Population and Nesting Site Evidence for Diamondback Terrapins, Malaclemys terrapin, in Northeast Florida

Introduction

Diamondback terrapins (Malaclemys terrapin) are listed as Vulnerable by the IUCN Red List Index of Threatened Species (Roosenburg et al., 2019). Among the challenges terrapins encounter are habitat loss due to coastal development and sea level rise, mortality at all life stages by mammalian and avian predators, road mortality (Maerz et al., 2018), boat strikes (Lester et al., 2018), harvest for the pet trade, and drowning in crab traps (Chambers and Maerz, 2018).

Commonly used references concerning reptile natural history (e.g., Ernst and Lovich, 2009; Powell et al., 2016) describe the distribution of diamondback terrapins to be from Cape Cod, Massachusetts to Corpus Christi, Texas. They provide range maps with a continuous line drawn along the Atlantic and Gulf coastlines between those two places. While these maps are useful for general information, terrapin distribution along those lines is not truly continuous due to natural or anthropogenic habitat interruptions. It would be helpful for researchers seeking to study local populations to know where terrapin concentrations exist. Accurate local distribution information can also inform governmental decisions concerning allocation of conservation resources and protection of essential habitats. To this end, one of the major objectives of the Diamondback Terrapin Working Group¹ has been to create a “living” map of historical and current terrapin populations throughout the range (Butler et al., 2006). Historical populations can be identified from existing literature or museum collections, while the distribution and abundance of contemporary populations is determined by surveys.

In Florida, terrapin populations are known from Merritt Island National Wildlife Refuge (Seigel, 1980a,b, c, 1984, 1993), the Keys (Wood, 1992; Baldwin et al., 2005), the western part of Everglades National Park (Hart and McIvor, 2008), Sanibel Island (C. Lechowicz, pers. comm.), Tampa Bay and St. Martins Key (C. Boykin, pers. comm), the Big Bend region (Butler and Heinrich, 2013), and the extreme western Panhandle (R. O’Conner, pers. comm.). In northeast Florida, several discrete terrapin populations in Nassau and Duval counties have been studied (Butler, 2000, 2002; Butler et al., 2004), but no systematic surveys were performed there. In a review of 58 museums only six terrapin records are listed for Florida’s four northeastern-most counties (Krysko et al., 2011): one from Nassau, four from Duval, one from St. Johns, and none from Flagler. The primary objective of this study was to identify terrapin populations and nesting sites in these four northeastern Florida counties.

Some oviparous reptiles, including diamondback terrapins, exhibit temperature-dependent sex determination (TSD) where offspring sex is a function of incubation temperature (Bull, 1980; Jeyasuria et al., 1994; Burke and Calichio, 2014; Wibbels et al., 2018). Incubation temperature depends on variables such as nest depth and shading, and in some cases shading by overstory vegetation affects nest depth or nest choice (Kolbe and Janzen, 2002; Czaja et al., 2020). Diamondback terrapins prefer to nest in sandy areas above the high tide line (Palmer and Cordes, 1988; Roosenburg, 1994). These areas often support some woody shrubs and trees that require such soils and do not withstand extensive flooding. Butler and Heinrich (2013) noted that several woody plant species were frequently associated with terrapin nesting areas, and we hypothesized that terrapins may use this vegetation as a distant visual signal that an area is appropriate for nesting. Thus, another objective was to determine if certain woody plant species could be indicators of terrapin nesting sites.

Materials and Methods

Study Site

The study area encompassed shorelines, marsh islands, tidal creeks and rivers associated with the Intracoastal Waterway (ICW) of the four northeastern-most coastal Florida counties of Nassau, Duval, St. Johns, and Flagler (Figure 1). The northern boundary was the St. Mary’s River and we surveyed southward nearly 160 km to the southern border of Flagler County. The area includes inlets at the St. Mary’s, Nassau, St. Johns, Fort George rivers, the city of St. Augustine, and the Matanzas Inlet. Most of the habitat adjacent to the ICW in Nassau, Duval and St. Johns counties is described as salt marsh by Montague and Wiegert (1990) with smooth cordgrass (Spartina alterniflora) dominating and intermittent stands of needlerush (Juncus roemerianus). About midway through St. Johns County, near the Guana-Tolomato-Matanzas National Estuarine Research Reserve (GTM), the northernmost black mangroves (Avicennia germinans) occur (Williams et al., 2014), but not until further south in Flagler County do mangroves dominate shorelines.

