Discovery of an Alligator Snapping Turtle (Macrochelys temminckii) Population in Metropolitan Houston, Harris County, Texas
Eric Munscher1, 2*, Jordan Gray1, Arron Tuggle2, Day B. Ligon3,
Valeria Gladkaya1, Carl Franklin4,
Chris Drake5, Viviana Ricardez4,
Brian P. Butterfield6, Kelly Norrid7, and Andrew Walde1
1Turtle Survival Alliance – North American Freshwater Turtle Research Group, 1030 Jenkins Road, Charleston, SC 29407, USA. 2SWCA Environmental Consultants, 10245 West Little York Road, Houston, TX 77040, USA. 3Department of Biology, Missouri State University, 901 South National Avenue, Springfield, MO 65897, USA. 4TexasTurtles.org, 1001 Denmark Street, Grand Prairie, TX 75050, USA.
5Estancia Electric Company, 2611 Radcliff Drive, Sugarland, TX 77498, USA. 6Freed-Hardeman University, 158 East Main Street, Henderson, TN 38340, USA. 7Texas Parks and Wildlife Department, 14320 Garrett Rd, Houston, TX 77044, USA. *Corresponding author.
Urban Naturalist, No. 32 (2020)
Habitat loss through urbanization is an important threat to many wildlife species. While some species thrive in suboptimal urbanized conditions, many species appear to be incapable of adapting to urbanization. Despite the adaptability of some reptile species to urban habitats, populations are often small in comparison to those that inhabit areas outside of urban areas where habitat alterations are far less extreme and suitable habitat more expansive. Globally, a disproportionate number of turtle species are facing population declines, local and regional extirpations, and extinction. In the United States, many species are suffering regional population declines. The Alligator Snapping Turtle is the largest species of freshwater turtle in the United States. Despite its large geographic range, distribution data gaps exist for this iconic species. Notably, research on this species in the westernmost portion of its Texas range has been sporadic and not all-encompassing. In surveys beginning in 2016, we documented the presence of a seemingly robust Alligator Snapping Turtle population inhabiting waterways in and around Harris County, Texas, the third most-populous county in the United States. We trapped turtles on a monthly basis from December 2016–October 2018 and captured 23 males, 22 females, and 12 juveniles. Catch-per-unit effort, expressed as captures per net-night, ranged from 0.00–0.83 turtles per net-night, with an overall rate of 0.40 turtles per net-night. Future work with this population should include increasing trapping efforts to calculate population estimates and demographics such as density, biomass, and annual survivability.
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Discovery of an Alligator Snapping Turtle
(Macrochelys temminckii) Population in
Metropolitan Houston, Harris County, Texas
Eric Munscher1, 2*, Jordan Gray1, Arron Tuggle2, Day B. Ligon3,
Valeria Gladkaya1, Carl Franklin4, Chris Drake5, Viviana Ricardez4,
Brian P. Butterfield6, Kelly Norrid7, and Andrew Walde1
Abstract - Habitat loss through urbanization is an important threat to many wildlife species. While
some species thrive in suboptimal urbanized conditions, many species appear to be incapable of adapting
to urbanization. Despite the adaptability of some reptile species to urban habitats, populations are
often small in comparison to those that inhabit areas outside of urban areas where habitat alterations
are far less extreme and suitable habitat more expansive. Globally, a disproportionate number of turtle
species are facing population declines, local and regional extirpations, and extinction. In the United
States, many species are suffering regional population declines. The Alligator Snapping Turtle is the
largest species of freshwater turtle in the United States. Despite its large geographic range, distribution
data gaps exist for this iconic species. Notably, research on this species in the westernmost portion
of its Texas range has been sporadic and not all-encompassing. In surveys beginning in 2016, we documented
the presence of a seemingly robust Alligator Snapping Turtle population inhabiting waterways
in and around Harris County, Texas, the third most-populous county in the United States. We trapped
turtles on a monthly basis from December 2016–October 2018 and captured 23 males, 22 females,
and 12 juveniles. Catch-per-unit effort, expressed as captures per net-night, ranged from 0.00–0.83
turtles per net-night, with an overall rate of 0.40 turtles per net-night. Future work with this population
should include increasing trapping efforts to calculate population estimates and demographics such as
density, biomass, and annual survivability.
