2012 NORTHEASTERN NATURALIST 19(3):475–486
Tidal Migrations of Intertidal Salt Marsh Creek Nekton
Examined with Underwater Video
Matthew E. Kimball1,2, 3,* and Kenneth W. Able3
Abstract - Nekton tidal migration patterns were examined in oligo-mesohaline intertidal
salt marsh creeks using underwater video observations collected throughout multiple tidal
cycles (i.e., flood–ebb) during summer 2005–2006. Underwater video observations indicated
that species composition and abundances varied with tide stage. Three intertidal salt
marsh species (Fundulus heteroclitus, Morone americana, Menidia menidia) were the most
abundant species observed. In general, resident species were most abundant in early flood
and late ebb tide stages, whereas transient species were most abundant around slack high
tide. F. heteroclitus displayed a consistent symmetrical tidal migration pattern and primarily
occurred in early flood and late ebb tide stages. M. americana occurred throughout flood and
high tides, but were largely absent from intertidal creeks during ebb tide. M. menidia was
observed during all tide stages, but displayed no distinct migration patterns. The results of
this study highlight the advantages and disadvantages of using underwater video for examining
small-scale tidal migrations of nekton in intertidal salt marsh creeks.
Introduction
Salt marshes are a mosaic of multiple interconnected habitats that include the
vegetated marsh surface, marsh ponds and pools, intertidal and subtidal creeks,
and open-water habitats (Minello et al. 2003, Rountree and Able 2007). During
periods of tidal inundation, intertidal creeks function as an important physical
and biological corridor linking marsh surface with subtidal habitats (McIvor and
Odum 1988, Rozas et al. 1988). Nekton utilization of salt marsh habitats varies
temporally and spatially relative to physical and biological factors such as tidal
cycle and species-specifi c migration patterns (Cattrijsse and Hampel 2006, Kneib
1997, Rozas 1995). In general, nekton migrate or follow the tide as it rises (i.e.,
floods), thereby gaining access to highly productive intertidal marsh surface areas,
then similarly follow the ebbing tide as waters recede into subtidal habitats.
Beyond this widely accepted general pattern, however, information is lacking to
describe tidal migration patterns for many species commonly found in intertidal
salt marsh creeks.
The majority of studies on intertidal salt marsh creek nekton have focused on
a single tide stage (e.g., high tide) or a large consolidated portion of the tidal cycle
(e.g., ebb tide) (Bozeman and Dean 1980; Cain and Dean 1976; Desmond et al.
2000; Jin et al. 2007, 2010; Koutsogiannopoulou and Wilson 2007; LeQuesne
2000; Paterson and Whitfi eld 1996, 2000, 2003; Quan et al. 2009; Reis and Dean
1GTM National Estuarine Research Reserve, 505 Guana River Road, Ponte Vedra Beach,
fl32082. 2Department of Biology, University of North Florida, 1 UNF Drive, Jacksonville,
fl32224. 3Marine field Station, Institute of Marine and Coastal Sciences, Rutgers
University, 800 c/o 132 Great Bay Boulevard, Tuckerton, NJ 08087. *Corresponding
author - m.kimball@unf.edu.
476 Northeastern Naturalist Vol. 19, No. 3
1981; Shenker and Dean 1979). Relatively few studies have examined the distribution
and habitat utilization of nekton in intertidal creeks on smaller temporal and
spatial scales throughout tidal cycles (but see Bretsch and Allen 2006b, Cattrijsse
et al. 1994, Hampel et al. 2003, Salgado et al. 2004). The diffi culties associated
with sampling nekton in salt marshes (e.g., highly dynamic environmental conditions),
along with the limitations of traditional sampling gears (e.g., block nets,
seines, fyke nets), often limit the scale (both temporal and spatial) and scope of
examination possible in various salt marsh habitats, including intertidal creeks
(Connolly 1999, Rozas and Minello 1997). Recently, underwater video has been
successfully used in shallow (less than 1.5 m) salt marsh habitats (e.g., fringing intertidal
mangrove, shallow patches in open estuarine waters, salt marsh ditches) to examine
fi sh behavior (Becker et al. 2010, Ellis and Bell 2008, James-Pirri et al. 2010).