FIGURE 1

Figure 1. The northeast Florida Diamondback Terrapin study area showing boundaries of the four counties along with major inlets to the ICW.

From May 7 through August 6, 2013, three researchers surveyed 1 day per week for terrapins employing head counts and land surveys (Butler and Heinrich, 2013) in St. Johns County between GTM and Marineland. In 2014, from May 1, through August 1, three researchers surveyed for diamondback terrapins 3–4 days per week in all four of Florida’s northeastern-most counties. Some data collected between 1995 and 2002 from all but Flagler County during earlier studies by JB are included in our maps in the interest of completeness, but they are not counted as new data for this study.

Head Counts

Harden et al. (2009) compared terrapin head counts to population estimates derived from mark-recapture studies. Head counts, while less accurate for quantifying population levels, allow researchers to determine occupancy of an area without needing to engage in time-consuming capture techniques. We counted terrapin heads from our boat as we traveled at idle speed in adjacent tidal creeks, rivers, and occasionally the ICW. For each sighting we recorded GPS locations using a hand-held unit (Garmin GPSMAP 78 SC).

Land Surveys

We conducted walking surveys of all shorelines and dredge spoil or natural marsh islands exhibiting potential terrapin nesting habitat (i.e., above the high tide line with soil composed mostly of sand or sand-shell mix, Palmer and Cordes, 1988; Roosenburg, 1994). At such sites we detected terrapin presence by recording depredated terrapin nests, terrapin remains (carcasses, bones, or scutes), intact nests, or crawls (Butler and Heinrich, 2013; Roosenburg and Burke, 2018). Raccoons (Procyon lotor) are major predators of diamondback terrapin nests throughout their range (Burger, 1977; Roosenburg, 1992; Feinberg and Burke, 2003). When raccoons excavate nests, they usually eat the egg contents at the nest site, leaving the eggshells behind. Therefore, we identified depredated nests by finding the eggshells associated with exhumed nests. Further, raccoons often kill female terrapins before they have time to nest (Seigel, 1980a), which was the source of most of the terrapin remnants we found. Occasionally, substrate conditions were such that tracks left in the sand by nesting terrapins could be identified indicating terrapin usage (crawls, Butler, 2002).

Other

Several of our data points resulted from encounters with live terrapins that were not from head counts, not anticipated, and defied placement within our categories. These will be explained below.

Maps

We used Geographic Information System software (ArcGIS 10.3, ESRI, Redlands, CA, United States) to create a geodatabase for all field observations using the GPS locations and field notes. Although vegetation survey locations were included in the geodatabase, maps included here focus on the locations of terrapin evidence and waypoints that indicate the areas surveyed.

Statistical Analysis

We recorded our time spent in the field on most days allowing calculation or the number of data points recorded over time (CPUE as # of records/time).

To establish whether terrapin evidence data points were distributed randomly, we applied an optimized hot spot analysis (Getis-Ord Gi*) in ArcGIS Pro version 2.9.0 using all terrapin evidence points with the total number of observations as the analysis field.

To determine whether vegetation composition affected nest site choice by terrapins, during the land surveys in 2014, we recorded the presence/absence of 10 plant species associated with Florida salt marshes. We limited our records to woody species because most are sensitive to extensive flooding and therefore occur above the high tide line where terrapins normally nest. We did not record the number of each species, only presence/absence. The shrub and tree species we documented are: marsh elder (Iva frutescens), saltbush (Batis halimifolia), Christmas berry (Lycium carolinianum), southern red cedar (Juniperus silicicola), wax myrtle (Myrica cerifera), cabbage palm (Sabal palmetto), saw palmetto (Serenoa repens), yaupon (Ilex vomitoria), oak (Quercus spp.), and pine (Pinus spp., elliotii or palustris).

We compared the presence/absence of the 10 woody species at sites where nesting was detected and locations lacking nests using specialized matched-pairs t-testing, to determine if plant species composition differences between nesting and non-nesting sites were statistically significant. We then used decision tree analysis and a generalized ordinal logistic fit regression to model the odds of a nesting or non-nesting event using SAS 9.4 and JMP 15.0.

Results

We documented 404 records of terrapin evidence in northeast Florida (Table 1 and Figure 2). For ease of analysis, we bundled the data into three groups referred to herein as the Nassau evidence (Figures 3A,B), the Duval evidence (Figure 4), and the St. Johns evidence (Figure 5). Sixty-eight percent of our records were from Nassau County, with another 20% from Duval County. St. Johns County records were from several discrete areas, and we had only one record from Flagler County.

