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22001155 SOUTHEASTERN NATURALIST 1V4o(4l.) :1642,3 N–6o3. 44
Fish and Water Quality in the Forested Wetlands Adjacent
to an Oxbow Lake
Caroline S. Andrews1, Leandro E. Miranda2,*, and Robert Kroger1
Abstract - Forested wetlands represent some of the most distinct environments in the Lower
Mississippi Alluvial Valley. Depending on season, water in forested wetlands can be warm,
stagnant, and oxygen-depleted, yet may support high fish diversity. Fish assemblages in
forested wetlands are not well studied because of difficulties in sampling heavily structured
environments. During the April–July period, we surveyed and compared the water quality
and assemblages of small fish in a margin wetland (forested fringe along a lake shore), contiguous
wetland (forested wetland adjacent to a lake), and the open water of an oxbow lake.
Dissolved-oxygen levels measured hourly 0.5 m below the surface were higher in the open
water than in either of the forested wetlands. Despite reduced water quality, fish-species
richness and catch rates estimated with light traps were greater in the forested wetlands than
in the open water. The forested wetlands supported large numbers of fish and unique fish
assemblages that included some rare species, likely because of their structural complexity.
Programs developed to refine agricultural practices, preserve riparian zones, and restore
lakes should include guidance to protect and reestablish forest ed wetlands.
Introduction
Forested wetlands represent some of the most distinct environments in the
Lower Mississippi Alluvial Valley (LMAV). These wetlands have been described
as mysterious and primordial (Mitsch and Gosselink 2007), supporting a diversity
of unique aquatic species adapted to survive under seasonally risky water-quality
conditions (Hoover and Killgore 1998, Wharton et al. 1982). Depending on the
season, water in forested wetlands can be warm, stagnant, and oxygen-depleted
(Conner and Buford 1998). Yet, in regions with high fish-species diversity such as
the LMAV, forested wetlands reportedly include a high percentage of the total species
count (Baker et al. 1991, Hoover and Killgore 1998).
Three types of forested wetlands are often associated with oxbow lakes in the
LMAV. Margin wetlands, also identified as fringe wetlands, are transitional areas
between lakes and upland areas, and of variable width depending on bank topography
and lake age (Snodgrass and Burger 2001). The natural levee of oxbow lakes
may produce a littoral zone that allows only a narrow margin of wetland. However,
ridge and swale formations found in large meanders may provide a wider marginal
wetland on the swale side of oxbow lakes and access to additional depressional
lands inside the meander bend (Hodges 1997). Terminus wetlands develop over
1Department of Wildlife, Fisheries, and Aquaculture, Mississippi State University, Mississippi
State, MS 39762. 2US Geological Survey, Mississippi Cooperative Fish and Wildlife
Research Unit, Mississippi State University, Mississippi State, MS 39762. *Corresponding
author - smiranda@usgs.gov.
Manuscript Editor: Quenton Tuckett
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sediment plugs in one or both ends of oxbow lakes (Mitsch and Gosselink 2007).
The shallower depth provided by sediment plugs facilitates development of these
sites into forested terminus wetlands, and over time the forests advance towards
the meander bend as lakes slowly lose depth due to sedimentation (Westlake et al.
2009). Contiguous wetlands abut lakes and may represent ancient channels or other
depressions in forested or vegetative succession. These 3 types of forested wetlands
are characterized by a mix of Taxodium distichum (L.) Rich. (Bald Cypress), Nyssa
spp. (tupelos), Salix spp. (willows), Betula nigra L. (River Birch), Populus deltoides
Bartram ex Marshall (Cottonwood), Quercus lyrata Walter (Overcup Oak),
Carya aquatica (Michx. f.) (Water Hickory), and others depending on wetland age
and hydrology (Hodges 1997, Shepard et al. 1998).