In this study, we used underwater video to examine small-scale tidal migration patterns
of nekton in intertidal salt marsh creeks throughout the tidal cycle to elucidate
nekton behavior and habitat use that may have heretofore been overlooked or unobservable
using traditional sampling gears.
Methods
field-site description
Sampling occurred in the oligo-mesohaline salt marshes in the Hog Islands area
of the Mullica River–Great Bay estuary (39°34'46.35"N, 74°31'52.20"W), which
is part of the Jacques Cousteau National Estuarine Research Reserve (JCNERR)
located in southern New Jersey. Intertidal marsh areas were characterized by
semi-diurnal tides and marsh vegetation consisting of a mix of species including
(all species names from United States Department of Agriculture Plant Database,
http://plants.usda.gov/java/): Atriplex patula L. (Spear Saltbush), Pluchea odorata
(L.) Cass. var. succulenta (Fernald) Cronquist (Sweetscent), Schoenoplectus
maritimus (L.) Lye (Cosmopolitan Bulrush), Spartina alterniflora Loisel (Smooth
Cordgrass), S. patens (Aiton) Muhl. (Saltmeadow Cordgrass), and large interspersed
stands of Phragmites australis (Cav.) Trin. ex Steud. (Common Reed).
field sampling
Intertidal creeks sampled (n = 4 creeks) had similar widths (mean width at
mouth = 3.4 m, SE = 0.3) and lengths (mean length = 75.7 m, SE = 13.1), and
all creeks had soft mud substrate bottoms with a few remaining pools of water
at low tide. Average water depth at slack high tide in all creeks was <1 m. All
creeks had a similar degree of sinuosity, terminated on the high marsh, and were
unconnected to other creeks at high tide.
To observe nekton, an underwater video sampling system was positioned upstream
of the mouth of each creek (mean distance from creek mouth = 19.4 m,
SE = 3.5), consisting of a flume (fig. 1), low-light black-and-white camera (2.8
mm, f2.8 wide-angle lens, 0.27 Lux), self-contained video recorder, and battery.
To guide intertidal creek nekton past the camera, the flume was constructed in
an "X" shape with a center channel (length x width x depth = 0.9 x 0.4 x 0.9 m)
and four wings (1.2 x 0.9 m) extending onto the marsh surface at approximately
45° angles. The flume frame was constructed of PVC piping, and cloth mesh
2012 M.E. Kimball and K.W. Able 477
(3.2 mm) was used for the walls of the wings and one side of the center channel
(i.e., the camera side). The wall opposite from the camera consisted of a solid
sheet of white plastic to provide a contrasting background that enhanced nekton
identifi cation (e.g., Daum 2005). The camera was placed 30 cm above the creek
bottom with the lens inserted through the mesh and positioned flush with the
channel wall. In this confi guration, the water column from approximately 15–50
cm could be observed (fi eld of view at distance of 40 cm: 45 x 35 x 52 cm). Once
constructed, flumes were left in place in all creeks for the duration of the study,
while video equipment was moved among sampling sites.
In order to determine nekton abundance throughout the tidal cycle, each intertidal
creek was sampled with underwater video during consecutive flood and ebb
tides. To coincide with periods of high abundance for the dominant salt marsh
nekton species in Mid-Atlantic Bight estuaries (Able and Fahay 2010), sampling
occurred monthly in late summer: from August to September in 2005 (n = 8 tidal
cycles) and from July through September in 2006 (n = 10 tidal cycles). During
daylight hours of each sampling day, two creeks were sampled, flood through
ebb tide, for a total of 18 tidal cycles observed. On each sampling day, prior to
tidal inundation, the camera, recorder, and battery were integrated with the flume
in each creek. Video recording began when the camera was totally submerged
on the flood tide and continued uninterrupted until the camera emerged during
ebb tide. Surface temperature and salinity were measured in individual creeks,
figure 1. Overhead diagram of video sampling system flume in an intertidal creek (video
recorder and battery are not pictured). The camera backdrop is indicated by the solid
line. Dashed lines indicate mesh walls. Arrows indicate the creek center channel flow
directions.
