Both authors contributed equally to the work.
Physiological adaptation along environmental gradients and replicated hybrid zone structure in swordtails (Teleostei: Xiphophorus)
Article first published online: 25 JUL 2012
© 2012 The Authors. Journal of Evolutionary Biology © 2012 European Society For Evolutionary Biology
Journal of Evolutionary Biology
Volume 25, Issue 9, pages 1800–1814, September 2012
How to Cite
Culumber, Z.W., Shepard, D.B., Coleman, S.W., Rosenthal, G.G. and Tobler, M. (2012), Physiological adaptation along environmental gradients and replicated hybrid zone structure in swordtails (Teleostei: Xiphophorus). Journal of Evolutionary Biology, 25: 1800–1814. doi: 10.1111/j.1420-9101.2012.02562.x
- Issue published online: 14 AUG 2012
- Article first published online: 25 JUL 2012
- Received 2 April 2012; revised 17 May 2012; accepted 23 May 2012
- ecological niche modelling;
- elevation gradient;
- population genetics;
- thermal tolerance
- Top of page
- Materials and methods
- Supporting Information
Local adaptation is often invoked to explain hybrid zone structure, but empirical evidence of this is generally rare. Hybrid zones between two poeciliid fishes, Xiphophorus birchmanni and X. malinche, occur in multiple tributaries with independent replication of upstream-to-downstream gradients in morphology and allele frequencies. Ecological niche modelling revealed that temperature is a central predictive factor in the spatial distribution of pure parental species and their hybrids and explains spatial and temporal variation in the frequency of neutral genetic markers in hybrid populations. Among populations of parentals and hybrids, both thermal tolerance and heat-shock protein expression vary strongly, indicating that spatial and temporal structure is likely driven by adaptation to local thermal environments. Therefore, hybrid zone structure is strongly influenced by interspecific differences in physiological mechanisms for coping with the thermal environment.
- Top of page
- Materials and methods
- Supporting Information
Geographic variation in environmental conditions affects survival and reproduction of organisms and determines their distribution across small and large spatial scales (McArthur et al., 1988; Peterson, 1993; Rainey & Travisano, 1998; Slabbekoorn & Smith, 2002; Novembre & Di Rienzo, 2009). As such, environmental variation is a key driver in the evolution of biodiversity, giving rise to genetic and phenotypic variation within species (Mayr, 1963; Endler, 1977; Kawecki & Ebert, 2004; Shepard & Burbrink, 2011) and also mediating the evolution of reproductive isolation, resulting in closely related species being distributed along environmental gradients (e.g. Schluter, 2000; Doebeli & Dieckmann, 2003; Rundle & Nosil, 2005; Keller & Seehausen, 2012). Environmental gradients not only provide an initial stimulus for divergence, but may also serve as conduits for secondary contact between related species occurring in distinct environments, thus facilitating hybridization. Consequently, hybrid zones commonly coincide with environmental gradients (Fritsche & Kaltz, 2000; Yanchukov et al., 2006; Kameyama et al., 2008), and two types in particular, tension zones and zones of bounded hybrid superiority, tend to occur along gradients in biotic and abiotic variables (Good et al., 2000; Gay et al., 2008; Ruegg, 2008).
The longstanding belief that hybrid zones are evolutionary sinks that inhibit diversification (Mayr, 1963; Wagner, 1970) has been subtly perpetuated due to a focus on tension zones, in which reduced hybrid fitness is balanced by inward dispersal and continual hybridization of parentals (reviewed in Barton & Hewitt, 1985). However, hybridization can be a source of evolutionary novelty and produce transgressive or intermediate phenotypes that outperform parentals under certain environmental conditions (Lewontin & Birch, 1966; Seehausen, 2004; Bell & Travis, 2005; Parnell et al., 2008; Tobler & Carson, 2010). These hybrid zones are often referred to as cases of ‘bounded hybrid superiority’ (Moore, 1977) because hybrids can have greater fitness than either parental species in intervening transitional habitats (i.e. ecotones). These cases in which hybrids outperform parental species remain less well understood, even though hybrid superiority is a requisite for homoploid hybrid speciation (e.g. Salzburger et al., 2002; Schliewen & Klee, 2004; Gompert et al., 2006; Mallet, 2007; Jiggins et al., 2008). Elucidating the mechanisms underlying hybrid superiority involves identifying both the traits mediating adaptation and the selective forces that determine fitness in the respective environment (for review, see Arnold & Martin, 2010). This can be particularly challenging because environmental gradients are notoriously complex due to covariation among multiple abiotic and biotic environmental variables (Grether et al., 2001; Reznick et al., 2001; Tobler & Plath, 2011).
Here, we examine a case in which hybrids are abundant in an area of secondary contact between two swordtail fish species occurring along an elevational gradient. In the Río Pánuco basin, along the eastern slopes of the Sierra Madre Oriental of Mexico, Xiphophorus birchmanni is distributed throughout the lowlands and foothills, generally below 400 m above sea level. In contrast, X. malinche has a strictly highland distribution and is known from only six sites in headwater streams (Rauchenberger et al., 1990; Gutiérrez-Rodríguez et al., 2008; Culumber et al., 2011). Fertile hybrids of the two species are abundant at intermediate elevations (Rosenthal et al., 2003; Culumber et al., 2011). This high–intermediate–low-elevation distribution of X. malinche, hybrids and X. birchmanni is observed in a replicated fashion in at least seven separate stream reaches (Culumber et al., 2011), indicating that natural selection along the elevational gradient maintains replicated hybrid zone structure. However, it is as yet unknown what environmental factors stabilize the hybrid zones and what traits mediate local adaptation of parentals and hybrids in their respective environments. Additionally, if this is a case of bounded hybrid superiority maintained by abiotic variables, then we would expect to find certain variables that restrict parentals to their areas of occurrence and for which hybrids outperform parentals in their area of occurrence.
