J. Great Lakes Res. 30(1):58–69
Internat. Assoc. Great Lakes Res., 2004
The Ecological Patterns of Benthic Invertebrates in a
Great Lakes Coastal Wetland
Richard A. MacKenzie*, Jerry L. Kaster, and J. Val Klump
Center for Great Lakes Studies
University of Wisconsin W.A.T.E.R. Institute
600 E. Greenfield Ave.
Milwaukee, Wisconsin 53204
ABSTRACT. Benthic macroinvertebrates were sampled in the summer of 1997 using a standard D
frame kick net along a transect across the Peshtigo wetland, a river delta wetland on the coast of Green
Bay, Lake Michigan, to describe the spatial and temporal dynamics of the invertebrate community. Various abiotic factors, including sedimentation rates determined from 210Pb and 137Cs as a proxy for delivery of riverine organic matter, were also measured to determine which factors influenced these dynamics.
Significant decreasing gradients in dissolved oxygen and pH with distance from the river, coupled with
trends in sedimentation rates, chloride, and sum nitrate (nitrate + nitrite), revealed that riverine water
was mixing with wetland water up to 100 m from the wetland-river interface. Aboveground primary production and total invertebrate densities exhibited Weibull type distributions, with highest rates and numbers occurring 20 to 100 m from the Peshtigo River. Invertebrate densities were largely represented by
Asellus sp. isopods (12–53%) and exhibited highest numbers in September. Invertebrate diversity at the
genus level linearly decreased with distance from the river based on the Simpson’s index of diversity (r2
= 0.60, p < 0.05) and the Shannon-Wiener function (r2 = 0.73, p < 0.01). Patterns observed suggest that
there is an “optimal” zone for benthic invertebrates in the Peshtigo wetland 20 to 60 m from the Peshtigo
River that is protected from high-energy events (e.g., storms, boating) in the Peshtigo wetland by a buffer
zone (0 to 20 m) but is close enough to benefit from replenished levels of dissolved oxygen, nutrients, and
organic matter delivered via the Peshtigo River.
INDEX WORDS: Coastal wetlands, spatial patterns, benthic invertebrates, densities, diversity, Green
Bay, Lake Michigan.
INTRODUCTION
Great Lakes coastal wetlands provide important
habitat (i.e., spawning, nursery grounds) for many
migratory waterfowl (e.g., Canadian geese, Branta
canadensis) (Prince et al. 1992) and for fish found
in the open waters of the Great Lakes (e.g., yellow
perch, Perca flavescens) (Becker 1983). This is
largely due to the benthic macroinvertebrates residing there, a valuable food resource for these organisms (Prince et al. 1992, Brazner and Beals 1997).
Recently, invertebrate communities in these systems have received increased attention (i.e., Botts
1999, Gathman et al. 1999, Kashian and Burton
2000). However, little is known of the spatial distri-
bution of benthic macroinvertebrates within Great
Lakes systems (but see Brady et al. 1995, Cardinale
et al.1997, Burton et al. 2003).
In coastal wetlands, inundation via spring runoff, seiches, or storm events can lead to fluctuations
in water levels (Prince and Burton 1996), creating
“high energy” zones at the interface between wetlands and adjacent bodies of water (Krieger 1992).
Energy from these events can mix water between
wetlands and adjacent bodies of water and result in
measurable gradients in various physicochemical
parameters in the water column (i.e., dissolved oxygen, turbidity, pH) (e.g., Cardinale et al. 1997). In a
littoral wetland in Saginaw Bay, mixing occurred in
wetland areas as far as 150 m from the wetland
edge-lake interface (Brady et al. 1995, Cardinale et
al. 1997). The presence of stalks of dead and live
emergent macrophytes (e.g., sedge (Carex sp.), bur
*Corresponding author. E-mail: rmackenzie@fs.fed.us
Present address: U.S.D.A. Forest Service, Institute for Pacific Islands
Forestry, 1151 Punchbowl St. Rm. 323, Honolulu, HI 96813
58
Invertebrates in a Great Lakes Wetland
reed (Sparganium sp.)) at the wetland edge in riverine systems can reduce the flow of inundating waters (Meeker 1996) and attenuate the energy from
these events. This reduced flow results in the deposition of suspended sediments or seston (Rasmussen
and Rowan 1997). Thus, benthic invertebrates at the
wetland edge may benefit to a greater degree than
organisms in the wetland interior from the continual
replenishment of oxygenated water, nutrients, or organic matter (i.e., phytoplankton) from an adjacent
river or lake.
