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22001144 SOUTHEASTERN NATURALIST 1V3o(3l.) :1534,7 N–5o7. 13
Fish Assemblages on Sand/gravel Bar Habitat in the
Alabama River, Alabama
T. Heath Haley1,2 and Carol E. Johnston1,*
Abstract - The Alabama River drainage is a biologically diverse system containing over
180 native fishes and at least 33 endemics. Many studies have surveyed single species of
conservation concern, such as the federally endangered Scaphirhynchus suttkusi (Alabama
Sturgeon), Alosa alabamae (Alabama Shad), and Crystallaria asprella (Crystal
Darter), but few have documented entire fish assemblages. Maintaining fish-assemblage
data is an important process in monitoring species and assemblage composition through
time so that large-scale ecological change can be detected. In this study, we surveyed
fish assemblages of sand/gravel bar habitat in the lower Alabama River and compared
these data to those collected from historical surveys. Diel and seasonal surveys were conducted
along 19 sandbars from Dixie Landing (river mile 22) to Claiborne Lock and Dam
(river mile 72). We recorded a total of 48 species in 41 collections during summer, fall,
and spring 2010–2011. Based on the Jaccard index, these samples had low similarity to
historical samples collected by R.D. Suttkus and the Geological Survey of Alabama, suggesting
temporal fish assemblage shifts. In 2010, we detected extremely high numbers of
Brevoortia patronus (Gulf Menhaden) during summer and fall, which is a new distributional
record. Diel comparisons using the Morisita index indicate low similarity reflecting
large numbers of catfish species detected mostly in night collections. These data also
indicate seasonal faunal changes among sandbar fish assemblages. Ongoing habitat alteration
on the Alabama River is a potential factor leading to assemblage homogenization
and potential loss of biodiversity. Future monitoring in the Alabama River should consider
diel and seasonal sampling to accurately document fish species and assemblages,
including potential shifts that may be occurring over space and time.
Introduction
Anthropogenic changes to aquatic environments often result in alteration of
species assemblages and a decline in biodiversity (Ganasan and Hughes 1998, Poff
et al. 2007, Strayer and Dudgeon 2010). Because of our heavy reliance on freshwater
for water supply, transportation, agriculture, and recreation, riverine systems
are often dammed and dredged, and these habitat modifications threaten biotic
integrity (Dudgeon et al. 2005, Poff et al. 2007, Taylor et al. 2008). For example,
damming of rivers isolates fish assemblages to fragmented habitats both upstream
and downstream of dams, which leaves the assemblages vulnerable to habitat degradation
and changes in hydrology and water quality (Greathouse et al. 2006, Poff
et al. 2007, Rypel and Bayne 2009, Taylor et al. 2008). These isolation events may
also have tremendous effects on migratory fluvial fauna that use both upstream and
1Fish Biodiversity Lab, Department of Fisheries, Auburn University, Auburn, AL 36849.
2Current address - Alabama Department of Conservation, 64 North Union Street, Montgomery,
AL 36130. *Corresponding author - Johnsc5@auburn.edu.
Manuscript Editor: Andrew Rypel
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downstream areas as spawning sites (Bunn and Arthington 2002, Kondolf and Wolman
1993). Damming also results in the congestion of sediment flow throughout
the lotic system, and homogenization of aquatic habitat downstream of the structure
may occur due to the deposition of sediment (Kondolf 1997).
Many studies have found that flow regimes impact both the structure and persistence
of fish assemblages (Freeman et al. 2001, Shea and Peterson 2007). Poff
and Allan (1995) hypothesized that organization of fish communities was related
to hydrological variability and conducted a study in which they sampled 34 sites
in Wisconsin and Minnesota. They found a strong relationship between hydrological
variability and fish assemblage structure, suggesting that changes in flow
could potentially modify the fish assemblage structure of an aquatic system.
Fish studies are often focused on single species, but monitoring diversity within
entire assemblages can provide information on the status of ecosystems more
generally (Johnston and Maceina 2009, Scott and Helfman 2001). For example,
information on entire assemblages can provide insight into homogenization and
shifts in assemblage structure that may be occurring over space and time (Scott
and Helfman 2001).
To maintain passage, riverine systems used for navigation are also dredged,
causing significant disturbance to the entire system and the destruction of shallow-
water habitats (Licursi and Gomez 2009). Removal of the substrate not only
destroys the natural habitat, but can create new, low-velocity, sediment-rich habitats.
Consequently, these types of habitats are unsuitable for many riverine fishes
that require flow (Padmalal et al. 2008, Paukert et al. 2008). The disruption of sediment
causes an increase of nutrients (soluble phosphorus) and toxic substances in
the water column that can cause changes in aquatic assemblages (Lewis et al. 2001,
Licursi and Gomez 2009).
Monitoring efforts are needed to adequately quantify potential effects of these
factors on fish assemblages. For a monitoring program to adequately address detection,
variability in diel and seasonal patterns must be understood. Studies have been
conducted noting significant diel variation of riverine fish assemblages among their
associated habitats (Arrington and Winemiller 2003, Hoeinghaus et al. 2003, Roach
and Winemiller 2011). Many factors affect diurnal and nocturnal turnover in fish assemblages
and community structure including water temperature, water transparency
or light levels, and resource availability (Helfman 1981, Reid and Mandrak 2009,
Roach and Winemiller 2011). Seasonal effects, primarily driven by temperature, can
also effect the detection of fishes and corresponding assemblage structure. For example,
higher water temperatures enhance fish activity levels and therefore frequently
also yield higher catch rates (Gelos et al. 2010, Gries et al. 1997).
Of the 20 species of conservation concern found in the Mobile system (Mirarchi
et al. 2004), monitoring programs for target species such as Alosa alabamae
(Alabama Shad) and Scaphirhynchus suttkusi (Alabama Sturgeon) are well established.
However, few recent survey efforts have been aimed at documenting trends
in non-game fish assemblages. The objectives of this study were to: 1) provide
current data on fish assemblages found in sand/gravel bar habitat in the Alabama
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River downstream of river mile 72 (Claiborne Lock and Dam), 2) compare current
collections along sand/gravel bar habitat to historic collections to evaluate assemblage
persistence, and 3) assess temporal variability among fish assemblages via
diel and seasonal collections.