Water quality and fish communities in forested wetlands are not well studied
relative to other aquatic systems, likely due to the difficulties of sampling in these
heavily structured environments. It is generally assumed that forested wetlands
adjacent to waterbodies enrich fish assemblages and may provide temporary
nursery habitats for many fish species (Jude and Pappas 1992, Ward et al. 1999).
Killgore and Baker (1996) studied fish assemblages in a river channel and in adjacent
forested wetlands. They reported that species richness was similar among
these environments due to hydraulic mixing, but that some families were more
common and overall abundances were higher in forested wetlands. Adams et al.
(2007) reported that backwaters contiguous to a stream, intermittent floodplain wetlands,
and isolated floodplain wetlands had distinct fish-assemblages—contiguous
backwaters supported open-water species, isolated backwaters supported typical
swamp species, and intermittent floodplain wetlands supported a mixture of species.
Nevertheless, no equivalent information is available for fish assemblages that
develop in forested wetlands adjacent to oxbow lakes. This information is needed
to inform decisions about protection and restoration of the wetlands surrounding
the hundreds of oxbow lakes that occur in the LMAV.
We examined assemblages of small fish and water-quality conditions in margin
wetlands, contiguous wetlands, and the open water of an oxbow lake. Specifically,
our objective was to determine if the 2 forested wetlands accommodated unique fish
assemblages relative to the open water. Water-quality conditions often play a major
role in structuring fish assemblages, and water-quality conditions reportedly can
be harsh in wetlands (Verhoeven et al. 2006). Thus, to aid in interpreting potential
differences in fish assemblages among wetlands and open-water environments, a
secondary objective was to investigate selected water-quality variables to determine
if they differed temporally and spatially among environments. We included a
temporal component because seasonal variation in water quality and seasonal-habitat
needs of juvenile and other small fish may be important factors in structuring
fish assemblages. We hypothesised that fish-taxa composition would differ among
environments and that these differences would correspond to habitat preferences
shaped by water quality. We further hypothesized that these differences would vary
temporally over the course of the spring and early summer as water quality changed
over the reproductive period.
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Study Site
Blue Lake is an oxbow lake in west-central Mississippi. The 21-ha lake is shallow
(mean depth = 1.3 m, maximum depth = 4.4 m), 3.5 km long, and permanently
connected at its upper end to Gayden Brake, a 334-ha cypress-tupelo contiguous
wetland with a mean depth of 0.6 m and a maximum depth of 1.1 m. Blue Lake and
Gayden Brake reportedly are prehistoric channels of the Ohio River, which presently
flows 400 km north of the study site (Fisk 1944). The connection between
Blue Lake and Gayden Brake represents a unique transition zone that includes
an open-water environment with mean and maximum depths of 2.6 m and 3.0 m,
respectively, and a margin wetland with mean and maximum depths of 0.4 m and
1.0 m, respectively (Fig. 1). Precipitation in nearby Greenwood, MS during January–
July 2012 (77 cm) was nearly normal (79 cm); thus, water levels in the study
area were typical. Average Secchi-disk visibility in Blue Lake is 60 cm (Andrews
2013).
Methods
Water-quality assessment
We used a Eureka Manta Multiprobe (Eureka Environmental, Austin, TX) to
determine diel temperature and dissolved oxygen (DO) trends. We deployed a
multiprobe 0.5 m below the surface in each environment to record water-quality
Figure 1. Blue Lake and Gayden Brake, in the Bear Creek watersh ed, MS. The lower inset
shows approximate location of light-traps fished along transects in (1) open water, (2) margin
wetlands, and (3) contiguous wetlands. Each transect was ~100 m long.
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parameters hourly at a stationary location (Fig. 1). The probes recorded complete
diel water-quality cycles over 95 days from early April through mid-July 2012. We
collected the multiprobes weekly and downloaded the data. Water-quality trends
were represented by temperature means and maxima and DO mean and minima
computed from complete 24-hour diel cycles.