Habitat loss is one of the most significant factors driving declines of reptiles worldwide
(Gibbons et al. 2000), and urbanization, in particular, can dramatically affect reptile
diversity and ecology (Hamer and McDonnell 2010, Hunt et al. 2013, Rebelo et al. 2011).
However, while many species are simply intolerant of the dramatic environmental changes
wrought by urbanization, others manage to persist—and some even thrive—in such fragmented
landscapes. This has been notably true for a small, but diverse, suite of lizard species
such as the Cuban brown anole, Italian wall lizard, and Mediterranean house gecko that
thrive in urban environments even outside of their native ranges (Angetter et al. 2011, Burke
et al. 2002, Meshaka et al. 2006). City parks and other pockets of relatively undisturbed
habitat frequently support other reptiles, as well (Baneville and Bateman 2012, Dawson
and Hostetler 2008, Ferguson et al. 2008). Despite the persistence of some reptile species
in urban areas, populations are often small in comparison to those that inhabit areas outside
1Turtle Survival Alliance – North American Freshwater Turtle Research Group, 1030 Jenkins Road,
Charleston, SC 29407, USA. 2SWCA Environmental Consultants, 10245 West Little York Road, Houston,
TX 77040, USA. 3Department of Biology, Missouri State University, 901 South National Avenue,
Springfield, MO 65897, USA. 4TexasTurtles.org, 1001 Denmark Street, Grand Prairie, TX 75050,
USA. 5Estancia Electric Company, 2611 Radcliff Drive, Sugarland, TX 77498, USA. 6Freed-Hardeman
University, 158 East Main Street, Henderson, TN 38340, USA. 7Texas Parks and Wildlife Department,
14320 Garrett Rd, Houston, TX 77044, USA. *Corresponding author- firstname.lastname@example.org.
Manuscript Editor: Travis Ryan
E. Munscher, et al.
2020 No. 32
of cities where habitat alterations are generally less extreme and suitable habitat more expansive
(Rebelo et al. 2011).
As is true of many turtles world-wide, Macrochelys temminckii (Troost in Harlan) the
Alligator Snapping Turtle is declining throughout much of its range (Lovich et al. 2018;
Pritchard 1989, 2006; Riedle et al. 2008; Rhodin et al. 2018; Turtle Taxonomy Working
Group 2017; Wagner et al. 1996). The species’ distribution may be even more constricted
than presently reported because many locality records in recent decades are based upon
observations of single specimens that may be lone relicts rather than representative of viable
populations (Riedle et al. 2008, Shipman et al. 1995). Nonetheless, robust populations
remain in pockets of the species’ historic range.
In Texas, much of what is known about the species’ range is based upon occurrence
records, with no studies establishing population densities or demographics. Alligator Snapping
Turtles are generally described as ranging as far west as the Trinity River watershed
(Dixon 2013), although a fossil specimen from the Brazos river drainage suggests that it
once occurred farther westward (Hay 1911). The species was added to the state list of protected
species in 1987 (Texas Register 1987). Recent surveys, in combination with verified
incidental observations, have documented the species in 36 counties of Texas, and there are
unverified records from another four counties (Dixon 2013, Rudol f et al. 2002; Fig. 1).
Here, we describe the presence of an unusual population of Alligator Snapping Turtles
that inhabits waterways in metropolitan Houston, Texas, the third most-populous city in the
We conducted our study in Buffalo Bayou in Harris County, Texas, USA. Buffalo Bayou
lies to the west of the Trinity River, but both drain into Trinity Bay. Our trapping sites were
all within the city limits of Houston. Fed by a combination of groundwater discharge and
surface runoff, Buffalo Bayou is an approximately 85-km slow-moving river flowing in a
sinuous meander through suburban, urban, and parkland environments. The Buffalo Bayou
is contained within a 264-km2 watershed within the San Jacinto River basin (Aulbach 2012,
Harris County Flood Control District 2013). Greater than 80% of the watershed is urbanized;
a 2010 census reported a human population of more than 2.3 million (Harris County
Flood Control District 2013). The principal waterway of Harris County and the Greater
Houston metropolitan area, the Buffalo Bayou connects to a multitude of associated bayous
and tributaries, including Carpenters, Greens, Sims, and Brays bayous, and Rummel, Soldiers,
and Turkey Creeks (Harris County Flood Control District 2013). To the west of our
study site, two reservoirs completed by the US Army Corps of Engineers in the 1940s exert
some control over water flow in the Buffalo Bayou (Aulbach 2012, Harris County Flood
Control District 2018).