Field-Site Description
The Alabama River system (including the Tallapoosa, Coosa, and Cahaba subsystems)
flows through a rich physiographic region with high levels of ichthofaunal
diversity and endemism including 184 native fishes and 33 endemics (Boschung
and Mayden 2004, Freeman et al. 2005). The system includes species that are
federally listed as threatened or endangered such as the Alabama Sturgeon and
Cyprinella caerulea (Blue Shiner) (Freeman et al. 2005). The Alabama River is
formed by the confluence of the Coosa and Tallapoosa rivers just north of Montgomery,
AL. The river flows west to Selma and then southwest until it converges
with the Tombigbee River. The river measures 312 miles in length and is entirely
navigable throughout. The Alabama River has three dams: Claiborne (RM 72.5),
Miller’s Ferry (RM 133), and Jones Bluff (RM 236.2), all of which were installed
to assist with navigation of the river by barges and other watercraft and for power
generation. Currently, the river is maintained at a 9-foot channel depth by periodic
dredging to ensure uninterrupted navigation. The study area is concentrated in the
most free-flowing stretch of the Alabama River, below Claiborne Lock and Dam
(river mile 72.0) on sand/gravel bar habitat.
Methods
Beginning 28 June 2010, we sampled 19 sand/gravel bars from river mile
22.9 to 72.0 of the Alabama River during June–August and October 2010 (Fig. 1,
Appendix 1). Selected sites were sampled during both day and night for diel comparisons,
and fall for seasonal comparison (n = 41). We also resampled selected
sites during April 2011 (n = 3; Fig. 1, Appendix1). Fishes were collected in these
habitats using 15- or 30-m seines (5–10 seine hauls per site). We conducted seining
according to techniques described by Murphy and Willis (1996).
Seine selection and length of each sand/gravel bar haul was dictated by the depth
of the reach and presence of obstructions, but generally ranged between 30–100 m.
We re-sampled selected sites at night and in multiple seasons to monitor diurnal
and seasonal assemblage changes (4 diel samples and 8 seasonal samples). After
each haul, all fish were identified to species, if possible, and enumerated. Those of
conservation concern were recorded and returned to the river. Fish that could not be
identified to species in the field were preserved and transported to the Fish Biodiversity
Lab for further identification; we first anesthetized these specimens in MS 222
(tricane methanesulfonate) prior to preserving them in a 10% formalin solution.
We evaluated long-term temporal variability among fish assemblage structure
by comparing recent collections from this study to significant historic collections
(Shepard et al. 2000; Royal D. Suttkus Fish Collection, Tulane Museum of Natural
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History, New Orleans, LA). Although both of these researchers used seining (thus
sampling gears were equivalent), there was no possible method to standardize effort
among the samples. Furthermore, comparisons with Suttkus’ early samples are
limited because most of the sand/gravel bars he sampled for his long-term study
are no longer present. However limited these comparisons to historical data are, an
examination of assemblage structure is useful for identifying potential homogenization
and other faunal shifts during this time period. Due to potential discrepancies
in effort, we used the Jaccard index for comparisons of current to historical fish assemblage
structure. This metric does not include abundance, which can be strongly
influenced by effort. Current diel and seasonal collections were also made in order
to assess fish assemblage change over short time scales. We compared current, replicated
samples to validate sampling methods.
Jaccard and Morisita indices of similarity were used to compare collections
(Ecological Methodology ver. 7.0). The Morisita index takes species abundance
into account, and we used this analysis for comparisons of our samples, which
Figure 1. Distribution
map of sample sites in
the Alabama River and
associated tributaries.
Site numbers correspond
to Appendix 1.
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2014 Vol. 13, No. 3
were all collected using the same methodology. The Morisita index is a measure of
dispersio n and is used to measure overlap among samples: s
CD = (2Σxiyt) / ([Dx + Dy)XY, i = 1
where xi is the number of times species i is represented in the total X from one
sample, yi is the number of times species i is represented in the total Y from another
sample, and Dx and Dy are Simpson index values for the x and y samples respectively.
The index value ranges from 0 to 1. A value 0 indicates no similarity, or
shared species, between the collections. A value of 1 indicates complete similarity
between the collections (Krebs 1999, Spellerberg 1991).
For historical comparisons, we used the Jaccard index because sampling methods
may have differed between current and historical collections, causing fish
abundance bias. The Jaccard similarity index is a measure of community similarity
and as sesses the presence or absence of species: J = w ,
A + B - w
where w is the number of species common to both samples (or community) and A is
the number of species in sample one and B is the number of species in sample two.
The index value ranges from 0 to 1. A value of 0 indicates no similarity, or shared
species, between the collections. A value of 1 indicates complete similarity between
the collections (Krebs 1999, Spellerberg 1991).
Correspondence analysis (CA) was used to compare the collections of sites 1,
8, and 10. These sites were sampled in three seasons. Correspondence analysis is
a statistical tool used to test the probability of association between variables in
a tabular data set. In this study, CA was used to show how species abundance corresponds
to season. We ran CA for this study using PAST (Paleontological Statistics
Version 2.13).
We employed ArcGIS to measure spatial parameters of the sand/gravel bar
habitats among our sampling area using a projected base layer of the lower Alabama
River watershed from Alabamaview.org, and aerial digital ortho quarter
quads (DOQQs) of our sampling area (river miles 22.9–72.0). We transferred the
projected images (.tiff ) to an appropriate coordinate system and digitized the sand/
gravel bar habitats into polygons.
Using the spatial analysis tool in ArcGIS, we measured the area (acres and
m2) of each digitized sand/gravel bar, and we measured proximity (m) between
neighboring sand/gravel bars with Google Earth (version 6.1.0). Using these
data, we estimated spatial relationships between sand/gravel bars and their associated
fish assemblages.
Pearson’s correlation coefficient and linear regression were used to test the
relationship between sandbar proximity or area and species richness. This correlation
coefficient can measure the strength of linear dependence between two
variables. The coefficient value (r) ranges between -1 and 1. A coefficient value of
r = 1 indicates a perfect positive linear relationship between the two variables. A
correlation coefficient of r = 0 suggests that no correlation exists between the two
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variables. A correlation coefficient of r = -1 indicates a perfect negative correlation,
or inverse linear relationship, between the two variables (Kachigan 1986).