Fish collection
We assessed trends in small-fish assemblages with light traps fished in fixedstation
transects within each of the 3 environments. Light traps are selective for fish
attracted to light and target primarily larval and juvenile stages, or adults of small
fish-species (Hickford and Schiel 1999). We based our light-trap design on a modified
quatrefoil pattern, ~25 cm x 25 cm x 30 cm with a 7-cm-wide vertical entrance
covered with a 1-mm-mesh screen; a funnel-collection assembly as described by
Secor et al. (1992) facilitated fish removal. The light source was a solar-powered
high-intensity LED light (Gyekis et al. 2006). We suspended 6 light traps along
each transect, with the lower end positioned approximately in line with the Manta
multiprobes. We placed traps ~20–25 m apart, a distance reported to attenuate light
intensity so that trap collections are independent (Fisher and Bellwood 2002). We
deployed the traps from early April through mid-July approximately weekly at
nearly the same locations to ensure standardized sampling. The sampling period
represented spring and early summer, a time span during which most local fish species
start and finish spawning (Ross 2001). We set all traps at dusk and retrieved
them ~40 h later at dawn, allowing for 2 nightly cycles. Upon collection, we preserved
individual-trap contents in 10% formalin until identification with taxonomic
keys (Wallus and Simon 2008). We pooled the catches from the 6 traps deployed in
each transect by sampling date to reduce statistical complications associated with
excessive zero counts.
Statistical analysis
We analyzed water-quality and fish data to assess patterns across the 3 environments.
We assessed each data matrix with a permutation multivariate analysis of
covariance (perMANCOVA; 1000 permutations) with either temperature (mean
and maxima), dissolved oxygen (mean and minima), or fish counts (multiple taxa)
as the response variables; environment type as the predictor variable; day-of-year
(DOY) as a covariate; and an interaction term between environment type and DOY.
We included DOY to account for temporal variation across the sampling season and
the interaction term to detect potential differences in response among environments
as the season progressed. Variables were loge(x + 1)-transformed as needed to meet
assumptions of linearity or distribution. We analyzed the water-quality data using
a Euclidean-similarity coefficient and the fish data using a Bray-Curtis coefficient.
Analyses were conducted with PRIMER version 6 (Clarke and Gorley 2006) and
the PERMANOVA+ add-on package (Anderson et al. 2008).
If the perMANCOVA identified a statistically significant (P ≤ 0.05) DOY effect
on fish counts, we examined cumulative fish catch of selected taxa over DOY. We
expected that cumulative catches would exhibit a sigmoidal response over time,
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2015 Vol. 14, No. 4
with a relatively flat curve initially as few fish were caught early in the year, a rising
curve as catch rates increased through mid-season, and a flattening curve once
catch rates slowed or stopped later in the season. The sigmoidal pattern was fit with
a logistic model as:
y = bo + b1·DOY + b2·(DOY × environment) (1)
and
y = loge [(1 / Pcum) - 1], (2)
where Pcum = cumulative frequency of catch expressed as a proportion (0 - 1), b0 =
intercept of model, b1 = slope of model for DOY, and b2 = slope modification for
DOY according to environment.
In equation (1), b0 / - (b1 + b2) represents the inflection point in the sigmoid curve
given in days. The inflection point reflects the DOY when 50% of the fish had been
collected. A significant b2 suggests that inflection points occurred at different DOY
depending on environment. If so, a t-test determined which paired environments
differed. The logistic analyses were run using the GLM procedure (SAS 2008).
Results
Water-quality assessment
The water-quality data overlapped with the light-trap samples but did not always
coincide, because the water-quality equipment could be deployed for longer time
periods. Due to battery issues associated with multiprobe deployment, environments
were unequally sampled, with 20 cycles in the open-water environment, 45
cycles in the margin wetland, and 30 cycles in the contiguous wetland.
The perMANCOVA detected spatial (F = 4.8, P < 0.01), temporal (F = 80.1,
P < 0.01), and interaction (F = 5.1, P < 0.01) effects on temperature and DO descriptors.
These results suggested that there were differences among environments,
conditions changed over time, and trends differed among all or some environments.
