There's a new kid in town


Editor's Introduction

Rapid evolution of a native species following invasion by a congener

annotated by
Fred Wasserman, Sandra Blumenrath

In recent years, biologists have increasingly recognized that evolutionary change can occur rapidly when natural selection is strong. In a field study conducted on small islands in Florida, Stuart et al. found that native lizards adapted to higher perches when a related species invaded their habitat. Within only about 3 years (or 20 generations) the perch height shift led to inherited morphological changes, including larger toepads.

Video. Anole lizards offer a great opportunity for researchers like Yoel Stuart and Jonathan Losos, two of the authors of this paper, to study natural selection in action. Looking at how anoles interact with their environment can answer how and why they have diversified into so many different species.


Paper Details

Supporting Media Partner

Original title
Rapid evolution of a native species following invasion by a congener
Yoel Stuart et al.
Original publication date
Vol 346, Issue 6208, pp. 463-466
Issue name


In recent years, biologists have increasingly recognized that evolutionary change can occur rapidly when natural selection is strong; thus, real-time studies of evolution can be used to test classic evolutionary hypotheses directly. One such hypothesis is that negative interactions between closely related species can drive phenotypic divergence. Such divergence is thought to be ubiquitous, though well-documented cases are surprisingly rare. On small islands in Florida, we found that the lizard A. carolinensis moved to higher perches following invasion by A. sagrei and, in response, adaptively evolved larger toepads after only 20 generations. These results illustrate that interspecific interactions between closely related species can drive evolutionary change on observable time scales.


In their classic paper, Brown and Wilson (1) proposed that mutually negative interactions between closely related species could lead to evolutionary divergence when those species co-occurred. In the six decades since, this idea has been debated vigorously, with support that has vacillated, depending on the latest set of theoretical treatments and comparative studies [reviewed in (2–5)]. However, tests of interaction-driven evolutionary divergence have been slow to capitalize on the growing recognition that evolutionary change can occur rapidly in response to strong divergent natural selection [but see (69)]; thus, evolutionary hypotheses about phenomena once thought to transpire on time scales too long for direct observation can be tested in real time while using replicated statistical designs.

An opportunity to study such real-time divergence between negatively interacting species has been provided by the recent invasion of the Cuban brown anole lizard, Anolis sagrei, into the southeastern United States, where Anolis carolinensis is the sole native anole. These species have potential to interact strongly [e.g., (10)], being very similar in habitat use and ecology (11). We investigated the eco-evolutionary consequences of this interaction on islands in Florida (12) using an A. sagrei introduction experiment, well-documented natural invasions by A. sagrei, genomic analyses of population structure, and a common garden experiment. This multifaceted approach can rule against several of the most difficult alternative hypotheses [e.g., plasticity, ecological sorting, environmental gradients (25)] while directly testing two predictions for how A. carolinensis responds to its congeneric competitor.


Image. Both anole species eat insects, are active during day, and live on the ground or low down on bushes and tree trunks. (A. carolinensis photo by Euku/Wikimedia Commons)

Typical of solitary anoles (13), A. carolinensis habitat use spans ground to tree crown (14). However, where A. carolinensis and A. sagrei (or their close relatives) co-occur elsewhere, A. carolinensis perches higher than A. sagrei (1316). Thus, we used an introduction experiment to test Collette’s prediction (14) that competitive interactions with A. sagrei should drive an increase in A. carolinensis perch height. In early May 1995, we chose six islands that contained resident populations of A. carolinensis and collected pre-introduction perch height data from undisturbed lizards (12). Later that month, we introduced small populations of A. sagrei to three treatment islands, leaving three control islands containing only A. carolinensis (12). From May to August 1995–1998, we measured perch heights for both species. The A. sagrei populations grew rapidly [table S1; (17)], and by August 1995, A. carolinensis on treatment islands already showed a significant perch height increase relative to controls, which was maintained through the study [Fig. 1, fig. S1, and table S2; (12)].

Video. An example of how different anole species in Puerto Rico divide up their habitat to avoid competition.


Fig. 1.  Perch height shift by A. carolinensis after the experimental introduction of A. sagrei.  We introduced A. sagrei to one small, one medium, and one large island (treatment; closed symbols) in 1995, keeping three similarly sized control islands (open symbols). Island means (±1 SE) are shown for perch height. Anolis sagrei introduction corresponds with a significant perch height increase by A. carolinensis (linear mixed models: treatment × time interactions, all < 0.001 [(12)]; tables S1 and S2].