478 Northeastern Naturalist Vol. 19, No. 3
at slack high tide, with a handheld meter (YSI model 85): temperature (n = 18),
but not salinity (n = 15), was recorded for each tidal cycle. Turbidity (NTU) was
measured with a nearby datasonde (Lower Bank) deployed as part of the System-
Wide Monitoring Program at JCNERR (data made available from the NERRS
Central Data Management Offi ce).
Data analysis
Each video record was viewed completely, and all individuals observed in
each 1-min increment were identifi ed and enumerated. Because of low abundances
and patchiness of migrating individuals, sub-sampling at time increments
>1 min was not feasible. To examine nekton tidal utilization patterns, video footage
also was segmented by tidal stage. We divided each complete flood (beginning of
recording to slack high tide) and ebb (slack high tide to end of recording) tide into 8
tide stages of equal length (flood: tide stages 1–8, mean duration = 25 min, SE = 1;
ebb: tide stages 9–16, mean duration = 20 min, SE = 1). In each tide stage (1–16), the
counts (i.e., number of individuals of a given species) from each 1-min increment
were summed by species. This protocol removed the time component within the
tidal cycle and provided species totals for each of the 16 tide stages.
Because the purpose of this study was to examine fi sh behavior in intertidal
creeks throughout the tidal cycle, we sought to minimize the influence of sometimes
highly variable site-specifi c differences in nekton species abundances
on statistical analyses. Therefore, species abundance for individual tide stages
was expressed as a fraction of the maximum tide-stage abundance observed for
that species during an entire tidal cycle (i.e., individual tide-stage abundance/
maximum tide-stage abundance) (e.g., Ellis and Bell 2008). Thus, regardless
of the total number of individuals observed for a given species during any tidal
cycle, abundance values for each tide stage ranged from 0 to 1 (Ellis and Bell
2008). Using this calculation allows us to treat each tidal cycle as independent,
and therefore compare nekton tidal behavior among the observed tidal cycles to
examine the consistency of migration patterns. For each tidal cycle, mean species
tide-stage abundance values were calculated for three tide classes: flood, stages
1–6; high, 7–10; ebb, 11–16. Tide class abundance data for 18 tidal cycles was
then analyzed with a repeated measures analysis of variance (PROC GLM; SAS
2003). Differences in tide class abundances (the repeated factor) were analyzed
with individual contrasts (von Ende 2001). Only species with a total abundance
≥ 75 individuals for all tidal cycles combined were analyzed (n = 3 species; this
analysis included 98% of all individuals observed with underwater video during
this study; see Table 1). Individual species were assigned to an estuarine category
(i.e., resident, transient, freshwater) (Able and Fahay 1998, 2010; Arndt 2004).
Environmental and water quality data were examined with descriptive statistics.
Results
A total of 109.5 h of underwater video data from intertidal marsh creeks
recorded over 18 tidal cycles was reviewed for analysis. During fi eld recordings,
temperatures were similar between years (mean temperatures: 2005 = 26.4
°C, SE = 0.04; 2006 = 25.7 °C, SE = 1.0). Salinities were lower in 2006 (mean
2012 M.E. Kimball and K.W. Able 479
salinity = 5.6, SE = 1.3) than in 2005 (mean salinity = 11.9, SE = 0.6). Turbidities
were lower in 2005 (mean turbidity = 5.1 NTU, SE = 1.8) than in 2006 (mean
turbidity = 14.4, SE = 7.4).
Based on underwater video data, fi shes dominated the intertidal creek nekton
with 9 species and 5679 individuals out of a total of 11 species and 5722 individuals
observed (Table 1). Callinectes sapidus Rathbun (Blue Crab) (n = 35)
and Malaclemys terrapin Schoepff (Diamondback Terrapin) (n = 8) were also
observed during the study. Four resident marsh nekton species accounted for
88% of the total, and most (87%) of these individuals were Fundulus heteroclitus
L. (Mummichog). Other resident marsh nekton included Morone americana
Gmelin (White Perch), Gobiosoma bosc Lacepède (Naked Goby), and M. terrapin.
five transient marsh nekton species made up 11% of the total. These
were primarily Menidia menidia L. (Atlantic Silverside; 9%), but also included
C. sapidus, Brevoortia tyrannus Latrobe (Atlantic Menhaden), Pomatomus saltatrix
L. (Bluefi sh), and Anguilla rostrata Lesueur (American Eel). Two freshwater
species, Ameiurus nebulosus Lesueur (Brown Bullhead) and Notemigonus crysoleucas
Mitchill (Golden Shiner), were infrequently observed and represented
only 1% of the total. Shrimps were infrequently observed in video recordings and
were not reported on in this study.