Results
Collections provided unique records for the Alabama River including Brevoortia
patronus (Gulf Menhaden), Fundulus grandis Baird and Girard (Gulf Killifish) and
Menidia beryllina (Inland Silverside), all of which are considered primarily marine
fishes. Gulf Menhaden, a marine clupeid species not previously recorded from our
study area, dominated sand/gravel bar samples. We collected Gulf Menhaden at 12
of 19 sites during our survey (Table 1). The species was absent from the lowermost
sample sites of our survey (Table 1, Fig. 1). Numbers of individuals per sample
ranged from 1 to over 144,000. Higher numbers were collected in the fall (Table 1).
An estimated 393,646 Gulf Menhaden were collected from Alabama River Miles
72–26.3 (Table 1). The presence of such large numbers of one species compounded
comparisons, and current comparisons were made with and without Gulf Menhaden
included (Tables 2, 3).
Morisita index values differed tremendously when collections with large
numbers of Gulf Menhaden were included in the analysis. For example, diel
and seasonal comparisons for site 19 exhibited high similarity including Gulf
Menhaden, and low similarity excluding Gulf Menhaden. Higher Morisita index
values resulted for all seasonal and diel comparisons where Gulf Menhaden were
detected and included in the analysis (Table 2).
Table 1. Number of Gulf Menhaden collected in sand/gravel bar samples in the Alabama River in
2010. Site numbers correspond to locality data in Appendix 1 and to Figure 1.
Summer Fall
Site # Day Night Day Night
19 5649 8159 18,590 495
18 8 0 0 0
17 1 0 0 0
16 4 1 144,464 29,934
15 0 0 109,052 0
14 1 0 0 0
13 1200 0 0 0
12 321 0 0 0
11 16,607 65 420 72
10 2 178 3 36
9 14 0 14,067 0
8 0 0 690 0
7 808 0 2474 0
6 29,195 0 0 0
5 8520 0 0 0
4 2616 0 0 0
3 0 0 0 0
2 0 0 0 0
1 0 0 0 0
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Menhaden were collected in both day and night samples (Tables 1, 2). Standard
lengths (SL; mm) of preserved menhaden were measured to assess their age classes
via length–frequency analysis. While most individuals were age 0 (mean = 54 mm
SL, n = 94), larval specimens were also collected in summer samples (mean = 21
mm SL, n = 13). These lengths fall into year classes described by Lassuy (1983) and
Raynie and Shaw (1994). While age-0 individuals dominated fall samples, larger
individuals (90–100 mm SL) were present in small numbers (n = 10).
Correspondence analyses for the three sites sampled during spring, summer, and
fall showed that species compositions showed a strong seasonality to their structures,
and spring samples showed low faunal similarity to those from summer and
fall seasons (Table 3). Cyprinid species such as Notropis atherinoides (Emerald
Shiner) and Notropis edwardraneyi (Fluvial Shiner) were largely associated with
Table 2. Morisita index values for diel and seasonal comparisons. The index was run for data including
and excluding Gulf Menhaden. Index scores below 0.4 are considered as low similarity comparisons,
those above 0.6 are judged as highly similar.
Day vs Night Summer vs Fall
Site # Summer Fall Day Night
19 With menhaden 0.93 0.93 1.00 0.96
Without menhaden 0.05 0.13 0.25 0.40
16 With menhaden 0.10 1.00 0.06 0.00
Without menhaden 0.01 0.10 0.63 0.36
8 With menhaden 0.08 0.23 0.98 0.65
Without menhaden 0.06 0.14 0.03 0.65
13 With menhaden 0.13 0.37 0.05 0.12
Without menhaden 0.12 0.38 0.05 0.38
10 With menhaden 0.08
Without menhaden 0.03
12 With menhaden 0.56
Without menhaden 0.23
11 With menhaden 0.06
Without menhaden 0.30
7 With menhaden 0.98
Without menhaden 0.18
Table 3. Morisita index values for daytime spring comparisons. The index was run for data including
and excluding Gulf Menhaden. Index scores below 0.4 are considered as low similarity comparisons,
those above 0.6 are judged as highly similar.
Site # Spring vs Summer Spring vs Fall
With Gulf Menhaden
19 0.001 0.000
168 0.003 0.000
1510 0.084 0.000
Without Gulf Menhaden
19 0.125 0.051
168 0.003 0.049
1510 0.084 0.309
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spring samples (Fig. 2). Centrarchid species such as Micropterus henshalli (Alabama
Bass), Micropterus salmoides (Largemouth Bass), and Lepomis megalotis
(Longear Sunfish) corresponded to summer sampling (Fig. 2). Cyprinella venusta
(Blacktail Shiner) showed an association with fall samples.
Overall, fish assemblages differed between day and night on gravel/sand bar
habitat, as indicated by low similarity Morisita index values (excluding Gulf Menhaden;
Tables 2, Appendix 2). This pattern was true for both summer and fall diel
samples (Table 2). Seasonally, sample similarity varied by site, and night samples
tended to be more similar in summer and fall (Table 2). Species such as Ictalurus
furcatus (Blue Catfish) and Ictalurus punctatus (Channel Catfish) were detected in
great numbers (n = 3479) during nighttime hours and rarely collected during day
samples (n = 4) (Appendix 2). Twenty of the 30 Crystal Darters in the samples were
collected during nighttime hours. Hiodon tergisus (Mooneye; n = 2), Lepisosteus
occulatus (Spotted Gar; n = 17), and Lepisosteus osseus (Longnose Gar; n = 2)
were largely collected during nighttime hours in our diel survey (Appendix 2). Riverine
minnows such as Fluvial Shiner and Macrhybopis storeriana (Silver Chub)
were also detected in larger numbers during nighttime hours (Appendix 2). In general,
large numbers of Gulf Menhaden had a negative effect on Shannon diversity
and evenness indices (Appendix 2).