In this study, we used an integrative approach to elucidate the role of abiotic environmental conditions, particularly climatic and hydrographic variables, in stabilizing the replicated hybrid zone structure between X. birchmanni and X. malinche. Our approach included the following: (i) We used ecological niche modelling (ENM) to test whether the distributions of X. birchmanni, X. malinche and their hybrids could be predicted by abiotic environmental variables and whether they occupy different environmental niches. We further used spatially explicit climatic and hydrographic data to compare environments occupied by both parental species and hybrids in order to identify the specific variables that differ among the three groups. (ii) Using the variables found to differ between the two parental species, we tested whether we could predict spatial and temporal variation in species-specific allele frequencies at a finer scale within only hybrid localities. To do this, we genotyped individuals from multiple hybrid populations using single-nucleotide polymorphism (SNP) markers and related allele frequencies with environmental variables to analyse variation in both space and time. If the factors that emerge in spatial analyses do in fact impose selection related to thermal tolerance, then temporal analyses should demonstrate concomitant changes in allele frequencies. (iii) With temperature emerging as a key predictor variable in various analyses, we examined thermal tolerance to compare physiological trait differentiation among parental and hybrid populations. We used a loss-of-equilibrium assay to quantify both heat and cold tolerance of wild-caught parentals and hybrids during summer and winter. We also tested pure parental fish born and reared in a common garden environment to determine whether between-species variation in tolerance can be attributed to genetic differences or to phenotypic plasticity. (iv) Finally, we quantified and compared gene expression of heat-shock proteins (hsps), which act as molecular chaperones to buffer against cell damage in response to thermal stress (Feder & Hoffmann, 1999), in wild-caught fish and in laboratory-acclimated fish exposed to acute thermal stress.
Materials and methods
- Top of page
- Materials and methods
- Supporting Information
Ecological niche modelling
To evaluate the abiotic environmental factors that influence the distribution of each parental species and their hybrids and test whether they occupy distinct environments, we conducted GIS-based analyses of each species’ environmental niche using ENM techniques (Peterson, 2001; Kozak et al., 2008; Elith & Leathwick, 2009). We obtained locality point data for each species and their hybrids (Table S1) from our own fieldwork (Culumber et al., 2011; GGR and MT unpublished data) and the published literature (Gutiérrez-Rodríguez et al., 2008). Localities where only pure X. birchmanni or pure X. malinche were observed were classified as X. birchmanni and X. malinche sites, respectively. Any locality where hybrids were present was classified as a hybrid site. Next, we assembled a set of coverages for 24 environmental variables from the Worldclim (http://www.worldclim.org) and Hydro1k (http://eros.usgs.gov/#/Find_Data/Products_and_Data_Available/gtopo30/hydro) project databases. Data layers were either downloaded or projected at 30 arc-seconds (∼1 km2) resolution. The Worldclim data set is composed of 19 bioclimatic variables related to temperature, precipitation and seasonality, whereas the Hydro1k data set is composed of five variables related to hydrography (Hijmans et al., 2005; Kozak et al., 2008). The variables in these data sets have been used successfully in previous studies on freshwater fish species employing ENM (e.g. Domínguez-Domínguez et al., 2006; Chen et al., 2007; McNyset, 2009; Costa & Schlupp, 2010). We clipped data layers to a region that included the north-eastern portion of the state of Hidalgo, and adjacent parts of Veracruz, San Luis Potosí and Querétaro states (20.5–21.4° N and 97.9–99.1° W; Fig. 1). This region encompasses the Río Pánuco and its tributaries and spans an elevation range from 45 to 2527 m above sea level (Fig. 1). This spatial extent should provide adequate information to train the ENMs while also restricting analyses to a geographic area in which species could possibly occur (Anderson & Raza, 2010; Barve et al., 2011; Elith et al., 2011).
We constructed ENMs for each species and their hybrids using a maximum entropy method implemented in the program Maxent v.3.3.2 (Phillips et al., 2006; Phillips & Dudik, 2008). Maxent uses environmental variables from localities at which a species has been documented previously (i.e. training data) to build a predictive model of where else the species may occur due to the presence of similar environmental conditions (see Elith et al., 2011 for details). The output of Maxent consists of a threshold-independent measure of the overall performance of the model (area under the receiver operating curve or AUC) and a grid map with each cell having an index of suitability between 0 and 1 (logistic output); higher values indicate higher predicted suitability. An AUC value of 0.5 indicates that the predictive model is no better than random, whereas higher AUC values indicate better predictive ability with a value of 1 indicating perfect prediction. Results also include an analysis of each variable’s relative contribution to the model and can be used to assess which variables are most important in predicting the species’ distribution. Maxent has been shown to perform better than other methods for constructing ENMs, especially when the number of occurrence points is low (e.g. 5–10; Elith et al., 2006; Pearson et al., 2007; Costa et al., 2010). We used autofeatures in Maxent and the default regularization multiplier parameter (1.0). Additionally, we removed duplicate presence points (i.e. points that mapped to the same 1-km2 grid cell) and increased the number of iterations to 5000 in order to allow the program to run to the default convergence threshold (10−5).