In Lake Michigan, wetland loss has been greatest
along the southern coastline, primarily in urban and
industrial areas near Milwaukee and Chicago.
Today, wetlands along the northern coast of Lake
Michigan and Green Bay continue to be threatened
by increased development (Douglas Wilcox USGS,
pers. comm.). Few studies have examined the invertebrate communities in Green Bay wetlands, and
those that have, focused on insect emergence
(McLaughlin and Harris 1990, King and Brazner
1999). Clearly additional information is needed on
invertebrate community structure in Green Bay
wetlands in order to understand how development
and loss of coastal wetlands might impact the bay.
The objectives of this study were to describe the
spatial and temporal dynamics of the benthic
macroinvertebrate community residing in the
Peshtigo wetland, and to determine which abiotic
factors influenced these dynamics. Sedimentation
rates calculated from 210Pb (e.g., Robbins and Edgington 1975) and 137Cs (e.g., Livingston et al. 1988)
radionuclide chronologies associated with the
stratigraphy of sediment cores were used as a proxy
for delivery of riverine organic matter (i.e., phytoplankton, bacterially conditioned detritus). It was
hypothesized that: 1) a river-wetland mixing continuum will result in decreasing gradients of physicochemical factors (i.e., nutrients, dissolved oxygen)
and sedimentation rates with distance from the
Peshtigo River, 2) primary production rates are influenced by the Peshtigo River and will decrease
with distance from the river, 3) benthic macroinvertebrate densities and diversity will be greatest at the
riverine-wetland interface due to gradients in
physicochemical parameter and the increased delivery of riverine organic matter.
MATERIALS AND METHODS
Study Site
This study was conducted in the Peshtigo River
wetland, a 4 km2 river delta wetland located at the
59
confluence of the Peshtigo River and Green Bay in
northeastern Wisconsin (Fig. 1). The Peshtigo River
is a 5th order river draining a watershed of 2,800
km2 that consists largely of wetlands, farmland, and
second growth forests. Over the last 20 years, the
average river discharge has been 26.2 m3.s–1 with
the highest monthly discharge in April-May. The
Peshtigo estuary, south of the town of Peshtigo, has
not been channelized, and sediment deposition
throughout the estuary is the result of natural
processes.
Study Design
Stations sampled for this study were established
during the late fall of 1996 when the drained marsh
surface could be easily accessed to take sediment
cores for radionuclide analysis. Nine wetland stations (P30, P32, P34, P36, P37, P38, P39, P40, P41)
were randomly chosen along transects established
from the Peshtigo River towards the wetland interior to determine how far the river could deliver
sediments to the marsh surface. These stations were
then revisited at least once a month from May
through October of 1997 to collect biological and
physicochemical data. Four stations (P30E, P36E,
P38E, P41E) were also created in riverine areas directly adjacent to four wetland stations for collections of physicochemical data from the Peshtigo
River.
The nine wetland sampling stations were characterized by dense stands of emergent macrophytes
that included Typha sp., Carex sp., Sparganium sp.,
and/or Phalaris arundinacea as well as various
species of submergent vegetation (e.g., Potamogeton sp. and Myriophyllum sp.). Average water depth
was 0.5 ± 0.04 m and ranged from 0.1 to 0.8 m.
The four riverine sampling stations were characterized by open water to sparse emergent macrophytes that included Typha sp., Carex sp.,
Sagittaria sp., Scirpus sp., and/or Lythrum
salicaria. Submergent vegetation was also present
and consisted of Potamogeton sp. and Myriophyllum sp. Average water depth was 0.4 ± 0.02 m and
ranged from 0.3 to 0.8 m.
Physicochemical Parameters
Physicochemical parameters have previously
been used to demonstrate interactions between wetlands and adjacent bodies of water (e.g., Klopatek
1978, Sager et al. 1985, Cardinale et al. 1997).
Thus, several physicochemical parameters, includ-
60
MacKenzie et al.
