600 500 400

1

1

Fl

P^

300

-

f

^

r~|

■ 1 -. 1

1 1

i 1 |. j

-_\

1

200

- . ■ „

j

!

1

j

1 i

100

■H

i

--

-

LL

•-

-

i -r

-'i

J-- 1

4 - - -

n

r — — r-RriRfH

■- ■

--

\4

-f

—

--

-■

.-[

-i-

- 1

.J-..-.--'

LEL

SEL

Station

LEL = 26 ug/g SEL= 110 ug/g

Mercury (Summer)

3.5

3

2.5

D5 2

O)

=3 1.5

1

0.5

-
'--- -il	: .:|-..|---..^|^-^f^^^^-^-^^

LEL SEL

QU_X=^

03 CM CM CVJ CM

Station

Mercury (Fall)

3.5 3

2.5 2

1.5

1

0.5

LEL = 0.2ug/g SEL = 2 ug/g

- in %

■ .....-[oij-l-L-i-iU

! it.il- i r— ! I -J ; : -1

LEL SEL

Station

Cadmium (Summer)

1.60 1.40 1.20 1.00 O) 0-80 0.60 0.40 tt 0.20 0.00

-	■ i L	i	a
s* ■-■1 - !	n" .1	UZ HmR	i -In	' ^nnn		zn^	Fl

LEL

c\j CO rr lo CD

Station

Cadmium (Fall)

1.60 1.40 1.20 O) 1.00 ZJ 0.80 0.60 0.40 0.20 0.00

-		■			1			fZ- ■
;	i j	i -.1	- j 1	r î	1	z ■		i	1 1 ' 1 r-'^ i ' 1 1 : 1 , M, , ,

LEL

Station

LEL = 0.6ug/g SEL= lOug/g

Arsenic (Summer)

LEL

Station

Arsenic (Fall)

18 16 14

O)

D) 10 8 6 4 2

-	f		m _m, _ ^ H'
- nn lu 1 ! 1 J	1	: 1 i ;	~]	il.' : 1 i Il 1 1 . . li il- ., .,, ,, w ,1 i , fi , , 1

LEL

Station

LEL = 6 ug/g SEL = 33 ug/g

Zinc (Summer)

800

§^400

200

m	T	nnnr 1 1	J

LEL SEL

Station

Zinc (Fall)

800

600

400 -

200

Station

LEL= 120ug/g SEL = 820 ug/g

Iron (Summer)

120 100 80

O) 60

E

40 20

X
F:	r-	h i	:-	i *

LEL SEL

Station

Iron (Fall)

120 100 D) 80 E 60 40 20

-	i — :	In		1	Inn [Mn M-Jr--	n- inn nnn ^	n	1 j tt	Q !	n	n
	; j	V. \ -lii	1		i i -:	ijij j	. 1 " =1	i 1 i		i -j

LEL SEL

Station

LEL = 2% (20 mg/g) SEL = 4% (40 mg/g)

Nickel (Summer)

300

O) 200

100

F	1
FI ^		É---m

LEL SEL

Station

Nickel (Fall)

400

300

=J 200

100

-	:	! in	^-, ■	1 1 n	n	1 1	Ir-j 1 i 1 ; ! 1. '	r-	—j r^]
r-v-.-r-nnffl		Il i -H-1		h	1 i	i	Il i		1 ! :

LEL SEL

Station

LEL= 16ug/g SEL = 75 ug/g

Copper (Summer)

160	nn
D) 100 50		r-^	pp	z	n " - J .^	'n 1 --1	1 -.. i n :-■! zzbijjz		' : 1. i Z-.Z^	i -mm .] .-Jl-.-il

LEL SEL

Station

Copper (Fall)

150

100

50 h

f	1 1 f	I
npLi: .::	"i Zi ^ nZZZ i 1 11 \r-iA i Z n ^		--3
, , , , H -HZ 1:1 "Ji-P .., ., ii i: :Zil.i! .1 ,1.. ; , i;Z , , 1

LEL. SEL

Station

LEL= 16ug/g SEL =110 ug/g

Aluminum (Summer)

40

30

D) 20

10

i -i n M [.! ir-i i nP

No LEL . SEL or OWDG available

Station

Magnesium (Summer)

Station

No LEL . SEL or OWDG available

Loss On Ignition (Summer)

c 10

o

°- 6

t]

;MJiad to toj

Rm

y w

Mm

n

ni

I

I : i t -I t-^^j t^"-1 1-^

-cv*», v<0<b^ 'ï>^.Ç>^^^^.5^^^^^^^cÇ>cvcO'o?

Station

no LEL . SEL or OWDG available

Total Organic Carbon (Summer)

12.0

10.0 -

c 8.0

o

qS 6.0

4.0

2.0

0.0

1:-" 1:
r'":"7'-""7'7	^-rr"":"'"m"":'""":":u"'	::-J

LEL

SEL

Station

LEL = 1 percent SEL= 10 percent

Total Kjeldahl Nitrogen (Summer)

3.000

	2.500
CD	2,000
	1.500
	1.000
	500

F	1
■_ . r	' u ::

LEL

Station

LEL = 550 ug/g SEL = 4.800 ug/g

Total Phosphorus (Summer)

2.500

2.000

1.500

500

LEL SEL

Station

LEL = 600 ug/g SEL = 2000 ug/g

Total Cyanide (Summer)

OWDG

1.5

i.O

0.5

Station

Total Cyanide (Fall)

OWDG

1.5

1.0

0.5 -

Station

OWDG = 0. 1 ug/g Detection limit = 0. 05 ug/g

Oil and Grease (Summer)

Station

Oil and Grease (Fall)

12.000 10.000 8.000

O) 6.000

3

4.000

2.000

0

nnFlnnn

n

I

i[:in

OWDG

m

n

ra

Station

OWDG = 1 . 500 ug/g

Total PCB's (Fall)

0.16 0.14 0.12 0.10 0.08 0.06 0.04 0.02 0.00

"

•■'-i i

f^

r

R-!

-^

- 1 1

1 "1

1 ^ i ^ 1 i

1 , , , ,

^

1^

LEL

y- C\J CO -^ V) (O

Station

LEL = 0.07 ug/g

SEL cannot be calculated

Detection limit = 0 . 05 ug/g

Appendix III

Field observations of conductivity, dissolved oxygen, and water temperature during the fall survey.

97

	November Survey Conductivity /zmhos/cm
Station	North	Center	South
1	N/A	N/A	N/A
2	N/A	N/A	N/A
3	N/A	N/A	N/A
4	540	540	550
5	510	■530	530
6	500	500	500
7	500	500	505
8	540	500	500
9	450	400	400
10	425	430	425
10a	410	415	425
11	425	415	450
12	425	400	420
13	440	425	470
14	450	450	435
15	425	425	450
16	425	425	430
17	425	430	425
18	425	420	425
19	430	440	430
19a	450	450	450
20	475	450	450
21	450	450	450
22	310	315	360
23	340	325	325

98

	November Survey - Temperature and Dissolved Oxygen |
	North	Center	South 1
Station	Temp X	D.O. mg/L	Temp °C	D.O. ■ mg/L	Temp °C	D.O. mg/L
1	7.2	10.8	7.2	10.5.	7.9	10.3
2	7.5	10.2	7.8	10.0	7.5	10.2
3	7.5	10.2	7.9	10.1	7.7	10.1
4	6.9	8.6	7.0	8.4	7.0	8.4
5'	7.0	9.4	7.2	9.1	7.1	9.1
6	6.8	9.6	6.5	9.6	6.7	9.5
7	6.2	9.4	6.4	9.4	7.1	9.7
8	6.5	9.8	6.5	9.5	6.5	9.6
9	7.5	8.8	8.0	8.7	8.0	9.1
10	8.0	9.6	8.7	9.4	8.5	9.3
10a	8.2	9.2	8.5	9.4	8.7	• 9.3 •
11	8.0	9.7	8.0	9.7	8.5	9.6
12	8.5	9.6	8.3	9.5	8.8	9.4
13	8.2	9.2	8.3	9.5	8.5	9.5
14	8.5	9.8	8.5	9.6	8.5	9.6
15	8.5	9.3	8.1	8.3	8.1	8.3
16	7.5	8.8	7.5	8^7	8.1	8.6
17	8.4	8.9	8.1	8.9	8.4	8.7
18	8.0	8.8	8.0	8.8	8.2	8.8
19	8.0	8.8	7.9	8.9	8.0	8.9
19a	7.9	8.9	7.9	8.9	7.9	8.9
20	8.9	8.7	8.2	8.7	8.1	8.7
21	8.1	8.9	8.1	8.8	8.2	8.8
22	8.0	9.8	6.0	8.8	4.5	7.9
23	9.0	10.0	9.1	10.0	9.0	9.9

99

100

Appendix IV Benthic Invertebrate Species List

101

INSECTA: DIPTERA

Chironomidae: Chironominae:

Chironomini

Chironomus (Chaetolabis) sp.

Chironomus (Chironomus) sp.

Chironomus (C.) anthracinus group

Chironomus (C.) halophilus group

Chironomus (C.) plumosus group

Chironomus (C.) salinarius group

Chironomus (C.) staegeri group

Chironomus (C.) thummi group

Cladopehna sp.

Cryptochironomus sp.

Cryptotendipes sp.