Although Maxent is able to handle correlation among variables better than other niche modelling methods, reducing the number of variables to those considered ecologically relevant and nonredundant makes testing and interpretation more straightforward (Elith et al., 2011). Further, using fewer variables minimizes the potential for model overfitting (Warren & Seifert, 2011). To reduce the number of variables, we used the principal components tool in the ArcGIS v.9.3 Spatial Analyst extension to construct correlation matrices for our 19 bioclimatic and five hydrographic variables across our spatial extent. For variables that were correlated at r > 0.9, we retained only a single variable, preferentially choosing variables that measured extremes over those that measured averages (Shepard & Burbrink, 2008). Extremes (e.g. heat, cold, aridity) were preferentially chosen over averages because they are more likely to set the range limits of species as they provide greater opportunity for selection (Sexton et al., 2009). This procedure left us with 11 variables for use in analyses (eight Worldclim and three Hydro1k; Table S2).
To gauge the sensitivity of each species ENM to the samples used to train the model and to test the predictive ability of the models, we performed 10 replicate runs for each species using a different random seed and subsampling with 66% of samples allotted for training and 34% for testing. For each species, we examined the mean AUC across the 10 replicates and considered a mean AUC value ≥ 0.7 as evidence that the model had sufficient discriminatory ability (Swets, 1988). The final ENM for each species was constructed using all data points to train the model (X. birchmanni: n = 21, X. malinche: n = 6, Hybrids: n = 31). We overlaid the ENM for each species generated in Maxent on a map of the study region using the Minimum Training Presence threshold to classify grid cells as unsuitable (i.e. outside the species’ niche) if they fell below this value (Fielding & Bell, 1997; Liu et al., 2005).
To quantify the amount of niche overlap among species and test whether species occupy different environmental niches, we used a series of measures and tests in the program ENMTools (Warren et al., 2008, 2010). ENMTools uses the ENMs for two species and calculates the degree of niche overlap using two measures: Schoener’s D and Warren’s I (see Warren et al., 2008, 2010 for details). For both measures, niche overlap can range from 0, indicating no overlap, to 1, indicating complete overlap. To test whether species occupy different environmental niches, we performed a Niche Identity Test in ENMTools using 1000 iterations (Warren et al., 2008, 2010). Briefly, this test involves multiple iterations of randomizing the locality points for two species, building ENMs in Maxent using the randomized points and then calculating the degree of niche overlap. If the observed niche overlap is <95% of the randomized niche overlap values (one-tailed test), then the niches of the two species are considered significantly different (Warren et al., 2008, 2010).
Because niches may be expected to differ in species whose ranges do not overlap greatly, we also used the Background Test in ENMTools to test whether niches are more or less divergent than expected given how environmental conditions vary among species’ ranges (i.e. the background environment; Warren et al., 2008, 2010). This test involves multiple iterations in which niche overlap is calculated between one species’ ENM and an ENM constructed from random points within the range (i.e. background) of another species. Tests are conducted for all pairwise species comparisons and in both directions. The observed niche overlap is compared to the distribution of overlap values from the runs in each direction to determine whether species’ niches are significantly more or less divergent than expected (two-tailed test). Rejection of the null hypothesis indicates that observed niche differences are a function of habitat selection and/or availability, and is often interpreted as evidence for niche conservatism (niches more similar than expected) or niche divergence (niches more different than expected; Warren et al., 2008, 2010). Failure to reject the null hypothesis indicates that niche differentiation between species is explained by variation in the environmental conditions available to each within their respective ranges (Warren et al., 2008, 2010). To delimit species’ backgrounds for analysis, we created a minimum convex polygon (MCP) around each species’ data points (Warren et al., 2008). The space encompassed by each of these MCPs did not include any area outside the drainages where these species occur, so they contain potentially accessible habitats and should represent suitable backgrounds for analysis (Warren et al., 2008; McCormack et al., 2010). Because fish require aquatic habitats and random points within background areas may sometimes fall in grid cells without such habitats, we were concerned that species niches may appear to be more similar than expected due to their basic requirements for water rather than due to the environmental factors being examined. To address this possibility, we ran Background Tests twice: once with the 11 climatic and hydrologic variables and once with only the eight climatic variables. We ran each Background Test for 1000 iterations.
To further examine the ability of environmental conditions to explain the occurrence of each group and to identify variables driving niche differentiation, we extracted values for the 11 environmental variables used in ENM from each of our sampling sites and conducted a discriminant function analysis (DFA). The DFA was used to determine the percentage of sites that could be correctly assigned to parental and hybrid populations solely based on environmental conditions. This approach of ENM followed by a multivariate analysis such as DFA provides a more rigorous test of environmental differences among species than either analysis alone can provide (McCormack et al., 2010). ENMs provide a quantitative estimate of each species environmental niche and identify important variables for each species independent of the other species. Because the contributions of variables differ among species ENMs, ENM-based tests for niche differentiation do not reveal the specific environmental factors that differ among species. Using DFA with the same set of variables allows us to test which variables best explain differences in environmental conditions among species and separate their distributions.
Environmental effects on spatial and temporal variation in allele frequencies
Based on our prediction that abiotic environmental conditions will influence the distributions of parentals and hybrids in the Xiphophorus system, we asked whether environmental variables that differ between parental species, and potentially limit their distributions could predict spatial and temporal variation in allele frequencies in hybrid populations. To address spatial variation, we used data from one mitochondrial and three unlinked nuclear intron SNPs (Table S3; Culumber et al., 2011) from hybrid populations and subjected genotypic data to a principal components analysis (see Cavalli-Sforza & Feldman, 2003; Patterson et al., 2006). Only one component had an eigenvalue larger than one, and all four markers were highly and positively correlated with each other; that is, the first principal component adequately describes the frequency of X. birchmanni and X. malinche alleles within a population, with positive scores indicating a surplus of X. birchmanni alleles and negative scores a surplus of X. malinche alleles (Table S4). We used the results from a DFA of environmental variables separating the two parental species (Table S5a) to determine which variables were most important in discriminating between sites where parental X. birchmanni and parental X. malinche occur. Based on that discriminant function, five variables (mean temperature of the warmest quarter, minimum temperature of coldest month, maximum temperature of warmest month, precipitation of the driest quarter and mean daily temperature range) with the highest canonical correlations (r > 0.3) were used as independent variables in a multiple regression model (based on backwards elimination) to predict variation in X. birchmanni allele frequencies across hybrid populations in the SNP data set.
