Benthic Invertebrates of Fixed Sites in 


the Western Lake Michigan Drainages, 


Wisconsin and Michigan,1993–95 

By Bernard N. Lenz and S.J. Rheaume 

U.S. GEOLOGICAL SURVEY 

Water-Resources Investigations Report 95–4211–D 

National Water-Quality Assessment Program 

Western Lake Michigan Drainages 

Middleton, Wisconsin 

2000 
U.S. DEPARTMENT OF THE INTERIOR


BRUCE BABBITT, Secretary


U.S. GEOLOGICAL SURVEY


Charles G. Groat, Director


Any use of trade, product, or firm names is for descriptive purposes only and does not imply endorsement 

by the U.S. Government. 

For additional information write to: Copies of this report can be purchased from: 

District Chief U.S. Geological Survey 

U.S. Geological Survey Branch of Information Services 

8505 Research Way Box 25286 

Middleton, WI 53562-3586 Denver, CO 80225-0286 
CONTENTS 

Abstract ................................................................................................................................................................................. 1


Introduction........................................................................................................................................................................... 1


Western Lake Michigan Drainages Study Unit........................................................................................................... 2


Study design................................................................................................................................................................ 2


Purpose and scope....................................................................................................................................................... 2


Methods and materials .......................................................................................................................................................... 6


Collection of benthic invertebrates ............................................................................................................................. 6


Sampling gear and techniques..................................................................................................................................... 6


Sample preservation and identification....................................................................................................................... 6


Determination of benthic-invertebrate-community measures..................................................................................... 6


Benthic-invertebrate communities at fixed sites................................................................................................................... 6


Variability among fixed sites....................................................................................................................................... 8


Multiple-reach variability ........................................................................................................................................... 8


Multiple-year variability ............................................................................................................................................. 10


Reliability of benthic-invertebrate data as a water-quality indicator at fixed sites............................................................... 10


Factors affecting variability in invertebrate communities among fixed sites ............................................................. 10


Factors affecting multiple-reach variability in invertebrate communities .................................................................. 10


Factors affecting multiple-year variability in invertebrate communities.................................................................... 14


Summary ............................................................................................................................................................................... 14


References cited .................................................................................................................................................................... 15


FIGURES 

1.	 Map showing Western Lake Michigan Drainages study unit of the National Water Quality


Assessment Program............................................................................................................................................ 3


2.	 Map showing boundaries of relatively homogeneous units in the Western Lake Michigan Drainages


study unit and location of fixed sites ................................................................................................................... 4


3.	 Graph showing number of benthic-invertebrate families repeatedly identified during multiple-reach


sampling at selected fixed stream sites in the Western Lake Michigan Drainages study unit ............................ 11


4.	 Graph showing number of benthic-invertebrate families repeatedly identified during multiple-year 


sampling at selected fixed stream sites in the Western Lake Michigan Drainages study unit ............................ 11


5.	 Comparison diagram of benthic-invertebrate measures, habitat, and chemical water quality at selected


fixed stream sites in the Western Lake Michigan Drainages study unit.............................................................. 13


TABLES 

1. Selected information for the fixed sites in the Western Lake Michigan Drainages study unit ................................ 5


2. Breakdown of the number of families identified in benthic-invertebrate samples at fixed sites in the 

Western Lake Michigan Drainages study unit, 1993–95..................................................................................... 7


3.	 Summary statistics of benthic-invertebrate measures at 11 fixed sites in the Western Lake Michigan 


Drainages study unit, 1995 .................................................................................................................................. 9


4.	 Multiple-reach summary statistics of benthic-invertebrate measures at three fixed sites in the Western Lake 


Michigan Drainages study unit, 1994.................................................................................................................. 9


5.	 Multiple-year summary statistics of benthic-invertebrate measures at eight fixed sites in the Western Lake 


Michigan Drainages study unit, 1993–95............................................................................................................ 12


6.	 Numbers and types of benthic invertebrates collected in samples from 11 fixed sites in the Western Lake 


Michigan Drainages study unit, 1993–95............................................................................................................ 18


7.	 Median values of selected water-chemistry characteristics of fixed sites in the Western Lake Michigan


Drainages study unit, 1993–95 ............................................................................................................................ 29


8. Select habitat characteristics of fixed sites in the Western Lake Michigan Drainages study unit, 1993–95............ 30


CONTENTS V 
CONVERSION FACTORS, VERTICAL DATUM, AND MISCELLANEOUS ABBREVIATIONS 

Multiply By To Obtain 

inch (in.) 2.54 centimeter (cm) 

feet (ft) 0.3048 meter (m) 

square mile (mi2) 2.59 square kilometer (km2) 

acre 0.4047 hectare 

cubic feet per second (cfs) 0.02832 cubic meter per second (m3/s) 

Sea level: In this report, “sea level” refers to the National Geodetic Vertical Datum of 1929 (NGVD of 1929)—a geodetic datum derived 

from a general adjustment of the first-order level nets of both the United States and Canada, formerly called Sea Level Datum of 1929. 

Abbreviated water-quality units: Chemical concentrations and water temperature are given in metric units. Chemical concentration is 

given in milligrams per liter (mg/L) or micrograms per liter (μg/L). Milligrams per liter is a unit expressing the concentration of chemical 

constituents in solution as weight (milligrams) of solute per unit volume (liter) of water. One thousand micrograms per liter is equivalent 

to one milligram per liter. For concentrations less than 7,000 mg/L, the numerical values expressed as mg/L and μg/L are the same as for 

concentrations in parts per million and parts per billion, respectively. 

MISCELLANEOUS ABBREVIATIONS 

DATCP Wisconsin Department of Agriculture, Trade, and Consumer Protection 

DL Detection limit 

DNR (Wisconsin) Department of Natural Resources 

GLEAS Great Lakes Environmental Assessment Section 

GRN Groundwater Retrieval Network 

GIS Geographic Information Systems 

HBI Hilsenhoff Biotic Index 

IBI Index of Biological Integrity 

MCL Maximum Contaminant Level 

as N quantified as measured nitrogen 

NAWQA National Water-Quality Assessment Program 

NURE National Uranium Resources Evaluation 

PAH Polyaromatic hydrocarbons 

RASA Regional Aquifer-System Analysis 

SMCL Secondary Maximum Contaminant Level 

STAID USGS station identification number 

STORET Storage and Retrieval System 

USACE U.S. Army Corps of Engineers 

USEPA U.S. Environmental Protection Agency 

USGS U.S. Geological Survey 

VOC Volatile organic compound 

WATSTORE Water Storage and Retrieval 

WMIC Western Lake Michigan Drainages (NAWQA study area) 

VI CONVERSION FACTORS, VERTICAL DATUM, AND MISCELLANEOUS ABBREVIATIONS 
ACKNOWLEDGMENTS 

Technical Support 

Kevin D. Richards, Hydrologic Technician, U.S. Geological Survey, Middleton, Wis.


Barbara C. Scudder, Hydrologist, U.S. Geological Survey, Middleton, Wis.


Faith A. Fitzpatrick, Hydrologist, U.S. Geological Survey, Middleton, Wis.


Technical Reviewers 

Charles A. Peters, Supervisory Hydrologist, U.S. Geological Survey, Middleton, Wis.


Daniel J. Sullivan, Hydrologist, U.S. Geological Survey, Middleton, Wis.


Michael A. Miller, Biologist, Wisconsin Department of Natural Resources, Madison, Wis.


Michael C. Yurewicz, Supervisory Hydrologist, U.S. Geological Survey, Reston, Va.


Stephen K. Sorenson, Supervisory Hydrologist, U.S. Geological Survey, Reston, Va.


Editorial and Graphics 

Leah N. Hout, Editor, U.S. Geological Survey, Columbus, Ohio


Michael Eberle, Technical Publications Editor, U.S. Geological Survey, Columbus, Ohio


Michelle M. Greenwood, Chief, Publications Unit, U.S. Geological Survey, Middleton, Wis.


Heather E. Whitman, Physical Science Aid, U.S. Geological Survey, Middleton, Wis.


Susan Z. Jones, Editorial Assistant, U.S. Geological Survey, Middleton, Wis.


Karen A. Lonsdorf, Publication Graphics Specialist, U.S. Geological Survey, Middleton, Wis.


Approving Official 

Chester Zenone, Reports Improvement Advisor, U.S. Geological Survey, Reston, Va. 

ACKNOWLEDGMENTS VII 
Benthic Invertebrates of Fixed Sites in the Western Lake 

Michigan Drainages, Wisconsin and Michigan, 1993–95 

By Bernard N. Lenz and S.J. Rheaume 

Abstract 

This report describes the variability in 

family-level benthic-invertebrate population data 

and the reliability of the data as a water-quality 

indicator for 11 fixed surface-water sites in the 

Western Lake Michigan Drainages study area of 

the National Water-Quality Assessment Program. 

Benthic-invertebrate-community measures were 

computed for the following: number of individuals, 

Hilsenhoff’s Family-Level Biotic Index, number 

and percent EPT (Ephemeroptera, Plecoptera, and 

Tricoptera), Margalef’s Diversity Index, and mean 

tolerance value. Relations between these measures 

and environmental setting, habitat, and of chemical 

water quality are examined. 