Species composition and abundance, as observed by underwater video, were
influenced by tide stage (fig. 2). The number of species observed during flood
(n = 10 species) and ebb (n = 11 species) tide stages was similar, but resident
nekton dominated (>75%) early flood tide stages (1–3) and most ebb tide stages
(10–16). Transient nekton were most abundant in the late flood tide stages (4–8;
Table 1. Intertidal creek nekton species composition and abundance (number of nekton per tidal
cycle, expressed as catch-per-unit-effort, CPUE, with standard error, along with the maximum
number of individuals per an entire tidal cycle and the overall total number of individuals) observed
with underwater video during 18 tidal cycles. Each species was assigned to an estuarine category
(EC): estuarine resident (R), estuarine transient (T), or freshwater (F). The relative abundance of
estuarine resident, estuarine transient, and freshwater species is indicated as a percentage of the
total abundance.
Species EC CPUE SE Max Total
Ameiurus nebulosus F 0.78 0.78 14 14
Anguilla rostrata T 0.17 0.12 2 3
Brevoortia tyrannus T 1.67 0.91 16 30
Callinectes sapidus T 1.94 0.43 6 35
Fundulus heteroclitus R 277.11 107.32 1513 4988
Gobiosoma bosc R 0.06 0.06 1 1
Malaclemys terrapin R 0.44 0.20 3 8
Menidia menidia T 28.89 13.41 170 520
Morone americana R 4.17 1.41 19 75
Notemigonus crysoleucas F 1.61 1.55 28 29
Pomatomus saltatrix T 1.06 0.48 8 19
All species combined 317.89 107.70 1517 5722
Resident species 88%
Transient species 11%
Freshwater species 1%
480 Northeastern Naturalist Vol. 19, No. 3
maximum = 82% at stage 8) and the earliest ebb tide stage (9), when water depths
were greatest.
Tidal migration patterns were determined for the three most abundant intertidal
creek species: F. heteroclitus, M. menidia, and M. americana (fig. 3).
F. heteroclitus abundance in intertidal creeks varied by tide stage (Wilks’ Lambda:
F2,16 = 11.82, P = 0.0007), and generally followed a symmetrical tidal migration
pattern with greater abundances in flood and ebb tides, and almost no individuals
detected in the flume during high tide. Flood tide (F1,17 = 8.23, P = 0.0106)
and ebb tide (F1,17 = 19.48, P = 0.0004) abundances were greater than high tide
abundances, while flood and ebb tide abundances were not signifi cantly different
(F1,17 = 2.50, P = 0.1324). M. menidia abundance was unaffected by tide stage
(Wilks’ Lambda: F2,16 = 0.25, P = 0.7784) and displayed no distinct intertidal
creek migration patterns throughout flood, high, and ebb tides. M. americana
intertidal creek abundance varied by tide stage (Wilks’ Lambda: F2,16 = 5.59,
P = 0.0144), with individuals occurring throughout flood and high tides, and
largely absent from the area near the mouth of the intertidal creeks during ebb
tide. Both flood (F1,17 = 5.09, P = 0.0375) and high (F1,17 = 11.54, P = 0.0034)
tide abundances were greater than those observed for ebb tide, but M. americana
abundance at high tide was not signifi cantly different from flood tide (F1,17 = 4.15,
P = 0.0576).
Discussion
Underwater video has been used successfully in a variety of aquatic habitats
(Becker et al. 2010, Burrows et al. 1999, Ellis and Bell 2008, James-Pirri et al.
2010, Jury et al. 2001, Mueller et al. 2006), and was an effective method for examining
nekton behavior in these intertidal salt marsh creeks. Underwater video
allowed the observation of small-scale nekton utilization patterns (e.g., multiple
tide stages within flood and ebb tides) with minimal disturbance to the animals
or habitat, much reduced labor intensity (e.g., 1 person), and minimal time constraints.
Such observations are diffi cult (or impossible) to detect when sampling
figure 2. Percentage of estuarine resident, estuarine transient, and freshwater species in
relation to total abundance (all tidal cycles combined) per individual tide stage (1–16).