FIG. 1. Location of the study site and the nine sampling stations in the Peshtigo wetland on
Green Bay, Lake Michigan. Lightly shaded areas indicate the wetland surface. Riverine stations (P30E, P36E, P38E, P41E) are not labeled on the figure but were adjacent to their
respective wetland stations (P30, P36, P38, P41).
ing the conservative tracer chloride and conductivity (Wetzel and Likens 1991), were measured
monthly from riverine and wetland stations. Temperature and pH were measured in situ 1 to 2 cm
from the bottom using an Orion pH electrode and
a Beckman φ 11 pH meter, and conductivity was
measured using a Fisher conductivity probe. Triplicate samples of unfiltered water were collected
from each station 1 to 2 cm from the bottom with
minimal resuspension of sediments. Samples were
collected in 5-mL glass bottles and fixed immediately for dissolved oxygen (DO) measurements
using a micro modification of the Chesapeake Bay
Institute technique for the Winkler dissolved oxygen method (Carpenter 1965). An additional 25 mL
of water was taken from each station, filtered
through 0.2 µm membrane Whatman syringe filters,
and analyzed for alkalinity using Gran titrations
(Wetzel and Likens 1991), chloride using ion chromatography (APHA 1992), ammonium (NH 4 + )
using Koroleff’s technique (Koroleff 1969), total
filterable phosphorus (TFP) using the ascorbic acid
technique (APHA
1992), and total nitrate plus ni–
trite (Σ NO3 ) using a cadmium- reduction flow-in-
Invertebrates in a Great Lakes Wetland
jection technique (Patrick Anderson, Great Lakes
W.A.T.E.R. Institute, pers. comm.). Field equipment was calibrated prior to each sampling date.
Nutrient and chloride standards, laboratory duplicates, and intermittent standards were analyzed to
ensure accuracy.
Sediment cores were taken from each wetland
station once during the fall of 1996 by driving a 7.5
cm diameter, acrylic core liner into the peat using a
mallet. Cores were extruded and sectioned into
4-cm intervals, dried at 60°C to a constant weight,
and ground into a fine powder. Radioactive isotope
recovery tracers (either 208Po or 209Po) were added
to each sample in 1 mL aliquots. Hot acid digestions were used to extract 210Pb, 208Po, and 209Po
from ground sediments (Gin 1992), and concentrations were determined using alpha spectrometry.
137Cs activity was measured through direct gamma
emissions from the ground sediment using an automated NaI-detector multichannel analyzer, an
EG&G Ortec GMX Series GAMMA-x HPGE detector, or a Canberra 7224 Ge (Li) detector.
Biological Samples
Aboveground primary production has been
shown to be an effective tool to examine general
patterns in plant growth (e.g., Doust and Childers
1998, Rejmankova 2001). Emergent wetland plants
were sampled with a sharpened spade from duplicate 17 cm × 17 cm plots (0.3 m2) at each station
once a month during the 1997 growing season
(May–October). Live aboveground plant shoots
were clipped at the sediment-plant interface, dried
at 60°C until a constant weight was reached, and
weighed to the nearest 0.01 g. Aboveground net primary production (NPP) rates of emergent macrophytes were then calculated for each wetland
station by summing the monthly change (positive or
negative) in average plant biomass over the 6month sampling period.
Invertebrate samples were collected once a
month during the same period at wetland stations
(n = 9) by dragging a standard 30.5 cm D frame,
kick net (1-mm mesh) over 1 m of the wetland sediment (sampling area = 0.31 m 2 ). This sampling
method is more effective at sampling invertebrates
from dense stands of wetland vegetation than Hester-Dendy or core samplers (Turner and Trexler
1997). Macroinvertebrates were hand-picked from
unpreserved kick net samples using 4× magnifying
glasses, counted, identified to the lowest practical
taxon using various keys (Hilsenhoff 1975,
61
Brinkhurst and Gelder 1991, Brown 1991, Covich
and Thorp 1991, Davies 1991), and measured to the
nearest 1 mm for total lengths. Taxon identifications were verified when possible by comparison
with a specimen collection. Monthly densities
(no·m –2 ) were then determined by dividing the
counts by the sampled area (0.31 m2). Generic diversity values were calculated using the ShannonWiener method and the Simpson’s index of
diversity (Krebs 1989).
Statistical Analysis
Linear and nonlinear regression analyses of
physicochemical parameters, sedimentation rates,
and invertebrate diversity versus distance from the
Peshtigo River were performed in Sigma Plot 4.0
(1997. SPSS Inc, Chicago, Illinois). Monthly densities of genera that represented ≥ 10% of the total invertebrate population (Appendix 1) were compared
using repeated measures (RM) single factor
ANOVAs. Pearson’s product moment correlation
analysis was used to determine relationships among
dissolved oxygen, sedimentation rates, pH, nutrient
concentrations, primary production, and monthly
densities of genera that represented ≥ 10% of the
total invertebrate population. Statistical significances were Bonferroni adjusted at a p-value of
0.05. All statistical analyses were performed using
Systat 8.0 (1998. SPSS Inc., Chicago, Illinois). Because variance was greater then mean monthly densities of invertebrates (Appendix 1), densities were
log transformed in order to conform to assumptions
of normality (Elliot 1977) prior to statistical analyses.