Dicrotendipes sp.

Endochironomus sp.

Glyptotendipes (Glyptotendipes) sp

Microchironomus sp.

Parachironomous sp.

Paralauterborniella sp.

Polypedilum (Polydelium) sp.

Polypedilum (Tripodura) sp.

Pseudochironomus sp.

Rheotanytarsus sp.

Tanytarsus sp.

Tanypodinae:

Apsectrotanypus sp. Coelotanypus sp. Procladius sp. Tanypus (Tanypus) sp. Djalmabatista sp. Macropelopia sp.

Orthocladinae:

Diplocladius sp. Paracricotopus sp.

102

Ceratopogonidae: Bezzia sp. Culicoides sp. Mallochohelis sp.

Chaoboridae:

Chaoborus sp.

EPHEMEROPTERA: Ephemericlae:

Hexagenia sp. Caenidae:

Caenis sp.

COLEOPTERA:

Elmidae:

Dubiraphia sp. Dytiseidae:

Coptotomus sp.

MEGALOPTERA Sialidae:

Sialis sp.

LEPTIDOPTERA

Pyralidae:

TRICOPTERA

Polycentropodidae:

Polycentropus sp.

Cyrnellus sp. Hydropsychidae:

Cheumatopsyche sp. Hydroptilidae:

Hydroptila sp. Leptoceridae:

Oecetis sp.

ODONATA

Coenagrionidae:

Enallagma sp.

103

OLIGOCHAETA:

Tubificidae:

Limnodrilus hoffmeisteri L. profundicola L. angustipennis L. claparedianus L. sp.

Spirosperma ferox Quistadrilus multisetosus Aulodrilus sp. Tubificidae immature

Naididae

Pristinella sp. P. sima P. osborni P. jenkinae Pristina ? sp. Nadidae

Lumbriculidae

NEMATODA: ■ PLANARIA: HIRUDINEA: HYDRACHNIDIA:

CRUSTACEA: Amphipoda

Gammarus sp.

Hyalella sp. Isopoda

Caecidotea sp.

MOLLUSCA:

GASTROPODA

Valvatidae

Valvata sp.

V. tricarinata

V. sincera Hydrobiidae

Hydrobiidae

104

Bithyniidae

Bithynia tentaculata Lymnaeidae

Physa sp.

Stagnicola sp.

Fossaria sp. Planorbidae

Gyralus sp.

Helisoma anceps

BIVALVA

Sphaeriidae

Sphaerium sp.

Musculium sp.

Psidium sp. Corbiculidae

Corbicula sp Unionidae

Quadrula quadrula

Ligumia sp.

Ligumia nasuta Dressenidae

Dreissena polymorpha

105

106

Appendix V Benthic Invertebrate Species Counts

107

IC 2A 2B

Station 2C 3A 3E

3C 4A 4B 4C

INSECTA: DIPTERA Chironomidae: Chironominae:

Chironomini

Chironomus (Chaetolabis ) sp.

Chironomus (Chironomus) sp.

Chironomus (C.) anthracinus group

Chironomus (C.) halophilus group

Chironomus (C.) plumosus. group

Chironomus (C. ) salinarius group

Chironomus (C.) staegeri group

Chironomus (C.) thummi group

Cladopelma sp.

Cryptochironomus sp. 2

Cryptotendipes sp.

Dicrotendipes sp.

Endochironomus sp.

Glyptotendipes (Glyptotendipes ) sp 10

Microchironomus sp.

Parachironomous sp.

Paralauterborniella sp.

Polypedilum (Polydelium) sp.

Polypedilum (Tripodura) sp. 14

Pseudochironomus sp.

Rheotanytarsus sp.

Tanytarsus sp. 4

Tanypodinae: Apsectrotanypus sp. Coelotanypus sp. Procladius sp. Tanypus (Tanypus) sp. D jalmabatista sp. Macropelopia sp.

			12		6	4		3	5	4
44	6	4	6	8	8	8	5	4	7	2
15	10	8	3	14	4	6	10	9	6	2
20			21		6	8	5		3

Orthocladinae: Diplocladius sp, Paracricotopus sp.

Ceratopogonidae: Bezzia sp. Culicoides sp. Mallochohelis sp.

Chaoboridae: Chaoborus sp.

EPHEMEROPTERA: Ephemeridae: Hexagenia sp.

Caenidae: Caenis s

station lA IB IC 2A 2B 2C 3A 38 3C 4A 48 4C

COLEOPTERA: Elmidae:

Dubiraphia sp. Dytiseidae:

Coptotomus sp.

MEGALOPTERA Sialidae: Sialis sp.

LEPTIDOPTERA Pyralidae:

TRICOPTERA Polycentropodidae :

Polycentropus sp.

Cyrnellus sp. Hydropsy chidae:

Cheumatopsyche sp. Hydroptilidae: • Hydroptila sp. Leptoceridae:

Oecetis sp.

ODONATA Coenagrionidae Enallagma sp.

Oligochaeta: TUBIFICIDAE Limnodrilus hoffmeisteri L. profundicola L. angustipennis L. claparedianus L. sp.

Spirosperma ferox Quistadrilus multisetosus Aulodrilus sp. Tubificidae immature

NADIDAE Pristinella sp. P. sima P. osborni P. jenkinae Pristina ? sp. Nadidae

LUMBRICULIDAE

Nematoda: Planaria: Hirudinea: Hydrachnidia

109

station lA IB IC 2A 2B 2C 3A 3B 3C 4A 48 4C

Crustacea: AMPHIPODA

Gammarus sp.

Hyalella sp. PODOCOPA ISOPODA

Caecidotea sp. DECAPODA

Cambaridae

Mollusca: GASTROPODA Valvatidae

Valvata sp.

V. tricarinata

V. sincera Hydrobiidae

Hydrobiidae Bithyniidae

Bithynia tentaculata Lymnaeidae

Physa sp.

Stagnicola sp.

Fossaria sp. Planorbidae

Gyralus sp.

Helisoma anceps

3IVALVA Sphaeriidae

Sphaerium sp.

Musculium sp.

Psidium sp. Corbiculidae

Corbicula sp Unionidae

Quadrula quadrula

Ligumia sp.

Ligumia nasuta Dressenidae

Dreissena polymorpha

3 12 2 2

1

110

5C 6A 6B

Station 6C 7A 7E

INSECTA: DIPTERA Chironomidae : Chironominae :

Chironomini

Chironomus (Chaetolabis ) sp.

Chironomus (Chironomus) sp.

Chironomus (C. ) anthracinus group

Chironomus (C.) halophilus group

Chironomus (C.) plumosus group

Chironomus (C.) salinarius group

Chironomus (C. ) staegeri group

Chironomus (C. ) thummi group

Cladopelma sp.

Cryptochironomus sp.

Cryptotendipes sp.

Dicrotendipes sp.

Endochironomus sp.

Glyptotendipes (Glyptotendipes ) sp.

Microchironomus sp.

Parachironomous sp.

Paralauterborniella sp.

Polypedilum (Polydelium) sp.

Polypedilum (Tripodura) sp.

Pseudochironomus sp.

Rheotanytarsus sp.

Tanytarsus sp.

Tanypodinae: Apsectrotanypus sp. Coelotanypus sp. Procladius sp. Tanypus (Tanypus) sp. D jalmabatista sp. Macropelopia sp.

11 10 6

Orthocladinae: Diplocladius sp. Paracricotopus sj

Ceratopogonidae : Bezzia sp. Culicoides sp. Mallochohelis sp.

Chaoboridae: Chaoborus sp.

EPHEMEROPTERA: Ephemeridae:

Hexagenia sp. Caenidae:

Caenis sp.

Ill

station 5A 5B 5C 6A 6B 6C 7A 7B 7C 8A 80 8C

COLEOPTERA: Elmidae:

Dubiraphia sp. Dytiseidae:

Coptotomus sp.

MEGALOPTERA Sialidae: Sialis sp.

LEPTIDOPTERA Pyralidae:

TRICOPTERA Polycentropodidae :

Polycentropus sp.

Cyrnellus sp. Hydropsychidae:

Cheumatopsyche sp. Hydroptilidae:

Hydroptila sp. Leptoceridae:

Oecetis sp.

ODONATA Coenagrionidae Enallagma sp.

Oligochaeta: TUBIFICIDAE Limnodrilus hof fmeisteri L. profundicola L. angustipennis L. claparedianus L. sp.

Spirosperma ferox Quistadrilus multisetosus Aulodrilus sp. Tubificidae immature

63 19 13 7

3 13 95 2

28 41 13 23

NAD I DAE Pristinella sp. P. sima P. osborni P. jenkinae Pristina ? sp. Nadidae

LUMBRICULIDAE

Nematoda: Planaria: Hirudinea: Hydrachnidia

station

6C 7A 7B 7C 8A

Crustacea: AMPHIPODA

Gammarus sp.

Hyalella sp. PODOCOPA ISOPODA

Caecidotea sp. DECAPODA

Cambaridae

Mollusca: GASTROPODA Valvatidae

Valvata sp.

V. tricarinata

V. sincera Hydrobiidae

Hydrobiidae Bithyniidae

Bithynia tentaculata Lymnaeidae

Physa sp.

Stagnicola sp.

Fossaria sp. Planorbidae

Gyralus sp.