Benthic-invertebrate communities varied 

greatly among fixed sites and within individual 

streams among multiple-reach and multiple-year 

sampling. The variations between multiple reaches 

and years were sometimes larger than those found 

between different fixed sites. Factors affecting 

benthic invertebrates included both habitat and 

chemical quality. Generally, fixed-site streams with 

the highest diversity, greatest number of benthic 

invertebrates, and those at which community measures indicated the best water quality also had the 

best habitat and chemical quality. 

Variations among reaches are most likely 

related to differences in habitat. Variations among 

years are most likely related to climatic changes, 

which create variations in flow and/or chemical 

quality. The variability in the data analyzed in this 

study shows how benthic invertebrates are affected 

by differences in both habitat and water quality, 

making them useful indicators of stream health; 

however, a single benthic-invertebrate sample 

alone cannot be relied upon to accurately describe 

water quality of the streams in this study. Benthicinvertebrate data contributed valuable information 

on the biological health of the 11 fixed sites when 

used as one of several data sources for assessing 

water quality. 

INTRODUCTION 

In 1991, the U.S. Geological Survey (USGS) began 

full-scale implementation ofthe National Water-Quality 

Assessment (NAWQA) Program. The objectives of the 

NAWQA Program are to (1) describe current waterquality conditions for a large part of the Nation’s freshwater streams, rivers, and aquifers, (2) describe trends 

in water quality over time, and (3) improve understanding of the primary natural and human factors that affect 

water-quality conditions (Gilliom and others, 1995; 

Hirsch and others, 1988). This information is useful for 

planning future management actions and examining 

their likely consequences. More than 50 study areas 

have begun activities on a staggered time scale. The 

Western Lake Michigan Drainages (WMIC) was 

selected as one of the 20 study areas in which data 

collection and analysis began in 1991. 

One of the major goals of the NAWQA program is 

to develop a better understanding of the interaction 

among physical, chemical, and biological characteristics of streams in selected environmental settings 

(Gurtz, 1994). Ecological studies are included in the 

NAWQA program to provide data on biological communities that contribute to the understanding of this 

interaction. Aspects of the NAWQA ecological studies 

include (1) understanding how biological communities 

and stream habitat differ among selected environmental 

settings, (2) identifying physical and chemical characteristics that influence biological communities, 

(3) understanding how spatial scales affect relations 

between physical, chemical, and biological characteristics, and (4) understanding how biological communities 

affect physical and chemical characteristics (Gurtz, 

1994). Stream-habitat characteristics, collected at a 

variety of spatial scales, are useful in expanding the 

Abstract 1 
understanding of how physical, chemical, and biological characteristics interact. 

Western Lake Michigan Drainages Study Area 

The Western Lake Michigan Drainages study area 

(fig. 1) encompasses 51,541 km2 of eastern Wisconsin 

and the Upper Peninsula of Michigan. Ten major rivers 

drain the study area: the Escanaba and Ford Rivers in 

Michigan; the Menominee River, which partially 

defines the state boundary between Wisconsin and 

Michigan; the Peshtigo and Oconto Rivers in northeastern Wisconsin; the Fox/Wolf River complex in eastcentral Wisconsin, which drains into Green Bay; and the 

Manitowoc, Sheboygan, and Milwaukee Rivers, which 

drain the southeastern part of the study area. 

The overall population in the study area is 

2,435,000 (U.S. Bureau of Census, 1991). The major 

cities and their populations are Milwaukee, 628,000; 

Green Bay, 96,000; Racine, 84,000; Kenosha, 80,000; 

and Appleton, 66,000. Urban land use accounts for less 

than 4 percent of the study area. Agriculture makes up 

37 percent of the land use in the basin and is devoted 

almost exclusively to cropland and pasture for dairy 

production. About 40 percent of the study area is forested; most forested areas are in the northwest part of 

the study area. Wetlands account for 15 percent of the 

land use in the study area. Lake Winnebago, a 55,442­

hectare lake in the Fox River Basin, is a major surfacewater feature of the study area. 

Study Design 

The WMIC study area was subdivided into 28 environmental settings, called relatively homogeneous units 

(RHU’s), on the basis of bedrock geology, texture of 

surficial deposits, and land use/land cover which are 

believed to influence water quality. Eleven fixed stream 

sites (fig. 2) were established to represent status of and 

trends in water quality in the WMIC. Eight of the 11 

sites were chosen to represent the water quality of one 

specific RHU. These fixed sites are referred to as “indicator sites” because the water quality at these sites is 

assumed to be indicative of the average condition for 

the RHU in which the entire drainage basin for each site 

is located. The other three sites were chosen to represent 

a large proportion of the water leaving the WMIC study 

area (Robertson and Saad, 1995). These fixed sites are 

referred to as “integrator sites” because the drainage 

basin for each contains more than one RHU, thereby 

integrating the effects of several land uses, surficial 

deposits, or geology types. Three sites, two indicator 

and one integrator, were selected for frequent and extensive surface-water sampling and are referred to as 

“intensive” fixed sites. General descriptions and 

selected information on the environmental setting of the 

fixed sites is available in Sullivan and others (1995). 

Benthic-invertebrate samples were collected at 

multiple reaches and in multiple years at the 11 fixed 

sites as one part of multi-metric water-quality assessment at these sites. Benthic-invertebrate samples and 

additional data including streamflow, water chemistry, 

organic compounds and trace elements in streambed 

sediment and biological tissues, fish and algal communities, and stream habitat were collected at the 11 fixed 

sites from March 1993 through June 1995. Some 

selected information on the environmental setting of 

fixed sites can be found in table 1. 

This investigation discusses the variability of 

benthic-invertebrate populations in different streams, 

reaches, years, and environmental settings, and a general assessment of water quality based on benthic-invertebrate-community measures at each site. Additional 

biological investigations in this series of fixed-site studies focused on the interaction of water quality, stream 

habitat, fish populations, and algal communities (Fitzpatrick and Giddings, 1995; Sullivan and Peterson, 

1995). 

Purpose and Scope 

This report provides information on the spatial and 

temporal variability of benthic-invertebrate communities at 11 fixed stream sites in the WMIC study area. 

The distribution, relative abundance, and community 

structure of the benthic invertebrates of these streams 

are discussed on the basis of samples collected at specific stream reaches described by Sullivan and others 

(1995). Information provided for macroinvertebrate 

communities includes richness measures, enumeration, 

and biotic indices of these invertebrate populations. 

Effects of environmental setting, habitat, and water 

quality on benthic-invertebrate communities and the 

usefulness of the invertebrate communities as waterquality indicators is discussed. 

The benthic-invertebrate information included in 

this report represents only part of the biotic information 

2 Benthic Invertebrates of Fixed Sites in the Western Lake Michigan Drainages, Wisconsin and Michigan, 1993–95 
88° 

Source: Seaber and others, 1986. 

89° 

87° 

46° 

45° 

44° 

43° 

0 25 50 MILES 

0 25 50 KILOMETERS 

WISCONSIN 

MICHIGAN 

Basin boundary 

County boundary 

Streams 

EXPLANATION 

Sheboygan 

M

R

anitowoc R 

Lake Winnebago 

Lake Butte des Morts 

Lake 

Poygan 

Milwaukee

R 

Wolf R 

Oconto R 

Peshtigo R 

Menom nee R 

Ford R 

Escanaba R 

Fox R 

Wolf R 

Fox R 

Green Bay 

Milwaukee 

Racine 

Escanaba 

Appleton 

i

Figure 1. Western Lake Michigan Drainages study unit of the National Water-Quality Assessment Program. 

INTRODUCTION 3 
88° EXPLANATION

Relatively Homogeneous Unit (RHU) and number 

Characteristics listed for each RHU are bedrock, land use, and separated by commas. Abbreviations are as follows: Carb, caand/or metamorphic; Shle, shale; Snds, sandstone; Ag, agricu

Benthic Invertebrates of Fixed Sites in the Western Lake Michigan Drainages, Wisconsin and Michigan, 1993–95 04087000 040869415 040863075 04085109 04085139 04072050 04071795 04080798 04067500 04063700 04062085 43° 44° 45° 46° 89° 18 19 16 22 7 12 7 6 14 14 13 17 12 21 24 2 15 1 1 20 3 19 9 10 2 28 27 25 3 3 23 5 9 11 4 26 9 1 9 8 87° 0 25 50 MILES 

0 25 50 KILOMETERS 

1 Carb, Ag, clayey 2 Carb, Ag, loamy 3 Carb, Ag, sandy 4 Carb, Ag, sand and gravel 5 Carb, Ag/wet forest, sandy/

 sand and gravel 6 Carb, dry forest, loamy 7 Carb, wet forest, loamy 8 Carb, wet forest, sandy 9 Carb, urban, clayey 10 Carb, urban, sandy 11 Carb, urban, sand and gravel 12 Carb, Ag/wet forest, loamy 13 Carb, wet forest, sandy 14 Carb, wet forest, sandy/sand and gravel 15 IgMet, Ag, loamy/sand and gravel 

Type of site 

Indicator site Integrator site Intensive fixed site Integrator site and intensive fixed site 

16 IgMet, dry 17 IgMet, dry  and gravel 18 IgMet, dry 19 IgMet, dry  and gravel 20 IgMet, dry  sand and gra21 IgMet, wet 22 IgMet, wet  and gravel 23 Shle, Ag, c24 Snds, Ag, 25 Snds, Ag, 26 Snds, dry f and gravel 27 Snds, wet 28 Snds, wet 

Mixed areas Open water 

Figure 2. Boundaries of relatively homogeneous units (R

H

U’s) in the Western Lake Michigan Drainages study unit and location of fixed s

4 
Table 1. Selected information for the fixed sites in the Western Lake Michigan Drainages study unit 

[Mean discharge calculated through September 1994; USGS, U.S. Geological Survey; mi2, square miles; km2, square kilometers; ft3/s, cubic feet per second; m3/s, cubic m

measurement made; ft, feet; m, meters] 

Site name USGS 

number 

Latitudelongitude Drainage area (mi2 [km2]) Mean discharge (ft3/s [m3/s]) Stream type Mean width (ft [m]) Reach length (ft [m]) 

Peshekee River near Martins 

Landing, Mich. 