In general, the open-water and contiguous wetlands followed similar temporal
trends in mean and maximum temperature and in mean DO (Fig. 2). Although the
trends were similar, temperature was consistently higher in the contiguous wetland
than the open water (~1.5–2 oC warmer), and mean DO was consistently lower
(~1.8 mg/L lower). The margin wetland followed a different trend in that it had a
higher mean and maximum temperature and mean DO early in the sampling season,
but values for these parameters were lower than those of other the 2 environments
late in the sampling season (Fig. 2). Minimum DO decreased over the sampling
season at different rates in all environments, with the margin wetland exhibiting
the fastest decrease and reaching levels below 2 mg/L in early June, about 1 month
sooner than the contiguous wetland. By the time the study was concluded on DOY
196, DO level remained above 2 mg/L only in the open water.
Fish collection
Fish catches in the light traps included 9 families, 14 taxa, and 1940 fish
ranging in total length (TL) from 7 to 80 mm (mean = 31 mm). Catch rates were
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highest in the margin wetland, followed by the contiguous wetland and then the
open-water environment (Table 1). Taxa richness followed the same pattern. The
most numerous individuals represented 3 taxa: Lepomis spp. (sunfish), Micropterus
salmoides (Largemouth Bass), and Labidesthes sicculus (Brook Silverside).
Nevertheless, the biggest differences among environments were not in the catch
rates of the most abundant species, but in the infrequent catches of uncommon
species (Table 1).
The perMANCOVA detected spatial (F = 1.8, P = 0.05), temporal (F = 8.2, P less than
0.01), and interaction (F = 2.6, P < 0.01) effects on catches of the 14 taxa. The
interaction effect indicated that spatial differences occurred, but the differences
depended on time. These differences were inspected for the most common taxa with
equation (1). Sunfish inflection points were DOY 155, 162, and 156 in open water,
margin wetland, and contiguous wetland, respectively, and were not significantly
Figure 2. Diel water-quality parameters in 3 habitats of Blue Lake, MS, 5 April–14 July
2012 (DOY 96–196).
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different (P = 0.87). Largemouth Bass inflection points were DOY 109, 136, and
121 in open water, margin wetland, and contiguous wetland, respectively, and were
significantly different (P < 0.01). Brook Silverside inflection points were DOY
162, 183, and 165 in open water, margin, and contiguous wetland, respectively,
and were significantly different (P < 0.01). Across these 3 taxa, inflection points
were consistently earliest in open water and latest in the margin wetland, earlier
for Largemouth Bass and latest for Brook Silverside, and least-well defined (i.e.,
highest standard error) for sunfish (Fig. 3). Assessment of temporal trends of other
taxa was not possible because catches were low and sporadic.
Table 1. Catch rate (fish/6 light-traps) of 14 taxa captured in 3 environments of Blue Lake, MS, with
passive light-traps during 13 sampling periods, April–July 2012. TL range = 7–80 mm (mean = 31).
Margin Contiguous
Taxa Common name Open water wetland wetland
Lepomis spp. sunfishes 15.7 30.2 28.8
Micropterus salmoides (Lacepède) Largemouth Bass 13.4 40.4 18.5
Labidesthes sicculus (Cope) Brook Silverside 17.3 11.8 23.3
Gambusia affinis (Baird and Girard) Western Mosquitofish 0.7 1.8 4.6
Pomoxis spp. Crappies 1.6 0.9 0.9
Fundulus chrysotus (Günther) Golden Topminnow - 2.1 0.5
Percidae Darters - 1.8 0.2
Notemigonus crysoleucas (Mitchill) Golden Shiner - 0.5 0.2
Opsopoeodus emiliae Hay Pugnose Minnow - - 0.5
Catostomidae Suckers - 0.2 -
Centrarchus macropterus (Lacepède) Flier - 0.2 -
Elassoma zonatum Jordan Banded Pigmy Sunfish - 0.2 -
Ictaluridae Catfishes - 0.2 -
Lepisosteidae Gars - - 0.2
All 48.7 90.3 77.7
Figure 3. The DOY
when 50% of the fish
had been collected
during the DOY 96–
196 sampling period.