Helisoma anceps

El VAL VA Sphaeriidae

Sphaerium sp.

Musculium sp.

Psidium sp. Corbiculidae

Corbicula sp Unionidae

Quadrula quadrula

Ligumia sp.

Ligumia nasuta Dressenidae

Dreissena polymorpha

113

station 9C lOA lOB lOC IIA IIB IIC 12A 12E

INSECTA: DIPTERA Chironomidae: Chironominae:

Chironomini

Chironomus (Chaetolabis ) sp.

Chironomus (Chironomus) sp.

Chironomus (C. ) anthracinus group

Chironomus (C. ) halophilus group

Chironomus (C. ) plumosus group

Chironomus (C. ) salinarius group

Chironomus (C. ) staegeri group

Chironomus (C.) thummi group

Cladopelma sp.

Cryptochironomus sp.

Cryptotendipes sp.

Dicrotendipes sp.

Endochironomus sp.

Glyptotendipes (Glyptotendipes ) sp.

Microchironomus sp.

Parachironomous sp.

Paralauterborniella sp.

Polypedilum (Polydelium) sp.

Polypedilum (Tripodura) sp.

Pseudochironomus sp.

Rheotanytarsus sp.

Tanytarsus sp.

Tanypodinae : Apsectrotanypus sp. Çoelotanypus sp. Procladius sp. Tanypus (Tanypus) s Djalmabatista sp. Macropelopia sp.

2 15 6 2 2 35 10 22

Orthocladinae: Diplocladius sp. Paracricotopus sp.

Ceratopogonidae : Bezzia sp. Culicoides sp. Mallochohelis sp.

Chaoboridae: Chaoborus sp.

EPHEMEROPTERA: Ephemeridae:

Hexagenia sp. Caenidae:

Caenis sp.

station 9C lOA lOB IOC llA IIB IIC 12A 12B 12C

COLEOPTERA: Elmidae:

Dubiraphia sp. Dytiseidae:

Coptotomus sp.

MEGALOPTERA Sialidae: Sialis sp.

LEPTIDOPTERA Pyralidae:

TRICOPTERA Polycentropodidae:

Polycentropus sp.

Cyrnellus sp. Hydropsychidae :

Cheumatopsyche sp. Hydroptilidae:

Hydroptila sp, Leptoceridae:

Oecetis sp.

ODONATA Coenagirionidae Enallagma sp.

Oligochaeta: TUBIFICIDAE Limnodrilus hof f meisteri L. profundicola L. angustipennis L. claparedianus L. sp.

Spirosperma ferox Quistadrilus mu'ltisetosus Aulodrilus sp. Tubificidae immature

64	40	5			64
12	2			1
	4	2	7	11	2
	4	1	1		6	1
80	32	3	7	10	52	5

1 10 10 10

1

NADIDAE Pristinélla sp. P. sima P. osborni P. jenkinae Pristina ? sp. Nadidae

LUMBRICULIDAE

Nematode: Planaria: Hirudinea: Hydrachnidia

115

station 9A 9B 9C lOA lOB lOC IIA IIB IIC 12A 128 12C

Crustacea: AMPHIPODA

Gammarus sp.

Hyalella sp. PODOCOPA ISOPODA

Caecidotea sp. DECAPODA

Cambaridae

1 6 1

Mollusca: GASTROPODA Valvatidae

Valvata sp.

V. tricarinata

V. sincera Hydrobiidae

Hydrobiidae Bithyniidae

Bithynia tentaculata Lymnaeidae

Physa sp.

Stagnicola sp.

Fossaria sp. Planorbidae

Gyralus sp.

Helisoma anceps

1 16 2 7 3 3 19 3

BIVALVA Sphaeriidae

Sphaerium sp. ■

Musculium sp.

Psidium sp. Corbiculidae

Corbicula sp Unionidae

Quadrula quadrula

Ligumia sp.

Ligumia nasuta Dressenidae

Dreissena polymorpha

13 22 6 1

16 18 2 2 7 3

station 13A 13B 13C 14A 14B 14C 15A 15B 15C 16A 168 16C

INSECTA: DIPTERA Chironomidae: Chironominae:

Chironomini

Chironomus (Chaetolabis ) sf

(Chironomus) sp. (C. ) anthracinus group (C.) halophilus group (C. ) plumosus group (C. ) salinarius group (C. ) staegeri group (C. ) thummi group

Chironomus

Chironomus

Chironomus

Chironomus

Chironomus

Chironomus

Chironomus

Cladopelma sp.

Cryptochironomus sp.

Cryptotendipes sp.

Dicrotendipes sp.

Endochironomus sp.

Glyptotendipes (Glyptotendipes ) sp.

Microchironomus sp.

Parachironomous sp.

Paralauterborniella sp.

Polypedilum (Polydelium) sp.

Polypedilum (Tripodura) sp.

Pseudochironomus sp.

Rheotanytarsus sp.

Tanytarsus sp.

Tanypodinae: Apsectrotanypus sp. Coelotanypus sp. Procladius sp. Tanypus (Tanypus) sp. Djairaabatista sp. Macropelopia sp.

Orthocladinae: Diplocladius sp. Paracricotopus sp.

Ceratopogonidae : Bezzia sp. Culicoides sp. Mallochohelis sp.

Chaoboridae: Chaoborus sp.

EPHEMEROPTERA: Ephemeridae:

Hexagenia sp. Caenidae:

Caenis sp.

8 26 13 22 2

117

station 13A 13B 13C 14A 14B 14C ISA 15B 15C 16A 16B 16C

COLEOPTERA: Elmidae:

Dubiraphia sp. Dytiseidae:

Coptotomus sp.

MEGALOPTERA Sialidae: Sialis sp.

LEPTIDOPTERA Pyralidae:

TRICOPTERA Polycentropodidae:

Polycentropus sp.

Cyrnellus sp. Hydropsychidae :

Cheumatopsyche sp. Hydroptilidae:

Hydroptila sp. Leptoceridae:

Oecetis sp.

ODONATA Coenagrionidaë Enallagma sp.

Oligochaeta: TUBIFICIDAE Limnodrilus hoffmeisteri L. profundicola L. angustipennis L. claparedianus L. sp.

Spirosperma ferox Quistadrilus multisetosus Aulodrilus sp. Tubificidae immature

12 42 35 36

NADIDAE Pristinella sp. P. sima P. osborni P. jenkinae Pristina ? sp. Nadidae

2

1

1 1

LUMBRICULIDAE

Nematoda: Planaria: Hirudinea: Hydrachnidia

118

station 13A 13B 13C 14A 14B 14C 15A 15B 15C 16A 16B 16C

Crustacea: AMPHIPODA

Gammarus sp.

Hyalella sp. PODOCOPA ISOPODA

Caecidotea sp. DECAPODA

Cambaridae

Mollusca: GASTROPODA Valvatidae

Valvata sp.

V. tricarinata

V. sincera Hydrobiidae

Hydrobiidae Bithyniidae

Bithynia tentaculata Lymnaeidae

Physa sp.

Stagnicola sp.

Fossaria sp. Planorbidae

Gyralus sp.

Helisoma anceps

31 7 2 14 20 16 13 13 2 5

2 7 9 19 17 6

5IVALVA Sphaeriidae

Sphaerium sp.

Musculium sp.

Psidium sp. Corbiculidae

Corbicula sp Unionidae

Quadrula quadrula

Ligumia sp.

Ligumia nasuta Dressenidae

Dreissena polymorpha

119

station 17A 17B 17C 18A 18B 18C 19A 19B 19C 20A 208 20C

INSECTA: DIPTERA Chironomidae: Chironominae:

Chironomini

Chironomus (Chaetolabis) sp.

Chironomus (Chironomus) sp.

Chironomus (C. ) anthracinus group

Chironomus (C.) halophilus group

Chironomus (C. ) plumosus group

Chironomus (C. ) salinarius group

Chironomus (C.) staegeri group

Chironomus (C. ) thummi group

Cladopelma sp.

Cryptochironomus sp.

Cryptotendipes sp.

Dicrotendipes sp.

Endochironomus sp.

Glyptotendipes (Glyptotendipes ) sp.

Microchironomus sp.

Parachironomous sp.

Paralauterborniella sp.

Polypedilum (Polydelium) sp.

Polypedilum (Tripodura) sp.

Pseudochironomus sp.

Rheotanytarsus sp.

Tanytarsus sp.

Tanypodinae: Apsectrotanypus sp. Coelotanypus sp. Procladius sp. Tanypus (Tanypus) sp. Djalmabatista sp. Macropelopia sp.

1		6	2					6
6	13	12	5	1	14	1	15	20
	1	2	1		2			2

Orthocladinae: Diplocladius sp. Paracricotopus sj

Ceratopogonidae: Bezzia sp. Culicoides sp. Mallochohelis sp.

Chaoboridae: Chaoborus sp.

EPHEMEROPTERA: Ephemeridae :

Hexagenia sp. Caenidae:

Caenis sp.

120

17A 17B lie ISA li

Station

18C 19A 19B 19C 20A 20B 20C

COLEOPTERA: Elmidae:

Dubiraphia sp. Dytiseidae:

Coptotomus sp.

MEGALOPTERA Sialidae: Sialis sp.

LEPTIDOPTERA Pyralidae:

TRICOPTERA Polycentropodidae:

Polycentropus sp.