To address temporal variation, we investigated whether temperature variables 90 days prior to the sampling date could predict the incidence of X. birchmanni alleles in 10 hybrid populations for which we had samples from more than one point in time. For those 10 hybrid populations, samples had been collected from two to eight different time points between 2003 and 2010 (Table S6). We amplified bi-allelic SNP markers following the methods of Culumber et al. (2011) and calculated the minimum temperature, maximum temperature and the mean temperature 90 days before each sampling date based on daily weather data from Tampico, Tamaulipas, Mexico (172 km from the centre of the focal region; obtained at http://www.wunderground.com). Allele frequencies (Table S6) were subjected to a principal components analysis as described above. We then subjected the first PC score (indicative of the frequency of X. birchmanni alleles in a population) to a repeated-measures linear mixed model, where population was a random factor and minimum temperature, maximum temperature and the mean temperature 90 days before each sampling date (all z-transformed) were covariates.
We conducted two thermal tolerance experiments. In the first, we tested wild-caught fish from populations along the elevational gradient. We further wanted to determine whether thermal tolerance is a plastic trait or whether observed differences in thermal tolerance among species were the result of adaptation to local conditions. Therefore, we tested fish that were raised at the CICHAZ field station in a common garden environment in a second experiment (details below).
Adult fish were collected using baited minnow traps, seines or dip nets from 11 sites along a continuum from high to low elevation (Table S1). Stream temperature was recorded at each sampling locality using a standard glass thermometer. Fish were transported alive to the CICHAZ field station and kept in thermally insulated coolers until testing (1–2 h) to maintain water temperature as close to the temperature at the collection site as possible. All fish were tested (N = 496; Summer N = 307, Winter N = 189) on the same day that they were collected, and the experiment was repeated twice for each population: once in June 2007 (summer) and again in December 2007/January 2008 (winter). Sample sizes were smaller for the winter season because water flow is greater and temperatures are lower during the winter in this region, making fish less active and more difficult to collect.
In order to test whether variation in thermal tolerance is due to local adaptation or phenotypic plasticity, we reared fish in a common garden environment in concrete stock tanks (1 × 1 × 2 m) with a water flow-through system at a common elevation of 981 m at the CICHAZ field station. Forty-eight gravid females of each parental species were collected from Chicayotla for X. malinche and Coacuilco for X. birchmanni. Those 48 females were divided evenly among 16 concrete tanks such that each of eight tanks received six gravid X. malinche and eight tanks received six gravid X. birchmanni. Females were allowed to give birth in the tanks, and fry were reared out with minimal interference other than to supplement food in the first months until natural fauna and flora such as algae began to develop and provide a food source. The fish were allowed to mature for a period of 1 year and then were tested in thermal tolerance trials. As above, the temperature of the water in the stock tanks was measured prior to testing. From each of the 16 stock tanks, we tested one male and one female in hot trials and one male and one female in cold trials. For X. malinche, we tested a total of 32 fish: 16 (8M: 8F) in hot and 16 (8M: 8F) in cold. The same numbers of X. birchmanni fish were tested except that only seven females were tested in hot for a total of 31 fish. To avoid potential researcher bias, these trials were carried out blindly such that the observer did not know which species were in which stock tanks.
In all thermal tolerance trials, a HOBO temperature logger (Onset Corporation) was submerged in the hot and cold test tank to obtain an exact reading of temperature throughout each trial. For hot trials, an enamel container containing a 4 L of water and the test fish was placed onto an inverted ceramic plate inside a larger enamel container. The apparatus was suspended over a gas burner and heated at a rate of 0.3 °C per min. In cold trials, fish were placed in a standard volume of water in a plastic container and frozen gel packs were placed in the water to reduce the temperature by 0.3 °C per min. Water temperature at initial loss of equilibrium (ILOE), analogous to the critical thermal maximum and minimum, was recorded for each individual in all trials. Initial loss of equilibrium is the time at which a fish begins to lose its ability to right itself. At final loss of equilibrium, when the fish had lost all ability to maintain its balance and stayed on its side for more than one full second, we removed it from the trial and placed it in a recovery tank. For Experiment 1, we used anova to test for the effects of species, population nested within species, season and the interaction term species × season on cold and heat tolerance. For Experiment 2, we used anova to test for the effects of species and sex on the dependent variables cold and heat tolerance.
hsp expression and thermal stress
For the experiment examining hsp expression, we collected Xiphophorus birchmanni from the locality Garces on the Río Garces, X. malinche from Chicayotla on the Arroyo Xontla and hybrids from Calnali-mid on the Río Calnali (see Table S1). Specimens for baseline gene expression were collected in the wild and preserved whole in RNAlater (Life Technologies Corporation, Carlsbad, CA, USA). Quantification of baseline hsp expression in wild-caught fish has been previously described (Coleman et al., 2009), and relative expression following thermal stress in the laboratory followed the same methods.
To characterize the regulation of hsp response, four X. birchmanni, four X. malinche and four hybrids were subjected to an acute heat stress followed by qPCR. All fish had been collected in the wild and housed in 23 °C water for 14 months, and then, those same fish were subjected to the heat stress experiment. We stressed fish by putting them individually in an Erlenmeyer flask with 1000 mL of water at 23 °C, placing the flask above a lit Bunsen burner and heating the water to 33 °C at a rate of 1 °C per min. We killed fish immediately following and placed their heads in RNAlater until RNA isolation, cDNA synthesis and qPCR (methods followed Coleman et al., 2009) using QuantumRNA Universal 18s rRNA (Ambion, Inc.) as an internal reference gene to normalize each sample. We used anova to test for differences in mean baseline hsp expression among populations, as well as mean relative hsp expression following acute heat stress. When a significant difference (P < 0.05) was observed, Fisher’s LSD was used to test for differences between populations with Bonferroni correction for multiple comparisons.