RESULTS
Physicochemical Parameters
Only dissolved oxygen (both concentration r2 =
0.34, p < 0.01 and percent saturation r 2 = 0.22,
p < 0.01) and pH (r2 = 0.36, p < 0.05) exhibited exponential decreases with distance from the Peshtigo
River, with the lowest values occurring in station
P37 (Fig. 2). Both chloride and sum nitrate (ΣNO3–)
(only reported from July due to incomplete data
sets for other months) also exhibited decreasing
trends with distance from the river, with ΣNO3– decreasing by nearly a factor of 4 within the first 100
m from the river. Chloride, conductivity, and alkalinity exhibited increased levels at station P37.
Total filterable phosphorous (TFP) concentrations
exhibited elevated concentrations from 20 to 120 m
62
MacKenzie et al.
or temperature, which ranged from 15.4 to 21.3°C
(average 19.1 ± 0.6°C).
Sedimentation rates could not be determined
from four of the nine stations (P38, P39, P40, P41)
because cores were not long enough to obtain background levels of 210Pb and thus determine inputs of
“new” 210Pb via sedimentation (Robbins and Edgington 1975). The five remaining cores (P30, P32,
P34, P36, P37) revealed that sedimentation rates
were greatest in wetland stations near the river and
decreased exponentially with distance from the
Peshtigo River (r2 = 0.99, p > 0.05) (Fig. 2). The
lack of significance between sedimentation rates
and distance was likely a result of the small sample
size (n = 5).
Primary Production
Annual aboveground NPP for emergent macrophytes calculated from monthly values ranged from
330 to 2,040 g dry wt·m–2·yr–1. Aboveground NPP
rates exhibited a positively skewed peak with distance from the river, similar to a three-parameter
Weibull type distribution (Evans et al. 2000) (Fig.
3). Maximum rates were observed 30 to 100 m
from the river with lower rates occurring near the
river and in wetland stations > 100 m from the
river. Rates of NPP were significantly correlated to
NH4+ (r = 0.40, p < 0.01) and TFP (r = 0.46, p <
0.01) concentrations.
FIG. 2. Spatial gradients in average monthly
measurements of dissolved oxygen concentrations,
pH, alkalinity, conductivity, and total filterable
phosphorus (TFP) concentrations. Data for chloride and ∑ NO3 concentrations are only from the
month of July due to incomplete data sets. Sedimentation rates are based upon 210Pb and 137Cs
profiles from a single core taken from each station. Error bars represent ± 1 SE.
from the river with lower concentrations observed
in the river and in the wetland interior. No patterns
were observed in NH 4 + concentrations, which
ranged from 0.25 to 2.3 µM (average 1.4 ± 0.2 µM),
Macroinvertebrate Patterns
One hundred and ten different taxa were identified from the Peshtigo wetland. Only those organisms whose average monthly densities were ≥ 1%
of the total invertebrate densities in one of the wetland stations are reported (Appendix 1). For a complete species list, see MacKenzie (2001).
Average monthly densities of total invertebrates
ranged from 1,562 ± 445 (station P41) to 344 ± 60
no·m–2·yr–1 (station P37). Like NPP, total invertebrate densities exhibited a Weibull type distribution
with distance from the river (Fig. 3). Densities initially increased with distance from the river with
maximum densities occurring in wetland stations 20
to 60 m from the river. Invertebrate densities were
lower in wetland stations > 60 m from the river
with the exception of P32, which was marked by a
high density of snails (Gyraulus sp., Aplexa sp.)
and isopods (Asellus sp.). Of the taxa listed in Appendix 1, the seven most abundant organisms in the
nine wetland stations were: Aplexa sp., Asellus sp.,
Invertebrates in a Great Lakes Wetland
63
FIG. 3. The spatial distribution of average monthly densities of total invertebrates, seven
major invertebrate taxonomic groups (Aplexa sp. snails, Asellus sp. isopods, Chironomus
sp. midge flies, Crangonyx sp. amphipods, Dicrotendipes sp. midge flies, Gammarus sp.
amphipods, Gyraulus sp. snails), net primary production, and diversity indices from the
Peshtigo wetland. Diversity regressions do not include values reported from P32. Error
bars represent + 1 SE.