The hypothesis being tested is that there will be competition when A. sagrei is introduced to an island occupied by A. carolinensis, and that A. carolinensis will shift to higher perches to avoid that competition. The type of competition is not studied in this experiment.

Experimental control

The control for the experiment was to look at the change in height used by A. carolinensis when no introduction occurred. The bottom three lines in the figure (those with open symbols) represent the results from the control experiment.


The top three lines in the figure (those with closed symbols) represent the A. sagrei introduction experiment. They show that A. carolinensis moved to higher perches after the introduction of A. sagrei, regardless of the size of the island.

In the control experiment without A. sagrei, A. carolinensis did not shift to higher perches during the time of the study (bottom three lines).

Island Sizes

To make sure the size of the island was not a confounding variable that could affect the results the researchers choose three different sizes for both the treatment and control (small, medium, and large). The graph has a separate line for each island.

We next predicted, following (14), that this arboreal shift by A. carolinensis would drive the evolution of larger toepads with more lamellae (adhesive, setae-laden, subdigital scales). Toepad area and lamella number (body-size corrected) correlate positively with perch height among anole species (14, 18–20), and larger and better-developed toepads improve clinging ability (20), permitting anoles to better grasp unstable, narrow, and smooth arboreal perches.

Video. Johnathan Losos and Sean Carroll demonstrate why toepad size matters, comparing a ground-dwelling lizard with one that lives in the canopy.

Image. Anole lizards gain their tree-clinging abilities in part from the size of their toepadsand the of ridges (or lamellae) on each toepad. Anole species known to live in trees all have toepads. Both A. sagrei and A. carolinensis live on the ground, so their toepads are relatively small.

We tested the prediction in 2010 on a set of islands partially overlapping those used in 1995–1998 (12). We surveyed 30 islands and found that A. sagrei had colonized all but five (12). We compared A. carolinensis populations on these five islands without the invader (hereafter “un-invaded”) to A. carolinensis populations on six islands that, on the basis of 1994 surveys, were colonized by A. sagrei sometime between 1995 and 2010 (hereafter “invaded”) [Fig. 2; (12)].


Fig. 2.  2010 study islands along the Intracoastal Waterway. Anolis carolinensis inhabits all study islands. Six study islands were invaded by A. sagrei sometime between 1995 and 2010 (closed circles), and five study islands remain un-invaded today (open circles). Nineteen additional non–study islands were surveyed [“x”; (12)]; 17 of these contained A. carolinensis and were invaded by A. sagrei; and two were empty of both species.

Study area

The map shows where the study took place and identifies the study islands. This research was conducted on the east coast of Florida, north of Orlando, near Cape Canaveral and the Kennedy Space Center.

The inset provides a zoomed-out view of Florida and identifies the precise location of the islands along the coast relative to the rest of Florida (small rectangle).


The study islands were all close to shore. The closed and open circles indicate 11 islands surveyed to answer questions about toepad evolution—six islands that were naturally invaded by A. sagrei (closed circles, black) and five that remained non-invaded (open circles, white). Four of the invaded islands were close to each other (top left).

Islands marked with an X symbol are 19 additional islands that were surveyed but not included in the study. 17 of these contained A. carolinensis and were invaded by A. sagrei, and two were empty of both species.

From May to August 2010, we measured perch height for undisturbed lizards and found that, as in the 1995 introduction experiment, A. carolinensis perch height was significantly higher on invaded islands [fig. S2 and table S3; (12)]. We then tested whether the perch height shift had driven toepad evolution by measuring toepad area and lamella number of the fourth toe of each hindleg for every A. carolinensis captured (12).

Image. The researchers measured toepad size and counted lamellae on the fourth toe of each lizard's right foot. The image shows the foot of a native A. carolinensis individual. (Photo by Yoel Stuart)
Video. Data collection procedures in the field: Although the researchers conduct a different anole study in this video, the measurements they take are the same. All lizards in the video are A. sagrei.

We found that A. carolinensis on invaded islands indeed had larger toepads and more lamellae [traits corrected for body size; Fig. 3, A and C, and table S3; (12)]).