The 37 km segment of Buffalo Bayou in which we conducted our surveys featured an
assortment of adjacent habitat types including urban parkland featuring forested riparian
buffers; private golf courses; open, managed parkland with little to no riparian buffer;
bicycle and walking paths; and private and commercial real estate. This section of the
Buffalo Bayou is characterized by moderate and variable water flow, high turbidity, and
an abundance of submerged and emergent structures and sand bars. Water levels in these
areas fluctuate with rainfall and releases from upstream dams. Furthermore, the easternmost
3.6 river-km is tidally influenced and brackish (Bosquez 2010). Trapping locations
were limited by availability of access points in the city, and to periods of low water and
E. Munscher, et al.
2020 No. 32
favorable weather forecasts in order to avoid the risk of submerging traps and potentially
drowning turtles (Fig. 2). We have not reported precise study locations to protect the sites
from potential poaching or molestation.
Following an initial survey conducted in October 2016 that confirmed the presence
of Alligator Snapping Turtles, we conducted three-day trapping sessions monthly from
December 2016 until October 2018. However, due to flooding and inclement weather we
were unable to sample in March, May, August, September 2017 (Fig. 2). In 2018, we were
forced to skip trapping sessions in January, February, May, July, August, and September
due to unsafe flow rates. An additional sampling session was added in April 2018 to augment
the paucity of trapping during the winter months (January, February, and March). For
most sampling sessions, we deployed five single-throated hoop nets (1.2 m dia., 3.6 m long;
Louisiana Sports Net, Baton Rouge, Louisiana, USA). In October 2018, up to 13 traps were
deployed. Traps were set with a portion of the trap above water to provide trapped turtles
Figure 1. Map of Texas counties showing the known distribution of Alligator Snapping Turtles in the
state. There was just one historical record in Harris County (denoted with a closed circle) prior to
E. Munscher, et al.
2020 No. 32
with access to air. Traps were adjusted to accommodate the rise and fall of water levels to
ensure that any trapped turtles would not drown due to an overnight influx of rainfall and/or
dam release (Fig. 2). We baited and rebaited traps daily with either whole or fileted Oreochromis
aureus (Steindachner) (Blue Tilapia), cut Ictalurus punctatus (Rafinesque) (Channel
Catfish), or Ictiobus bubalus (Rafinesque) (Smallmouth Buffalo). Bait was held in place
by metal wire that was looped through the trap and through the fish. Traps were checked
regularly over the next 40 hours and were never left unchecked for more than 16 hours.
We recorded straight mid-line carapace length (SCL) from the precentral (nuchal) to
postcentral marginal scutes to the nearest mm using 700-mm aluminum tree calipers (Haglof
Inc., Madison, Mississippi, USA), save for the first six captured turtles (two males, two
females, and two juveniles) as we did not have the necessary equipment on hand at the time
of capture. Sex of turtles was determined by visual inspection of sexually dimorphic characters,
including distance from the cloaca to the posterior edge of the plastron, proportional
head width, and overall size (Ernst and Lovich 2009). Male Alligator Snapping Turtles have
more distally positioned cloacae, larger heads, and reach larger sizes than females (Ernst
and Lovich 2009). We measured mass of all turtles using a 130-kg hanging scale (Cabela’s
Inc., Sidney, Nebraska, USA). Turtles were marked using a variation of the shell notching
technique described by Cagle (1939) and Riedle et al. (2016) and with passive integrated
transponder (PIT) tags (Buhlmann and Tuberville 1998). We released turtles back into the
Buffalo Bayou at their capture location immediately after processing.