TABLE 1

Table 1. Records of Carolina Diamondback Terrapins in the four northeastern-most Florida counties of Nassau, Duval, St. Johns, and Flagler in 2013 and 2014.

FIGURE 2

Figure 2. Northeast Florida study area with the three evidence centers outlined and labeled as Nassau, Duval, and St. Johns evidence, with an important Terrapin concentration at Jackson Creek (Figure 3B). Blue triangles depict all places where we conducted surveys. Red triangles indicate locations where evidence of Terrapins was found, and each represents between 1 and 102 findings.

FIGURE 3

Figure 3. The Nassau Terrapin evidence. All records are indicated in (A) along with the Jackson Creek concentration in the box. The Jackson Creek concentration is highlighted in (B). Green asterisks are places where Terrapin evidence was recorded before the current study, and they are discussed in the body of the paper. Triangles as defined in Figure 2.

FIGURE 4

Figure 4. The Duval Terrapin evidence. Triangles and asterisks as in Figures 2, 3, respectively.

FIGURE 5

Figure 5. The St. Johns Terrapin evidence. Triangles and asterisks as in Figures 2, 3, respectively.

Head Counts

Of our 404 observations, 31 (7.7%) were from head counts (Table 1). The largest single head count (8) was in Jackson Creek (Figure 3B) in Nassau County and most of our head count records occurred in May 2014 (24), which is when we surveyed most of Nassau and Duval counties; we counted only six heads in St. Johns County and none in Flagler.

Land Surveys

Most of our terrapin evidence records were of depredated nests (51%) and again most were in Nassau County (Table 1). Among our observations in that county were 88 depredated nests at boat ramps (Figure 3A, Holly Point Ramp 58, Goffinsville Ramp 30), 19 on a spoil island in Broadbent Creek, and another 10 along railroad tracks beneath the SR 200 Bridge (Figure 3B). In Duval County, we found 12 depredated nests on islands within the marsh between the ICW (called Sisters Creek in this area) and Fort George Island (Figure 4), but most often we found fewer than five at a time. In St. Johns County, we recorded 17 depredated nests at a shoreline upstream in Robinson Creek, three on an island in Sombrero Creek, and other observations were of single raided nests (Figure 5). Finally, in Flagler County we located a single depredated nest on a spoil island just south of Marineland. Burke et al. (2009) determined that in Jamaica Bay Wildlife Refuge, New York, raccoons shifted their behavior later in the nesting season such that they devoured eggshells, rather than leaving them near the nest site. If this is the case in northeast Florida, our depredated nest counts would be undercounted.

We discovered most of the terrapin remains in Nassau County (Table 1), and it is notable that 87 of these were collected on 1 day from a site near the mouth of Jackson Creek (Figure 3B, where we also recorded the most heads). We recorded all 11 crawls on 1 day at Sawpit Island in Duval County (Figure 4), a known terrapin nesting site (Butler et al., 2004; Munscher et al., 2012). A terrapin deposited a nest near the Fernandina Harbor Marina (Nassau County, Figure 3A) on July 11, 2014 (C. Hoblin, Fernandina resident, pers. comm.). We dug to verify the presence of eggs (not clutch size) and recorded this as one of our intact nests. We discovered a nesting terrapin in St. John’s County on 16 July 2013 as it deposited a nest of three eggs on an island adjacent to Hospital Creek in St. Johns County (Figure 5). We recorded this as another intact nest (Table 1).

In Duval County, we sighted one terrapin abandoning a basking site in the marsh between Sisters Creek and Fort George Island, and we captured two others as they swam at the creek-mouth leading to the Isle of Palms community (Table 1, Other; Figure 4). Six terrapins were sighted swimming and photographed in Salt Run near a marina and restaurant in St. Johns County (S. Eastman, Florida DEP, and T. Dodson, St. Johns County Govt., pers. comm.). These nine individuals compose the “Other” column in Table 1.

Statistical Results

Of the 62 possible field days, we recorded time spent on 56 of them for a total of 263 h and 18 min. During that period, we recorded 276 terrapin evidence data points, so CPUE = 1.05 records/h. We did not include terrapin records obtained from sources other than our own methods in the calculation of CPUE. Further, we did not consider the number of researchers in the calculation, so the hours are not man-hours.