- Top of page
- Materials and methods
- Supporting Information
Ecological differentiation and niche modelling
Across the 10 subsampling replicates, the ENMs for all species produced mean test AUC values >0.7 (X. birchmanni: mean = 0.923, SD = 0.028; X. malinche: mean = 0.748, SD = 0.142; hybrids: mean = 0.940, SD = 0.017), indicating a sufficient ability to discriminate between presence and absence locations (Swets, 1988). In the final ENMs, species differed in which of the 11 variables contributed most to their model (Table S2). For X. malinche, minimum temperature of the coldest month (61.6%; relative contribution to Maxent model) and mean daily temperature range (36.3%) contributed the most, whereas flow accumulation (31.9%), precipitation of the driest quarter (22.0%) and minimum temperature of the coldest month (15.7%) had the highest contributions for X. birchmanni. For hybrids, the ENM was described primarily by annual temperature range (29.7%), mean diurnal temperature range (16.2%) and precipitation of the driest quarter (14.8%). The predicted distributions of X. birchmanni and hybrids fit relatively well with their actual distributions; however, the ENM of X. malinche predicts that the area where it occurs is marginally suitable and that environmental conditions are more optimal at higher elevations to the south-west (Fig. 1). However, X. malinche are not known to occur in that area and the fact that they occur farther north-west at slightly lower elevation than predicted by the ENM suggests that physical barriers to dispersal such as waterfalls may have prevented historical upstream migration. The small number of locality points for this narrowly distributed species (N = 6) may also limit the ability of ENM methods to predict the species distribution with high precision.
Niche identity tests showed that both parental species and hybrids occupy significantly different niches. Niche overlap between the parentals was significantly less than expected from random [Schoener’s D = 0.282, P < 0.001; Warren’s I = 0.560, P < 0.001]. Likewise, niche overlap between hybrids and parentals was significantly less than expected by chance [to X. birchmanni: D = 0.358, P < 0.001; I = 0.625, P < 0.001; to X. malinche: D = 0.392, P = 0.001; I = 0.710, P = 0.007]. Background tests indicate that the niche of X. birchmanni is more similar to the niche of X. malinche than expected by the background environment where X. malinche occurs (P = 0.014 for both D and I). However, the niche of X. malinche is more divergent from the niche of X. birchmanni than expected by the environmental background where X. birchmanni occurs, although significance was marginal (P = 0.092 for D, P = 0.046 for I). This seemingly counterintuitive result can be interpreted as both species having similar environmental preferences, but the availability of those preferred environmental conditions is limited within the range of the species showing greater differentiation than expected, which in this case is X. malinche (Nakazato et al., 2010). Niches of X. birchmanni and the hybrids are no more or less divergent than expected based on their respective background environments (hybrid vs. X. birchmanni background: P = 0.614 for D, P = 0.262 for I; X. birchmanni vs. hybrid background: P = 0.312 for D, P = 0.116 for I). The niche of hybrids was neither more nor less divergent from the niche of X. malinche than expected by the background environment of X. malinche (P = 0.308 for D, P = 0.304 for I); however, the niche of X. malinche was more divergent from the niche of hybrids than expected by the environmental background where hybrids occur (P = 0.002 for D, P = 0.012 for I). Again, this result may be due to limited availability of the preferred environmental conditions within the range of X. malinche. Results of niche identity and background tests were similar when analyses were run without the hydrologic variables (results not shown).
Using values of environmental variables extracted from each site, DFA indicated that 90.5% of the sites (compared to 33% based on random expectations) could be classified correctly as X. malinche, X. birchmanni or hybrid based on environmental conditions (Table S5b). Function 1 essentially separates X. birchmanni sites (positive scores) from X. malinche sites (negative scores), with hybrids being intermediate. Function 2 separates hybrid (positive scores) and X. malinche sites (negative scores), with X. birchmanni sites being intermediate. Temperature variables were the strongest variables separating species and contributing to the classification of sites.
Environmental effects on spatial and temporal variation in allele frequencies
The same abiotic environmental factors that differentiate habitats occupied by X. birchmanni and X. malinche also predicted frequencies of X. birchmanni alleles across hybrid populations (Table 1, Fig. 2). The only factor retained in the final multiple regression was the minimum temperature of the coldest month. The positive correlation of X. birchcmanni allele frequencies with minimum temperature of the coldest month was consistent with a priori expectations based on the DFA.
|Minimum temperature of coldest month||0.576||0.194||0.562||2.965||0.008|
Temperature variables also were instrumental in predicting parental allele frequencies in hybrid populations through time. As expected from the previous analysis, we found a significant effect of population on allele frequency (P = 0.038; see Table 2 for details). In addition, minimum temperature in the previous 90 days was significantly related to allele frequencies (P = 0.005; Fig. 3), whereas maximum temperature was marginally nonsignificant (P = 0.062). Mean temperature in the past 90 days had no significant relationship with allele frequency (P = 0.414).