Cyrnellus sp. Hydropsychidae :

Cheumatopsyche sp. Hydroptilidae:

Hydroptila sp. Leptoceridae:

Oecetis sp.

ODONATA Coenagrionidae Enallagma sp.

Oligochaeta: TUBIFICIDAE Limnodrilus hof f meisteri L. profundicola L. angustipennis L. claparedianus L. sp.

Spirosperma ferox Quistadrilus multisetosus Aulodrilus sp. Tubificidae immature

2	1 1		4	3
26 137	65	6	52	63

NADIDAE Pristinella sp. P. sima P. osborni P. jenkinae Pristina ? sp. Nadidae

LUMBRICULIDAE

Nematoda: Planaria: Hirudinea: Hydrachnidia

121

station 17A 17B ne 18A 18B 18C 19A 19B 19C 20A 208 20C

Crustacea: AMPHIPODA

Gammarus sp.

Hyalella sp. PODOCOPA ISOPODA

Caecidotea sp. DECAPODA

Cambaridae

Mollusca: GASTROPODA Vaivatidae

Valvata sp.

V. tricarinata

V. sincera Hydrobiidae

Hydrobiidae Bithyniidae

Bithynia tentaculata Lymnaeidae

Physa sp.

Stagnicola sp.

Fossaria sp. Planorbidae

Gyralus sp.

Helisoma anceps

13 17 6 6 27 1 1

10 63 13 22 21 34 9

BIVALVA Sphaeriidae

Sphaerium sp.

Musculium sp.

Psidium sp. Corbiculidae

Corbicula sp Unionidae

Quadrula quadrula

Ligumia sp.

Ligumia nasuta Dressenidae

Dreissena polymorphe

6 6 9 5 4 2 2 3 2

5 20 4 1 2

122

station 21A 21B 21C 22A 22B 22C 23A 231

23C 24A 24B 24C

INSECTA: DIPTERA Chironomidae: Chironominae: Chironomini

Chironomus ( Chaetolabis ) sp. Chironomus (Chironomus) sp.

(C.) anthracinus group (C. ) halophilus group

plumosus group salinarius group staegeri group thummi group

Chironomus

Chironomus

Chironomus (C. )

Chironomus (C.)

Chironomus (C. )

Chironomus (C. )

Cladopelma sp.

Cryptochironomus sp.

Cryptotendipes sp.

Dicrotendipes sp.

Endochironomus sp.

Glyptotendipes (Glyptotendipes) sp.

Microchironomus sp.

Parachironomous sp.

Paralauterborniella sp.

Polypedilum (Polydelium) sp.

Polypedilum (Tripodura) sp.

Pseudochironomus sp.

Rheotanytarsus sp.

Tanytarsus sp.

10

10 24 20 228 90 110 35

20 10 70

Tanypodinae: Apsectrotanypus sp. Coelotanypus sp. Procladius sp. Tanypus (Tanypus) sp. D jalmabatista sp. Macropelopia sp.

2 12 1

1 7 12 36 1 2

2 4 2 2

Orthocladinae: Diplocladius sp. Paracricotopus sp.

Ceratopogonidae : Bezzia sp. Culicoides sp. Mallochohelis sp.

Chaoboridae : Chaoborus sp.

EPHEMEROPTERA: Ephemeridae:

Hexagenia sp. Caenidae:

Caenis sp.

123

station 21A 21B 21C 22A 22B 22C 23A 23B 23C 24A 248 24C

COLEOPTERA: Elmidae:

Dubiraphia sp. Dytiseidae:

Coptotomus sp.

MEGALOPTEFLA Sialidae: Sialis sp.

LEPTIDOPTERA Pyralidae:

TRICOPTERA Polycentropodidae :

Polycentropus sp.

Cyrnellus sp. Hydropsychidae:

Cheumatopsyche sp. Hydroptilidae :

Hydroptila sp. Leptoceridae :

OecGtis sp.

ODONATA Coenagrionidae Enallagma sp.

Oligochaeta: TUBIFICIDAE Limnodrilus hoffraeisteri L. profundicola L. angustipennis L. claparedianus L. sp.

Spirosperma ferox Quistadrilus mult isetosus Aulodriius sp. Tubificidae immature

NADIDAE Pristinella sp. P. sima P. osborni P. jenkinae Pristina ? sp. Nadidae

1 5 2 22

2

2 6

14

35 3 1 9

26 24 22 30 54 33 29 9 83 25 3 21 2

LUMBRICULIDAE

Nematoda: Planaria: Hirudinea: Hydrachnidia

3 2 12 1 1 7

124

station 21A 21B 21C 22A 22B 22C 23A 23B 23C 24A 24B 24C

sp.

Crustacea: AMPHIPODA

Gammarus

Hyalella sp. PODOCOPA ISOPODA

Caecidotea sp. DECAPODA

Cambaridae

10 5

1

Mollusca: GASTROPODA Valvatidae

Valvata sp.

V. tricarinata

V. sincera Hydrobiidae

Hydrobiidae Bithyniidae

Bithynia tentaculata Lymnaeidae

Physa sp.

Stagnicola sp.

Fossaria sp. Planorbidae

Gyralus sp.

Helisoma anceps

BIVALVA Sphaeriidae

Sphaerium sp.

Musculium sp.

Psidium sp. Corbiculidae

Corbicula sp Unionidae

Quadrula quadrula

Ligumig sp.

Ligumia nasuta Dressenidae

Dreissena polymorpha

10 34 7 14 9 4

1 6 38

125

station 25A 25B 25C

INSECTA: DIPTERA Chironomidae: Chironominae:

Chironomini

Chironomus (Chaetolabis) sp.

Chironomus (Chironomus) sp.

Chironomus (C. ) anthracinus group

Chironomus (C.) halophilus group

Chironomus (C. ) plumosus group

Chironomus (C.) salinarius group

Chironomus (C.) staegeri group

Chironomus (C. ) thummi group

Cladopelma sp.

Cryptochironomus sp.

Cryptotendipes sp.

Dicrotendipes sp.

Endochironomus sp.

Glyptotendipes (Glyptotendipes ) sp.

Microchironomus sp.

Parachironomous sp.

Paralauterborniella sp.

Polypedilum (Polydelium) sp.

Polypedilum (Tripodura) sp.

Pseudochironomus sp.

Rheotanytarsus sp.

Tanytarsus sp.

Tanypodinae: Apsectrotanypus sp. Coelotanypus sp. Procladius sp. Tanypus (Tanypus) sp. Djalmabatista sp. Macropelopia sp.

Orthocladinae: Diplocladius sp. Paracricotopus sp.

Ceratopogonidae: Bezzia sp. Culicoides sp. Mallochohelis sp.

Chaoboridae: Chaoborus sp.

EPHEMEROPTERA: Ephemeridae:

Hexagenia sp. Caenidae:

Caenis sp.

126

station 25A 25B 25C

COLEOPTERA: Elmidae:

Dubiraphia sp.' Dytiseidae: Coptotomus sp.

MEGALOPTERA Sialidae: Sialis sp.

LEPTIDOPTERA Pyralidae:

TRICOPTERA Polycentropodidae :

Polycentropus sp.

Cyrnellus sp. Hy dropsy c h idae:

Cheumatopsyche sp. Hydroptilidae:

Hydroptila sp. Leptoceridae:

Oecetis sp.

ODONATA Coenagr ion idae Enallagma sp.

Oligochaeta: TUBIFICIDAE Limnodrilus hof fmeisteri 22 2

L. profundicola L. angustipennis L. claparedianus L. sp.

Spirosperma ferox 1

Quistadrilus multisetosus

Aulodrilus sp. 12

Tubificidae immature 34 23 12

NAD IDAE Pristinella sp. P. sima P. osborni P. jenkinae Pristina ? sp. Nadidae 1.

LUMBRICULIDAE

Nematoda:

Planaria:

Hirudinea: 1

Hydrachnidia

127

station 25A 25B 25C

Crustacea: AMPHIPODA

Gammarus sp.

Hyalella sp. PODOCOPA ISOPODA

Caecidotea sp. DECAPODA

Cambaridae

Mollusca: GASTROPODA Valvatidae

Valvata sp.

V. tricarinata

V. sincera Hydrobiidae

Hydrobiidae Bithyniidae

Bithynia tentaculata Lymnaeidae

Physa sp.

Stagnicola sp. .

Fossaria sp. Planorbidae

Gyralus sp.

Helisoma anceps

BIVALVA Sphaeriidae

Sphaerium sp.

Musculium sp.

Psidium sp. Corbiculidae

Corbicula sp Unionidae

Quadrula quadrula

Ligumia sp.

Ligumia nasuta Dressenidae

Dreissena polymorpha

128

Appendix VI

Benthic Invertebrate Species Abundances

129

station 5 6

INSECTA: DIPTERA Chironomidae: Chironominae:

Chironomini

Chironomus (Chaetolabis) sp.

Chironomus (Chironomus) sp.

Chironomus (C. ) anthracinus group

Chironomus (C.) halophilus group

Chironomus (C.) plumosus group

Chironomus (C. ) salinarius group

Chironomus (C. ) staegeri group

Chironomus (C. ) thummi group

Cladopelma sp.

Cryptochironomus sp.

Cryptotendipes sp.

Dicrotendipes sp.