Fig. 3.  Divergence in wild-caught and common garden A. carolinensis. Mean-of-island-means size-corrected residuals (±1 SE) are shown. The invasion of A. sagrei corresponds to a significant increase in both traits for wild-caught lizards (A and C) in 2010 [five islands un-invaded, six invaded; linear mixed models (LMM); (A) toepad area, βinvaded = 0.15, t= 2.7, = 0.012; (C) lamella number, βinvaded = 0.54, t= 3.1, = 0.009]. (B and D) Common garden offspring from invaded islands had significantly larger toepad characteristics [four un-invaded islands; four invaded; LMM; (B) toepad area, βinvaded = 0.14, t6= 2.1, = 0.043; (D) lamella number, βinvaded = 1.45, t= 3.6, = 0.006]. All values are one-tailed.

Wild-caught lizards

When lizards perch higher and on thin branches, it becomes harder for them to hold on to the surface. The researchers therefore wanted to test whether on invaded islands A. carolinensis had evolved larger toepads with more lamellae (or ridges) as an adaptation to moving to higher perches compared to lizards on noninvaded islands, making it easier to cling to surfaces and grasp thin branches.

The researchers measured toepad area and the number of lamellae of the fourth toe of each hindleg.

Common garden lizards

The researchers also conducted a common garden experiment to test whether toepad features, such as size and number of lamellae (or ridges), could not be changed by environmental factors during development and were instead determined by genes passed down from their parents.

They took eggs from female A. carolinensis living on islands with and without A. sagrei (invaded and noninvaded islands) and raised them under exactly the same environmental conditions in the lab. They then compared differences in the offspring’s toepad features with differences in toepad features in the wild-caught lizards that live on the different islands.

If the differences found in the wild are recovered in the lab, it suggests genetic control, and rules out the possibility that toepad features could be determined by environmental factors, such as how much time a lizard spends high in the bushes versus on the ground.

Results: Wild-caught

Panels A and C show that after the introduction of A. sagrei on the invaded islands A. carolinensis had significantly larger toepads (Panel A) with more lamellae (Panel C).

Note that the researchers corrected the lamella results for toepad size, because larger toepads typically also have more lamellae. What they were interested in was whether lizards have more lamellae relative to body size, because relatively more lamellae means that they can cling better to surfaces.

Results: Common garden

Panels B and C show that when raised under identical conditions in the laboratory, lizards had toepad area and lamella number similar to their parents.


The offspring (common garden lizards) had toepad characteristics similar to their parents.

The researchers were now able to rule out that posthatching, developmental responses to physical challenges during development, such as having to climb higher perches, could have been responsible for the toepad changes measured in lizards living on invaded islands (wild-caught lizards).

This morphological change occurred quickly. Assuming, conservatively, that A. sagrei reached all six invaded islands in 1995, A. carolinensis populations on invaded and un-invaded islands have diverged at mean rates of 0.091 (toepad area) and 0.077 (lamellae) standard deviations per generation [haldanes (21); rates > zero, each one-tailed < 0.02; (12)], comparable to other examples of rapid evolution (21) such as soapberry bug beak length (22) or guppy life history (23).

We tested several alternative processes that could have generated the observed divergence. First, we used a common garden experiment to investigate possible posthatching, developmental responses to physical challenges imposed by arboreality during growth (i.e., phenotypic plasticity). We took gravid A. carolinensis females from four invaded and four un-invaded islands in July 2011, collected their eggs in the laboratory, and raised the offspring in identical conditions (12). The effect of A. sagrei invasion on A. carolinensis toepad characteristics persisted in the common garden [Fig. 3, B and D, and table S4; (12)], suggesting genetically based divergence in nature (though we cannot rule out transgenerational plasticity).

Second, observed divergence in A. carolinensis could have arisen through nonrandom migration of individuals with large toepads among invaded islands, instead of arising independently on each island. Thus, we tested whether relatedness among A. carolinensis populations is independent of A. sagrei invasion. In 379 A. carolinensis individuals from four un-invaded and five invaded islands, we genotyped 121,973 single-nucleotide polymorphisms across the genome [table S5, (12)]. Individuals from the same island were closely related, and islands were largely genetically independent (pairwise-FST 0.09–0.16; table S6). We found no evidence that population relatedness in A. carolinensis was correlated with whether an island had been colonized by A. sagrei [Fig. 4; (12)] or with distance between islands (Mantel test; P> 0.25), suggesting that gene flow is relatively limited among islands and that island populations were independently founded from the mainland.


Fig. 4.  Neighbor-net analysis of genetic distance for A. carolinensis individuals from invaded (red) and un-invaded (blue) islands (12).  Small shaded areas enclose individuals that do not cluster with their own island; the color of these areas represents invasion status of their home islands.