Values are identified
according to open
water, margin wetland,
and contiguous
wetland, and according
to 3 taxa. Error
bars represent ± 1
SE.
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Discussion
The 3 distinct environments we studied showed differences in water-quality
conditions and fish assemblages. The contiguous wetland was the warmest and
least oxygenated of the 3 environments, but had greater catch-rates compared to
the cooler, better-oxygenated open-water environment. While it seems counterintuitive
that heavily shaded water in the forest was warmer than open water, we
suspect that protection from recurring cold fronts in winter and spring, and reduced
depth and wind in summer kept the contiguous wetland warmer. The margin wetland
exhibited the slowest rise in temperature and the steepest decline in oxygen,
yet also showed the highest relative fish abundance and taxa ric hness.
As expected, DO was highest in the open water and, for most of the season, lowest
in the contiguous wetland. The open water was deeper and possibly less affected
by sediment respiration than the contiguous wetland. Moreover, besides receiving
less sunlight due to increased canopy cover, the contiguous wetland accumulated
leaf and woody debris generated by the forest, creating additional oxygen demand
via microbial respiration (Sharitz and Mitsch 1993). We expected that oxygen
conditions in the margin wetland would be intermediate because mixing with the
open water would temper the effects of the forest. Nevertheless, oxygen conditions
decreased faster in the margin wetland over the course of the season than in the
other environments. Over time, the margin wetland developed dense mats of emergent
aquatic macrophytes (principally Alternanthera philoxeroides (Mart.) Griseb.
[Alligator Weed]), which tend to reduce DO and increase diel DO fluctuations (Miranda
and Hodges 2000). Unlike the contiguous wetland, the margin wetland had
more light that allowed development of emergent aquatic macrophytes. By July,
mean DO in the margin wetland had dropped to 2 mg/L, a level generally considered
a lower threshold for warm-water fish (Breitbur g et al. 2009).
Water-quality conditions may have different effects on the fish assemblages in
the 2 types of forested wetlands. Fish inhabiting the contiguous wetland may find
it more difficult to escape occasional hypoxia, whereas those in the margin wetland
have easier access to open water where water quality is higher. This effect is
analogous to that reported in large stands of aquatic macrophytes (Miranda et al.
2000). On one hand, the plants provide abundant invertebrate foods, cover, and an
environment with few or no large predators. On the other hand, water-chemistry
conditions can be precarious, and fish at these sites run the risk of being trapped
in unsuitable microhabitats during the daily reshuffling of physical and chemical
conditions. Activity changes, such as increased energy allocation to ventilation,
may nullify the benefits of an abundant food supply. Also, surfacing for respiration
at the air–water interface and other movements forced by adverse water-quality
conditions may increase the chance of predation by other fish or by avian predators.
Shallow wetlands, like large stands of aquatic macrophytes, provide food and cover
but can have negative water-quality consequences. By summer, when DO levels
drop to potentially dangerous levels, we speculate that only specialized species can
remain in contiguous wetlands, but fish may exhibit daily movements in and out of
margin wetlands.
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Inflection points in sigmoid cumulative curves provided insight into distribution
of common fish over time. Of the 3 most-common taxa trapped, we collected Largemouth
Bass earliest, sunfish next, and Brook Silverside soon after, following an
expected temperature-related sequence in hatching (Ross 2001). For each of these 3
taxa, 50% of the catch was attained earliest in open water and latest in margin wetland.
Small fish recruited into these environments over the spring and summer may
be disproportionately recruited into forested wetlands. This pattern is particularly
true of the margin wetland given that emergent macrophytes that develop over the
growing season potentially attract small fish seeking shelter from predation. We do
not know if these 3 generalist taxa remained in the forested wetlands after water
quality was reduced because as they grew they were no longer captured by the light
traps; however, we hypothesize that many of them exited the wetlands in summer
after water-quality conditions declined. Additional research is needed to track latesummer
and fall use of these wetlands by fish.