Endochironomus sp.

Glyptotendipes (Glyptotendipes ) sp.

Microchironomus sp.

Parachironomous sp.

Paralauterborniella sp.

Polypedilum (Polydelium) sp.

Polypedilum (Tripodura) sp.

Pseudochironomus sp.

Rheotanytarsus sp.

Tanytarsus sp.

27 20

173 13

60

27

40 13 100

133

133 40

113 173 53 53 60 33 13 67 93 53 80 40

13

7		53 7
13	27
7	53
13
7

Tanypodinae: Apsectrotanypus sp. Coelotanypus sp. Procladius sp. Tanypus (Tanypus) s] Djalmabatista sp. Macropelopia sp.

	80	67	80	40	13	93
333	120	140	87	27	87	53	7
213	167	133	113	127	127	140	133
133	140	127	20	33

Orthocladinae: Diplocladius sp. Paracricotopus sp.

Ceratopogonidae : Bezzia sp. Culicoides sp. Mallochohelis sp.

Chaoboridae: Chaoborus sp.

7 20 13 13 27

EPHEMEROPTERA: Ephemeridae:

Hexagenia sp. Caenidae:

Caenis sp.

80 80 233 180 127 27 107

130

Statron 12 3 4 5 6 7

COLEOPTEFIA: Elmidae:

Dubiraphia sp. Dytiseidae: Coptotomus sp.

MEGALOPTEFIA Sialidae: Sialis sp.

LEPTIDOPTERA Pyralidae:

TRICOPTERA Polycentropodidae :

Polycentropus sp.

Cyrnellus sp. Hydropsychidae :

Cheumatopsyche sp. Hydr.optilidae:

Hydroptila sp. Leptoceridae:

Oecetis sp.

ODONATA Coenagrionidae Enallagma sp.

Oligochaeta: TUBIFICIDAE Limnodrilus hof fmeisteri L. profundicola L. angustipennis L. claparedianus L. sp.

Spirosperma ferox Quistadrilus multisetosus Aulodrilus sp. Tubificidae immature

NAD I DAE Pristinella sp. P. sima P. osborni P. jenkinae Pristina ? sp. Nadidae

40 7 7 7 33 13 13 7

7

47 140 67 100 153 133 107 180 727

13 80

13 47 13

40 7 33

180 340 247 260 547 133 460 293 767

LUMBRICULIDAE

Nematoda : Planaria: Hirudinea: Hydrachnidia

131

station 123456789

Crustacea: AMPHIPODA

Gammarus sp.

Hyalella sp. PODOCOPA ISOPODA

Caecidotea sp. DECAPODA

Catnbar idae

7 20 20 13 47

7 27 7 13

7 7 13 20 7 240

Mollusca: GASTROPODA Valvatidae

Valvata sp.

V. tricarinata

V. sincera Hydrobiidae

Hydrobiidae Bithyniidae

Bithynia tentaculata Lymnaeidae

Physa sp.

Stagnicola sp.

Fossaria sp. Planorbidae

Gyralus sp.

Helisoma anceps_

B I VAL VA Sphaeriidae

Sphaerium sp.

Musculium sp.

Psidium sp. Corbiculidae

Corbicula sp Unionidae

Quadrula quadrula

Ligumia sp.

Ligumia nasuta Dressenidae

Dreissena polymorpha

40 20 60 107 113 13 33 7

132

station 12 13 14

INSECTA: DIPTERA Chironomidae: Chironominae:

Chironomini

Chironomus ( Chaetolabis ) sp.

Chironomus (Chironomus) sp.

Chironomus (C. ) anthracinus group

Chironomus (C. ) halophilus group

Chironomus (C. ) plumosus group

Chironomus (C.) salinarius group

Chironomus (C. ) staegeri group

Chironomus (C. ) thummi group

Cladopelma sp.

Cryptochironomus sp.

Cryptotendipes sp.

Dicrotendipes sp.

Endochironomus sp.

Glyptotendipes (Glyptotendipes) sp.

Microchironomus sp.

Parachironomous sp.

Paralauterborniella sp.

Polypedilum (Poiydelium) sp.

Polypedilum (Tripodura) sp.

Pseudochironomus sp.

Rheotanytarsus sp.

Tanytarsus sp.

					7
40		67 13		20 13	13
.00	120	67		13
93	27	13		20
40	20	133 27	40	113	167

13 107

Tanypodinae: Apsectrotanypus sp. Coelotanypus sp. Procladius sp, Tanypus (Tanypus) S] D jalmabatista sp. Macropelopia sp.

53	93	40		13
60	67	267	27	73
	13	13		7

87 407 180 207 13 40 20

Orthocladinae: Diplocladius sp. Paracricotopus sp.

	13	67
3
3	133	40

Ceratopogonidae: Bezzia sp. Culicoides sp. Mallochohelis s

Chaoboridae: Chaoborus sp.

EPHEMEROPTERA: Ephemeridae:

Hexagenia sp. Caenidae:

Caenis sp.

13 7 7

33

COLEOPTERA: Elmidae:

Dubiraphia sp. Dytiseidae:

Coptotomus sp.

MEGfiLOPTERA Sialidae: Sialis sp.

LEPTIDOPTERA Pyralidae:

Station 10 10a 11 12 13 14 15 16 17

TRICOPTERA Polycentropodidae :

Polycentropus sp.

Cyrnellus sp. Hydropsy chidae:

Cheumatopsyche sp. Hydroptilidae:

Hydroptila sp. Leptoceridae:

Oecetis sp.

ODONATA Coenagrionidae Enallagma sp.

Oligochaeta: TUBIFICIDAE Limnodrilus hof fmeisteri L. profundicola L. angustipennis L. claparedianus L. sp.

Spirosperma ferox Quistadrilus multisetosus Aulodrilus sp. Tubificidae immature

7 33 53 253 613 40

7

133 160 7 200 20 20 47 7 7 47 33 7 7 40 33 13 107 7

460 327 33 93 373 627 753 607 567

NADIDAE Pristinella sp. P. sima P. osborni P. jenkinae Pristina ? sp. Nadidae

7	33	13	60	53
7		53 13		27	13
		20	7		7

LUMBRICULIDAE

Nematoda: Planaria: Hirudinea: Hydrachnidia

134

station 10 10a 11 12 13 14 15 16 17

Crustacea: AMPHIPODA

Gammarus sp.

Hyalella sp. PODOCOPA ISOPODA

Caecidotea sp. DECAPODA

Cambaridae

20 47

7 20 60 7

i7 7 87 7 20

Mollusca: GASTROPODA Valvatidae

Valvata sp.

V. tricarinata

V. sincera Hydrobiidae

Hydrobiidae Bithyniidae

Bithynia tentaculati Lymnaeidae

Physa sp.

Stagn.icola sp.

Fossaria sp. Planorbidae

Gyralus sp.

Helisoma anceps

BIVALVA Sphaeriidae

Sphaerium sp.

Musculium sp.

Psidium sp. Corbiculidae

Corbicula sp Unionidae

Quadrula quadrula

Ligumia sp.

Ligumia nasuta Dressenidae

Dreissena polymorphe

27 33 133 80 247 153 240 187 260 20 87 40

100 67 180 27 67 27 107 280 287 7

227 427 73 27 20 20 60 133 80 13 60 20 40 7 20 27

93 187 13

135

station 19a 20 21

INSECTA: DIPTERA Chironomidae : Chironominae:

Chironomini

Chironomus (Chaetolabis ) sp.

(Chironomus) sp.

(C.) anthracinus group

(C. ) halophilus group

(C. ) plumosus group

(C. ) salinarius group

(C.) staegeri group

(C. ) thummi group

Chironomus

Chironomus

Chironomus

Chironomus

Chironomus

Chironomus

Chironomus

Cladopelma sp.

Cryptochironomus sp.

Cryptotendipes sp.

Dicrotendipes sp.

Endochironomus sp.

Glyptotendipes (Glyptotendipes ) sp.

Microchironomus sp.

Parachironomous sp.

Paralauterborniella sp.

Polypedilum (Polydelium) sp.

Polypedilum (Tripodura) sp.

Pseudochironomus sp.

Rheotanytarsus sp.

Tanytarsus sp.

Tanypodinae: Apsectrotanypus sp. Coelotanypus sp. Procladius sp. Tanypus (Tanypus) sp. D jalmabatista sp. Macropelopia sp.

57

67

293

2853

80 200

13 233

13	40	7		33 7
33	247	40	193	133
20	13		27	20
13			53

Orthocladinae: Diplocladius sp. Paracricotopus sp.

Ceratopogonidae : Bezzia sp. Cuiicoides sp. Mallochohelis sp.

Chaoboridae: Chaoborus sp.

EPHEMEROPTERA: Ephemeridae:

Hexagenia sp. Caenidae:

Caenis sp.

136

station 18 19 19a 20 21 22 23

COLEOPTERA: Elmidae:

Dubiraphia sp. Dytiseidae: Coptotomus sp.

MEGALOPTERA Sialidae: Sialis sp.

LEPTIDOPTERA Pyralidae:

TRICOPTERA Polycentropodidae:

Polycentropus sp.

Cyrnellus sp. Hydropsychidae:

Cheumatopsyche sp. Hydroptilidae:

Hydroptila sp. Leptoceridae:

Oecetis sp.