We calculated the mean and standard deviation SCL of juveniles, females, and males. In
instances when individuals were recaptured one or more times, only the first set of measurements
was included in analyses. We conducted a Chi-Square goodness of fit test to determine
if the adult sex ratio differed from parity. We compared SCL between males and females using
a two-sample t-test. We set the threshold for significance at α = 0.05 for both tests.
Figure 2. Fluctuations in mean daily gage height and discharge rate during the span of reported sampling
efforts. The large spike in September 2017 was the result of Hurricane Harvey. The horizontal
line indicates the median gauge height. Black points along the x-axis indicate trapping sessions; the
red triangle represents an Alligator Snapping Turtle that was recovered by Houston Police. Note that
most trapping was conducted when water depth in Buffalo Bayou was below the median. Data obtained
from USGS Gage Station 08074000; discharge data were patchy and were available for only
23% of days between 1 October 2016 and 31 October 2018.
E. Munscher, et al.
2020 No. 32
We conducted 16 sampling sessions totaling 173 net nights over a 26-month period,
with at least one 2-day effort occurring in all seasons; however, surveys did not occur in
August and September of either year due to flooding (Fig. 2, Table 1). At least one Alligator
Snapping Turtle was captured during 15 of the 16 sampling sessions, and specimens were
captured in all seasons.
We made 69 captures of 57 individual Alligator Snapping Turtles comprising 23 males, 22
females, and 12 juveniles (1.05:1.00 male:female ratio) (Fig. 3). The sex ratio did not deviate
from parity (χ2 = 0.0221, P = 0.882). We captured an average of four Alligator Snapping Turtles
per sampling period, but results were variable, ranging from 0 to 19. Similarly, catch-per-unit
effort (CPUE), expressed as captures per net-night, was variable among sampling sessions,
ranging from 0.00–0.83 turtles per net-night (Table 1), with an overall rate of 0.40 turtles per
Female SCL; and males were significantly larger than females (tdf = 39 = 3.19, P < 0.001);
the mean ± s.d. SCL of males was 503 ± 104.7 mm (range: 289–647 mm, n = 21) whereas
females averaged 422 ± 46.8 mm (range: 323–477 mm, n = 20). The mean SCL for juveniles
was 269 ± 40.0 mm (range 218–335 mm, n = 10; Fig. 3).
Little is known about Alligator Snapping Turtle populations in Texas because few
population-level studies have been conducted (Fitzgerald and Nelson 2011, Rudolf et al.
2002). The paucity of information, compared to other western states in the species’ range
such as Oklahoma, Arkansas, and Louisiana, may in part be a consequence of land ownership
patterns in the state, where approximately 94% of land is privately owned and access
for wildlife research is limited (Texas Center for Policy Studies 2000, Texas General Land
Office 2019). Most of our knowledge of distribution in the state of Texas is derived from a
combination of historic records and a statewide survey from 1998–2001, which produced
48 captures across 17 survey sites (Rudolf et al. 2002). However, the chief objective of that
survey effort was to generate presence-absence data, so survey efforts at each location were
typically short, and were ended when the species was detected. Alligator Snapping Turtles
were detected in all major drainages in eastern Texas between the Sulphur and Navasota
rivers and new county records were documented in Angelina, Jasper, Leon, Nacogdoches,
San Jacinto, Collin, Sabine, and San Augustine Counties (Rudolf et al. 2002). The Collin
County record was obtained in a heavily developed urbanized area, conditions that were
similar to those we surveyed in our study. However, Rudolph et al. (2002) did not survey
Harris County due to a perceived lack of suitable habitat. Notably, our efforts to characterize
demographics of Alligator Snapping Turtles in Buffalo Bayou were nearly coincident with
two incidental observations that were made in the same calendar year (iNaturalist 2016a, b).