Gyraulus sp., Chironomus sp., Crangonyx sp., Dicrotendipes sp., and Gammarus sp. All but Crangonyx sp. exhibited spatial patterns in density
similar to total invertebrate densities, with greater
numbers in wetland stations 20 to 60 m from the
river (Fig. 3). Crangonyx sp. densities decreased
with distance from the river. Of these seven organisms, Asellus sp. was generally the most abundant
invertebrate throughout the wetland (84 to 795
no·m–2·mo–1), representing 12–56% of the invertebrates sampled.
Invertebrate densities were highest from June
through September, with the highest densities in
September (Fig. 4). Asellus sp. was typically the
most abundant invertebrate in all samples over
time, representing 20–50% of the average monthly
densities of all invertebrates, which did not significantly change over time. The high densities in September were a result of increased Chironomus sp.,
Asellus sp., and Gyraulus sp. abundances. The significant seasonal differences in Chironomus sp.
abundances (p < 0.05) may have been due in part to
the mesh size of the sampling net which would
have missed the smaller instars that occur in the
spring and early summer.
Invertebrate diversity at the genus level decreased with distance from the river based on the
Shannon-Wiener function and Simpson’s index of
diversity. Excluding station P39 which was shown
to be an outlier, both measures of heterogeneity
64
MacKenzie et al.
FIG. 4. Temporal distribution of average densities of seven major taxonomic groups of
benthic macroinvertebrates in the Peshtigo wetland. Invertebrate abundance was dominated
by large numbers of Asellus sp. isopods. Other invertebrates represent the sum of remaining taxa ≤ 10% of the total density.
tracked a decreasing linear trend, which was significant for both abundant weighted (Simpson’s index)
(r2 = 0.60, p < 0.05) and rare-weighted (ShannonWiener) (r2 = 0.73, p < 0.01) measures of generic
diversity.
Dissolved oxygen was significantly and positively correlated with average monthly densities of
Crangonyx sp. (r = 0.31, p < 0.05) and Gammarus
sp. (r = 0.37, p < 0.01). Aboveground NPP was also
positively correlated to average monthly densities
of Crangonyx sp. (r = 0.33, p < 0.05) and Gammarus sp. (r = 0.37, p < 0.01). Sedimentation rates
were positively correlated to average monthly densities Dicrotendipes sp. (r = 0.34, p < 0.05) and
Crangonyx sp. (r = 0.34, p < 0.05). The only significant correlation between nutrient concentrations
and invertebrate densities was NH4+ and Crangonyx
sp. (r = 0.30, p < 0.05).
DISCUSSION
Wetland Physicochemical and
Primary Production Patterns
The significantly decreasing gradients in dissolved oxygen concentrations and pH with distance
from the Peshtigo River, coupled with trends observed in chloride, ∑NO3–, and sedimentation rates,
suggest the presence of a riverine-wetland mixing
continuum between the Peshtigo River (or Green
Bay) and the Peshtigo wetland. This was most apparent within the first 100 m away from the riverine-wetland interface (Fig. 2). The lower flow rates
in wetland stations compared to the adjacent river
(pers. obs.) suggest that these gradients were established as the river inundated the wetland and water
velocity was slowed by emergent vegetation.
The elevated levels of alkalinity, conductivity,
and chloride at station P37 (Fig. 2) may have been
Invertebrates in a Great Lakes Wetland
due to a localized input of groundwater high in
CaCO3, as the Peshtigo wetland is located above a
large dolomite deposit (Ostrum 1981). These parameters were thought to be responsible for the large
population of Pisidium sp. fingernail clams that
were also found there (Appendix 1) and can tolerate
the low levels of dissolved oxygen (McMahon
1991) that occurred there.
Aboveground NPP may have been higher 30 to
100 m from the river because of delivery of nutrients to plants via the Peshtigo River. This was supported by the significant correlations between
aboveground NPP and NH4+ and TFP. Few studies
have examined spatial patterns in plant growth in
riverine wetlands and those that have, focused on
standing crop or biomass. Although these are not
rate measurements, the gradients described from
these studies are similar to the gradient in NPP observed in the Peshtigo River wetland. In a riverine
wetland in Poland, standing crop of emergent plants
decreased with distance from the river, which was
attributed to inundation of the river, and nutrient release from sediments (Wassen et al. 2003). Metaphyton biomass and cover also decreased with
distance from inflows in a riparian freshwater
marsh because of the removal of nutrients by dense
mats of metaphyton at the wetland-river interface
(Wu and Mitsch 1998).