Slack high tide occurred between tide stages 8 and 9 (indicated by vertical dashed line).
2012 M.E. Kimball and K.W. Able 481
figure 3. Tidal migration patterns (mean species abundance with standard error)
for the three most abundant species observed with underwater video during 18 tidal
cycles. Species abundance was calculated as a percentage of the maximum tide-stage
abundance observed for that species during an entire tidal cycle: (individual tidestage
abundance / max tide-stage abundance)*100. Tidal cycles were divided into
16 tide stages and grouped into three tide classes: flood, stages 1–6; high, 7–10; ebb,
11–16. Slack high tide occurred between tide stages 8 and 9.
482 Northeastern Naturalist Vol. 19, No. 3
with other commonly used traditional gears (e.g., block nets, fyke nets) over
complete tide stages. Deployment of traditional sampling gears is often labor
intensive and results in disturbance to the animals and possibly habitat alteration.
Traditional sampling gears, however, are typically inexpensive (to purchase) and
widely used (and therefore standardized), which facilitates data analyses and promotes
multi-study comparisons. In contrast, initial costs are often relatively high
for underwater video equipment (although rapidly becoming less expensive),
and the specifi c operating requirements (i.e., good visibility) may preclude the
use of underwater video in more characteristically turbid salt marshes; though it
should be noted that turbidity was not a problem in this study despite observing
higher turbidities than those reported for other studies using underwater video
(e.g., Becker et al. 2010, Mueller et al. 2006; few studies reported turbidity levels).
Analysis and interpretation of video data is diffi cult and, for example, initial
attempts to sub-sample video footage (at time increments >1 min) in the present
study were abandoned because several species that were present were not being
detected. Because it is almost impossible to determine whether an individual
fi sh left the fi eld of view then returned (Ellis and Bell 2008), there is a risk of
individuals being counted multiple times, although this circumstance should be
reduced by sub-sampling (i.e., sampling at a scale less than the full amount of
data collected). In addition, while the present study focused only on the number
of individuals, sampling and analysis protocols for the use of underwater video to
observe nekton behavior could (and should) be designed to permit the collection
of additional data, such as size and swimming direction for each individual.
The arrangement of the underwater video sampling system, particularly the
camera, influences data collection and may introduce sampling biases. In the present
study, tidal migration patterns of nekton in intertidal creeks were observed in
a fi xed portion of the water column throughout the tidal cycle. The portion of the
water column examined in this study (i.e., 15–50 cm) coincides with the depths of
maximum abundance for many common intertidal nekton species (see figs. 2–5 in
Bretsch and Allen 2006b, fig. 5 in Ellis and Bell 2008); however, some individuals
migrating above or below the view of the camera might not be detected. Therefore,
species that migrate in surface waters at the highest tide stages, or those that
migrate on or close to the creek bottom throughout all tide stages (e.g., shrimps or
crabs) might be underrepresented. It should be noted, however, that most of the
nekton species commonly found in oligo-mesohaline intertidal salt marsh habitats
in Mid-Atlantic Bight estuaries (Able and Fahay 1998, 2010) were observed with
underwater video in this study. Also, although nekton were not observed with underwater
video at or around the entrance to the flume in this study (see James-Pirri
et al. 2010), intertidal nekton appeared to be unaffected by the flume and camera
set-up as individuals were observed swimming through the center channel of the
flume in a direct manner and did not hesitate or change direction.
As observed with underwater video, intertidal salt marsh creeks were characterized
by a few abundant and ubiquitous intertidal salt marsh nekton species,
primarily F. heteroclitus. Nekton species composition and abundance observed
with underwater video was similar to those found in previous studies of intertidal
habitats in these same salt marshes (Able and Hagan 2000, Hastings 1984). In
2012 M.E. Kimball and K.W. Able 483
general, the intertidal creek nekton tidal use patterns observed with underwater
video in this study were similar to those reported from other studies in North
America (Bretsch and Allen 2006b; Kimball and Able 2007a, b) and Europe
(Cattrijsse et al. 1994, Hampel et al. 2003). Resident species were most abundant
in early flood tide stages and were abundant in most ebb tide stages. Transient
species were most abundant around slack high tide, and the greatest abundances
occurred in late flood tide stages. The divergent tidal use patterns of resident and
transient species in intertidal creeks may be due to a number of factors including
refuge from predation, foraging behavior, and water-depth preferences (Ellis and
Bell 2008, Rountree and Able 2007, Rypel et al. 2007, Salgado et al. 2004).