04062085 88°01’20" 

46°36’35" 

49.0 

[127] 

173 

[2.1] 

Meandering 39 

[12] 

745 

[227] 

Popple River near Fence, Wis. 04063700 88°27’50" 

45°45’50" 

139 

[360] 

119 

[3.4] 

Meandering 69 

[21] 

1,090 

[332] 

Menominee River at 

McAllister, Wis. 

04067500 87°39’40" 

45°19’20" 

3,930 

[10, 200] 

3,470 

[98.3] 

Meandering -- 110 

[360] 

Pensaukee River near Krakow, 

Wis. 

04071795 88°16’35" 

44°45’09" 

35.8 

[92.7] 

12 

[.34] 

Meandering 23 

[7] 

508 

[155] 

Duck Creek near Oneida, Wis. 04072050 88°13’08" 

44°27’57" 

95.5 

[247] 

253 

[1.5] 

Meandering 30 

[9] 

492 

[150] 

Tomorrow River near 

Nelsonville, Wis. 

04080798 89°20’16" 

44°31’28" 

44.0 

[114] 

31 

[.88] 

Meandering 30 

[9] 

469 

[143] 

East River near DePere, Wis. 04085109 88°04’47" 

44°23’12" 

47.0 

[122] 

360 

[1.7] 

Meandering 16 

[5] 

564 

[172] 

Fox River at Green Bay, Wis. 04085139 88°00’16" 

44°32’22" 

6,332 

[16,400] 

5,330 

[151] 

Channelized -- -- 

North Branch Milwaukee River 

near Random Lake, Wis. 

040863075 88°03’10" 

43°33’25" 

51.4 

[133] 

35 

[.99] 

Meandering 36 

[11] 

705 

[215] 

Lincoln Creek at 47th Street at 

Milwaukee, Wis. 

040869415 87°58’20" 

43°05’49" 

9.6 

[24.8] 

8.5 

[.24] 

Channelized 37 

[11] 

922 

[281] 

Milwaukee River at 

Milwaukee, Wis. 

04087000 87°54’32" 

43°06’00" 

696 

[1,800] 

431 

[12.2] 

Channelized -- -- 

1Mean discharge for station 04062085 was calculated from drainage-area ratio and discharge record from station 04062100 (66.5 mi2 drainage area). 2Mean discharge for station 04072050 was calculated from drainage-area ratio and discharge record from station 04072150 (108 mi2 drainage area). 3Mean discharge calculated from average of monthly mean discharge owing to missing record. 

INTRODUCTION 5 
collected at these streams in the WMIC study area of the 

NAWQA program. Other information collected to 

assess the water quality of these fixed stream sites 

includes environmental settings, habitat, water chemistry, and algal and fish community data and appear in 

additional reports in this series. 

METHODS AND MATERIALS 

Collection of Benthic Invertebrates 

Benthic invertebrates were collected from eight 

wadeable and three nonwadeable streams. The eight 

wadeable streams were sampled in the spring of 1993, 

1994, and 1995 for multiple-year comparisons with the 

same reaches being sampled each year at approximately 

the same time of year. In 1994, at three of these wadeable streams, samples were collected at three reaches to 

compare within-stream variation. The three nonwadeable streams were sampled at one reach in the spring of 

1995. Sample procedures and protocol remained the 

same throughout the study to allow for among-stream, 

-year, and -reach comparisons. 

Sampling Gear and Techniques 

Benthic-invertebrate samples were collected from 

habitat most likely to have the greatest variety and 

quantity of organisms, usually the largest two riffles in 

each stream reach. A riffle was considered to be the part 

of the stream where the water flows swiftly over completely or partially submerged coarse substrate that produce surface agitation. Samples were collected from 

locations within the riffle where the greatest number 

and diversity of invertebrates in the reach were most 

likely to be found, as inferred by substrate, water depth, 

flow, and canopy cover. Sample locations generally had 

an open canopy, gravel or cobble substrate, the highest 

flow velocities in the riffle, and water depth sufficient to 

remain submerged during low flows. 

Samples were collected according to the NAWQA 

protocol as defined by Cuffney and others (1993a,b). 

Data from 10 of the 11 streams in this report came from 

kick samples collected by use of a modified Slack sampler (425-μm mesh). One stream-reach sample consisted of a composite of six kick samples—three each 

collected at an upstream and downstream riffle in the 

same reach—which were processed and identified as 

one sample. Distances between kick samples in the 

same riffle were rarely greater than 5 m. The sample 

area for each kick sample was 0.5 m by 0.5 m (depth 

0.1 m). According to protocol, the 1995 Fox River sample was collected by means of artificial substrate (rock 

baskets) owing to the lack of natural coarse-grain substrate and snags at this nonwadeable site. 

Sample Preservation and Identification 

Samples were processed in the field in accordance 

with the NAWQA protocol. Composite samples were 

reduced in the field by swirling and sieving (425-μm 

mesh sieve) until sample volumes were less than 

750 mL. Samples were preserved in the field in 10 percent buffered formalin, and within 3 days they were 

drained and refilled with 70 percent ethanol and stored 

until they could be shipped to the USGS laboratory for 

identification. Benthic-invertebrate enumeration and 

taxonomic identifications were done by the USGS 

National Water Quality Laboratory, Biological Unit, at 

Arvada, Colo., using methods described by Cuffney and 

others (1993b). All benthic invertebrates collected were 

processed. 

Determination of Benthic-InvertebrateCommunity Measures 

Benthic-invertebrate measures were calculated by 

use of a program created at the University of Wisconsin–Stevens Point (http://www.uwsp.edu/acad/cnr/biomonitoring/index3.htm). A detailed accounting of the 

calculation of these measures can be found in Rheaume 

and others (1996). Only measures that use taxonomic 

identifications of family level or higher are discussed in 

this report because much of the taxonomic data for this 

report is identified only to the family level. Data on 

community structure of aquatic arthropods collected 

from the 11 streams are summarized in tables 2–5. 

BENTHIC-INVERTEBRATE COMMUNITIES 

AT FIXED SITES 

The invertebrates collected at each of the 11 fixedsite streams were identified to the lowest taxonomic 

level possible (table 6, at back of report). Most major 

aquatic invertebrate taxa common to Wisconsin were 

represented in the 11 fixed-site stream samples; 

6 Benthic Invertebrates of Fixed Sites in the Western Lake Michigan Drainages, Wisconsin and Michigan, 1993–95 
Table 2. Breakdown of the number of families identified in benthic-invertebrate samples at fixed sites in the Western Lake 

Michigan Drainages study unit, 1993–95 

Reach A: Multiple­ 1994: Multiple- Multiple-year and 

Stream YearReach 

Found

 in individual 

Sample 

year samples reach samples reach samples 

Found in 

each of 

3 years 

Found 

in 

any year 

Found in 

each of 

3 reaches 

Found in 

any reach

 Found in 

any year in 

any reach 

Peshekee River 93-A 24 

94-A 25 15 33

95-A 24 

Popple River 93-A 24 

94-A 26 13 32

95-A 19 

Menominee River 95-A 13 

Pensaukee River 93-A 14 

94-A 14 8 18 

95-A 12 

Duck Creek 93-A 15 

8 18 8 17 22 

94-A 10 

94-B 15 

94-C 12 

95-A 11 

Tomorrow River 93-A 26 

15 27 16 24 30 

94-A 17 

94-B 23 

94-C 19 

95-A 18 

East River 93-A 9 

94-A 5 2 11 

95-A 4 

Fox River 95-A 12 

North Branch Milwaukee River 93-A 18 

12 23 16 23 24 

94-A 21 

94-B 18 

94-C 20 

95-A 13 

Lincoln Creek 93-A 2 

94-A 3 1 5

95-A 2 

Milwaukee River 95-A 5 

BENTHIC-INVERTEBRATE COMMUNITIES AT FIXED SITES 7 
54 families within 14 orders were identified. Trichoptera was the best-represented order (13 families), 

followed by Chironomidae (10 families), and 

Ephemeroptera (9 families). Chironomidae was the 

most abundant family in terms of numbers of individuals in the sample (46 percent of the total). 

Taxonomic population data were used to calculate 

common quantitative community measures. Variability 

observed among fixed sites, difference among multiplereach data at specific fixed sites, and difference in the 

data from three years of sampling were analyzed by 

comparing presence/absence data for benthic-invertebrate families and by statistical comparison of selected 

invertebrate measures using Kruskal-Wallis and Tukey 

tests (Iman and Conover, 1983). 

Invertebrate measures calculated for this study 

include count (per area) (Weber, 1973; Resh and 

Grodhaus, 1983), Hilsenhoff’s Family-Level Biotic 

Index (FBI) (Hilsenhoff, 1988), number and percent 

Ephemeroptera, Plecoptera, and Trichoptera (EPT) 

(Lenat, 1988), Margalef’s Diversity Index (MDI) 

(Margalef, 1969; Rosenberg and Resh, 1993), and 

average tolerance value (Lillie and Schlesser, 1994). 