The optimized hot spot analysis calculated optimal neighborhood size as 5003.5 m, so we rounded to 5 k. There is a high level of confidence (95 to 99%) that the only collection of non-random terrapin evidence data points occurs at the “Jackson Creek Concentration” in Nassau County (Figures 3A,B).

We documented vegetation data during 184 land surveys: 147 were from non-nesting sites and 37 were from nesting sites which resulted in 911 woody species observations. The most commonly occurring woody species in both nesting and non-nesting areas was southern red cedar (J. silicicola), followed closely by marsh elder (Iva frutescens), then yaupon (Ilex vomitoria) and cabbage palm (S. palmetto, Table 2).

TABLE 2

Table 2. Records of presence of 10 species of woody plants observed during land surveys of Diamondback Terrapin nesting and non-nesting habitats in northeast Florida.

A specialized matched-pairs t-test resulted in a mean difference of 52.3 (i.e., an average difference of 52.3 more non-nesting than nesting sites). The | t| ratio provided strong evidence that the difference between non-nesting and nesting was significant (Figure 6). In addition, the specialized matched-pairs t-test confirmed there are no outliers, indicating that decision tree analysis was an appropriate next step.

FIGURE 6

Figure 6. Specialized matched-pairs t-testing comparing woody species composition of nesting and non-nesting sites with a |t| ratio of 6.93 with |t| < 0.0001. A specialized matched-pairs t-test resulted in a mean difference of 52.3 represented by the solid red line and a 95% confidence interval of (40.8, 80.2) represented by the dotted red lines.

Decision tree analysis allowed us to predict terrapin activity based on available choices such as the presence of woody species at potential nesting sites (Stiglic et al., 2012). These results indicate that terrapins prefer to nest when Christmas berry (L. carolinianum) is present amongst the other available woody species, with the choices being equally weighted except for saw palmetto and pine, and with oak (Q. spp.) and wax myrtle (M. cerifera) following closely behind (Figures 7A,B). This conclusion is supported as R² = 0.025 in the least squares regression with four splits using a Classification and Regression Trees (CART) algorithm and a Whole Model Effects test outcome with |Prob > χ²| = 0.012 which is statistically significant.

FIGURE 7

Figure 7. (A) Partition via Classification and Regression Trees (CART) analysis supporting the conclusion that woody plant data suggest that significantly more nesting occurred when Christmas Berry (Lycium carolinianum) was present, and nesting was less likely when either Wax Myrtle (Myrica cerifera) or Oak (Quercus spp.) were present. (B) Decision tree with R² = 0.025 in the least squares regression with four splits using the CART algorithm.

Finally, we used a generalized linear binomial distribution fit model (i.e., GLM with binomial logit and maximum likelihood estimation) to determine whether the results from the decision tree were supported by the overall parameter estimates. Generalized linear binomial distribution fit produced a Whole Model test outcome showing that sites where Christmas berry was present exhibited a significantly higher proportion of terrapin nesting (|Prob > χ²| = 0.001) than those without (Table 2). Conversely, nesting was significantly less likely when either wax myrtle (|Prob > χ²| = 0.060) or oak (|Prob > χ²| = 0.021) were present. The presence of the other plant species had no significant statistical effect (Table 2). Thus, both tests produced statistically significant results which indicate that terrapins were likely to nest at sites where Christmas berry is present and tended to avoid nesting when oak and/or wax myrtle are present (Figure 6).

Discussion

Based upon the evidence, the most active area for terrapins in northeast Florida is in Nassau County. In the northern part of Nassau County, we recorded evidence of terrapins in the Bells River, Little Tiger Island, and in and around the Fernandina Harbor Marina (Figure 3A). We found no evidence in the Jolly River, Lanceford Creek, the southern shoreline of the St. Mary’s River including that of Ft. Clinch State Park, or in Egan’s Creek. We visited most places only once during the survey, therefore not finding evidence is not conclusive; common sense would dictate that terrapins are likely present throughout areas where the habitat is appropriate and that are bordered by areas where terrapins have been observed and documented.

In the southern part of Nassau County, the Holly Point and Goffinsville boat ramps had numerous depredated nests, and their shorelines offer the only apparent nesting habitat in the area, even though both are of anthropogenic origin (Figure 3A). The unnamed marsh island adjacent to Back River was identified by Butler (2002) as a place where at least some terrapins that nest on Sawpit Island spend the rest of their seasons (Figure 3A, green asterisk); we did not visit that marsh during this survey. Further east, we found no terrapin evidence in Harrison Creek and counted only one head in Walker Creek, even though both produced numerous head counts in previous years (Butler, unpubl. data).