|Estimates of fixed effects||Estimate||SE||d.f.||t||P|
|Minimum temperature in past 90 days||−0.311||0.094||14.620||−3.323||0.005|
|Maximum temperature in past 90 days||−0.117||0.047||4.489||−2.468||0.062|
|Average temperature in past 90 days||0.065||0.076||9.389||0.855||0.414|
|Estimate of covariance parameters||Estimate||SE||Wald Z||P|
In wild-caught fish, both heat and cold tolerance varied significantly among populations along an elevational gradient (Fig. 4). anova for cold tolerance showed significant effects of season (F1,2 = 24.323, P = 0.038) and population nested within species (F9,227 = 13.142, P < 0.001). The interaction of species × season was significant (F2,227 = 8.374, P < 0.001), indicating a difference in cold tolerance among species but in only one season. Indeed, post hoc, least significant difference (LSD) tests showed that all pairwise comparisons of species’ cold tolerance were significant (P < 0.001). Full tables for cold and heat tolerance anova s are shown in Table S7. The effect of season stemmed from the fact that all species had lower cold tolerance in the winter than in the summer, but X. birchmanni and hybrids had larger seasonal downshifts, 3.70 and 2.93 °C, respectively, whereas X. malinche only decreased 2.16 °C. anova on heat tolerance also showed significant effects of season (F1,2 = 54.421, P = 0.017) and population nested within species (F9,239 = 19.306, P < 0.001). The significant interaction of species × season (F2,239 = 6.593, P = 0.002) again indicated significant species differences in heat tolerance in one season and post hoc LSD comparisons demonstrated that heat tolerance was significantly different in all species comparisons (P < 0.001). The significant interaction of species and season appeared to be due to a smaller seasonal downshift in heat tolerance in X. birchmanni (2.78 °C) compared to X. malinche and hybrids (4.54 and 4.56 °C, respectively). Temperatures of critical thermal maxima and minima in this study correspond to biologically relevant temperatures (GGR unpublished data). Data recorded from underwater temperature loggers have shown lows of 6 °C at high elevations typical of X. malinche (∼1100 m) and highs of 42 °C at an X. birchmanni locality (∼200 m).
Critical thermal maximum but not critical thermal minimum was significantly different between species raised in the common garden. In hot trials, X. birchmanni exhibited significantly greater heat tolerance than X. malinche (X. birchmanni, mean = 36.15 °C; X. malinche, mean = 35.48 °C; F1,30 = 6.829, P = 0.014). There was no difference between sexes (F1,30 = 0.140, P = 0.711). In cold tolerance trials, there was no significant difference between species (F1,30 = 0.139, P = 0.712) nor sexes (F1,30 = 0.014, P = 0.905).
hsp expression and thermal stress
When analyses of thermal tolerance were narrowed to only those populations used for hsp and thermal stress experiments, significant effects of species and season on both cold and heat tolerance were present (data not shown). For reference, the X. birchmanni, X. malinche and hybrid populations used for hsp and thermal stress analyses are denoted in Fig. 4a,b. The upstream-to-downstream patterns in thermal tolerance among these three populations mirrored that observed over the entire elevational gradient.
Baseline hsp expression levels of wild-caught individuals were significantly different among the three groups (hsp70: F2,9 = 5.46, P = 0.03; hsp90: F2,9 = 6.44, P = 0.02) and showed a pattern identical to that observed for thermal tolerance: X. birchmanni exhibited the highest expression, X. malinche the lowest, and hybrids were intermediate (Fig. 5). Following acute thermal stress experiments, we again found significant differences in hsp expression (hsp70: F2,9 = 82.63, P < 0.0001; hsp90: F2,9 = 60.93, P < 0.0001), but not in the same pattern of baseline expression. Instead, hybrids showed up-regulation of hsps equivalent to that of X. birchmanni, whereas X. malinche showed a relatively weak hsp response (Fig. 5).
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Physiological adaptation along an elevational gradient appears to play a key role in producing replicated structure in the birchmanni–malinche hybrid zones. The parental species, X. birchmanni and X. malinche, as well as their hybrids exhibited distinct ecological niches with abiotic environmental factors, in particular temperature variables, driving niche differences among groups. More interestingly, thermal tolerance of parentals and hybrids, which is mediated in part by expression of genes encoding heat-shock proteins (Feder & Hoffmann, 1999), matches their respective distribution patterns (X. birchmanni: low elevation, X. malinche: high elevation, hybrids: intermediate). Taken together this suggests that, in the face of historical physiological adaptation to different thermal conditions in parentals, the elevational gradient provides a conduit for secondary contact between the species, with hybrids experiencing equal or greater fitness in intermediate thermal environments. This study represents a major step towards understanding the physiological and genetic bases of a fitness-related trait that affects hybrid zone structure in the swordtail system. More broadly, these results build upon an understudied theme in evolutionary biology, namely understanding the role and importance of thermal adaptation in the emergence of reproductive isolation (Keller & Seehausen, 2012).
A weakness of correlative approaches, such as ENM, is the potential for results to be overinterpreted – as correlated environmental variables that are not actually used in the analysis might be the variables driving the observed patterns in the data. However, integrating mechanistic and correlative approaches, as we did here, provides a means to confirm whether variables used in the correlative analyses actually have direct and relevant effects on the focal organism. In this study, we used ENM techniques and correlations between environmental variables and allele frequencies to identify temperature as an important variable and then confirmed through mechanistic experiments and the quantification of gene expression that temperature does indeed have significant effects on organism performance.