Variability Among Fixed Sites 

The total number of families identified in any one 

sample ranged from 2 at Lincoln Creek in 1995 to 26 at 

Tomorrow River in 1993 and at Popple River in 1994. 

The total number of families identified at individual 

streams throughout the study (1993–95) ranged from 5 

at Lincoln Creek to 33 at Peshtigo River (table 2). No 

individual sample collected from the streams in this 

study contained every family found at that stream. Any 

one individual sample contained as few as 45 percent to 

as many as 88 percent of all families found at that 

stream during this study. 

Invertebrate measures consistently indicated 

Peshekee River, Popple River, Tomorrow River, and 

North Branch of Milwaukee River had the best water 

quality of the fixed-sites samples. FBI values, which are 

based on the benthic-invertebrate populations’ tolerance to organic pollution and the associated drop in dissolved oxygen, classify the water quality of these 

streams in a range from excellent (0.00–3.75) to very 

good (3.76–4.50) (Hilsenhoff, 1988). Ephemeroptera, 

Plecoptera, and Trichoptera (EPT), which are known to 

be intolerant to pollution, were present in high numbers 

at these sites. The high numbers of individuals and families collected, as well as higher MDI values, show 

strong overall abundance and diversity in the benthicinvertebrate populations of these streams. These 

streams drain both agricultural and forest land with 

loam, sand, or sand and gravel surficial deposits. 

Invertebrate measures for Lincoln Creek, East 

River, and Milwaukee River indicate the poorest water 

quality of sites in the study. FBI values classify the 

water quality in these streams as very poor (10.00–8.51) 

to fair (5.51–6.50). Few or no pollution-intolerant EPT 

taxa were found in these streams, total numbers of individuals were low, and diversity was low; all these measures indicate that the benthic invertebrates in these 

streams have been negatively impacted. These streams 

drain agricultural and urban land with clay surficial 

deposits (table 3). 

Multiple-Reach Variability 

Three streams were sampled at three different 

reaches in 1994. The variability in multiple-reach samples differed among rivers. Eight of the 17 (47 percent) 

families identified in samples from Duck Creek, 16 of 

the 24 (67 percent) families in samples from Tomorrow 

River, and 16 of the 23 (70 percent) families in samples 

from North Branch of the Milwaukee River were identified in every reach sampled. Invertebrate samples 

from a single reach contained as few as 59 percent to as 

many as 96 percent of the families identified in all samples from multiple reaches of the respective rivers 

(table 2, fig. 3). 

Between reach variability in calculated community 

measures was greatest for the Tomorrow River. The 

greatest variation was in number of individuals, which 

ranged from 180 in reach A to 7,861 in reach B. Each 

reach sampled in the Tomorrow River was dominated 

by a different family (table 4). 

Enumeration measures such as number of individuals, number of families, and number of EPT varied as 

much between samples from multiple reaches in the 

same stream as they did between samples from different 

streams. FBI and mean tolerance value were the only 

measures that varied less between reaches than between 

streams based on Kruskal-Wallis tests (p<0.05). Mean 

tolerance was the only measure with statistically significant differences between streams in Tukey tests making it the only benthic-invertebrate-community measure 

that indicated differences in water quality at the three 

fixed sites using multiple-reach sampling. 

8 Benthic Invertebrates of Fixed Sites in the Western Lake Michigan Drainages, Wisconsin and Michigan, 1993–95 
Table 3. Summary statistics of benthic-invertebrate measures at 11 fixed sites in the Western Lake Michigan Drainages study unit, 1995 

[%, percent; MDI, Margalef’s Diversity Index; EPT, Ephemeroptera, Plecoptera, and Trichoptera; FBI, Hilsenhoff’s Family-Level Biotic Index] 

BENTHIC-INVERTEBRATE COMMUNITIES AT FIXED SITES 

Stream 

name 

Station 

Number RHU 

Number 

of 

individuals 

Number 

of 

families 

MDI 

Dominant family/ 

Percent dominant 

family 

Number 

of EPT 

Percent 

EPT FBI 

Peshekee River 04062085 16 3,631 24 2.67 Simuliidae/47% 1,289 35 4.46 Popple River 04063700 22 4,839 19 1.11 Chironomidae/84% 697 14 3.52 Menominee River 04067500 -- 4,939 13 1.94 Chironomidae/45% 164 3 5.56 Pensaukee River 04071795 2 24,955 12 .94 Chironomidae/62% 530 2 5.73 Duck Creek 04072050 1 4,307 11 1.41 Chironomidae/68% 968 22 4.01 Tomorrow River 04080798 20 5,757 18 1.86 Chironomidae/65% 1,099 19 3.02 East River 04085109 23 2,260 4 .30 Chironomidae/96% 33 1 10.00 Fox River 04085139 -- 19,970 12 .51 Chironomidae/93% 552 3 5.24 North Branch of 040863075 3 4,282 13 1.95 Chironomidae/53% 1,519 35 1.89 

Milwaukee River 

Lincoln Creek 040869415 9 2,336 2 .76 Chironomidae/78% 0 0 6.00 Milwaukee River 04087000 -- 1,498 5 1.15 Chironomidae/69% 32 2 4.22 

Table 4. Multiple-reach summary statistics of benthic-invertebrate measures at three fixed sites in the Western Lake Michigan Drainages [%, percent; MDI, Margalef’s Diversity Index; EPT, Ephemeroptera, Plecoptera, and Trichoptera; FBI, Hilsenhoff’s Family-Level Biotic Index] 

Stream 

name 

Station 

Number Reach 

Number 

of 

individuals 

Number 

of 

families 

MDI 

Dominant family/ 

Percent dominant 

family 

Number 

of EPT 

Percent 

EPT 

A 180 17 3.52 Hydropsychidae/29% 128 71 

Tomorrow River 04080798 B 7,861 23 3.30 Elmidae/25% 2,146 27 

C 6,535 19 2.62 Chironomidae/42% 1,589 24 

A 3,475 10 2.04 Chironomidae/43% 1,068 31 

Duck Creek 04072050 B 2,311 15 2.76 Chironomidae/39% 594 26 

C 1,703 12 1.81 Chironomidae/56% 388 23 

A 4,885 21 2.79 Chironomidae/41% 2,026 41 

North Branch of 

Milwaukee River 040863075 B 3,393 18 1.93 Chironomidae/62% 781 23 

C 5,926 20 1.66 Chironomidae/72% 1,066 18 

9 
Multiple-Year Variability 

Benthic-invertebrate collections were made at 

eight wadeable fixed sites during three consecutive 

years at approximately the same date each year. The 

number and types of families collected from a site 

tended to vary from year to year. At a given site, a single 

yearly sample contained as few as 36 percent and as 

many as 96 percent of all the families identified in all 

samples at that site. The consistency at which families 

were identified in samples also varied. Two of the 

eleven (18 percent) families in samples from East River 

were identified all three years while 15 of the 27 

(55 percent) families in samples from Tomorrow River 

were identified all three years. Other families were 

identified in only one or two of the years (table 2, 

fig. 4). 

No one fixed site had significantly greater multiple-year variations in community measures than 

another. The benthic-invertebrate measures for number 

of individuals, number of families, and FBI value show 

statistically significant differences between sites based 

on Kruskal-Wallis tests (p<0.05). Additional analysis 

with Tukey tests show these differences to be statistically significant only between some of the fixed sites. 

The sites with significant differences also had the greatest difference in chemical water quality and habitat. 

Kruskal-Wallis testsshow variation in the values of EPT 

enumeration, EPT percent, and MDI are as great 

between years as between sites (p>0.05). Tomorrow 

River was the only stream dominated by a different 

family each year (table 5). 

RELIABILITY OF BENTHICINVERTEBRATE DATA AS A WATERQUALITY INDICATOR AT FIXED SITES 

The variability of the invertebrate measures, along 

with taxa presence, distribution, and abundance are discussed in the following paragraphs with reference to 

how they were affected by environmental setting, habitat, and chemical water quality. Chemical water-quality 

and habitat data for fixed sites were taken from Sullivan 

and others (1995) (table 7, at back of report) and from 

Fitzpatrick and Giddings (1995) (table 8, at back of 

report). Mean benthic-invertebrate measures were compared to median habitat, environmental setting factors, 

and chemical water-quality data collected at fixed sites 

between 1993 and 1995 (fig. 5). Quartiles were calculated for non-categorical data. Streams where invertebrate measures indicate the best water quality also 

tended to have the best chemical water quality and 

habitat. 

Factors Affecting Variability in Invertebrate 

Communities Among Fixed Sites 

Variability in benthic-invertebrate populations at 

fixed sites can be influenced by differences in chemical 

water quality, available habitat, and flow variability. 

Variations in sample collection method or analysis precision can also cause variations in the data. 

The fixed-site streams where benthic-invertebrate 

measures indicated the best water quality were Popple, 

Peshekee, and Tomorrow Rivers. These streams have 

been rated excellent by overall Great Lakes Environmental Assessment Section (GLEAS) habitat scores, 

(Michigan Department of Natural Resources, 1991) had 

low erodability and embeddedness scores, and all maintain consistent year-round base flows. These three 

streams drain mainly forested land; however, Tomorrow 

River also drains a considerable amount of agricultural 

land, mostly in parts of the basin away from the river. 