The area around Jackson Creek (Figure 3B) yielded a variety of terrapin evidence including head counts, depredated nests, and many remains. The marsh area north of Jackson Creek abuts property owned by Rayonier Incorporated, which specializes in pulp, paper, and other cellulose products. Numerous depredated nests were recorded in 1995 on the southern banks of the Rayonier settling pond (Butler, unpubl. data, green asterisk on Figure 3B), but we were not granted permission to search the property for the current survey. Jackson Creek and its adjoining tributaries have been intensively trapped for blue crabs (Callinectes sapidus) for decades (P. Leary, resident of Jackson Creek, pers. comm.) and many terrapins enter and drown in crab traps in that area (Butler and Heinrich, 2007). Although most crab trappers would likely leave drowned terrapins in their traps as bait, we wonder if the extensive terrapin remains at the mouth of Jackson Creek are related to crab trapping. Conversely, these remains could be the result of extensive raccoon predation. Much of the habitat between Jackson Creek and SR 200 is owned by the Amelia Island Yacht Basin and considerable nesting occurs along the shoreline and some other high spots on the property. We found numerous depredated nests on the shoulders of the railroad tracks just northeast of SR 200.

Some of the Nassau evidence indicates that terrapins are not averse to exploiting habitat opportunities created anthropogenically. Most alterations of habitat by humans (i.e., channel dredging, bulkheading, building roads through salt marshes) are considered threats to terrapin survival (Maerz et al., 2018). However, Seigel (1980c) found terrapins using man-made lagoons and nesting on adjacent dyke roads. Feinberg and Burke (2003) recorded highest depredated terrapin nest densities on man-made trails. Roosenburg et al. (2014) demonstrated that terrapins will sometimes use artificially produced habitats for nesting with some success. The nesting activity associated with the Goffinsville and Holly Point boat ramps would not be possible without the construction associated with the ramps. Further, the construction of the SR 200 bridge and associated railroad tracks created more nesting opportunities at its base.

Within Duval County (Figure 4) the most notable area for terrapins is the nesting beach of Sawpit Island, which has been studied and monitored intermittently since 1996 (Butler, 2000, 2002; Butler et al., 2004; Munscher et al., 2012). In recent years, currents at the mouth of the Nassau River have led to extensive beach erosion, and part of the island has been breached to the extent that human passage is difficult or impossible during high tide (M. Simmons, Florida Fish and Wildlife, pers. comm.). Sand loss has decreased the area available for nesting, thus facilitating nest detection by predators. If the shoreline is destroyed, the fate of the terrapins that depend on this beach is unclear, as appropriate nesting habitat is scarce in the area.

Between Sawpit Island and the Ft. George River, terrapin evidence was present on most marsh islands and tributaries of the ICW. The area between the Ft. George and St. Johns rivers was also studied extensively during the late 1990s with head counts recorded in Cedar and Deep creeks nearly daily and radio telemetry studies done in Deep and Garden creeks (Butler, 2000, 2002). The current survey is notable for its paucity of terrapin evidence in all three of those creeks. Butler (2002) reported numerous terrapin heads in Deep Creek nearly every day during the nesting seasons over a three-year period (Figure 4, green asterisk). In 2014, despite traveling the entire length of Deep Creek on two separate days in May, we recorded no heads; and we saw no heads in Garden Creek. All creeks in that area were periodic sites of commercial crab trapping in the 1990s, and we fear the terrapin population could have been depleted. From the St. John’s River south to the Duval/St. John’s County line we found little evidence of terrapins.

In parts of northern St. John’s County, we were unable to perform land surveys because both east and west shorelines were privately owned (Figure 2); from the boat neither appeared to be appropriate nesting habitat. One locale in that county worthy of further research is the St. Augustine Inlet. On the western shoreline, both Hospital and Robinson creeks produced a variety of terrapin evidence. Further, the numerous adult terrapin sightings in Salt Run, to the southeast, signal what may be a notable population, and it is important to know where they nest so those areas can be protected. We recorded several depredated nests on the adjacent Conch Island, but these were sparse and do not appear to reflect a significant nesting site. Finally, in a May 2002 survey in St. Johns County, 15 swimming terrapins were counted while researchers waded an unnamed creek on the west shoreline of the Matanzas River, directly across from the north end of Rattlesnake Island, which is the home of the Ft. Matanzas National Monument (Butler and Heinrich, unpubl. data; green asterisk, Figure 4). We visited this creek during this survey in 2014 and found no evidence of terrapins.