ODONATA Coenagrionidae Enallagma sp.

Oligochaeta: TUBIFICIDAE Limnodrilus hoffmeisteri L. profundicola L. angustipennis L. claparedianus L. sp.

Spirosperma ferox Quistadrilus mult isetosus Aulodrilus sp. Tubificidae immature

307 360 160 73 53 253 233

27 27 7 7

20

13

7 13 53 93

20 47 7

7 80 60

1520 807 460 140 480 780 807

NAD I DAE Pristinella sj: P. sima P. psborni P. jenkinae Pristina ? sp. Nadidae

33 20

13 7

27 20 13

LUMBRICULIDAE

Nematode : Planaria: Hirudinea: Hydrachnidia

13 7 40 27 47

.37

station 18 19 19a 20 21 22 23

Crustacea: AMPHIPODA

Gammarus sp.

Hyalella sp. PODOCOPA ISOPODA

Caecidotea sp. DECAPODA

Cambaridae

20 100 27 7

Mollusca: GASTROPODA Valvatidae

Valvata sp.

V. tricarinata

V. sincera Hydrobiidae

Hydrobiidae Bithyniidae

Bithynia tentaculata Lymnaeidae

Physa sp.

Stagnicola sp.

Fossaria sp. Planorbidae

Gyralus sp.

Helisoma anceps

BIVALVA Sphaeriidae

Sphaerium sp.

Musculium sp.

Psidium sp. Corbiculidae

Corbicula sp Unionidae

Quadrula quadrula

Ligumia sp.

Ligumia nasuta Dressenidae

Dreissena polymorpha

80 193 53 180 93 7

13 13

67 507 287 433 260 267 20 7

127 193 60 93 340 100 47 33 20 60 280

7

13 7

138

Appendix VII

Taxonomic Composition of Benthic Communities as defined by Cluster Analysis

Numbers are mean abundances (#/m^)

,39

		Community
Invertebrate Taxa	1	2	3	4
DIPTERA
Chironomidae:
Chironominae:
Chironomini	12	I	3 ■	0
Chironomus (Chaetolabis) sp.	23	0	0	0
Chironomus (Chironomus) sp.	13	4	27	47
Chironomus (C.) anthracinus group	2	4	37	0
Chironomus (C.) halophilus group	3	■ 0	0	0
Chironomus (C.) plumosus group	3	1	0	0
Chironomus (C.) salinarius group	12	1	105	0
Chironomus (C.) staegeri group	22	0	0	0
Chironomus (C.) thummi group	14	2	77	0
Cladopelma sp.	7	2	0	0
Cryptochironomus sp.	53	66	68	37
Cryptotendipes sp.	5	0	0	33
Dicrotendipes sp.	1	2	20	153
Endochironomus sp.	2	1	0	1543
Glyptotendipes (Glyptotendipes) sp.	11	0	5	0
Microchironomus sp.	2	Ô	0	0
Parachironomous sp.	3	1	0	0
Paralauterboraiella sp.	0	0	0	40
Polypedilum (Polydelium) sp.	11	1	8	333
Polypedilum (Tripodura) sp.	12	0	0	0
Pseudochironomus sp.	2	0	0	3
Rheotanytarsus sp.	5	0	0	0
Tanytarsus sp.	9	0	0	33
Tanypodinae:
Apsectrotanypus sp.	47	19	47	0
Coelotanypus sp.	107	1	0	0
Procladius sp.'	144	157	160	330
Tanypus (Tanypus) sp.	57	12	7	0
Djalmabatista sp.	0	2	0	0
Macropelopia sp.	0	6	0	0
Orthocladinae:	0	0	20	0
Diplocladius sp.	0	0	8	0

140

Community

Invertebrate Taxa

Paracricotopus sp. 5 1 55 0

Ceratopogonidae:

Bezzia sp. 10 2 2 0

Culicoides sp. 12 0 0

Mallochohelis sp. 0 10 0

Chaoboridae:

Chaoborus sp. 5 10 0

EPHEMEROPTERA: Ephemeridae:

Hexagenia sp. Caenidae:

Caenis sp. COLEOPTERA:

Elmidae: Dubiraphia sp.

Dytiseidae: Coptotomus sp. MEGALOPTERA Sialidae:

Sialis sp.

LEPTIDOPTERA Pyfalidae: TRICOPTERA

Polycentropodidae: Polycentropus sp. Cyrnellus sp.

Hydropsychidae:

Cheumatopsyche sp.

Hydroptilidae: Hydroptila sp.

Leptoceridae:

Oecetis sp. ODONATA

Coenagrionidae

Enallagma sp.

04	4	10	3
1	1	0	0
15 .	2	10	13
I	0	0	0
0	0	3	0
0 .	0	12	27
1	1	0	0
0	2	2	0
0	0	0	3
0	0	2	0
3	1	0	0

Invertebrate Taxa

Community

TUBIFICIDAE

Limnodrilus hoffmeisteri

L. profundicola

L. angustipennis

L. claparedianus

L. sp.

Spirosperma ferox

Quistadrilus multisetosus

Aulodrilus sp.

Tubificidae immature NADIDAE

Pristinella sp.

P. sima

P. osborni

P. jenkinae

Nadidae

LUMBRICULIDAE Nematoda: Planaria: Hirudinea: Hydrachnidia Crustacea: AMPHIPODA

Gammarus sp.

Hyalella sp. ISOPODA

Caecidotea sp. GASTROPODA

Valvatidae

Valvata sp.

V. tricarinata

V. sincera

116	178	310	243
2	5	22	3
0	0	0	3
0	0	0	10
8	0	5	7
0	29	85	73
1	25	30	0
0	8	0	30
308	584	397	793
0	10	7	7
1	15	2	13
0	2	0	0
0	10	0	0
2	8	0	0
0	0	0	3
2	8	25	0
0	0	0	10
0	11	35	37
2	0	2	0
8	12	28	63
0	0	2	3
7	19	82	7
0	161	48	3
0	13	5	7
0	6	0	0

142

Community

Invertebrate Taxa

■ 1	2	• 3	4
0	46	0	0
2	186	87	14

Hydrobiidae

Hydrobiidae Bithyniidae

Bithynia tentaculata Lymnaeidae

Physa sp.

Stagnicola sp.

Fossaria sp. Planorbidae

Gyralus sp.

Helisoma anceps BIVALVA Sphaeriidae

Sphaerium sp.

Musculium sp.

Psidium sp. Corbiculidae

Corbicula sp Unionidae

Quadrula quadrula

Ligumia sp.

Ligumia nasuta Dressenidae

Dreissena polymorpha 0 4 327

0	2	0	0
0	0	2	0
0	0	0	7
2	0	0	0
0 .	1	0	0
48	105	250	73
1	1	0	0
0	19	22	140
1	0	12	0
0	1	0	0
0	2	0	0
0	1	2	0
0	1	0	0

143

144

Appendix VIII

Component loadings and percent total variance explained for the PCA on benthic invertebrate abundances

145

Appendix VIII: Component loadings and percent total variance for the PCA of the benthic invertebrate abundances

Component Loadings

TAXA

Factor I

Factor II

Chironomini

Chironomus (Chaetolabis) sp.

Chironomous (Chironomous) sp.

Cladopelma sp.

Cryptochironomus sp.

Cryptotendipes sp.

Dicrotendipes sp.

Endochironomus sp.

Glyptotendipes (Glyptotendipes) sp.

Microchironomus sp.

Parachironomous sp.

Paralauterbomiella sp.

Polypedilum (Polydelium) sp.

Polypedilum (Tripodura) sp.

Pseudochironomus sp.

Rheotanytarsus sp.

Tanytarsus sp.

Apsectrotanypus sp.

Coelotanypus sp.

Procladius sp.

Tanypus (Tanypus) sp.

Djalmabatista sp.

Macropelopia sp.

Orthocladinae:

Diplocladius sp.

Paracricotopus sp.

Bezzia sp.

Culicoides sp.

Mallochohelis sp.

Chaoborus sp.

Hexagenia sp.

Caenis sp.

Dubiraphia sp.

Coptotomus sp.

Sialis sp.

Pyralidae:

Polycentropus sp.

Cymellus sp.

Cheumatopsyche sp.

Hydroptila sp.

Oecetis sp.

Enallagma sp.