The researchers wanted to be sure that the difference in toepad size observed in lizards living on invaded and noninvaded islands were not simply because a few A. carolinensis lizards with larger toepads, for example, happened to migrate to invaded islands.

If this were the case, then A. carolinensis populations on the islands where A. sagrei invaded would be related more to each other than to populations on islands where there were no invasions. The authors therefore tested the relatedness of the different A. carolinensis populations.


The researchers genotyped 121,973 single-nucleotide polymorphisms across the genome.


Lizards closely related to each other are clustered together, and red and blues circles represent individual islands.

The figure shows that, with few exceptions, lizards grouped together in a cluster also live on the same island. This means that individuals from the same island were more closely related to each other than to individuals from other islands, and that islands were largely genetically independent.

Relatedness was also independent of whether an island had been invaded by A. sagrei or not: Lizards on invaded island (red circles) are no more related to each other than to lizards on noninvaded islands (blue circles).


The authors found that the relatedness of A. carolinensis populations was independent of whether an island had been colonized by A. sagrei. Therefore, differences in toepads were evolving separately each time on each island.

Third, toepad changes could have been generated by adaptation to environmental differences among islands that are confounded with the presence of A. sagrei [e.g., (24)]. However, invaded and un-invaded islands do not differ in characteristics important to perching or arboreal locomotion [e.g., vegetated area, plant species richness, or available tree heights; table S7; (12)]. Fourth, toepad changes could have arisen through ecological sorting, wherein A. sagrei was only able to colonize those islands on which the existing A. carolinensis population was already sufficiently different. However, A. sagrei seems capable of successfully colonizing every island it reaches, regardless of resident A. carolinensis ecology or morphology: All 10 A. sagrei populations introduced in 1994–1995 are still extant (12), and A. sagrei inhabits nearly every other island surveyed in the lagoon (Fig. 2). Finally, toepad changes observed in A. carolinensis in 2010 could be unrelated to interactions with A. sagrei if the latter’s invasion merely missed the five islands with the lowest A. carolinensis perch heights (fig. S2) by chance; however, this would occur only one time in 462. In sum, alternative hypotheses of phenotypic plasticity, environmental heterogeneity, ecological sorting, nonrandom migration, and chance are not supported; our data suggest strongly that interactions with A. sagrei have led to evolution of adaptive toepad divergence in A. carolinensis.

Brown and Wilson called evolutionary divergence between closely related, sympatric species “character displacement” (1), and our data constitute a clear example of this. Resource competition has been the interaction suggested most often as the source of divergent selection during character displacement [sometimes specifically called “ecological character displacement” (13)]. For A. carolinensis and A. sagrei, resource competition for space likely is important: Allopatric A. carolinensis and A. sagrei overlap in their use of the habitat (1214,16); moreover, when they co-occur, the two species interact agonistically (10), and our experimental data show a rapid spatial shift by A. carolinensis following A. sagrei introduction. The two species also overlap in diet and thus may compete for food (17). Competition for food is strong among co-occurring Anolis and has been shown to be mitigated by differences in perch height (11). Evolutionary divergence may also arise, however, from selection to reduce interspecific hybridization; yet, such “reproductive character displacement” (4) seems an unlikely explanation for our results, as A. carolinensis and A. sagrei already differ markedly in species-recognition characteristics, males of both species nearly exclusively ignore heterospecific females in staged encounters (25), and the species have never been reported to successfully produce hybrids. We note, finally, that other mutually negative interactions such as apparent competition (26) and intraguild predation (27) could also produce divergence among overlapping species. These remain to be explored in this system, though some evidence exists for at least the latter (17).

Here, we have provided evidence from a replicated, natural system to support the long-held idea (4) that interspecific interactions between closely related species are an important force for evolutionary diversification (2). Moreover, we show that evolutionary hypotheses such as character displacement can be rigorously tested in real time following human-caused environmental change. Our results also demonstrate that native species may be able to respond evolutionarily to strong selective forces wrought by invaders. The extent to which the costs of invasions can be mitigated by evolutionary response remains to be determined (28), but studies such as this demonstrate the ongoing relevance of evolutionary biology to contemporary environmental issues.

Video. Micro- vs. macroevolution: The study demonstrates how interactions between two species can lead to evolutionary change. But for two anole species to arise, other conditions have to be met.


  1. W. L. Brown, E. O. Wilson, Character displacement. Syst. Zool. 5, 49–64 (1956)

  2. D. Schluter, The Ecology of Adaptive Radiation (Oxford Univ. Press, Oxford, UK, 2000).

  3. T. Dayan, D. Simberloff, Ecological and community?wide character displacement: The next generation. Ecol. Lett. 8, 875–894 (2005).