All five comparisons with historical data indicated low faunal similarity (J < 0.5;
Table 4). Current repeated collections at two sites (RM 72 and RM 39.6) resulted in
high faunal similarity (J > 0.9; Table 4). Notable changes in species composition
in current collections included, in addition to Gulf Menhaden, the presence of Blacktail
Shiners in our samples. Fluvial shiners were more abundant in previous collections
and have declined. A current comparison to a historic collection by R.D. Suttkus at Alabama
River Mile 72 shows notable differences in species detected, especially large
Figure 2. Correspondence analysis for seasonal collections (Sites 19, 16, and 15 combined).
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river minnows such as Fluvial Shiner, Silver Chub, and Silverside Shiner. More centrarchid
species were also collected in current collections than historic ones.
Fish species richness did not differ by sand/gravel bar size (Fig. 3). There was
also no relationship between fish species richness and distance to next sand/gravel
bar (Fig. 4).
Discussion
In spite of the limitations with comparisons of current and historical data,
some key temporal shifts in fish community structure and diversity were detected,
including the reduction of some cyprinid species and the presence of cosmopolitan
species in current collections. In addition, seasonal and diel fish assemblage
shifts were documented. However, the size and distance between sand/gravel bars
seems unrelated to fish assemblage structure. New distributional records of three
marine species were also documented (Inland Silverside, Gulf Killifish, and Gulf
Menhaden), including large numbers of Gulf Menhaden.
Figure 3. Richness-area relationship for sand/gravel bar habitat (y = -0.0072x + 1.0629, R2 =
0.00036, P > 0.05).
Table 4. Jaccard’s index of similarity for current samples vs historical samples from the Alabama
River study area from other researchers. GSA = Geological Survey of Alabama and AU = Auburn
University (this study).
Site R.D. Suttkus GSA AU Jaccard’s index
Alabama RM 72 July 1968 July 2010 0.23
Alabama RM 66 August 1989 June 2010 0.15
Alabama RM 60 September 1998 July 2010 0.16
Alabama RM 47 September 1998 July 2010 0.33
Alabama RM 33 July 1964 July 2010 0.11
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The data suggest some homogenization of the fish assemblage in the Alabama
River below RM 72. Natural habitats have been altered in the Alabama River due
to damming and dredging, and many historical sites could not be re-sampled during
our study because the gravel/sand bars were no longer present. All comparisons
with historical data indicated low faunal similarity, suggesting historic fish assemblage
shifts. Rahel (2002) noted that invasion by cosmopolitan species alone can
increase homogenization of an assemblage; however, if the invading species causes
declines in native fauna, the effect is amplified. Notable changes in species composition,
in addition to Gulf Menhaden, include the cosmopolitan Blacktail Shiner.
Historically, this species was not detected in the study area. Native cyprinids, such
as Fluvial Shiners and Macrhybopsis sp. were much more abundant in historical
collections, and current collections show increased numbers of centrarchids, a
group of cosmopolitan species.
Night samples show high similarity in summer and fall, but when excluding Gulf
Menhaden, diel comparisons exhibit very low similarity. Dissimilarity between diel
samples is likely due to high numbers of ictalurid species collected during nighttime
hours. These findings are similar to those of Roach and Winemiller (2011),
who studied diel changeover of fish assemblages on sandbanks of the Brazos River,
TX. Roach and Winemiller (2011) found diel changeover was mostly due to ictalurids
and palaemonids. The authors suggested that these species were moving onto
the sandbanks during nighttime hours to forage, but retreated in diurnal hours to
more complex habitats to avoid predation.
Figure 4. Richness-distance to nearest bar relationship for sand/gravel bar habitat (y =
-0.1063x + 1.3158, R2 = 0.06191, P > 0.05).
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Diel turnover is often conceptualized as a form of resource partitioning, when
species exploit the same resources but use them at different times of the day (Roach
and Winemiller 2011). Predatory species are often more efficient in higher water
temperatures and increased water transparency; consequently, lower water temperatures
at night lead to many species foraging at night when darkness serves as
a refugium (Gelos et al. 2010). Changes in water transparency and ambient light
concentrations at twilight and dawn trigger changeover in fish-assemblage structure
(Arrington and Winemiller 2003, Gelos et al. 2010). In our study, cyprinid
species (Silver Chub, Emerald Shiner, Silverside Shiner, and Fluvial Shiner) were
more abundant in night collections. These species could be utilizing sand/gravel bar
habitats during nighttime hours to avoid predators such as centrarchids. Contrarily,
low transparency may also favor predators that use olfactory and tactile organs to
locate prey (Gelos et al. 2010, Roach and Winemiller 2011). Most gar species in
our study were collected during nighttime hours, which may reflect this type of
resource partitioning.
Fish assemblages varied seasonally. Some species were detected in greater numbers
during fall samples, such as Gulf Menhaden and Crystal Darters, which could
be due to low water levels. Cyprinid species were most abundant in spring collections
and may correspond to increased water levels and lower water temperatures.
However, Ostrand and Wilde (2002) found that fish assemblage structure in the
upper Brazos River, TX, was influenced more by average environmental conditions
of a particular site than seasonal changes overall.
It is not uncommon to find marine species in the Alabama River as far north
as Claiborne Lock and Dam (river mile 72.0), including species such as Trinectes
maculatus (Hogchoker), Paralichthys lethostigma Jordan and Gilbert (Southern
Flounder), Mugil cephalus (Striped Mullet), and Strongylura marina (Atlantic
Needlefish) (Boschung and Mayden 2004). Inland Silversides were collected
throughout the study area, but most were collected below Claiborne Lock and Dam
at Site 1 (RM 72). One Gulf Killifish was also collected at Site 1. Large numbers
of Gulf Menhaden were collected during this study, and are a new distributional
record for the study area (Haley et al. 2010). The exceptionally large numbers of
this species affected assemblage eveness.