0.337	0	364
0.459	0.	187
0.098	0	361
0.009	-0	127
0.083	-0	046
0.125	0	385
0.390	0	524
0.432	0	511
0.132	0	227
0.194	0	304
0.104	-0	005
0.350	0	381
0.263	0	639
0.339	0	172
0.134	0	579
0.447	0	304
0.141	0	463
0.335	-0	120
0.821	0	372
0.196	0	129
0.522	-0	182
0.069	-0	258
0.166	-0	369
0.009	-0	095
0.194	0	038
0.060	0	134
0.492	0	078
0.024	-0	230
0.069	-0	258
0.172	-0	056
0.631	0	288
0.024	0	128
0.197	0	602
0.417	0	124
0.094	-0	054
0.649	0	608
0.061	0	016
0.250	-0	149
0.403	0	506
0.257	0	182
0.548	0	151
0.194	0	038

I4(S

Appendix VIII: (continued)
TAXA	Componen	Lx)adin2S
Factor I	Factor II
L. sp.	0.484	0.282
Spirosperma ferox	0.668	0.032
Quistadrilus multisetosus	■ 0.380	-0.546
Aulodrilus sp.	0.359	0.094
Tubificidae immature	0.663	0.084
Pristinella sp.	0.493	-0.473
Pristina ? sp.	0.149	-0.222
Nadidae	0.085	-0.509
LUMBRICULIDAE	0.403	0.506
Nematoda:	-0.309	-0.044
Planaria:	0.542	0.637
Hirudinea:	0.806	0.099
Hydrachnidia	-0.293	0,237
Gammarus sp.	0.560	0.341
Hyalella sp.	0.438	0.406
Caecidotea sp.	0.247	0.085
Valvata sp.	0.444	-0.730
Hydrobiidae	0.472	-0.710
Bithynia tentaculata	0.115	-0.078
Physa sp.	0.069	-0.258
Stagnicola sp.	-0.094	-0. 054
Fossaria sp.	0.403	0.506
Gyralus sp.	-0.227	-0.028
Helisoma anceps	-0.028	-0. 158
Sphaerium sp.	0.418	-0.208
Musculium sp.	-0. 194	-0. 142
Psidium sp.	0.480	-0.305
Corbicula sp	-0.012	0.045
Unionidae	0.104	-0 . 299
Quadrula quadrula	0.142	-0.344
Ligumia sp.	0.305	-0.275
Dreissena polymorpha	0.537	-0.087
Percent Variance	12.791	10.687

147

148

Appendix IX

Fish Species found in the study area

149

Appendix IX: Fish species found in the study area

Lower Lower Welland Welland River' River^

Welland River^

Welland 12-Mile Rivei^ Creek^

Niagara River*

White Crappie '^ White Bass White Perch Channel Catfish Gizzard Shad Freshwater Drum White Sucker *

Yellow Bullhead Shprthead Redhorse Carp *

Pumpkinseed *

Rock Bass *

Smallmouth Bass Spottail Shiner * Emerald Shiner * Johnny Darter * Brook Silverside Sculpin

Banded Killifish Golden Shiner Creek Chub Blntnose minnow Brown Bullhead Tadpole Madtom Mudminnow Northern Pike Black Crappie Yellow Perch Smelt

Bluegill Sunfish Sea Lamprey Brown Trout Brook Trout Hog Sucker Northern Pearl Dace

150

Appendix IX - continued

Lower Lower

Welland Welland Welland Welland 12-Mile Niagara

River' River^ River^ River^ Creek^ River*

Redside Dace Northern Redbelly Dace Finescale Dace River Chub Blacknose Dace Longnose Dace Rosyface Shiner Common Shiner Brassy Minnow Fathead Minnow American Eel Rainbow Darter Fantail Darter Brook Stickleback Longnose Sucker Silver Redhorse River Redhorse Black Redhorse Greater Redhorse Stonecat

Brindled Madtom Black Bullhead Lake Sturgeon Longnose Gar Bow fin Alewife Rainbow Trout Lake Trout Coho Salmon Cisco

Lake Whitefish Round Whitefish Mooneye Muskellunge Lake Chub

151

Appendix IX - continued

Lower Lower

Welland Welland Welland Welland 12-Mile Niagara

River' River^ River^ River^ Creek^ River*

Blackchin Shiner

Blacknose Shiner

Spotfin Shiner

Sand Shiner

Mimic Shiner

Burbot

Threespine Stickleback

Ninespine Stickleback

Trout-Perch

Green Sunfish

Largemouth Bass

Sauger

Walleye

Iowa Darter

Least Darter

Log-Perch

Blackside Darter

Goldfish

Chain Pickerel

1 - Johnson, 1964

2 - Tarandus Associates Limited, 1990 - Summer and Fall field surveys

3 - Brindle ei al., 1988 - goldfish actually a carp/golfish hybrid 4- Steele, 1981

5 - Department of Commerce and Development, 1960

6 - Fish species thought to occur in the Niagara River area - Scott and Grossman, 1973

152

Appendix X

Flow calculations for sections A, B, and C.

153

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.56

Appendix XI

Water Quality Data

157

Water and Sediment Parameter Abbreviations:

Abbreviation	Parameter
Pb	Lead
Zn	Zinc
Cd	Cadmium
Cr	Chromium
Fe	Iron
Se •	Selenium
As	Arsenic
Sb	Antimony
Ba	Barium
Be	Beryllium
Co	Cobalt
Cu	Copper
Mo	Molybdenum
Ni	Nickel
V	Vanadium
Ag	Silver
Hg	Mercury
CN	Cyanide
Mn	Manganese
Mg	Magnesium
AI	Aluminum
PCB	Polychlorinated biphenyls
OC	Organochlorine
PAH	Polycyclic Aromatic Hydrocarbons
NH4	Ammonia
TP	Total Phosphorus
TKN	Total Kjeldahl Nitrogen
NO2	Nitrite
NO3	Nitrate
TOC	Total Organic Carbon
LOI'	Loss on Ignition
SAR'	Sodium Adsorption Ratio

158

Water - Summer Survey

SITE	Zn	Cd	Mn	Co	Cu	Fe	Pb	Cr
mg/L	mg/L	mg/L	mg/L	mg/L	mg/L	mg/L	mg/L
1	<0.01	< 0.002	0.18	< 0.005	0.03	2.1	<0.01	< 0.005
2	<0.01	< 0.002			0.015		<0.01	< 0.005
3	<0.01	< 0.002			0.005		<0.01	< 0.005
4	<0.01	<■ 0.002			0.03		<0.01	< 0.005
5	<0.01	< 0.002			0.04		<0.01	< 0.005
6	<0.01	< 0.002			0.05		<0.01	< 0.005
7	<0.01	< 0.002			0.03		<0.01	< 0.005
8	<0.01	< 0.002			0.02		<0.01	< 0.005
9	<0.01	< 0.002	0.01	< 0.005	0.02	0.095	<0.01	< 0.005
10	<0.01	< 0.002			0.01		<0.01	< 0.005
10a	0.02	< 0.002			0.005		<0.01	< 0.005
11	<0.01	< 0.002			0.015		<0.01	< 0.005
12	<0.01	< 0.002			0.015		<0.01	< 0.005
13	<0.01	< 0.002			0.02		<0.01	< 0.005
14	<0.01	< 0.002			0.01		<0.01	< 0.005
15	<0.01	< 0.002	0.02	<0.005	0.005	0.43	<0.01	<0.005
16	<0.01	< 0.002			0.035		<0.01	< 0.005
17	<0.01	< 0.002			0.025		<0.01	< 0.005
18	<0.01	< 0.002			0.01		<0.01	0.0075
19	<0.01	< 0.002			0.03		• <0.01	< 0.005
19a	<0.01	< 0.002			0.005		<0.01	< 0.005
20	<0.01	< 0.002			0.01		<0.01	< 0.005
21	<0.01	< 0.002	0.01	< 0.005	0.015	0.4	<0.01	< 0.005
22	<0.01	< 0.002			0.0125		<0.01	< 0.005
23	<0.01	< 0.002	0.01	< 0.005	0.005	0.06	<0.01	< 0.005

159

Water - Summer Survey (Continued)

SITE	Ni	Be	Mo	V	A!	Ba	Hg	As
mg/L	mg/L	mg/L	mg/L	mg/L	mg/L	Mg/L	Mg/L
1	< 0.005	< 0.005	< 0.005	< 0.005	1.74	0.04	0.3	<5
2					1.42		0.25	<5
3					1.155		0.125	<5
4					0.97		0.1	<5
5					0.81		<0.05	<5
6					0.82		<0.05	<5
7					0.75		<0.05	<5
8					0.28		<0.05	<5
9	< 0.005	< 0.005	< 0.005	< 0.005	0.12	0.02	<0.05	<5
10					0.12		<0.05	<5
10a					0.13		<0.05	<5
11					0.11		<0.05	<5
12					0.1		<0.05	<5
13					0.3		<0.05	<5
14					0.28		<0.05	<5
15	< 0.005	< 0.005	< 0.005	< 0.005	0.36	0.02	<0.05	<5
16					0.24		<0.05	<5
17					0.3!		<0.05	<5
18					0.295		<0.05	<5
19					0.34		<0.05	<5
19a					0.32		<0.05	<5
20					0.3		<0.05	<5
21	< 0.005	< 0.005	< 0.005	< 0.005	0.32	0.02	<0.05	<5
99					0.16		<0.05	<5
23	< 0.005	< 0.005 ■	< 0.005	< 0.005	0.16	0.02	<0.05	<5

160

Water - Summer Survey (Continued)

SITE	Se	Ag	CN	Colour	Cond	Ammnia-N	Sb	Nitrite
Mg/L	mg/L	mg/L	TCU	uS/cm	mg/L	/^g/L	mg/1
1	<1	< 0.005	0.002	48	440	0.008	<2	0.003
2			0.002		440
3			0.002		415
4			0.002		420
5			0.002		360
6			0.002		350
7			0.002		310
8			0.002		290
9	<1	< 0.005	0.002	3	290	0.008	<2	0.005
10			0.002		290
10a			0.002		290
11			0.002		310
12			0.002		310
13			0.002		300
14			0.002		300
15	<1	< 0.005	0.002	4	290	0.008	<2	0.023
16			0.002		290
17			0.002		290
18			0.002		300
19			0.002		300
19a			0.002		300
20			0.002		310
21	<1	< 0.005	0.002	4	300	0.33	<2	0.04
22			0.002		280
23	<1	< 0.005	0.002	9	290	0.23	<2	0.003