  4. D. W. Pfennig, K. S. Pfennig, Evolution's Wedge (Univ. of California Press, Berkeley, 2012).

  5. Y. E. Stuart, J. B. Losos, Ecological character displacement: Glass half full or half empty? Trends Ecol. Evol. 28, 402-408 (2013).

  6. P. R. Grant, B. R. Grant, Evolution of character displacement in Darwin’s finches. Science 313,224–226 (2006).

  7. J. G. Tyerman, M. Bertrand, C. C. Spencer, M. Doebeli, Experimental demonstration of ecological character displacement. BMC Evol. Biol. 8, 34 (2008). 

  8. L. M. Bono, C. L. Gensel, D. W. Pfennig, C. L. Burch, Competition and the origins of novelty: Experimental evolution of niche-width expansion in a virus. Biol. Lett. 9, 20120616 (2013).

  9. M. L. Taper, in Bruchids and Legumes: Economics, Ecology, and Coevolution, K. Fujii, A. Gatehouse, C. D. Johnson, R. Mitchel, T. Yoshida, Eds. (Kluwer, Dordrecht, Netherlands, 1990), pp. 289–301.

  10. J. R. Edwards, S. P. Lailvaux, Do interspecific interactions between females drive shifts in habitat use? A test using the lizards Anolis carolinensis and A. sagreiBiol. J. Linn. Soc. Lond. 110, 843–851 (2013). doi:10.1111/bij.12180

  11. J. B. Losos, Lizards in an Evolutionary Tree: Ecology and Adaptive Radiation of Anoles (Univ. of California Press, Berkeley, 2009).

  12. T. W. Schoener, Presence and absence of habitat shift in some widespread lizard species. Ecol. Monogr45, 233–258 (1975).

  13. B. B. Collette, Correlations between ecology and morphology in anoline lizards from Havana, Cuba, and southern Florida. Bull. Mus. Comp. Zool. 125, 137–162 (1961).

  14. L. R. Schettino, J. B. Losos, P. E. Hertz, K. de Queiroz, A. R. Chamizo, M. Leal, V. R. González, The anoles of Soroa: Aspects of their ecological relationships. Breviora 520, 1–22 (2010).

  15. J. R. Edwards, S. P. Lailvaux, Display behavior and habitat use in single and mixed populations of Anolis carolinensis and Anolis sagrei lizards. Ethology 118, 494–502 (2012).

  16. T. S. Campbell, thesis, University of Tennessee, Knoxville (2000).

  17. D. Glossip, J. B. Losos, Ecological correlates of number of subdigital lamellae in anoles. Herpetologica 53, 192–199 (1997).

  18. T. E. Macrini, D. J. Irschick, J. B. Losos, Ecomorphological differences in toepad characteristics between mainland and island anoles. J. Herpetol. 37, 52–58 (2003). 

  19. J. Elstrott, D. J. Irschick, Evolutionary correlations among morphology, habitat use and clinging performance in Caribbean Anolis lizards. Biol. J. Linn. Soc. Lond. 83, 389–398 (2004).

  20. A. P. Hendry, M. T. Kinnison, Perspective: The pace of modern life: Measuring rates of contemporary microevolution. Evolution 53, 1637–1653 (1999).

  21. S. P. Carroll, C. Boyd, Host race radiation in the soapberry bug: Natural history with the history. Evolution 46, 1052–1069 (1992).

  22.  D. N. Reznick, F. H. Shaw, F. H. Rodd, R. G. Shaw, Evaluation of the rate of evolution in natural populations of guppies (Poecilia reticulata). Science 275, 1934–1937 (1997). 

  23. S. Meiri, D. Simberloff, T. Dayan, Community-wide character displacement in the presence of clines: A test of Holarctic weasel guilds. J. Anim. Ecol. 80, 824–834 (2011).

  24. R. R. Tokarz, J. W. Beck Jr., Behaviour of the suspected lizard competitors Anolis sagrei and Anolis carolinensis: An experimental test for behavioural interference. Anim. Behav35, 722–734 (1987).

  25. R. D. Holt, Predation, apparent competition, and the structure of prey communities. Theor. Popul. Biol. 12, 197–29 (1977).

  26. G. A. Polis, C. A. Myers, R. D. Holt, The ecology and evolution of intraguild predation: Potential competitors that eat each other. Annu. Rev. Ecol. Syst. 20, 297–330 (1989).