Gulf Menhaden is a marine species common to central areas of the Gulf of
Mexico (Hoese and Moore 1977, McEachran and Fechhelm 1998). It is a schooling
species and forms large clusters near the surface supporting purse seine fisheries
throughout the Gulf of Mexico. The Gulf Menhaden fishery is one of the largest by
weight and most valuable in the United States (Christmas et al. 1982, Ross 2001,
Vaughan et al. 2000). This commercially important species is tolerant of a wide
range of salinities, and can be found from offshore areas of the Gulf of Mexico
to the lower reaches of major gulf drainages, including the Tombigbee River and
Tensaw Delta (Boschung and Mayden 2004, Lassuy 1983, Mettee et al. 1996, Ross
2001). Typically, spawning takes place in the open waters of the Gulf of Mexico
in spring and fall (Ahrenholz 1991). Gulf Menhaden produce pelagic eggs, which
hatch into larvae after approximately five days (Raynie and Shaw 1994). Larvae are
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then carried via currents to inshore marshes where they undergo periods of growth
and metamorphosis until they are of juvenile age. As larvae, menhaden selectively
consume zooplankton and phytoplankton, and then transition to non-selective filter
feeders as adults (Ross 2001). Late-stage larvae and early-stage juveniles spend a
variable amount of time in estuarine habitats before migrating offshore into openocean
habitats (Ahrenholz 1991, Deegan 1990, Lassuy 1983).
Due to their life history, the presence of Gulf Menhaden as far as Alabama
River Mile 72 is very unusual. Mettee et al. (1996) recommended sampling for this
species in the lower Alabama River during late summer and times of “saltwater
intrusion”, believing that they might enter these habitats if salinity was high. Although
it is noted that the time spent in estuarine habitats is variable for this species,
and they often move to nearby areas of lower salinity as growth occurs, we would
expect these individuals to migrate back to open sea by fall (Deegan 1990, Fore and
Baxter 1972, Raynie and Shaw 1995). Also, the presence of larval individuals may
be an indication that Gulf Menhaden spawned in the Alabama River. From 17–24
mm SL, Gulf Menhaden are considered to be larval and rely on offshore currents
to carry them to estuarine/marsh habitats (Christmas et al. 1982, Raynie and Shaw
1994, Ross 2001, Vaughan et al. 2000), so it seems unlikely that they migrated upstream
into the Alabama River.
Conclusion
In conclusion, a total of 48 species were collected in our Alabama River survey,
including unique distributional records such as Gulf Menhaden. The presence
of such large numbers of planktivoruos fish in the Alabama River ecosystem is
intriguing. A concern is their possible impact on other native clupeid fishes, including
the rare Alabama Shad, as well as their effect on the food web. Future
work monitoring their persistence and abundance in the Alabama River is important
for assessing any impacts they may have on the ecosystem and its native
fishes. Results of this study indicate changes in native cyprinid abundance and
presence of Blacktail Shiner, and an increase in centrarchids. Diel turnover was
observed on sand/gravel bar habitats. Most notable were the large numbers of
Blue Catfish and Channel Catfish present during nighttime samples. Species corresponded
seasonally and were variable by site.
Ongoing habitat alteration, such as dredging, may have tremendous impacts
on the native fauna in the Alabama River. Fish assemblages in our study area are
becoming homogenized with potential loss of biodiversity. It is recommended that
ongoing monitoring of fish assemblages in the Alabama River downstream of RM
72 be conducted to detect further changes in the fish assemblage. Diel and seasonal
sampling is recommended, when possible, to effectively document fish assemblages
occupying these sand/gravel bars.
Acknowledgments
This study was funded by the US Fish and Wildlife Service, Daphne, AL. We are grateful
to the Alabama Department of Conservation and Natural Resources, Steve Rider, Jeff Powell,
Kyle Bolton, Katie Dowling, Kasie Goodsen, and Amy Rutherford for field assistance.
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2014 Vol. 13, No. 3
Literature Cited
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Appendix 1. Collection locality information for all sites sampled. Collection records include day/night collection, season, GPS of collection site, river
mile, site description, date, ambient temperature, and approximate sampling time. Site numbers correspond to Figure 1.
Day/ River
Site night Season Latitude (°) Longitude (°) Mi. Site Description (°C) Date Gear used Begin time End time