Benthic Invertebrate Ecological Parameters
The most abundant invertebrates in the Peshtigo
wetland were the Asellus sp. isopods, which were
the densest invertebrates at most stations both spatially and temporally (Figs. 3 and 4), as in other
wetlands (e.g., Pickard and Benke 1996, Smock
1999). Their abundance in the May samples was
likely due to their ability to over-winter in wetland
sediments (pers. obs.) coupled with their high
spring production rates (Duffy and LeBar 1994) allowing them to rapidly re-colonize and exploit detrital food sources, an important component of their
diet (Smock and Harlowe 1983). The lack of shredder organisms in this system (Appendix 1) suggests
that isopods likely play an important role in the mechanical breakdown of the large amounts of aboveground NPP that occurs there.
Trends in invertebrate density and diversity patterns, physicochemical parameters, and aboveground NPP from the Peshtigo wetland suggest that
invertebrate communities in delta river wetland systems may be laterally influenced by abiotic and biotic factors from the riverine and wetland interior
65
(or upland) sides. Similar patterns have been described for salt marsh plant communities (e.g.,
Bertness 1991a, b) and intertidal invertebrate communities (e.g., Menge and Sutherland 1987,
Beukema and Flach 1995) where community structure is influenced by abiotic (e.g., wave action, inundation, nutrient availability) or biotic (e.g.,
competition, predation) factors occurring on the
oceanic or estuarine and upland sides, respectively.
In the Peshtigo wetland, the lower invertebrate densities in stations 0 to 20 m from the river may have
been influenced by high-energy events that occur in
the river such as spring run-off, seiches, or storm
events (Krieger 1992). Other high energy events in
the Peshtigo River include recreational boating or
ice scour in the early spring when portions of
plants, sediments, or invertebrates can be broken
off the wetland edge as rafts of frozen material
(Geis 1985).
Predation by transient fish from the river or
Green Bay may also have affected invertebrate densities in wetland stations 0 to 20 m from the river.
In a separate study, juvenile yellow perch (Perca
flavescens) and largemouth bass (Micropterus
salmoides) were found in wetland stations closer to
the Peshtigo River (unpublished data) and are
known to feed on invertebrates during this life stage
(Becker 1983).
The lower dissolved oxygen concentrations in
wetland stations further from the Peshtigo River
may be important in causing the lower invertebrate
densities and diversity there. Microbial decomposition of plant material in wetlands can lead to limiting oxygen levels, which reduces invertebrate
numbers (Gabor et al. 1994) and diversity (Thorp
and Covich 1991). Dissolved oxygen levels of 85%
saturation can increase mortality rates of amphipods
(Pilgrim and Burt 1993). Thus, the low levels of
dissolved oxygen occurring in stations further from
the Peshtigo River at the wetland interior (20–40%
saturation) may have resulted in the lower invertebrate densities, particularly Gammarus sp. and
Crangonyx sp., that occurred there.
Plant production in the Peshtigo wetland suggests
that consumers were not limited by detrital input
(e.g., Batzer 1998). The quality, rather than the
quantity, of food may have been an important factor
contributing to patterns observed in invertebrate
densities. The significant correlation between sedimentation rates and densities of Crangonyx sp. and
Dicrotendipes sp., coupled with the higher sedimentation rates in stations near the river, suggests
that certain organisms may benefit from the deliv-
MacKenzie et al.
66
ery of riverine phytoplankton and particulate organic matter.
Thus, there appears to be an “optimal” zone for
benthic invertebrates in the Peshtigo wetland 20 to
60 m from the Peshtigo River established by biotic
and abiotic factors influenced by mixing of riverine
and wetland water. This optimal zone is close
enough to the Peshtigo River to benefit from inputs
of nutrients, dissolved oxygen, or organic matter,
but appears to be protected by a buffer zone (0 to
20 m) from high energy events such as storms, seiches, or boating activity.
ACKNOWLEDGMENTS
This research was supported in part by the Wisconsin Sea Grant Institute under grants from the
National Sea Grant College Program, National
Oceanic and Atmospheric Administration, U.S. Department of Commerce, and the State of Wisconsin.