Diamondback terrapins were more likely to nest in areas where Christmas berry was present. We do not suggest that terrapins seek out or even recognize Christmas berry, rather that it is present at most nest sites and can be a useful marker for researchers. This shrub is common in coastal marshes throughout Florida and the southeastern United States and is resistant to high salt concentrations, periodic flooding, and drought (Nelson, 1996). When present, Christmas berry is usually the first woody vegetation encountered as one proceeds inland from the water’s edge, and likely affords some cover for nesting terrapins and desirable thermal conditions for egg development. Conversely, terrapins were less likely to nest when oak and/or wax myrtle were present, and both species, when present in coastal regions, are typically found further inland (Johnson and Barbour, 1990). These areas may be unappealing to terrapins because they provide cover to mammalian nest predators (Burger and Montevecchi, 1975). Further, thicker canopies lead to lower nest temperatures (Jeyasuria et al., 1994) which would result in overproduction of male hatchlings, and Roosenburg (1996) suggested that female terrapins choose nesting sites that will produce both sexes. Christmas berry and marsh elder were often associated with terrapin nesting sites in the Big Bend area of Florida and their presence was used by the researchers as a possible nest site indicator (Hackney, 2010; Butler and Heinrich, 2013) found many depredated terrapin nests under wax myrtle in Virginia, and we report that in northeast Florida terrapins are less likely to nest in areas where this species is present. Future research on woody species as terrapin nest site markers could include comparing relative concentrations and canopy cover of each; Mitchell and Walls (2013) looked at this but not at the species level.

Data Availability Statement

The raw data supporting the conclusions of this article will be made available by the authors, without undue reservation.

Ethics Statement

The animal study was reviewed and approved by the Institutional Animal Care and Use Committee – UNF.

Author Contributions

JB contributed as the principal investigator, wrote grants for field study, managed students, and wrote most of the verbiage concerning terrapins. JL oversaw all terrapin data, produced maps for Figures 1–5, and provided interpretations when necessary. MD ran all vegetation statistics and provided interpretation. DM did fieldwork with JB and did some lab studies associated with the study. All authors contributed to the article and approved the submitted version.

Funding

We received funding from the UNF Coastal Biology Program, UNF Transformational Learning Opportunities Scholarships, UNF Student Summer Research Scholarship, a UNF Environmental Center Seed Grant, and a grant from the Diamondback Terrapin Working Group. We had a Florida Fish and Wildlife Conservation Commission Scientific Collecting Permit (LSSC-11-00080C) and project approval from the UNF Institutional Animal Care and Use Committee (IACUC 13-003).

Conflict of Interest

The authors declare that the research was conducted in the absence of any commercial or financial relationships that could be construed as a potential conflict of interest.

Publisher’s Note

All claims expressed in this article are solely those of the authors and do not necessarily represent those of their affiliated organizations, or those of the publisher, the editors and the reviewers. Any product that may be evaluated in this article, or claim that may be made by its manufacturer, is not guaranteed or endorsed by the publisher.

Acknowledgments

We appreciate field assistance from UNF Biology majors Sofia Herrera, Lili Kolluri, Mary Jo Monk, Lisa Parnell, Sam Shannon, and Dylan Van Pelt. Alice Bard, Scott Eastman, and Marie Melnechuk (all of FL DEP), and Tara Dodson (St. Johns County Environmental Supervisor) provided several reliable terrapin sightings from St, Johns County. Charlie Hoblin (resident of Fernandina Beach) alerted us to an intact terrapin nest in Nassau County and Mike Simmons (FL DEP) informed us of changing conditions on Sawpit Island. We thank the following people and organizations who allowed us to store/dock the boat at various times during the project: Talbot Islands State Park, GTM, Joe Springer at Fernandina Harbor Marina, Beach Marine, Camachee Cove Yacht Harbor, and Eric Ziecheck and Chris Kelly of Ripple Effect Ecotours at Marineland Marina. We thank Eric Johnson of the UNF Biology Department for assistance with statistical analysis and David Wilson of the UNF Center for Instruction and Research Technology for help constructing the maps.

Footnotes

1. ^ www.dtwg.org

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