Among the seven counties that border Harris County, there are no records of the species
in three counties, unconfirmed records in two counties, one recently confirmed record in
Montgomery County (Munscher et al. 2019) and records based on museum specimens in
one county. Prior to our study, there was one historical record from Harris County. This observation
occurred on August of 1968, on White Oak Bayou, a large man-made bayou with a
cement bottom that flows into Buffalo Bayou from the northwest. The individual was found
approximately 10 miles northwest of the Buffalo Bayou confluence (Biodiversity Research
and Teaching Collections at Texas A&M University -specimen TCWC - 103149 and Baylor
University, Mayborn Museum Complex - Specimen R 11196).
E. Munscher, et al.
2020 No. 32
Table 1. Alligator Snapping Turtle captured from Buffalo Bayou from October 2016 through October 2018.
Juveniles Total CPUE
15–16 Oct 10 2 – 2 – 2 6 0.60
18–20 Dec 10 2 – – – – 2 0.20
20–22 Jan 10 4 – – – – 4 0.40
10–12 Feb 10 2 – 1 – 1 4 0.40
7–9 Apr 10 – (1) 5 – – 5(1) 0.60
9–11 Jun 10 – – – – 4 4 0.40
7–9 Jul 10 1 – 1 – – 2 0.20
13 Sep† 0 – (1) – – – (1) N/A
6–8 Oct 10 1 – 1 – – 2 0.20
10–12 Nov 10 2 – – (1) – 2(1) 0.30
1–3 Dec 10 – (2) 2 – 2(2) 0.40
23–25 Mar 10 3 – 1 (1) 1 5(1) 0.60
20–22 Apr 10 1 – – – 0 1 0.10
27–29 Apr 10 – – 1 – 1 2 0.20
2–4 Jun 10 1 – 1 – 1 3 0.30
13–15 Jul 10 – – – – – – 0.00
11–13 Oct 23 4 (2) 7 (4) 2 13(6) 0.83
Totals 173 23 6 22 6 12 57(12) 0.40
†No traps were set. Incidental capture by Houston police.
E. Munscher, et al.
2020 No. 32
Our trapping results suggest that a reproductively viable population of Alligator Snapping
Turtles inhabits Buffalo Bayou in the heart of downtown Houston. At this time, we
do not have sufficient data to calculate population estimates; however, overall CPUE is
consistent with results from robust populations in Arkansas (Trauth et al. 1998, Wagner et
al. 1996), southern Alabama (Folt and Godwin 2013), and with Macrochelys suwanniensis
(Suwannee Alligator Snapping Turtle, Thomas et al. 2014) in western Florida (Moler 1996),
and Southern Georgia (Jensen and Birkhead 2003). Our CPUE was noticeably higher than
has been reported in areas with known harvest and poaching. For example, Boundy and
Kennedy (2006) reported an average rate of 0.06 turtles per trap night in Southeastern Louisiana
and a recent survey conducted by Huntzinger et al. (2019) in Southwestern Louisiana
resulted in an even lower CPUE of 0.021. In Oklahoma, a capture rate of 0.058 was reported
by Riedle et al. (2005) and in Missouri, Lescher et al. (2013) documented a CPUE value of
0.116. In most of these studies with low CPUE, the authors reported more juveniles than
adults being captured, suggestive of populations where adults have been removed by harvest.
Many of the studies within Appendix 1 were extensive regional or state-wide surveys
that listed CPUE values for individual trapping locations as well as an average CPUE for
their entire study. It must be noted that CPUE values in Appendix 1 are illustrative, with
Figure 3. Size classes, based on midline carapace length, of Macrochelys temminckii captured at
Buffalo Bayou in metropolitan Houston, Texas. The first six turtles captured were marked but were
not measured and therefore are not included.
E. Munscher, et al.
2020 No. 32
trends showing that harvested areas have lower CPUE. However, we caution strict interpretation
as studies that present multiple sites could have lower results due to sites with low,
or no, CPUE values being averaged into the study results.