Niche differentiation and the abiotic environment
Parental X. birchmanni and X. malinche occur at opposite ends of an elevational gradient, and hybrids dominate at intermediate elevations (Rosenthal et al., 2003; Culumber et al., 2011), suggesting that this pattern is maintained by adaptation to local conditions along the environmental gradient. The use of ENM in other systems, combining geo-referenced species occurrence data with spatially explicit data on abiotic and/or biotic variables (reviewed in Kozak et al., 2008), has proven useful for delineating species distributions (Raxworthy et al., 2007; Shepard & Burbrink, 2008, 2011; McCormack et al., 2010), but is in its infancy in dissecting the basis of hybrid zone structure (Cicero, 2004; Swenson, 2006; Chatfield et al., 2010). Here, ENM enabled us to disentangle the complexity of environmental differences along the elevational gradient. As with many environmental gradients, stream gradients are multivariate, consisting of superimposed and correlated abiotic and biotic variables, such as temperature, precipitation, food availability, vegetation and predation (Endler, 1995; Grether et al., 1999; Kolluru et al., 2007; Walsh & Reznick, 2009). Using ENM followed by DFA allowed us to identify abiotic factors important in predicting the distribution of parentals and their hybrids, and helped us to focus on fitness-relevant variables that were the strongest drivers of the observed patterns.
Among factors included in our analysis that vary along the elevational gradient, temperature variables emerged as the strongest predictors of hybrid zone structure at multiple levels of analysis. Temperature plays a critical role in determining plant (C4 grasses, Edwards & Still, 2008; aquatic macrophytes, Sawada et al., 2003) and animal distributions (Myotis bats, Humphries et al., 2002; land birds; Root, 1988; zooplankton, Southward et al., 1995) and can drive local adaptation within species (Miller & Packard, 1977; Feminella & Matthews, 1984; Ayres & Scriber, 1994). Moreover, temperature may be an important factor in structuring other hybrid zones, yet few studies have considered the multidimensionality of temperature variation and instead have focused mostly on mean temperature (Swenson, 2006; Cheviron & Brumfield, 2009). Our data suggest that extreme temperature events are likely to have more important physiological and survival consequences than mean temperature. Similarly, short-term exposure of corals and associated sea anemones to above or below average temperatures significantly increases loss of symbiotic zooxanthellae, accelerating bleaching (Steen & Muscatine, 1987; Jokiel & Coles, 1990).
Temperature variables were good predictors for broad spatial patterns in the occurrence of Xiphophorus, contributing not only to the correct classification of more than 90% of sites as pure X. birchmanni, pure X. malinche or hybrid based on environmental conditions, but also to the successful prediction of allele frequencies in hybrid populations. Correlations between parental allele frequencies and minimum temperature in the coldest month matched the a priori prediction based on parental species niche differentiation. Moreover, temperature variables were able to explain temporal variation in species-specific allele frequencies in hybrid populations, indicating that even at a finer scale within hybrid populations, temperature was still able to predict variation in population genetic structure. Correlations between temporal variation in allele frequencies and temperature revealed a significant and marginally nonsignificant effect of minimum and maximum temperature, respectively, but no effect of mean temperature. One interpretation that we cannot entirely rule out is that fish respond behaviourally, shifting their distribution in response to seasonal changes in temperature. This is not well supported by the data given that mean temperature, the best predictor of seasonal temperature change, was unrelated to allele frequencies. Rather, the data suggest that extreme, short-term changes in temperature serve as selective events and are sufficient to significantly alter the structure of hybrid populations leading to long-term maintenance of hybrid zone structure.
Selection on thermal tolerance
Thermal tolerance is a performance metric of the ability to buffer against a wide range of negative, temperature-dependent physiological and behavioural changes that can directly impact an individual’s fitness (Donaldson et al., 2008 and references therein). The dominant role of temperature in explaining the spatial structure of the birchmanni–malinche hybrid zones suggested that animals should be adapted to local thermal conditions along the elevational gradient. Indeed, along the gradient, both species and population significantly explained performance in thermal tolerance experiments for both heat and cold tolerance. X. birchmanni and X. malinche performed best in warmer and cooler temperatures, respectively. However, hybrids outperform both parental counterparts at intermediate elevations because they exhibit greater cold tolerance than X. birchmanni and greater heat tolerance than X. malinche. These results are qualitatively similar to those found in an intertidal copepod, Tigriopus californicus, which face trade-offs between thermal tolerance at extreme temperatures and competitive ability at moderate temperatures (Willett, 2010). Taken together, these results have important implications for hybrid zones occurring along environmental gradients. For example, in our system, each parental species exhibits better performance at their respective end of the elevation spectrum, but underperforms hybrids at intermediate elevations where temperatures are more moderate. When extreme temperatures do occur at intermediate elevations where hybrid populations are found, species-specific allele frequencies responded accordingly with decreases in X. birchmanni alleles following cold events and decreases in X. malinche alleles following hot events. Furthermore, variation in long-term averages of climatic variables at hybrid sites is mirrored by changes in parental allele frequencies.
Importantly, X. birchmanni and X. malinche reared under identical environmental conditions at a common elevation still exhibited significant differences in heat tolerance. This indicates that phenotypic plasticity alone cannot explain the variation in thermal tolerance observed along the elevational gradient. This is further supported by the significant temporal relationship between temperature and allele frequencies. Cold tolerance, while different in wild-caught parentals, did not differ between parentals reared in the common garden. One potential explanation for this is the unusually cold temperatures that common garden fish experienced during rearing in the winter of 2010 prior to our experiments. Temperatures reached as low as 13 °C for several days, and increased mortality was observed in X. birchmanni stock tanks compared to X. malinche tanks during this period. Thus, the cold temperatures likely represented a strong selective event against the least cold-tolerant X. birchmanni, thereby leaving the most cold-tolerant survivors. This is consistent with observations that allele frequencies in hybrid populations fluctuate according to the temperature in the previous 90 days and seems more plausible than assuming that cold tolerance is plastic whereas heat tolerance is not, given that they are under the control of the same family of genes. Regardless of what might explain this result in the present study, it is nonetheless consistent with other findings. For example, Barrett et al. (2011) observed a significant variation in cold tolerance between marine and freshwater sticklebacks but no difference in their heat tolerance.