19 Day Summer 31.606766 87.550967 72.0 Downstream of Claiborne Dam 30.0 6/28/10 50' seine 8:25 AM 9:25 AM
19a Day Summer 31.608425 87.551257 72.1 Downstream of Claiborne Dam 32.0 7/8/10 100' seine 9:47 AM 10:50 AM
19b Night Summer 31.607965 87.551087 72.0 Downstream of Claiborne Dam 31.2 7/27/10 100' seine 10:15 PM 12:33 AM
19c Night Fall 31.607564 87.550947 72.0 Downstream of Claiborne Dam 23.1 10/14/10 100' seine 10:30 PM 12:00 AM
19d Day Fall 31.608583 87.550989 72.0 Downstream of Claiborne Dam 24.0 10/15/10 100' seine 1:00 PM 2:20 PM
18 Day Summer 31.567631 87.513743 68.3 Downstream of paper plant 31.3 6/28/10 100' seine 9:47 AM 10:20 AM
18a Day Summer 31.567598 87.513762 68.3 Downstream of paper plant 31.0 7/8/10 30' seine 11:24 AM 12:21 PM
17 Day Summer 31.549879 87.516141 66.9 Upstream of Hwy 84 bridge 33.0 7/8/10 30' seine 12:45 PM 1:05 PM
17a Day Summer 31.547998 87.517645 66.7 At Hwy 84 bridge 33.0 7/8/10 30' seine 1:15 PM 1:45 PM
16 Day Summer 31.523702 87.610241 60.0 Across from Pigeon Creek 32.0 7/8/10 100' seine 2:06 PM 3:15 PM
16a Night Summer 31.523725 87.610925 60.0 Across from Pigeon Creek 31.0 8/2/10 100' seine 10:30 PM 11:45 PM
16b Nght Fall 31.523681 87.610989 60.0 Across from Pigeon Creek 23.0 10/14/10 100' seine 8:00 PM 9:26 PM
16c Day Fall 31.523841 87.610255 60.0 Across from Pigeon Creek 24.0 10/15/10 100' seine 10:55 AM 12:25 PM
15 Day Summer 31.508194 87.615469 58.3 Mrs. Grey's Bar right bank 32.0 7/8/10 100' seine 3:55 PM 4:55 PM
(downstream)
15a Day Fall 31.508480 87.615571 58.3 Mrs. Grey's Bar right bank 23.3 10/14/10 100' seine 5:30 PM 6:40 PM
(downstream)
14 Day Summer 31.382167 87.717499 40.3 Across from Euryka Landing 31.5 7/9/10 100' seine 8:20 AM 9:13 AM
13 Day Summer 31.371523 87.725739 39.3 Downstream and across from 31.7 7/9/10 50' seine 9:20 AM 10:15 AM
Irvin Creek
13a Night Summer 31.369525 87.726053 39.2 downstream and across from 30.6 8/10/10 50' seine 12:05 AM 1:46 AM
Irvin Creek
13b Day Summer 31.369839 87.726100 39.2 Downstream and across from 32.5 8/10/10 50' seine 11:45 AM 12:16 PM
Irvin Creek
13c Night Fall 31.370694 87.726122 39.2 Downstream and across from 22.5 10/15/10 50' seine 7:20 PM 8:45 PM
Irvin Creek
13d Day Fall 31.370718 87.726146 39.2 Downstream and across from 22.1 10/16/10 50' seine 11:16 AM 12:15 PM
Irvin Creek
12 Day Summer 31.336299 87.751640 35.4 Choctaw Bluff 33.4 7/9/10 100' seine 10:36 AM 11:20 AM
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Day/ River
Site night Season Latitude (°) Longitude (°) Mi. Site Description (°C) Date Gear used Begin time End time
12a Day Fall 31.336819 87.752356 35.4 Upstream of Choctaw Bluff 24.0 10/15/10 100' seine 4:45 PM 6:25 PM
11 Day Summer 31.363272 87.756877 33.3 Choctaw Bluff (east bank) 36.5 7/9/10 100' seine 12:00 PM 12:36 PM
11a Day Fall 31.363176 87.755872 33.3 Choctaw Bluff (east bank) 26.2 10/16/10 100' seine 12:55 PM 1:45 PM
10 Day Summer 31.414326 87.627276 47.0 Shackleford Bar and English 31.5 7/26/10 30' seine 10:50 AM 12:20 PM
Landing
10a Day Summer 31.416228 87.630366 47.0 Shackleford Bar and English 31.5 7/26/110 50' seine 10:50 AM 12:20 PM
Landing
9 Day Summer 31.424393 87.640235 46.4 Frenchs Landing and English 31.0 7/26/10 50' seine 9:00 AM 10:30 AM
Landing
8 Day Summer 31.377482 87.721757 39.6 Upstream of Irvin Creek 34.5 7/26/110 100' seine 1:52 PM 3:20 PM
8a Night Summer 31.380454 87.718138 39.6 Upstream of Irvin Creek 31.5 8/9/10 100' seine 8:45 PM 11:55 PM
8b Day Summer 31.380648 87.717944 39.6 Upstream of Irvin Creek 33.5 8/10/10 100' seine 10:30 AM 11:28 AM
8c Night Fall 31.379762 87.718719 39.6 Upstream of Irvin Creek 21.2 10/15/10 100' seine 9:00 PM 10:15 PM
8d Day Fall 31.379856 87.718624 39.6 Upstream of Irvin Creek 22.8 10/16/10 100' seine 10:00 AM 11:15 AM
7 Day Summer 31.340333 87.772578 31.6 Sandbar (Island) ≈1.3 mi below 31.4 7/27/10 50' seine 8:49 AM 9:55 AM
Choctaw Bluff
7a Day Fall 31.339600 87.77209 31.6 Sandbar (Island) ≈1.3 mi below 26.1 10/16/10 100' seine 2:00 PM 3:05 PM
Choctaw Bluff
6 Day Summer 31.327761 87.784254 29.9 0.8 mi downstream from 31.6 7/27/10 100' seine 10:01 AM 11:12 AM
Matthewsons Bar
5 Day Summer 31.303009 87.775094 28.4 Dixie Landing 33.0 7/27/10 100' seine 12:00 PM 1:15 PM
4 Day Summer 31.297774 87.785475 26.3 Dixie Cutoff and Monroe Point 32.5 7/27/10 100' seine 1:30 PM 3:30 PM
3 Day Summer 31.295258 87.795414 25.5 Downstream of Monroe Point 34.5 8/2/10 100' seine 10:47 AM 12:24 PM
2 Day Summer 31.276208 87.784050 24.0 Alabama River Sandbar 33.5 8/2/10 50' seine 1:00 PM 1:45 PM
1 Day Summer 31.268720 87.802023 22.9 Earl Bar 33.5 8/2/10 50' seine 2:05 PM 2:20 PM
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Appendix 2. Diel and seasonal collection data for selected sites. Site numbers correspond with Appendix 1 and Figure 1.