These three streams have the lowest average phosphorus, nitrite plus nitrate, and ammonia concentrations of 

the fixed sites (tables 7 and 8). 

The fixed-site streams where benthic-invertebrate 

measures indicated the poorest water quality were Lincoln Creek and East River. These streams have been 

rated fair by GLEAS habitat scores and are more erodible and embedded than other fixed-site streams. Both 

basins have clay surficial deposits and highly variable 

flow regimes that include periods of extremely low 

flow. These streams also had the highest average specific conductance and ammonia concentration of the 

fixed sites (tables 7 and 8). 

Factors Affecting Multiple-Reach Variability in 

Invertebrate Communities 

Although many of the same common benthicinvertebrate taxa were found in all three reaches of a 

particular river, taxa number and (or) type of taxa collected differed among reaches at all three streams. Measures associated with invertebrate sensitivity to water 

quality, such as FBI, appear to be less variable than enumeration measures for multiple-reach sampling. Most 

taxa in the stream, regardless of family, had similar 

10 Benthic Invertebrates of Fixed Sites in the Western Lake Michigan Drainages, Wisconsin and Michigan, 1993–95 
35 

30 

25 EXPLANATION

Duck Creek Tomorrow River North Branch Milwaukee River 

0 

5 

10 

15 

20

NUMBER OF FAMILIES

Number of families found in 

only one of the three reaches 

Number of families found in 

two of the three reaches 

Number of families found in 

all three reaches 

Figure 3. Number of benthic-invertebrate families repeatedly identified during multiple-reach sampling at selected fixed 

stream sites in the Western Lake Michigan Drainages study unit. 

0 

5 

10 

15 

20 

25 

30 

NUMBER OF FAMILIES

Number of families found in 

only one of the three years 

Number of families found in 

two of the three years 

Number of families found in 

all three years 

EXPLANATION 

Duck Tomorrow North Lincoln East Pensaukee Peshekee Popple 

Creek River Branch Creek River River River River 

Milwaukee 

River 

Figure 4. Number of benthic-invertebrate families repeatedly identified during multiple-year sampling at selected fixed 

stream sites in the Western Lake Michigan Drainages study unit. 

RELIABILITY OF BENTHIC-INVERTEBRATE DATA AS A WATER-QUALITY INDICATOR AT FIXED SITES 11 
Table 5. Multiple-year summary statistics of benthic-invertebrate measures at eight fixed sites in the Western Lake Michigan 

Drainages study unit, 1993–95 

[%, percent; MDI, Margalef’s Diversity Index; EPT, Ephemeroptera, Plecoptera, and Trichoptera; FBI, Hilsenhoff’s Family-Level Biotic Index] 

Stream 

name 

Station 

Number Year 

Number 

of 

individuals 

Number 

of 

families 

MDI 

Dominant family/ 

Percent dominant 

family 

Number 

of 

EPT 

Percent 

EPT 

FBI 

Mean 

tolerance 

value 

1993 5,941 24 2.81 Chironomidae/37% 2,222 37 3.90 2.50 

Peshekee River 04062085 1994 3,987 25 2.81 Simuliidae/40% 1,323 33 4.62 2.41 

1995 3,631 24 2.67 Simuliidae/47% 1,289 35 4.46 1.84 

1993 3,906 24 2.97 Chironomidae/41% 1,488 38 3.19 3.05 

Popple River 04063700 1994 7,177 26 2.02 Chironomidae/57% 2,924 41 3.53 2.65 

1995 4,839 19 1.11 Chironomidae/84% 697 14 3.52 3.46 

1993 6,473 14 1.55 Chironomidae/61% 738 11 6.62 6.00 

Pensaukee River 04062085 1994 13,362 14 2.06 Chironomidae/30% 3,939 29 3.92 5.57 

1995 24,955 12 .94 Chironomidae/62% 530 2 5.73 5.29 

1993 8,450 15 1.20 Chironomidae/79% 760 9 4.53 4.80 

Duck Creek 04072050 1994 3,475 10 2.04 Chironomidae/43% 1,068 31 5.36 4.67 

1995 4,307 11 1.41 Chironomidae/68% 968 22 4.01 5.00 

Tomorrow River 04080798 

1993 

1994 

3,752 

180 

26 

17 

2.66 

3.52 

Brachycentridae/28% 

Hydropsychidae/29% 

2,007 

128 

53 

71 

2.05 

2.82 

3.94 

2.64 

1995 5,757 18 1.86 Chironomidae/65% 1,099 19 3.02 3.29 

North Branch of 

Milwaukee 

River 

040863075 

1993 

1994 

1995 

1,659 

4,885 

4,282 

18 

21 

13 

1.73 

2.79 

1.95 

Chironomidae/70% 

Chironomidae/41% 

Chironomidae/53% 

196 

2,026 

1519 

12 

41 

35 

3.70 

3.48 

1.89 

4.00 

4.50 

4.31 

East River 04085109 

1993 

1994 

450 

4,885 

9 

21 

1.14 

2.79 

Chironomidae/82% 

Chironomidae/41% 

17 

2,026 

4 

41 

5.00 

3.48 

6.00 

4.50 

1995 2,260 4 .30 Chironomidae/96% 33 1 10.00 10.00 

1993 96 2 .25 Chironomidae/96% 4 4 4.00 5.00 

Lincoln Creek 040869415 1994 

1995 

776 

2,336 

3 

2 

1.78 

.76 

Chironomidae/51% 

Chironomidae/78% 

256 

0 

33 

0 

3.67 

6.00 

6.00 

6.00 

12 Benthic Invertebrates of Fixed Sites in the Western Lake Michigan Drainages, Wisconsin and Michigan, 1993–95 
 Hilsenhoff (family-level) Biotic Index categories in Hilsenhoff, 1988 

2 GLEAS categories in Michigan Department of Natural Resources, 1991 

EXPLANATION 

Abbreviations Categories Quartiles 

Best EPT Number of Ephemeroptera, Plecoptera, Excellent 0–25th percentile and Trichoptera genera 

Good 26th–50th percentile 

GLEAS	 Michigan Great Lakes Environmental 

Assessment Section Procedure Fair 51st–75th percentile 

Ag Agricultural Poor 76th–100th percentile Worst


F Forest
 Very poor Missing data

Ur Urban Missing data 

Two-year, seven-day low flow of zero 

H	 Two-year flood greater than ten times 


annual mean flow 


L 

STREAM NAME 

Dominant Land Use

Flow 

BENTHIC 

INVERTEBRATE 

MEASURES 

HABITAT WATER QUALITY 

Hilsenhoff (familylevel) Biotic Index 1 Percent EPT

Margalef’s

Diversity Index

GLEAS 

2

Erodibility

Embeddedness

Conductance

Total Phosphorus

Nitrite + Nitrate

Ammonia 

INDICATOR SITES

Duck Creek 

N. Br. Milwaukee River 

Lincoln Creek 

East River 

Pensaukee River 

Popple River 

Menominee River 

Milwaukee River 

Fox River 

Peshekee River 

Tomorrow River 

F 

F 

Ag L 

Ag L, H 

Ag/F H 

Ag L, H 

Ag H 

Ur H 

INTEGRATOR

SITES 

Ag 

Ag 

Ag 

1

Figure 5. Comparison of benthic-invertebrate measures, habitat, and chemical water quality at selected fixed 

stream sites in the Western Lake Michigan Drainages study unit. 

RELIABILITY OF BENTHIC-INVERTEBRATE DATA AS A WATER-QUALITY INDICATOR AT FIXED SITES 13 
tolerances to increased concentrations of organic pollutants and the associated decrease in dissolved oxygen. 

Variations in benthic-invertebrate-community 

measures between reaches could be attributed to the 

preference of benthic invertebrates for certain habitat 

and flow characteristics. Numerous microhabitats are 

present in all streams. Some streams, such as the 

Tomorrow River, have highly varied types of substrate, 

vegetation, canopy cover, and flow within a single 

reach. Picking a representative sampling location that 

includes all microhabitats in a reach is difficult if not 

impossible. An effort was made to minimize variation 

by selecting a representative reach and by compositing 

six riffle samples from different locations in the reach. 

Although the type and number of benthic invertebrates collected from multiple reaches varied, the associated tolerance to organic pollution of those invertebrates that were collected tended to be fairly similar. 

This relation was observed in past studies as well (Lenz 

and Miller, 1995; Rheaume and others, 1996), an indication of the strength of these tolerance-based measures 

in predicting water quality at the fixed sites. 

The choice of sample location and the homogeneity 

of the stream can affect how representative a single 

benthic-invertebrate sample is of the overall population 

in the stream and result in variations between multiple 

samples. 

Factors Affecting Multiple-Year Variability in 

Invertebrate Communities 

Invertebrates were collected near the same date 

each spring to minimize variance associated with emergence and differences in instars (life stages between 

molts). Because different species of invertebrates 

emerge from the river as adults to mate and reproduce 

at different times, young instars are not present or are 

not identifiable at certain times. Hence, the population 

of the benthic-invertebrate community that can be collected and identified changes throughout the year. 