Federal grant number R/EC-2, project number
NA446RG0481. Support was also provided by the
National Science Foundation, NSF OCE-9727151,
and the University of Wisconsin—Milwaukee
(Mortimer Award). We thank Tracy Sykes, Jeremy
Solin, Jim Waples, and Don Szmania for their invaluable assistance in the field and the lab. Constructive review of this paper was provided by
Michele Dionne, Katherine C. Ewel, and two
anonymous reviewers.
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Accepted: 16 December 2003
Editorial handling: Lynda D. Corkum
APPENDIX 1. Average monthly densities of macroinvertebrates (± 1 SE) that represented ≥ 1% of the
total invertebrate population sampled from the nine stations in the Peshtigo wetland from May through
October of 1997. Bold values represent major taxa groups and are equal to the sum of all species collected
from that group. Trophic guilds are indicated in bold parentheses after genera and are based upon
descriptions of food preference and functional feeding mechanisms (Pennak 1978, Brown 1991, Davies
1991, Covich and Thorpe 1991, Merritt and Cummins 1996). These categories include collector filterers
(CF), collector gatherers (CG), detritivores (D), filterers (F), predators (P), and scrapers (S).
Average Monthly Density (no⋅m–2⋅mo–1)
Station
distance from river (m)
Taxon
Phylum Mollusca
Class Gastropoda
Order Pulmonata
Family Planorbidae
Gyraulus sp. (D)
Promenetus sp. (D)
Planorbula sp. (D)
Family Physidae
Aplexa sp. (D)
Physa sp. (S)
Physella sp. (S)
Class Pelecypoda
Family Sphaeriidae
Pisidium sp. (F)
Phylum Annelida
Class Oligochaeta
Family Lumbriculidae
Family Naididae
Class Hirudinea
Family Erpobdellidae
Mooreobdella sp. (P)
Family Glossiphoniidae
Alboglossiphonia sp. (P)
Batrocobdella sp. (P)
Glossiphonia sp. (P)
Helobdella sp. (P)
P36
5
P30
6
P41
19
P38
28
P40
56
P39
86
P37
117
P32
277
P34
551
174 ± 700 210 ± 260
230 ± 980
274 ± 830
91 ± 29
154 ± 790
45 ± 12
475 ± 256 175 ± 118
126 ± 490
11 ± 10
5±3
91 ± 30
40 ± 29
14 ± 10
163 ± 105
59 ± 30
2±2
172 ± 590
72 ± 32
7±3
36 ± 12
32 ± 13
—
105 ± 700
43 ± 29
—
18 ± 13
—
5±4
185 ± 113
3±2
13 ± 70
18 ± 14
—
—
—
31 ± 25
—
—
17 ± 900
—
—
6±2
—
24 ± 14
—
—
16 ± 70
1±1
—
5±5
—
—
9±5
9±7
91 ± 67
42 ± 20
37 ± 36
60 ± 37
59 ± 49
21 ± 21
—
—
—
—
—
—
68 ± 37
17 ± 12
1±1
23 ± 90
27 ± 13
111 ± 620
48 ± 23
111 ± 620
7±3
21 ± 13
70 ± 43
42 ± 25
13 ± 60
—
7±3
—
12 ± 70
14 ± 14
1±1
7±4
12 ± 70
14 ± 14
—
—
18 ± 12
1±1
68 ± 43
—
36 ± 26
—
—
—
—
1±1
—
—
—
1±1
—
1±1
—
—
—
—
—
—
—
1±1
8±7
—
—
1±1
18 ± 10
1±1
—
—
5±4
—
8±6
67 ± 49
18 ± 13
4±2
—
16 ± 80
5±4
1±1
8±6
67 ± 49
1±1
2±1
—
4±3
1±1
—
—
1±1
1±1
1±1
—
1±1
4±3
—
1±1
1±1
Invertebrates in a Great Lakes Wetland
APPENDIX 1.
69
Continued.