Site 19 Site 16
(31.606766°, 87.550967°) (31.523725°, 87.610925°)
Spring Summer Fall Spring Summer Fall
Species Day Day Night Day Night Day Day Night Day Night
Polyodon spathula (Walbaum) (Paddlefish) 1
Atractosteus spatula (Lacepède) (Alligator Gar) 1
Lepisosteus oculatus Winchell (Spotted Gar) 13 1 2
Lepisosteus osseus (L.) (Longnose Gar) 1 1
Hiodon tergisus Lesueur (Mooneye) 1 1
Anchoa mitchilli (Valenciennes) (Bay Anchovy) 2 9
Alosa chrysochloris (Rafinesque) (Skipjack Herring) 2 15 2 4 1 1
Brevoortia patronus Goode (Gulf Menhaden) 4042 8159 18,590 495 4 1 144,464 29,934
Dorosoma cepedianum (Lesueur) (Gizzard Shad) 2 25 25 15 1 4 8 29 15
Dorosoma petenense (Günther) (Threadfin Shad) 83 2593 6 41 23 6 3 3
Campostoma oligolepis Hubbs and Greene (Largescale Stoneroller) 1
Cyprinella venusta Girard (Blacktail Shiner) 9 2 106 1 1 8 1 2 3
Hybognathus nuchalis Agassiz (Mississippi Silvery Minnow) 3
Macrhrybopsis aestivalis (Girard) (Speckled Chub)
Macrhrybopsis storeriana (Kirtland) (Silver Chub) 13 112 7 1 47 19
Notropis atherinoides Rafinesque (Emerald Shiner) 8 2 167 2 8
Notropis candidus Suttkus (Silverside Shiner) 30 119 13 2 109 6
Notropis edwardraneyi Suttkus and Clemmer (Fluvial Shiner) 9 1 5 38 14 84
Notropis uranoscopus Suttkus (Skygazer Shiner)
Pimephales vigilax Baird and Girard (Bullhead Minnow)
Carpiodes cyprinus (Lesueur) (Quillback)
Carpiodes velifer (Rafinesque) (Highfin Carpsucker) 2 2 1 1
Moxostoma poecilurum Jordan (Blacktail Redhorse) 1 1
Ictalurus furcatus (Lesueur) (Blue Catfish) 88 16 2
Ictalurus punctatus (Rafinesque) (Channel Catfish) 37 41 256 31
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Site 19 Site 16
Spring Summer Fall Spring Summer Fall
Species Day Day Night Day Night Day Day Night Day Night
Pylodictis olivaris (Rafinesque) (Flathead Catfish) 1
Mugil cephalus L. (Striped Mullet) 4 1 10 3 8 2 2 2
Menidia beryllina (Cope) (Inland Silverside) 1 1 1
Strongylura marina (Walbaum) (Atlantic Needlefish) 73 8 9 1 2
Gambusia affinis (Baird and Girard) (Western Mosquitofish) 1
Gambusia holbrooki Girard (Eastern Mosquitofish) 2
Morone chrysops (Rafinesque) (White Bass) 33 2 11 2
Morone chrysops x saxatilis 2
Morone mississippiensis Jordan and Eigenmann (Yellow Bass) 2
Morone saxatilis (Walbaum) (Striped Bass) 7 104 1 20 22 10
Morone sp. (hybrid) 1
Lepomis macrochirus Rafinesque (Bluegill) 1 8 9 2 32 13 42 1
Lepomis megalotis (Rafinesque) (Longear Sunfish) 7 1 1 19 1
Lepomis microlophus (Günther) (Redear Sunfish) 1
Micropterus henshalli Hubbs and Bailey (Alabama Bass) 1 12 2 2
Micropterus salmoides (Lacepède) (Largemouth Bass) 4 1
Pomoxis annularis Rafinesque (White Crappie)
Pomoxis nigromaculatus (Lesueur) (Black Crappie) 1 1 3
Ammocrypta beani Jordan (Naked Sand Darter)
Crystallaria asprella (Jordan) (Crystal Darter) 1 7 6 1 1 2
Percina kathae Thompson (Mobile Logperch)
Aplodinotus grunniens Rafinesque (Freshwater Drum) 3 66 2
Trinectes maculatus (Blotch and Schneider) (Hogchoker) 1 3 42 1 1 3 1
Species richness 5 15 13 12 17 9 21 21 9 22
Shannon diversity 0.92 0.16 1.82 2.16 2.22 0.77 2.44 1.68 0.00 2.21
Evenness 0.50 0.07 0.47 0.72 0.54 0.24 0.54 0.25 0.11 0.41
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Site 15 Site 8
(31.50848°, 87.615571°) (31.370718°, 87.726146°)
Spring Summer Fall Summer Fall
Species Day Day Day Day Night Day Night
Polyodon spathula (Paddlefish)
Atractosteus spatula (Alligator Gar)
Lepisosteus oculatus (Spotted Gar) 1
Lepisosteus osseus (Longnose Gar) 1
Hiodon tergisus (Mooneye)
Anchoa mitchilli (Bay Anchovy) 1
Alosa chrysochloris (Skipjack Herring) 1
Brevoortia patronus (Gulf Menhaden) 109,052 4328 65 420 72
Dorosoma cepedianum (Gizzard Shad) 1 4 6 35 1
Dorosoma petenense (Threadfin Shad) 643 50 1
Campostoma oligolepis (Largescale Stoneroller) 1
Cyprinella venusta (Blacktail Shiner) 15 41 25 17 10 63
Hybognathus nuchalis (Mississippi Silvery Minnow) 1
Macrhrybopsis aestivalis (Speckled Chub) 1
Macrhrybopsis storeriana (Silver Chub) 4 21 82 10 150
Notropis atherinoides (Emerald Shiner) 162 9 5 14
Notropis candidus (Silverside Shiner) 28 177 39
Notropis edwardraneyi (Fluvial Shiner) 23 3 1 20
Notropis uranoscopus (Skygazer Shiner) 1
Pimephales vigilax (Bullhead Minnow) 4 1
Carpiodes cyprinus (Quillback) 1
Carpiodes velifer (Highfin Carpsucker) 21 24 13 72
Moxostoma poecilurum (Blacktail Redhorse)
Ictalurus furcatus (Blue Catfish) 520 21
Ictalurus punctatus (Channel Catfish) 1 469 200
Pylodictis olivaris (Flathead Catfish) 1
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Site 15 Site 8
Spring Summer Fall Summer Fall
Species Day Day Day Day Night Day Night
Mugil cephalus (Striped Mullet) 5
Menidia beryllina (Inland Silverside)
Strongylura marina (Atlantic Needlefish) 2 1
Gambusia holbrooki (Eastern Mosquitofish)
Morone chrysops (White Bass)
Morone chrysops x saxatilis
Morone mississippiensis (Yellow Bass)
Morone saxatilis (Striped Bass) 2 9 10
Morone sp. (hybrid)
Lepomis macrochirus (Bluegill) 12 6 10 68
Lepomis megalotis (Longear Sunfish) 4 1
Lepomis microlophus (Redear Sunfish)
Micropterus henshalli Hubbs and Bailey (Alabama Bass) 7 2 5 4 3