Yearly variations in temperature and streamflow 

can affect when invertebrates emerge and the success of 

individual species’ reproduction that year. Emergence 

dates may be a function of degree days and/or flow 

rather than calendar days (Hilsenhoff, 1988). An unusually warm, cold, wet, or dry spring may shift the emergence cycle of a river and cause variations in the 

invertebrate community sampled, even when collection 

occurred near the same calendar day each year. Weather 

patterns throughout the year can affect the survival rates 

of the adults and the instars. Dry conditions and resulting low flows can expose critical riffles, whereas a large 

rain event and resulting high flow can scour the channel 

and wash invertebrates out of riffles. The amount of surface-water runoff and the organic contaminants associated with it vary yearly and can have a significant effect 

on benthic-invertebrate populations in streams. 

Streams in this study had unusually high flows in 

1993 because of the unusually wet Midwestern summer. 

In contrast, parts of the Pensaukee River (mostly riffles) 

were dry in 1995 because dry weather conditions were 

compounded by newly constructed beaver dams 

upstream from the sampling reach. These and other 

variations in runoff, flow, and associated change in 

water quality likely caused much of the variability seen 

in multiple-year samples at the sites. 

SUMMARY 

Benthic invertebrates were one of several waterquality indicators for which data were collected as part 

of the USGS NAWQA program in the WMIC study 

area; other data collected include those on chemical 

water quality, stream habitat, and fish and algal communities. Benthic-invertebrate populations vary between 

streams, reaches on a given stream, years, and environmental settings, but can be a good indicator of a 

stream’s general health. 

Benthic-invertebrate samples were collected at 

eight wadeable fixed sites once a year for three years; at 

three of these sites, multiple-reach samples were collected. Three nonwadeable streams were sampled once 

in 1995. Most dominant aquatic invertebrates common 

to Wisconsin were represented in the 11 fixed-site 

stream samples; 54 families within 14 orders were identified. The results of the sampling were analyzed for 

variability among streams, reaches, and years. 

In all cases, sampling in multiple reaches or in multiple years resulted in more invertebrate families being 

identified at a given stream than would have been identified in a single sample, a single year, or a single reach. 

Any one benthic-invertebrate sample identified as many 

as 88 percent (North Branch Milwaukee River, Reach 

A, 1994) and as few as 45 percent (Duck Creek, Reach 

A, 1994) of all the families found in that river during 

this study. The percentage of families identified every 

year during multiple-year sampling ranged from 55 percent at Tomorrow River to 18 percent at East River. The 

percentage of families identified in every reach during 

14 Benthic Invertebrates of Fixed Sites in the Western Lake Michigan Drainages, Wisconsin and Michigan, 1993–95 
multiple-reach sampling ranged from 70 percent at the 

North Branch of the Milwaukee River to 47 percent at 

Duck Creek. 

Benthic-invertebrate communities and measures of 

these communities varied among fixed sites. Factors 

affecting benthic-invertebrate samples included habitat, 

chemical water quality, and flow variability. Generally, 

fixed-site streams containing the highest number of 

invertebrate families intolerant to organic pollution, and 

the highest invertebrate diversity were those fixed sites 

with the best habitat and chemical water quality. 

Benthic-invertebrate communities and community 

measures at individual streams also varied among 

reaches and years. Variations among multiple reaches 

and years were larger than those found between different fixed sites in some cases. Mean tolerance value was 

the only benthic-invertebrate-community measure that 

indicated statistically significant differences in water 

quality at the three fixed sites using multiple-reach sampling. Number of individuals, number of families and 

FBI value all indicate statistically significant differences in water quality only between some of the 

multiple-year sampling sites—those which also had 

the greatest difference in water quality and habitat. 

The values of EPT enumeration, EPT percent, and MDI 

varied as much between years as between sites during 

multiple-year sampling. 

The variationsin benthic-invertebrate communities 

found in this study show how benthic invertebrates are 

affected by changes in both habitat and chemical water 

quality. Variation among years can most likely be attributed to climatic changes causing variations in flow and 

(or) chemical water quality, whereas variation between 

reaches is likely due to habitat variations. Major differences between fixed sites with significantly different 

chemical water quality, habitat, or environmental setting can be distinguished by use of benthic-invertebrate 

data; however, a single benthic-invertebrate sample 

cannot, alone, be relied upon to accurately describe 

water quality at the streams in this study. Benthic-invertebrate data contributed valuable information on the 

biological health of the 11 fixed sites when used in conjunction with other data sets to assess overall water 

quality. 

REFERENCES CITED 

Cuffney, T.F., Gurtz, M.E., and Meador, M.R., 1993a, Methods for collecting benthic invertebrate samples as part of 

the National Water-Quality Assessment Program: U.S. 

Geological Survey Open-File Report 93–406, 66 p. 

____1993b, Guidelines for the processing and quality assurance of benthic invertebrate samples collected as part of 

the National Water-Quality Assessment Program: U.S. 

Geological Survey Open-File Report 93–407, 80 p. 

Fitzpatrick, F.A., and Giddings, E.M., 1995, Stream habitat 

characteristics of fixed sites in the Western Lake Michigan Drainages, Wisconsin and Michigan, 1993–95: U.S. 

Geological Survey Water-Resources Investigations 

Report 95–4211–B, 58 p. 

Gilliom, R.J., Alley, W.M., and Gurtz, M.E., 1995, Design of 

the National Water-Quality Assessment Program– 

Occurrence and distribution of water-quality conditions: 

U.S. Geological Survey Circular 1112, 33 p. 

Gurtz, M.E., 1994, Design of biological components of the 

National Water-Quality Assessment (NAWQA) Program, in Loeb, S.L., and Spacie, A., eds., Biological 

monitoring of aquatic systems: Boca Raton, Fla., Lewis 

Publishers, chap. 15, p. 323–354. 

Hilsenhoff, W.L., 1988, Rapid field assessment of organic 

pollution with a family-level biotic index: Journal of the 

North American Benthological Society, v. 7, p. 65–68. 

____1988, Seasonal correction factors for the biotic index: 

The Great Lakes Entomologist, v. 21, no. 1, p. 9–13. 

Hirsch, R.M., Alley, W.M., and Wilber, W.G., 1988, Concepts for a National Water-Quality Assessment Program: U.S. Geological Survey Circular 1021, 42 p. 

Iman, R.L., and Conover, W.J., 1983, A modern approach to 

statistics: New York, Jon Wiley and Sons, 497 p. 

Lenat, D.R., 1988, Water quality assessment of streams using 

a qualitative collection method for benthic macroinvertebrates: Journal of the North American Benthological 

Society 7, p. 222–233. 

Lenz, B.N., and Miller, M.A., 1996, Comparison of aquatic 

macroinvertebrate samples collected using different 

field methods: U.S. Geological Survey Fact Sheet 

96–216, 4 p. 

Lillie, R.A., and Schlesser, R.A., 1994, Extracting additional 

information from biotic index samples: Great Lakes 

Entomologist, v. 27, no. 3, p. 129–136. 

Margalef, R., 1969, Diversity and stability in ecological systems: Biology, v. 22, p 25–37. 

Michigan Department of Natural Resources, 1991, Qualitative biological and habitat survey protocols for wadable 

streams and rivers: Michigan Department od Natural 

Resources, Surface Water Quality Division, Great Lakes 

and Environmental Assessment Section, GLEAS Procedure 51, 40 p. 

Resh, V.H., and Grodhaus, G., 1983, Aquatic insects in urban 

environments, in Frankie, G.W., and Koehler, C.S., eds., 

Urban entomology–Interdisciplinary Perspectives: New 

York, Praeger Publications, p. 247–276. 

REFERENCES CITED 15 
Rheaume, S.J., Lenz, B.N., and Scudder, B.C., 1996, Benthic 

invertebrates of benchmark streams in agricultural areas 

of eastern Wisconsin-Western Lake Michigan Drainages: U.S. Geological Survey Water-Resources Investigations Report 96–4038–C, 39 p. 

Robertson, D.M., and Saad, D.A., 1995, Environmental factors used to subdivide the Western Lake Michigan 

Drainages into relatively homogeneous units for waterquality site selection: U.S. Geological Survey Fact Sheet 

FS–220–95, 4 p. 

____1996, Water-quality assessment of the Western Lake 

Michigan Drainages—Analysis of available data on 

nutrients and suspended sediment, water years 1971– 

1990: U.S. Geological Survey Water-Resources Investigations Report 96–4012, 166 p. 

Rosenberg, D.M., and Resh, V.H., eds., 1993, Freshwater 

biomonitoring and benthic macroinvertebrates: New 

York, Chapman and Hall, 488 p. 

Sullivan, D.J., Peterson, E.M., and Richards, K.D., 1995, 

Environmental setting of fixed sites in the Western Lake 

Michigan Drainages, Michigan and Wisconsin: U.S. 

Geological Survey Water-Resources Investigations 

Report 95–4211–A, 30 p. 

Sullivan, D.J. and Peterson, E.M., 1995, Fish communities of 

fixed sites in the Western Lake Michigan Drainages, 

Michigan and Wisconsin: U.S. Geological Survey 

Water-Resources Investigations Report 95–4211–C, 

23 p. 

U.S. Bureau of the Census, 1991, 1990 census of population 

and housing, summary population and housing characteristics, Wisconsin: U.S. Department of Commerce, 

1990 CPH–1–51, 370 p. 

U.S. Department of Agriculture, 1991, State soil geographic 

data base (STATSGO), data user’s guide: U.S. Department of Agriculture, Soil Conservation Service Miscellaneous Publication 1492, 88 p., scale 1:250,000. 