Extreme water temperatures typically suppress Alligator Snapping Turtle activity and
detectability (Fitzgerald and Nelson 2011, Riedle et al. 2005). Our overall capture rate of
0.40 turtles per net-night includes efforts from mid-summer and mid-winter survey work
when water temperatures are very warm and very cold, respectively. Alligator Snapping
Turtles’ activity levels are known to be suppressed during periods characterized by temperature
extremes (Spangler 2017), and capture rates appear to decline as a result (Riedle et
al. 2006). We predict that surveys restricted to the times of year when the species is most
active would result in capture rates at least comparable to those reported from the most robust
populations reported in neighboring Oklahoma and Arkansas (Howey and Dinkelacker
2013, Riedle et al. 2008, Trauth et al. 2016, Wagner et al. 1996) and studies of the Suwannee
Alligator Snapping Turtle (Folt and Godwin 2013, Johnson et al. 2015, Moler 1996, Thomas
et al. 2014). While we suspect that our calculated capture rate is likely reduced due to constraints
on when we were able to successfully survey, we question whether we will ever be
able to conduct surveys in this system during more typical trapping periods due to the corresponding
highly stochastic weather patterns at those times of year. Despite this constraint,
however, our survey results support the conclusion that a robust and demographically viable
population of Alligator Snapping Turtles inhabits Buffalo Bayou.
The city of Houston is the third most populous city in the United States, and the most
populous city in the southern United States (Morris 2016). As the principal waterway of
Harris County and the city of Houston, alterations have been made to the structure and
riparian zones of Buffalo Bayou, in part to facilitate draining water from the Greater Houston
metropolitan area with greater efficiency during periods of high precipitation (Harris
County Flood Control District 2018). These alterations turn segments of a usually low
energy, meandering aquatic system into segments with much higher energy. Additionally,
rain-induced flooding events are common, and occasionally extreme, as in 2017 during
Hurricane Harvey and 2019 Tropical Storm Imelda. Such events have the potential to effectively
scrub the channel of submerged structures resulting in habitat that is thought to be
less favorable for Alligator Snapping Turtles (Riedle et al. 2005).
Adding to anthropogenic pressure along the Buffalo Bayou, Houston is the largest
US city to have no zoning laws (Boburg and Reinhard 2017). From 2010 to 2017, more
than 7,000 residential buildings were constructed in Harris County in areas within the
100-year flood plain (Boburg and Reinhard 2017). Furthermore, for decades, Buffalo
Bayou has been—and continues to be—subject to pollutants emanating from runoff and
sewage discharge (Suayan 2018). Along with overharvesting and incidental drowning
from abandoned fishing equipment, habitat alteration and pollution are considered primary
causes for the decline of this species across its range (Reed et al. 2002, Riedle et
al. 2005, Shipman and Riedle 2008, Sloan and Lovich 1995). As such, a highly urbanized
and anthropogenically impacted watershed such as Buffalo Bayou drainage basin
differs markedly from the more rural watersheds of the Trinity, Neches, and Sabine river
basins. Despite these many factors that would seem to reduce Alligator Snapping Turtle
numbers, the results of our initial surveys suggest that the species has a robust population
within this environment despite atypical and seemingly suboptimal conditions. River and
land-management practices should continue to be scrutinized, as further degradation of
this habitat could lead to the decline of this, and other species of wildlife, in and along
the Buffalo Bayou. Additionally, the results from our research thus far lend credence to
E. Munscher, et al.
2020 No. 32
the notion that the Buffalo Bayou’s surroundings in one of the nation’s largest cities has
acted as a refugium for this frequently hunted species. Local, state, and county park law
enforcement should remain vigilant in guarding against potential poaching threats.
Our discovery of a seemingly robust, reproductively active population of the Alligator
Snapping Turtle in the Houston metropolitan area was unexpected but potentially encouraging
for the species’ long-term persistence in southeastern Texas. The fact that this large species
remained undetected in a heavily populated area for so long suggests that other populations
may exist in nearby watersheds. These observations, in combination with the recent discussed
elevation of the species’ to state-level conservation status to Critically Imperiled, (Texas Parks
and Wildlife, Austin, TX, 2018 pers. comm) support the need for concerted survey efforts to
better characterize the presence of Alligator Snapping Turtles in East Texas. In particular,
neighboring counties with no records of the species may yet support cryptic populations
similar to the one we discovered here. Furthermore, the persistence of an Alligator Snapping
Turtle population in a highly altered and heavily impacted habitat, where they were presumed
to have been extirpated, provides hope that other populations may occur in similar riverine
habitats in Texas and other states within the species’ range.