Micropterus salmoides (Lacepède) (Largemouth Bass) 1
Pomoxis annularis (White Crappie) 1
Pomoxis nigromaculatus (Black Crappie) 2
Ammocrypta beani (Naked Sand Darter) 5
Crystallaria asprella (Crystal Darter) 1
Percina kathae (Mobile Logperch) 2 1 9
Aplodinotus grunniens (Freshwater Drum) 1 34 3
Trinectes maculatus (Hogchoker) 2 4 22 3
Species richness 8 7 12 13 23 6 19
Shannon diversity 1.05 1.29 0.00 0.47 1.93 0.64 1.95
Evenness 0.35 0.52 0.08 0.12 0.30 0.31 0.37
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Site 13 Site 12
(31.380454°, 87.718138°) (31.336299°, 87.75164°)
Summer Fall Summer Fall
Species Day Night Day Night Day Day
Polyodon spathula (Paddlefish)
Atractosteus spatula (Alligator Gar)
Lepisosteus oculatus (Spotted Gar)
Lepisosteus osseus (Longnose Gar)
Hiodon tergisus (Mooneye)
Anchoa mitchilli (Bay Anchovy) 3 30 322 286 152
Alosa chrysochloris (Skipjack Herring)
Brevoortia patronus (Gulf Menhaden) 2 178 3 36 14 14,067
Dorosoma cepedianum (Gizzard Shad) 6 6 1 1 6
Dorosoma petenense (Threadfin Shad) 65 59
Campostoma oligolepis (Largescale Stoneroller)
Cyprinella venusta (Blacktail Shiner) 21 7 20 7 7
Hybognathus nuchalis (Mississippi Silvery Minnow)
Macrhrybopsis aestivalis (Speckled Chub)
Macrhrybopsis storeriana (Silver Chub) 66 98 7 30 1 22
Notropis atherinoides (Emerald Shiner) 31 96 19 8 2
Notropis candidus (Silverside Shiner) 16 50 162 21
Notropis edwardraneyi (Fluvial Shiner) 1 7 50
Notropis uranoscopus (Skygazer Shiner)
Pimephales vigilax (Bullhead Minnow) 1 1 12
Carpiodes cyprinus (Quillback) 1
Carpiodes velifer (Highfin Carpsucker) 28 3 5 8 46
Moxostoma poecilurum (Blacktail Redhorse)
Ictalurus furcatus (Blue Catfish) 1 942 1
Ictalurus punctatus (Channel Catfish) 102 3 753 10
Mugil cephalus (Striped Mullet) 1
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Site 13 Site 12
Summer Fall Summer Fall
Species Day Night Day Night Day Day
Menidia beryllina (Inland Silverside) 1 1
Strongylura marina(Atlantic Needlefish) 3
Gambusia affinis (Western Mosquitofish)
Gambusia holbrooki (Eastern Mosquitofish)
Morone chrysops (White Bass) 2 4
Morone chrysops x saxatilis
Morone mississippiensis (Yellow Bass)
Morone saxatilis (Striped Bass) 1 4 1 8
Morone sp. (hybrid)
Lepomis macrochirus (Bluegill) 1 1 3 2
Lepomis megalotis (Longear Sunfish) 1
Lepomis microlophus (Redear Sunfish)
Micropterus henshalli (Alabama Bass) 1 1 1
Micropterus salmoides (Largemouth Bass) 1 1 3
Pomoxis annularis (White Crappie)
Pomoxis nigromaculatus (Black Crappie) 1 1
Ammocrypta beani (Naked Sand Darter)
Crystallaria asprella (Crystal Darter)
Percina kathae (Mobile Logperch)
Aplodinotus grunniens (Freshwater Drum) 4 1
Trinectes maculatus (Hogchoker) 2 2 4 40 1 188
Species richness 12 20 13 14 12 17
Shannon diversity 1.64 1.48 0.97 1.37 2.03 0.21
Evenness 0.42 0.21 0.20 0.28 0.63 0.07
Southeastern Naturalist
T.H. Haley and C.E. Johnston
2014 Vol. 13, No. 3
570
Site 11 (31.363176°, 87.755872°) Site 7 (31.3396°, 87.77209°)
Summer Fall Summer Fall
Species Day Day Day Day
Polyodon spathula (Paddlefish)
Atractosteus spatula (Alligator Gar)
Lepisosteus oculatus (Spotted Gar)
Lepisosteus osseus (Longnose Gar)
Hiodon tergisus (Mooneye)
Anchoa mitchilli (Bay Anchovy)
Alosa chrysochloris 2 3
(Skipjack Herring) 6
Dorosoma cepedianum (Gizzard Shad) 690 808 2474
Dorosoma petenense (Threadfin Shad) 4 6 6
Campostoma oligolepis (Largescale Stoneroller) 87
Cyprinella venusta (Blacktail Shiner)
Hybognathus nuchalis (Mississippi Silvery Minnow) 2 43 37 30
Macrhrybopsis aestivalis (Speckled Chub)
Macrhrybopsis storeriana (Silver Chub)
Notropis atherinoides (Emerald Shiner) 58 9 166
Notropis candidus (Silverside Shiner) 7 31 3
Notropis edwardraneyi (Fluvial Shiner) 1
Notropis uranoscopus (Skygazer Shiner) 3 4
Pimephales vigilax (Bullhead Minnow)
Carpiodes cyprinus (Quillback)
Carpiodes velifer (Highfin Carpsucker)
Moxostoma poecilurum (Blacktail Redhorse) 1 130 13 362
Ictalurus furcatus (Blue Catfish)
Ictalurus punctatus (Channel Catfish) 1
Pylodictis olivaris (Flathead Catfish)
Mugil cephalus (Striped Mullet)
Southeastern Naturalist
571
T.H. Haley and C.E. Johnston
2014 Vol. 13, No. 3
Site 11 Site 7
Summer Fall Summer Fall
Species Day Day Day Day
Menidia beryllina (Inland Silverside)
Strongylura marina (Atlantic Needlefish)
Gambusia affinis (Western Mosquitofish)
Gambusia holbrooki (Eastern Mosquitofish) 1 1
Morone chrysops (White Bass)
Morone chrysops x saxatilis
Morone mississippiensis (Yellow Bass)
Morone saxatilis (Striped Bass)
Morone sp. (hybrid)
Lepomis macrochirus (Bluegill) 1 1
Lepomis megalotis (Longear Sunfish)
Lepomis microlophus (Redear Sunfish) 4 1
Micropterus henshalli (Alabama Bass) 2
Micropterus salmoides (Largemouth Bass)
Pomoxis annularis (White Crappie) 1 2 3
Pomoxis nigromaculatus (Black Crappie)
Ammocrypta beani (Naked Sand Darter)
Crystallaria asprella (Crystal Darter)
Percina kathae (Mobile Logperch)
Aplodinotus grunniens (Freshwater Drum)
Trinectes maculatus (Hogchoker)
Species richness 5 12 12 13
Shannon diversity 1.44 0.99 0.81 0.71
Evenness 0.84 0.22 0.18 0.15