Average Monthly Density (no⋅m–2⋅mo–1)
Station
distance from river (m)
P36
5
P30
6
P41
19
P38
28
P40
56
P39
86
P37
117
P32
277
P34
551
Phylum Arthropoda
Class Crustacea
Order Isopoda
Asellus sp. (D)
333 ± 178 382 ± 137
333 ± 178 382 ± 137
170 ± 770
170 ± 770
592 ± 279
592 ± 279
Order Amphipoda
Crangonyx sp. (D)
Gammarus sp. (D)
Hyallela sp. (D)
146 ± 530
69 ± 37
16 ± 10
—
67 ± 16
58 ± 17
6±4
3±1
349 ± 870
26 ± 17
266 ± 960
57 ± 24
111 ± 390
69 ± 37
32 ± 21
9±6
77 ± 23
66 ± 22
2±1
9±8
116 ± 350
34 ± 70
64 ± 27
17 ± 80
2±1
2±1
—
—
22 ± 80
22 ± 80
—
—
4±2
4±2
—
—
2±2
1±1
2±2
2±2
5±4
—
5±3
1±1
12 ± 10
181 ± 900 226 ± 136
506 ± 222
238 ± 930
254 ± 140
42 ± 16
43 ± 16
53 ± 45
17 ± 50
177 ± 890 221 ± 134
503 ± 221
234 ± 920
247 ± 137
38 ± 15
25 ± 12
47 ± 44
15 ± 50
Class Insecta
Order Coleoptera
Order Diptera
Family Chironomidae
822 ± 226 107 ± 280 126 ± 400 373 ± 150 297 ± 169
822 ± 226 107 ± 280 126 ± 400 373 ± 150 297 ± 169
Subfamily Chironominae
Tribe Chironomini
Chironomus sp. (CG)
Dicrotendipes sp. (CG)
Einfeldia sp. (CG)
Endochironomus sp. (S)
Polypedilum sp.
14 ± 11
27 ± 27
17 ± 17
14 ± 14
9±6
53 ± 48
97 ± 97
9±9
1±1
6±4
171 ± 156
11 ± 7
82 ± 33
89 ± 57
10 ± 6
52 ± 38
9±7
70 ± 45
21 ± 15
—
137 ± 88
2±2
37 ± 23
—
1±1
9±8
1±1
4±3
—
—
1±1
—
—
1±1
9±9
28 ± 26
9±9
1±1
—
—
5±3
1±1
—
—
3±3
Tribe Tanytarsini
Micropsectra sp. (CF)
Paratanytarsus sp. (CF)
Tanytarsus sp. (CF)
Stempellinella sp. (CF)
11 ± 8
42 ±30
24 ± 16
7±5
1±1
31 ± 26
19 ± 12
1±1
—
93 ± 61
4±3
—
1±1
43 ± 30
3±3
1±1
—
37 ± 30
16 ± 16
1±1
—
14 ± 13
2±1
3±3
—
—
—
9±5
—
4±4
1±1
1±1
—
1±1
2±1
—
5±5
46 ± 40
29 ± 16
9± 6
2±2
9+9
1±1
22 ± 22
—
—
—
19 ± 16
3±2
—
—
—
1±1
—
5±5
11 ± 70
7±7
—
—
5±5
—
—
—
—
—
—
35 ± 35
3+3
—
6±6
—
2±2
—
4±4
—
—
—
—
21 ± 21
—
—
3±3
3±3
2±2
2±2
124 ± 100
124 ± 100
57 ± 25
56 ± 24
35 ± 22
35 ± 22
3±2
2±2
—
—
14 ± 90
14 ± 90
3±2
1±1
12 ± 40
4±3
32 ± 19
40 ± 27
26 ± 23
1±1
18 + 11
7±4
18 ± 13
9±5
—
—
6±5
8±6
1±1
14 ± 12
3±1
11 ± 60
Suborder Zygoptera
Family Coenagrionidae
Enallagma sp. (P)
Nehalennia sp. (P)
—
1±1
—
3±3
21 ± 16
4±4
—
29 ± 28
1±1
16 ± 16
—
—
—
3±3
—
4±4
4±4
1±1
Order Trichoptera
1±1
1±1
—
9±5
1±1
3±2
1±1
—
1±1
Order Ephemeroptera
Family Caenidae
Caenis sp. (CG)
Family Siphlonuridae
Siphlonurus sp. (CG)
Family Leptophlebiidae
Habrophlebia sp. (CG)
Leptophlebia sp. (CG)
Order Hemiptera
Trichocorixa sp. (P)
Order Odonata
Suborder Anisoptera
Family Libellulidae
Libellula sp. (P)
Total
917 ± 186 881 ± 300 1,562 ± 44501,371 ± 379 1,423 ± 409 441 ± 122 344 ± 600 1,057 ± 3160 570 ± 238