Water - Summer Survey (Continued)

SITE	Mg	Nitrate	pH	Phenolics	TKN	ss	Turb	TP
mg/L	mg/L	-log[Hn	mg/L	mg/L	mg/L	NTU	mg/L
1	14.1	0.35	8	0.01	1	48	6.5	0.2
9			7.9	0.012	1.01		5.5	0.25
3			7.95	0.0025	0.955		7.3	0.1515
4			7.95	0.029	0.81		6.8	0.149
5			8.05	<0.001	0.62		4.3	0.098
6			8	0.004	0.56		4.2	0.083
7			8.15	0.004	0.43		1.8	0.053
8			8.1	<0.001	0.33		0.5	0.024
9	8.5	0.16	8.125	0.012	0.42	7	0.3	0.016
10			8.1	0.012	0.28		0.3	0.016
10a			8.2	0.001	0.3		0.3	0.013
11			8.25	0.002	0.33		0.8	0.066
12			8.15	0.001	0.4		1.1	0.064
13			8.15	0.022	0.38		0.7	0.044
14			8.1	0.03	0.4		0.8	0.045
15	8.9	0.31	8.1	0.024	0.39	14	0.5	0.041
16			8.05	0.016	0.37		0.5	0.042
17			8.1	0.031	0.34		0.4	0.042
18			8.45	0.008	0.33		0.55	0.048
19			8.15	0.002	0.39		0.6	0.053
19a			8.15	0.004	0.46		0.6	0.053
20			8.1	0.022	0.4		0.6	0.052
21	9.2	0.55	8.15	0.016	2.6	14	0.5	0.06
22			8.4	0.0015	0.315		0.3	0.0135
23	8.4	0.16	8.25	0.005	0.39	4	0.3	0.013

162

Water - Fall Survey

SITE	Cu	Al	Hg	Phenols
mg/L	mg/L	Mg/L	mg/L
1	0.005	1.85	<0.05	<0.001
2	0.01	2.7	<0.05	<0.001
3	0.005	3.4	<0.05	<0.001
4	0.01	1.03	<0.05	<0.001
5	0.005	0.86	<0.05	< 0.001
6	0.005	1.9		< 0.001
7	0.005	1.91		<0.001
8	0.005	1.14		<0.001
9	< 0.005	1.49		<0.001
10	0.01	0.54	<0.05	<0.00I
10a				<0.001
11				<0.001
12				<0.001
13				<0.001
14				<0.001
15	0.01	1.3	<0.05	<0.001
16				<0.001
17				<0.001
18				< 0.001
19				<0.001
19a				<0.001
20				<0.001
21	< 0.005	1.07	<0.05	<o.oor
22				<0.001
23	0.035	0.34	<0.05	<0.001

163

164

Appendix XII

Sediment Quality Data

165

Sediments - Summer Survey

SITE	CN	LOI	O&G	phenolics	PH	Zn	Cd	TOC
Mg/g	%	Mg/g	Mg/g	-log[H^]	Mg/g	Mg/g	%
1	0.13	14	2900	0.01	6.8	116	0.6	7.4
2	<0.05	11	1040	0.01	7	97	0.5
3	<0.05	12	980	0.01	6.9	116	0.45
4	0.075	10.5	845	0.01	6.95	104	0.425
5	<0.05	12	1070	0.02	7	108	0.55
6	<0.05	7.2	870	0.01	7.3	112	0.4
7	<0.05	7	1800	0.01	6.9	135	0.55
8	<0.05	7	2500	0.01	7	112	0.4
9	<0.05	7	4550	0.01	7	335	0.8	3.55
10	<0.05	7	2000	0.01	7	550	0.975
"lOa	<0.05	5	1990	0.01	7	270	0.4
11	<0.05	2	250	0.01	7.3	98	0.15
12	<0.05	6	3200	0.01	7.1	620	1.4
13	<0.05	2	195	0.01	7.5	75	0.25
14	<0.05	2	320	0.01	7.5	76	0.1
15	<0.05	2	410	0.01	7.3	83	0.15	0.92
16	<0.05	4	1110	0.01	7.1	116	0.2
17	<0.05	5	1670	0.01	7.2	163	0.35
18	0.09	5	3100	0.01	7.1	191	0.5
19	<0.05	5	2500	0.01	7.1	330	0.9
19a	<0.05	5	750	0.01	7.2	127	0.25
20	0.18	5	1280	0.01	7.2	69.5	0.1
21	0.1	3	860	0.01	7.2	95	0.2	1.13
22	<0.05	5	1240	0.025	7	75.5	0.675
23	<0.05	6	1670	0.01	7	55	0.3	2.5

166

Sediments - Summer Survey (Continued)

SITE	SAR	TKN	Mn	Co	Cu	Fe	Pb	Cr	Ni	Be
	Mg/g	/^g/g	Mg/g	Mg/g	Mg/g	Mg/ g	Mg/g	Mg/ g	A^g/g
.	1.14	2800	580	14.5	35	32000	49	40	33	1.5
2					24		26	40
3					33		37	49
4					29		31	43.5
5					31		34	43
6					30		34 ■	40
7					35		85	45
8					51		40	44
9	0.76	1910	430	10.75	93.5	30000	74.5	55.5	54	1
10					77		86	95
10a					50		38	91
11					28		25	53
12					85		62	260
13					34		21	162
14					26		22	79
15	0.83	290	960	■ 19	47	58000	26	300	178	I
16					31		23	43
17					58		50	300
18					64		45.5	265
19					115		41	107
19a					33		24	59
20					54.5		40.5	53
21	0.8	800	650	13	94	35000	29	97	75	1
. 22					19		20.5	22.5
23	0.9	1340	330	6.5	15	16400	16	19	19.5	0.5

167

Sediments - Summer Survey (Continued)

SITE	Mo	V	Al	Mg	Ba	Hg	Ag	Sb	TP	As
Mg/g	/^g/g	Mg/g	Mg/g	Mg/g	Mg/g	/^g/g	Mg/g	/^g/g	/ig/g
1	0.5	58	34000	9400	139	0.08	0.5	1	1020	5
2			33000			0.04				5
3			38000			0.12				7
4			34000			0.07				5
5			32000			0.06				5
6			31000			0.06				5
7			31000			0.1				6
8			26000			0.4				5
9	1.75	34.5	17750	15900	102.5	2.22	0.5	1	1005	5
10			34000			0.18				11
10a			35000			1.4				8
11			35000			0.02				6
12			38000			0.68				17
13			29000			0.02				6
14			29000			0.02				6
15	24	42	23000	13900	118	0.06	0.5	1	1060	6
16			32000			0.28				6
17			31000			0.1				6
18			22000			0.28				6.5
19			38000			0.26				10
19a			28000			0.08				6
20			25000			0.04				5.5
21	3.5	43	26000	14000	127	0.1	0.5	1	1300	6
22			15750			0.07				4
23	0.5	27	12400	17200	51	0.06	0.5	1	620	3

168

Sediments - Fall Survey

SITE	PCBs	Hg	Zn	Cd	CN	O&G
/^g/g	A^g/g	Mg/g	/^g/g	Mg/g	Mg/g
1	<0.05				<0.05	960
n					0.15	670
3	<0.05		■			1570
4						540
5	<0.05		130	0.4		720
6			112	0.6		970
7	0.13	0.36	177	0.9		2700
8	0.074	1.64	125	0.6		1660
9	0.11	3.11	309	0.7		4850
10	0.045	1.3	310	0.7		3600
10a		0.14	142	0.3		780
11		2	280	0.8		3400
12		0.92	570	1.5		11800
13		0.04	99	0.2		450
14			137	0.25		515
15	0.051		192	0.5		2000
16			187	0.6		1320
17			210	0.7	0.13	2600
18			210	0.6	0.15	2600
19			220	0.7	0.1	2700
19a	<0.05					6600
20			179	0.6	1.67	1560
21	0.142				0.12	3550
22					<0.05	1120
23	<0.05					1080

,69

Sediments - Fall Survey (Continued)

SITE	Mn	Co	Cu	Fe	Pb	Cr	Ni	As 1
/^g/g	Mg/g	Mg/g	/^g/g	Mg/g	Mg/g	Mg/g	Mg/g 1
5	850	15	31	38000	38	50	38
6	680	12.5	34	32000	36	43	34
7	570	12	72	29000	73	46	• 37	5
8	630	12	94	28000	47	49	41	5
9	615	13.3	109.5	35000	93.5	188.5	131	5
10	1210	38	168	118000	87	670	390	11
lOa	810	16.5	43	52000	38	149	98
11	740	18.5	73	53000	63	250	166	4
12	730	23	105	70000	91	460	270	10
13	980	17	52	60000	23	300	179	6
14	995	19	53.5	59000	28.5	385	230	6.5
15	940	18	66	54000	48	340	177	8
16	990	19.5	71	63000	44	420	240	5
17	960	20	71	59000	49	440	230	7
18	840	19	74	53000	49	380	210	5
19	840	19	116	54000	53	350	192	7
20	820	22	138	47000	80	260	192	8

170

t. -. -.