We predicted that forested wetlands would attract more small individuals and
more small species than the open-water habitats. As expected, in comparison to the
open water, catch was 1.9 times higher in the margin wetland and 1.6 times higher
in the contiguous wetland than in the open water. Species counts were 2.4 times
higher in the margin wetland than in the open water and 2.0 times higher in the
contiguous wetland than in the open water. Relative to species composition, both
forested wetlands contributed rare species to the overall collection. We collected
several species including Opsopoeodus emiliae (Pugnose Minnow), Centrarchus
macropterus (Flier), Elassoma zonatum (Banded Pygmy Sunfish), and Fundulus
chrysotus (Golden Topminnow) only in the forested wetlands, and there only infrequently.
These species comprise a distinct wetland assemblage in the LMAV, are
typically only found in shallow semi-isolated waterbodies, and their distribution
in the LMAV has been impacted disproportionally by wetland clearing and habitat
degradation. These species occur in the margin and contiguous wetlands for several
reasons including their adaptation to reduced water quality and their propensity to
exploit structurally complex habitats. Other than these rare species, fish assemblages
in the open water and wetlands were similar.
The results of our study demonstrated that habitat diversity provided by forested
wetlands associated with oxbow lakes contribute to fish-species diversity in at least
2 ways. First, these unique habitats promote rare species that show habitat specificity.
Second, they contribute to temporal diversity in environmental conditions that
help sustain habitat-generalist species. Although some of the species we collected
in forested wetlands are now considered rare, they might have once been more
common. Originally, the LMAV included nearly 10 million hectares of forested
wetlands, but towards the end of the 20th century there were only about 2 million
hectares left (MacDonald et al. 1979). The remaining wetlands have experienced
accelerated sedimentation rates from adjacent agricultural operations and increased
risk of dewatering during drought because the water table has been substantially
lowered by groundwater pumping in sections of the LMAV (Kingsbury et al. 2014).
Programs directed at refining agricultural practices, preserving riparian zones, and
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restoring lakes should consider expanding their conservation efforts to include protection
and reestablishment of forested wetlands.
A limitation of our study was that it represented a single lake/wetlands system.
This lack of treatment replication limits the applicability of our conclusions.
However, it is not unreasonable to hypothesize that margin wetlands in oxbow
lakes in general may support more fish of all life stages and higher species richness
because margin wetlands represent a large edge-zone that includes a mixture
of fish species adapted to both open water and nearshore structure. When water
quality deteriorates in margin wetlands, fish may find it easier to temporarily
escape into open water. Conversely, whereas contiguous wetlands with their
extensive structural complexity have the potential to support large numbers of
fish and unique fish assemblages, they may not always do so because fish may
avoid them seasonally to avoid entrapment during periods with inadequate water
quality. The extent to which forested wetlands interact with oxbow lakes to
shape overall fish assemblages is likely to be time- and site-specific depending
on factors such size and depth of the lake and of its associated wetlands, forest
type and maturity stage, distribution in the landscape, and inter-annual differences
in hydrology and temperature. Additional replication is needed to improve
understanding of the temporal and spatial interplay between water quality, fish
assemblages, and forested wetlands in the LMAV.
Acknowledgments
We thank D. Devries and E. Dibble for lending us light traps. B. Botti, C. Shoemaker, D.
Goetz, E. Mower, L. Kaczka, and M. Arnold provided field support. J. Killgore, D. Faust,
and 2 anonymous referees provided helpful reviews. This work was supported in part by
the US Army Corps of Engineers. Specimen collections were authorized under Mississippi
State University’s Institutional Animal Care and Use Committee protocol number 08–034.
Any use of trade, firm, or product names is for descriptive purposes only and does not imply
endorsement by the US Government.
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