Weber, C.I., ed., 1973, Biological field and laboratory methods for measuring the quality of surface waters and 

effluents: Cincinnati, Ohio, U.S. Environmental Protection Agency, EPA–670/4–73–001. 

16 Benthic Invertebrates of Fixed Sites in the Western Lake Michigan Drainages, Wisconsin and Michigan, 1993–95 
TABLES 6–8


Tables 6–8 17 
Table 6. Numbers and types of benthic invertebrates collected in samples from 11 fixed site streams in the Western Lake Michigan Drainage

ORDER 

FAMILY 

Lincoln 

Milwaukee Fox Duck East 

Genus and Species 

1993

1994

1995

1995

1995

1993

1994A

1994B

1994C

1995

1993

1994

1995

1993

PLECOPTERA 2 756 128 192 8 33 

PERLIDAE PERLODIDAE 

Isoperla sp. 

COLLEMBOLA 512 EPHEMEROPTERA 3 16 1 

BAETIDAE 4 32 4 567 260 196 65 547 5 2 1

Acerpenna sp. 6 

CAENIDAE 276 

Caenis sp. 128 1 1 

HEPTAGENIIDAE 84 17 55 132 36 

Stenacron interpunctatum Stenonema sp. 1 S. femoratum 24 2 57 165 102 S. mediopunctatum 

POTAMANTHIDAE 

Anthopotamus sp. 2 

LEPTOPHLEBIIDAE 17 1 

ODONATA 

COENAGRIONIDAE 4 

TRICHOPTERA 4 13 

GLOSSOSOMATIDAE 

Protoptila sp. 10 

18 Benthic Invertebrates of Fixed Sites in the Western Lake Michigan Drainages, Wisconsin and Michigan, 1993–95 
Table 6. Numbers and types of benthic invertebrates collected in samples from 11 fixed site streams in the Western Lake Michigan Drainage

Continued 

ORDER 

FAMILY 

Lincoln 

Milwaukee Fox Duck East 

Genus and Species 

1993

1994

1995

1995

1995

1993

1994A

1994B

1994C

1995

1993

1994

1995

1993

HELICOPSYCHIDAE 

Helicopsyche sp. H. borealis 16 

HYDROPSYCHIDAE 32 2 8 4 4 7 

Cheumatopsyche sp. 3 2 107 17 60 32 1 Hydropsyche sp. 6 32 H. betteni 1 3 Ceratopsyche bronta C. morosa bifida C. morosa morosa 16 

HYDROPTILIDAE 128 1 16 27 

Hydroptila sp. 128 1 8 H. grandiosa Ochrotrichia sp. 16 

LEPTOCERIDAE 8 

Oecetis sp. 4 

LIMNEPHILIDAE 

Anabolia sp. 1 1 2 2 Pycnopsyche sp. 9 15 3 6 

PHILOPOTAMIDAE 

Chimarra sp. 128 1 Wormaldia sp. 1 16

Table 6 19 
20 Benthic Invertebrates of Fixed Sites in the Western Lake Michigan Drainages, Wisconsin and Michigan, 1993–95 Ta

ble 6. Numbers and types of benthic invertebrates collected in samples from 11 fixed site streams in the 

Western Lake Michigan 

Drainage

Continued 

ORDER 

FA

MILY 

Genus and Species 

Lincoln 

Milwaukee Fox Duck East 

1993

1994

1995

1995

1995

1993

1994A

1994B

1994C

1995

1993

1994

1995

1993

POLYC

E

NTROPODIDAE 8 1 

Polycentropus sp. Paranyctiophylax sp. 1 

PSYCHOMYIIDAE 32 

Psychomyia flavida 44 

UENOIDAE 

Neophylax sp. 22 

COLE

O

PTERA 

DRYOPIDAE 

Helichus striatus 1 

EL

MIDAE 

Ancyronyx sp. 32 8 70 157 33 138 Dubiraphia sp. 1 D. bivittata Macronychus glabratus Optioservus sp. 292 27 O. fastiditus 36 Stenel

mis sp. 182 4 76 48 

DYTISCIDAE 1 49 HALIPLIDAE 

Haliplus sp. 4 
Table 6. Numbers and types of benthic invertebrates collected in samples from 11 fixed site streams in the Western Lake Michigan Drainage

Continued 

ORDER 

FAMILY 

Lincoln 

Milwaukee Fox Duck East 

Genus and Species 

1993

1994

1995

1995

1995

1993

1994A

1994B

1994C

1995

1993

1994

1995

1993

DIPTERA 52 96 4 96 

CERATOPOGONIDAE 8 129 4 

Bezzia sp. 32 

CHIRONOMIDAE 92 392 1824 1034 18561 6645 1488 891 951 2920 369 586 2162 1158 2EMPIDIDAE 8 

Clinocera sp. 4 

Hemerodromia sp. 4 17 2 Rhamphomyia sp. 1 

PSYCHODIDAE 

Psychoda sp. 1 

SIMULIIDAE 298 816 465 17 3 4 128 50 TABANIDAE 1 TIPULIDAE 1 

Antocha sp. 1 

Tipula sp. 1 

AMPHIPODA 388 33 131 298 64 32 

GAMMARIDAE 

Gammarus sp. 455 3 1 

ISOPODA 392 1 1 31 1536 64 141 HETEROPTERA 2 8 

CORIXIDAE 20 

NEUROPTERA 

SISYRIDAE 

Climacia areolaris 48 

Table 6 21 
22 Benthic Invertebrates of Fixed Sites in the Western Lake Michigan Drainages, Wisconsin and Michigan, 1993–95 

Table 6. Numbers and types of benthic invertebrates collected in samples from 11 fixed site streams in the 

Western Lake Michigan Draina

Continued 

ORDER Pensaukee Tomorrow Popple Pesh

FA

MILY 

Genus Species 

1993

1994

1995

1993

1994 A

1994 B

1994C

1995

1993

1994

1995

1993

1994

PLECO

PTERA 10 64 32 5 

CHLOROPE

R

LIDAE 

Haploperla sp. 

L

EUC

T

RIDAE 114 

Leuctra sp. 64 6 

NEMOURIDAE 32 

Amphinemura sp. 64 Nemoura sp. 64 

PERLIDAE 169 739 4 4 128 14 56 

Acroneuria sp. 40 9 1 117 A. lycorias Paragnetina sp. 2 1 P. media 2 1 1 6 5 7 Agnetina sp. 1 A. capitata 1 

PERLODIDAE 

Isoperla sp. 2 1 1 10 6 5 I. cotta 

PT

E

RONARC

YIDAE 

Pteronarcys sp. 2 

EPHEMEROP

TERA 48 7 96 40 

B

AETI

D

AE 1 2561 513 59 4 72 128 297 782 325 337 

CAE

NIDAE 32 64 

Caenis sp. 48 32 
Table 6. Numbers and types of benthic invertebrates collected in samples from 11 fixed site streams in the Western Lake Michigan Draina

Continued 

ORDER Pensaukee Tomorrow Popple Pesh

FAMILY 

Genus Species 

1993

1994

1995

1993

1994 A

1994 B

1994C

1995

1993

1994

1995

1993

1994

EPHEMERELLIDAE 17 1 284 34 

Ephemerella sp. 68 2 21 51 Eurylophella sp. 69 

EPHEMERIDAE 64 

Ephemera sp. 19 2 Hexagenia sp. 2 

HEPTAGENIIDAE 16 16 17 164 228 2

Epeorus sp. 32 16 E. vitreus 56 Rhithrogena sp. Stenacron sp. 1 S. interpunctatum 8 1 1 Stenonema femoratum 3 6 2 S. vicarium 7 69 9 13 1 S. modestum 3 

LEPTOPHLEBIIDAE 81 195 273 

Paraleptophlebia sp. 1 6 3 

LEPTOHYPHIDAE 1 ISONYCHIIDAE 

Isonychia sp. 1 

ODONATA 32 

AESHNIDAE 

Boyeria sp. 1 1 1 

B. vinosa Cordulegaster sp. 1 

Table 6 23 
24 Benthic Invertebrates of Fixed Sites in the Western Lake Michigan Drainages, Wisconsin and Michigan, 1993–95 

Table 6. Numbers and types of benthic invertebrates collected in samples from 11 fixed site streams in the 

Western Lake Michigan Draina

Continued 

ORDER 

FA

MILY 

Genus Species 

Pensaukee Tomorrow Popple Pesh

1993

1994

1995

1993

1994 A

1994 B

1994C

1995

1993

1994

1995

1993

1994

GOMPHIDAE 1 1 21 

Hagenius brevistylus 1 Ophiogomphus sp. Stylogomphus albistylus Stylurus sp. 