Future work on this population should include continued trapping efforts to estimate the
population size and describe its demographics. Additionally, this population is well suited to
study the effects that a suite of challenges that typify urban habitation (including restricted
nesting habitat, altered flow regimes, and high levels of pollution) can have on Alligator
Snapping Turtles. Finally, the proximity of Buffalo Bayou to the Gulf of Mexico provides
an opportunity to study the species’ use of brackish habitat, including its behavioral and
physiological responses to high and variable salinity.
We would like to thank the Texas Parks and Wildlife Department for managing this important species,
providing support, and making this research possible. We thank the Hess Foundation for provided much
needed funding for this project. Additionally, we would like to express our gratitude to the Memorial
Park Conservancy, specifically Carolyn White and Shellye Arnold for their support. We also thank all the
Turtle Survival Alliance—North American Freshwater Turtle Research Group members who assisted.
Finally, we are grateful to SWCA Environmental Consultants for their constant support. We would like to
offer our appreciation to Jeff Stein of SWCA Environmental Consultants for making the state distribution
map. Texas Parks and Wildlife Department approved all capture and handling protocols, and all methods
conformed to the ASIH/SSAR animal use guidelines (American Society of Ichthyologists and Herpetologists,
the Herpetologists League, and the Society for the Study of Amphibians and Reptiles 2001). We
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13 Appendix 1. Review of published Alligator Snapping Turtle catch per unit effort (
CPUE), sex ratios, trapping effort, and population estimates.
Source Location Study Type CPUE Total Net
Nights Sex Ratio Number of
This Study SE Texas Single site 0.40 173 1:1 57 NA
Rudolf et al. (2002) Texas Statewide 0.046 1,009 1:1 48 NA
Huntzinger et al. (2019) SW Louisiana Three river drainages 0.021 731 Juvenile bias 14 NA
Boundy and Kennedy (2006) E Louisiana Multiple sites 0.06 3,504 1:1 200 NA
Riedle et al. (2005) Oklahoma Multiple sites 0.059–0.620 1,085 1:1 63 NA
Riedle et al. (2008) Oklahoma Multiple sites NA 565 1:1 157 127.5 ± 24.5
East et al. (2013) Oklahoma Multiple sites NA NA Juvenile bias 40 22 ± 5
Wagner et al. (1996) Arkansas Statewide 0.234 1,905 NA 445 NA
Trauth et al. (1998) NE Arkansas Multiple sites 0.28 352 NA 98 NA
Trauth et al. (2016) Arkansas Multiple sites 0.24–0.92 416 Male bias 163 105–282
Lescher et al. (2013) SE Missouri Multiple sites 0.09 557 NA 51 NA
Shipman and Riedle (2008) SE Missouri Multiple sites 0.12 396 1:1 47 NA
*Folt and Godwin (2013) S Alabama Multiple sites 0.048 716 Female bias 35 NA
*Folt and Godwin (2013) S Alabama Multiple sites 0.081 570 Female bias 46 NA
*Folt and Godwin (2013) Fowl River - Alabama Single river 0.478 46 Female bias 22 NA
Howey and Dinkelacker (2013) S Alabama Multiple sites 0.10–0.13 NA 1:1 103 NA
Enge et al. (2014) Suwannee River - Florida Single river 0.25 NA 3.5:1 132 780−1,171
Moler (1996) W Florida Multiple sites 0.251 367 NA 92 NA
Mays et al. (2015) Florida Panhandle Multiple sites 0.01–0.53 (mean = 0.30) 308 1.5:1 88 NA
Johnston et al. (2015) N Florida Santa Fe River 0.006–0.181 1,727 1:1 109 NA
Jensen and Birkhead (2003) S Georgia Multiple sites 0.2 281 1:1 55 NA
King et al. (2016) Georgia Multiple sites 0.09 683 1:1 52 NA
It must be noted that CPUE values in Table 2 are illustrative, with trends showing that harvested areas have lower CPUE.
*Folt and Guyer sampled multiple locations across southern Alabama. Fowl river locality was taken out of paired site calculations to illustrate extremely high CPUE value.