  27. R. Shine, Invasive species as drivers of evolutionary change: Cane toads in tropical Australia. Evol. Appl. 5, 107–116 (2012).

  28. M. Tollis, S. Boissinot, Genetic variation in the green anole lizard (Anolis carolinensis) reveals island refugia and a fragmented Florida during the quaternary. Genetica 142, 59–72 (2014).

  29. T. S. Campbell, A. C. Echternacht, Introduced species as moving targets: Changes in body sizes of introduced lizards following experimental introductions and historical invasions. Biol. Invasions 5,193–212 (2003).

  30. A. S. Rand, Ecological distribution in anoline lizards of Puerto Rico. Ecology 45, 745–752 (1964).

  31. A. Gelman, J. Hill, Data Analysis Using Regression and Multilevel/Hierarchical Models. (Cambridge Univ. Press, Cambridge, UK, 2007).

  32. J. Pinheiro, D. Bates, S. DebRoy, D. Sarkar, nlme: Linear and Nonlinear Mixed Effects Models. R package version 3.1-117 (2014);

  33. J. Oksanen, F. G. Blanchet, R. Kindt, P. Legendre, vegan: Community Ecology Package Version 2.0-8. (2013).

  34. B. C. Lister, The nature of niche expansion in West Indian Anolis lizards I: Ecological consequences of reduced competition. Evolution 30, 659–676 (1976). doi:10.2307/2407808

  35. B. C. Lister, The nature of niche expansion in West Indian Anolis lizards II: Evolutionary components.Evolution 30, 677–692 (1976). doi:10.2307/2407809

  36. M. K. Hecht, Natural selection in the lizard genus AristelligerEvolution 6, 112–124 (1952).

  37. P. D. Etter, S. Bassham, P. A. Hohenlohe, E. A. Johnson, W. A. Cresko, SNP discovery and genotyping for evolutionary genetics using RAD sequencing. Methods Mol. Biol. 772, 157–178 (2011).

  38. J. Catchen, P. A. Hohenlohe, S. Bassham, A. Amores, W. A. Cresko, Stacks: An analysis tool set for population genomics. Mol. Ecol. 22, 3124–3140 (2013).

  39. B. Langmead, S. L. Salzberg, Fast gapped-read alignment with Bowtie 2. Nat. Methods 9, 357–359(2012).

  40. P. A. Hohenlohe, S. Bassham, P. D. Etter, N. Stiffler, E. A. Johnson, W. A. Cresko, Population genomics of parallel adaptation in threespine stickleback using sequenced RAD tags. PLOS Genet. 6, e1000862(2010).

  41. D. H. Huson, D. Bryant, Application of phylogenetic networks in evolutionary studies. Mol. Biol. Evol. 23,254–267 (2006).

  42. D. Bryant, V. Moulton, in Algorithms in Bioinformatics, Lecture Notes in Computer Science. R. Guigo, D. Gusfeld, Eds. (Springer Berlin Heidelberg, Berlin, Heidelberg, 2002), vol. 2452, pp. 375–391.

  43. B. S. Weir, C. C. Cockerham, Estimating F-statistics for the analysis of population structure. Evolution 38, 1358–1370 (1984).

  44. E. Paradis, J. Claude, K. Strimmer, APE: Analyses of phylogenetics and evolution in R language. Bioinformatics 20, 289–290 (2004). 

Acknowledgments: We thank A. Kamath, C. Gilman, A. Algar, J. Allen, E. Boates, A. Echternacht, A. Harrison, H. Lyons-Galante, T. Max, J. McCrae, J. Newman, J. Rifkin, M. Stimola, P. VanMiddlesworth, K. Winchell, C. Wiench, K. Wollenberg, and three reviewers; M. Legare and J. Lyon (Merritt Island National Wildlife Refuge), J. Stiner and C. Carter (Canaveral National Seashore); and Harvard University, Museum of Comparative Zoology, University of Massachusetts Boston, University of Tennessee Knoxville, University of Tampa, NSF (DEB-1110521), and NIH (P30GM103324) for funding. Y.E.S., T.S.C., and J.B.L. designed the study; Y.E.S., T.S.C., P.A.H., L.J.R, and R.G.R. collected the data; Y.E.S., T.S.C., and P.A.H. analyzed the data; all authors contributed to the manuscript. Data are accessioned on doi:10.5061/dryad.96g44.