TRICHOP

T

ERA 33 69 3 261 68 4 8 

BRACHYCENT

RIDAE 1595 9 385 768 32 

Brachycentrus a

mericanus 3 65 64 2 

Micrasema sp. 1 16 98 19 M. rusticum 8 

GLOSSOSOMATIDAE 

Glossosoma sp. 33 36 46 

Protoptila sp. 20 15 348 135 270 

HELICOPSYCHIDAE 

Helicopsyche borealis 1 2 2 

HYDROPSYCHIDAE 21 57 3 1 9 16 6 22 6 113 

Cheumatopsyche sp. 23 241 4 18 2 66 65 2 2 11 32 Hydropsyche sp. 66 74 5 1 H. betteni 2 8 2 1 

Ceratopsyche morosa bifida 83 1 66 4 78 10 261 C. morosa morosa 1 45 1C. slossonae 40 188 40 26 
Table 6. Numbers and types of benthic invertebrates collected in samples from 11 fixed site streams in the Western Lake Michigan Draina

Continued 

ORDER Pensaukee Tomorrow Popple Pesh

FAMILY 

Genus Species 

1993

1994

1995

1993

1994 A

1994 B

1994C

1995

1993

1994

1995

1993

1994

HYDROPTILIDAE 300 66 4 1 1 512 97 651 64 2 1

Hydroptila sp. 32 129 32 212 194 98 226 46 1Oxyethira rivicola 8 Stactobiella delira 16 

LEPTOCERIDAE 4 7 

Oecetis sp. 

Setodes sp. 16 76 

S. oligius 4 

LEPIDOSTOMATIDAE 

Lepidostoma sp. 8 67 24 32 16 

LIMNEPHILIDAE 1 1 8 

Anabolia sp. 1 5 2 Hydatophylax sp. Limnephilus sp. 1 Onocosmoecus sp. 1 O. unicolor 1 Pycnopsyche sp. 2 32 9 1 

ODONTOCERIDAE 

Psilotreta sp. 

P. indecisa 

PHILOPOTAMIDAE 

Chimarra sp. 1 92 1 444 3

POLYCENTROPODIDAE 32 

Neureclipsis sp. 

Table 6 25 
26 Benthic Invertebrates of Fixed Sites in the Western Lake Michigan Drainages, Wisconsin and Michigan, 1993–95 

Table 6. Numbers and types of benthic invertebrates collected in samples from 11 fixed site streams in the 

Western Lake Michigan Draina

Continued 

ORDER 

FA

MILY 

Genus Species 

Pensaukee Tomorrow Popple Pesh

1993

1994

1995

1993

1994 A

1994 B

1994C

1995

1993

1994

1995

1993

1994

PSYCHOMYIIDAE 64 

Lype sp. 1 

Lype diversa 4 Psychomyia sp. 32 P. flavida 32 4 133 1 258 33 32 

UENOIDAE 1 

Neophylax sp. 22 19 28 13 3 4 2 

MEGALO

P

TERA 

CORYDALIDAE 

Nigronia sp. 8 1 6 N. serricornis 8 4 5 2 1 

SIALIDAE 

Sialis sp. 4 

LE

PIDOP

T

E

RA 

PYRALIDAE 8 

COLEOPTERA 

DRYOPIDAE 

Helichus striatus 2 

E

LMIDAE 

Ancyronyx sp. 68 147 513 317 6 1961 1101 142 482 99 32 262 1Dubiraphia sp. 1 16 Optioservus sp. 4 32 O. fastiditus 33 4 8 64 O. trivittatus 4 64 Stenel

mis sp. 17 15 16 
Table 6. Numbers and types of benthic invertebrates collected in samples from 11 fixed site streams in the Western Lake Michigan Draina

Continued 

ORDER Pensaukee Tomorrow Popple Pesh

FAMILY 

Genus Species 

1993

1994

1995

1993

1994 A

1994 B

1994C

1995

1993

1994

1995

1993

1994

DYTISCIDAE 65 2 HALIPLIDAE 1 

DIPTERA 128 1 

ATHERICIDAE 

Atherix sp. 1 1 1 42 A. variegata 1 

BLEPHARICERIDAE 

Blepharicera sp. 

CERATOPOGONIDAE 512 4 1 CHIRONOMIDAE 3920 4075 15373 892 27 1911 2739 3719 1610 4065 4044 2210 7EMPIDIDAE 17 17 70 1 5 39 

Hemerodromia sp. 24 65 19 32 58 Chelifera sp. 40 64 128 1 

SIMULIIDAE 51 657 6412 8 2 321 257 66 37 64 992 16TABANIDAE 4 

Chrysops sp. 3 

TIPULIDAE 28 4 65 2 1 

Anocata sp. 257 4 782 324 5 52 1 36 Hexatoma sp. 1 1 Tipula sp. 1 1 1 

TANYTARSINI 

Stempellina sp. 

Table 6 27 
28 Benthic Invertebrates of Fixed Sites in the Western Lake Michigan Drainages, Wisconsin and Michigan, 1993–95 

Table 6. Numbers and types of benthic invertebrates collected in samples from 11 fixed site streams in the 

Western Lake Michigan Draina

Continued 

ORDER Pensaukee Tomorrow Popple Pesh

FA

MILY 

Genus Species 

1993

1994

1995

1993

1994 A

1994 B

1994C

1995

1993

1994

1995

1993

1994

AMPHIPODA 87 2560 3 125 517 322 640 

GAMMARIDAE 

Gammarus sp. 2 94 24 1 2 3 16 

ISOP

ODA 13 1728 1551 

ASELLIDA

E 1592 64 

NEUR

O

PTERA 

SISYRIDAE 

Climacia sp. 1 

COLLEMBO

LA 4 
Table 7. Median values of selected water-chemistry characteristics of fixed sites in the Western Lake Michigan Drainages study unit, 1993

[μs/cm, microsiemens per centimeter at 25 degrees Celsius; oC, degrees Celsius; mg/L, milligrams per liter, N, nitrogen; P, phosphorus; CaCO3, calcium carbonate] 

Indicator sites 

Peshekee River near


Martins Landing,


Mich.


Popple River near 
 Fence, Wis.


Pensaukee River 


near Krakow, Wis.


Duck Creek near 


Oneida, Wis.


Tomorrow River near 


Nelsonville, Wis.


East River near


DePere, Wis.


North Branch Milwaukee River near 

Random Lake, Wis.

Lincoln Creek at 47th 
 Street at Milwaukee,


Wis.


Menominee River at 


McAllister, Wis.


Specific conductance 38 148 628 733 381 770 684 768 248 

(μS/cm at 25°C) 

pH (standard units) 7.0 7.6 8.0 8.1 8.0 8.0 8.3 8.0 8.0 Ammonium, dissolved, .04 .03 .065 .085 .03 .10 .07 .08 .02 

mg/L as N 

Nitrate plus nitrite, .073 .057 .78 .84 1.8 1.0 1.6 .54 .096 

dissolved, mg/L as N 

Phosphorus, total, .008 .02 .16 .15 .02 .24 .14 .045 .02 

mg/L as P 

Phosphorus, dissolved, .007 .008 .095 .10 .005 .18 .085 .025 .01 

mg/L as P 

Alkalinity, mg/L as 16 68 280 260 190 270 310 160 110 

CaCO3 

Table 7 29 
30 Benthic Invertebrates of Fixed Sites in the Western Lake Michigan Drainages, Wisconsin and Michigan, 1993–95 

Table 8. Selected habitat characteristics of fixed sites in the Western Lake Michigan Drainages study unit, 1993–95 [--, missing data; km2, square kilometers; 

mi

2, square miles; k

m, kilometers; m, meters; m3

/s, cubic meters per second; ft

3/s, cubic feet per second] 

Indicator sites 

Peshekee River near 

Martins Landing, Mich.

Popple River near 

Fence, Wis.

Pensaukee River near 

Krakow, Wis.

Duck Creek near 

Oneida, Wis.

Tomorrow River near 

Nelsonville, Wis.

East River near DePere,

Wis.

North Branch Milwaukee 

River near Random 

Lake, Wis.

Lincoln Creek at 47th 

Street at Milwaukee,

Wis.

Menominee River at 

McAllister, Wis.

USGS site number Relatively homogeneous unit1 Drainage area (km2, [mi2

]) 

Great Lakes Environ

mental 

Assessment Score 

Erodibility factor2 

E

mbeddedness 

2-year flood (

m3/s, [ft

3/s]) 

Annual mean flow (m3/s, [ft3/s]) 

2-yr 7-day low flow (

m3/s [ft3/s]) 

Dominant Land Use 

04062085 

16 

127 

[49.0] 

102 

.13 

3.4 

2.4 

[85] 

Forest 

--

--

04063700 

22 

360 

[139] 

84 

.14 

2.6 

19 

[680] 

3.1 

[110] 

.86 

[30] 

Forest/ 

Wetland 

04071795 

2 

92.7 

[35.8] 

73 

.26 

2.5 

13 

[450] 

.28 

[10] 

0 

[0] 

Agriculture 

04072050 04080798 04085109 

1 20 23 

247 

[95.5] 

114 

[44.0] 

122 

[47.0] 

66 86 45 

.27 .16 .29 

2.8 1.8 0.5 

31 

[1,100] 

10 

[360] 

35 

[1,300] 

1.8 

[64] 

.82 

[29] 

1.2 

[41] 

0 

[0] 

.49 

[17] 

0 

[0] 

Agriculture 

Agriculture/ 

Forest 

Agriculture 

040863095 

3 

133 

[51.4] 

67 

.28 

1.5 

18 

[650] 

.88 

[31] 

.11 

[4.0] 

Agriculture 

040869415 

9 

24.8 

[9.56] 

37 

.33 

1.4 

7 

[250] 

.24 

[8.5] 

.07 

[2.3] 

Urban 

-

040675

10,20

[3,930

.24 

2.4 

430 

[15,00

79 

[2,800

41 

[1,400

Fores

--

--

1Relatively homogeneous units are described in Robertson and Saad (1995a).
2Percentage of erodibility factor was obtained from U.S. Department of Agriculture (1991).