Common intertidal marsh fi shes (i.e., F. heteroclitus, M. menidia, and
M. americana) displayed unique, species-specifi c tidal migration patterns based
on underwater video observations. Our results largely agreed with and expanded
upon nekton tidal migration observations from intertidal creeks elsewhere.
F. heteroclitus generally displayed a symmetrical tidal migration pattern. The
abundance of this species peaked during the early flood and late ebb tide stages.
This result is consistent with F. heteroclitus using marsh surface habitats near
slack high tide as reported for a Georgia salt marsh with flume-weir sampling
(Kneib and Wagner 1994) and a southern New Jersey salt marsh with flume-weir
and pit-trap sampling (Able and Hagan 2000), then moving back into intertidal
creeks as the water level dropped with the ebbing tide. This same tidal migration
pattern for F. heteroclitus also was observed in South Carolina with a sweep
flume (Bretsch and Allen 2006b) and Delaware Bay when sampled with seines
(Kimball and Able 2007a). This consistency suggests that, for F. heteroclitus,
variable habitat characteristics such as creek geomorphologies and environmental
parameters that may be associated with marshes along a latitudinal range do
not affect the timing of migration. The tidal migration pattern for M. americana
of peak occurrence during high tide, which may be due to foraging strategies
(McGrath and Austin 2009), was consistent with migration patterns observed in
a previous study (using seines) in Delaware Bay salt marshes (Kimball and Able
2007a). This result suggests that the tidal migration pattern of M. americana also
may be unaffected by intertidal creek characteristics that may be associated with
marshes along a latitudinal range.
While no migration patterns were observed with underwater video for
M. menidia in the present study, studies employing seines in Delaware Bay salt
marshes found M. menidia tidal migrations centered around slack high tide, with
a peak occurrence during late flood tide (Kimball and Able 2007b). A different
tidal migration pattern was observed with a sweep flume in South Carolina, however,
where M. menidia peak occurrence was during mid-ebb tide (Bretsch and
Allen 2006b). Such differences may be related to the sampling location in intertidal
creeks. For instance, in the present study, if M. menidia preferred the lower
portion of the intertidal creek, they would be more consistently detected with the
underwater video camera positioned near the creek mouth. Biotic factors, such
as species co-occurrence, can influence water-depth preferences of common salt
marsh nekton in shallow waters (Bretsch and Allen 2006a), and may have influenced
tidal migration patterns. Predation risk has been shown to differ with depth
484 Northeastern Naturalist Vol. 19, No. 3
for small prey fi shes in tidal creeks (Rypel et al. 2007), and therefore may influence
the timing of migration for common prey species, such as F. heteroclitus
(Kneib 1997, Nemerson and Able 2003).
In summary, the tidal migration patterns of the dominant species in intertidal
creeks, as detected near the creek mouth, were species-specifi c and probably
due to feeding patterns (i.e., feeding on marsh surface vs. intertidal creeks) and
water-depth preferences along the upper-to-lower creek gradient.
Acknowledgments
This project was funded by the National fish and Wildlife Foundation Budweiser Conservation
Scholarship awarded to M. Kimball. Additional fi nancial support for M. Kimball
was provided by the Rutgers University Marine field Station Graduate Student Research
Fund, the Academic Excellence Fund of the Rutgers University Graduate Program in Ecology
and Evolution, and the Manasquan River Marlin and Tuna Club. L. Rozas, R. Kneib,
C. Roman, and three anonymous reviewers provided constructive comments that greatly
improved this manuscript. S. Hagan, C. Kennedy, M. Sullivan, and M. Wuenschel provided
valuable fi eld, laboratory, and analytical assistance. The fi ndings and conclusions
presented in this paper are those of the authors and do not necessarily represent the views of
the NOAA National Estuarine Research Reserve system. This paper is Rutgers University
Institute of Marine and Coastal Sciences contribution No. 2012-1.
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