Thermal tolerance and hsp gene expression
Thermal tolerance depends in part on the expression of hsps (Feder & Hoffmann, 1999). Elucidating the genetic underpinnings of adaptive traits contributing to fitness has long been a goal of evolutionary biologists (Lewontin, 1974) and investigations into the genetics of hybridization have yielded many insights into the role of particular genes or interactions of genes that contribute to sterility, incompatibility and increased/reduced fitness of hybrids (for review, see Burke & Arnold, 2001). Few studies, however, have addressed how genetic mechanisms of superior hybrid fitness interact with specific environmental variables, which should play a deterministic role in structuring hybrid zones. Baseline gene expression of hsps closely matched thermal tolerance with hybrids intermediate to the parental species. Xiphophorus malinche showed a significantly weaker hsp response to acute heat stress than did X. birchmanni or hybrids. The significantly weaker hsp response, and overall lower hsp expression of X. malinche, suggests that it is confined to cooler waters with relatively stable thermal profiles, which is supported by ENM results. Indeed, X. malinche has a restricted distribution and is known from only six headwater populations (Rauchenberger et al., 1990; Rosenthal et al., 2003; Culumber et al., 2011). Although the patterns in hsp response closely matched what would be predicted based on results from ENM, spatial and temporal analyses and thermal tolerance trials, future replication would be ideal in order to confirm this pattern.
Plasticity and adaptation are two potential explanations for the significant correspondence between thermal tolerance (and hsp expression) and hybrid zone structure. The first, which we can largely rule out, is the extent to which thermal tolerance and hsp gene expression are plastic traits throughout life or may have an ontogenetic component. Our common garden experiment, rearing each parental under identical environmental conditions, demonstrated that critical thermal maxima were still significantly different between species. Additionally, several lines of evidence indicate that there is heritable variation in thermal tolerance among groups. For example, differences in hsp expression persisted in fish maintained under identical conditions in the laboratory for over a year. Given the robust ENM results, strong correlation between temperature variables and allele frequencies and maintenance of a significant difference in heat tolerance in the common garden, adaptation to the thermal environment along the elevational gradient is the most plausible explanation.
Temperature gradients and the maintenance of hybrid zone structure
In a recent literature review, Keller & Seehausen (2012) suggest that abiotic gradients, specifically thermal environments, may be a common driver of ecological speciation, but that it is an understudied area of research. In fact, they point out that the effect of thermal gradients might be particularly pronounced in aquatic environments of tropical mountain ranges and that such scenarios may provide opportunities for hybrids to outperform parentals in intermediate locations along the gradient. Our results indicate that the birchmanni–malinche hybrid zones, which are structured along a thermal gradient in an aquatic habitat of a neotropical mountain range, represent an example of the scenario they predict.
Two alternatives to bounded hybrid superiority are globally superior hybrids (hybrid swarm) and globally less-fit hybrids (tension zone). If hybrids were globally more fit than parentals, then hybrid zone structure would quickly erode creating a hybrid swarm and ‘extinction by hybridization’ of parentals. Hybrids have occurred since at least the late 1990s yet remain restricted to intermediate elevations in seven different stream reaches with pure parental populations remaining intact at either end of the hybrid zones (Rosenthal et al., 2003; Culumber et al., 2011). On the other hand, if hybrids are globally less fit, then hybrid zone structure could only be maintained with recurrent hybridization between pure parentals to produce new F1 offspring. With 8 years of genotyping data from this study and a previous study, including >500 individuals from populations where both pure parentals occur together, fewer than 2% have had F1 genotypes (Culumber et al., 2011). This is below expectations based on random chance and given misclassification rates based on the number of markers used.
Instead, data from a number of studies suggest that at least a subset of hybrid males are preferred by females due to transgressive segregation in male secondary sex traits (Rosenthal et al., 2003; Rosenthal & Garcia de Leon, 2006; Fisher et al., 2009). The present data show that intermediate elevations are too warm for X. malinche and too cold for X. birchmanni leading to superior performance by hybrids within the intermediate zone. Conversely, hybrids are bounded due to the fact that parental X. malinche and X. birchmanni outperform hybrids at high and low elevations, respectively, and that hybrids underperform in more extreme cold and hot temperatures. The hybrid zones are replicated across seven separate stream reaches (Culumber et al., 2011) and, as shown herein, the zone of abiotic conditions in which hybrids occur is also replicated in each of these stream reaches. Thus, the birchmanni–malinche hybrid zones more closely fit a model of bounded hybrid superiority than alternative models. This is consistent with thermal structuring along another elevational gradient in Drosophila, where a high- and low-elevation species are each best adapted to different temperature regimes which contributes to premating isolation and prevents significant gene flow along the gradient (Matute et al., 2009).
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Hybrid zones often coincide with variation in abiotic or biotic factors, and there is evidence that selection via particular abiotic variables contributes to hybrid zone structure and fitness differences (Nikula et al., 2008; Cheviron & Brumfield, 2009). Such studies provide a basis to identify specific agents of selection and then explicitly test the mechanisms involved. Yet, few studies have measured the effect of selective agents on individual performance and physiology across a hybrid zone. Our study demonstrates the power of using an integrative approach not only to identify variables that may underlie hybrid zone structure, but to then directly test performance and physiological response to relevant variables. The results of this approach indicate that natural selection based on thermal regimes, and possibly other factors correlated with elevational variation in temperature, stabilizes the replicated hybrid zones in this system. Adaptive physiology is an understudied but important determinant of hybrid zone structure and, more broadly, of the evolutionary outcomes of natural hybridization. Physiological and behavioural traits have long been neglected in the study of adaptive hybridization in animals, largely due to a lack of integration of laboratory and field studies. Future studies of how environmental variation and hybridization interact to affect adaptive processes will continue to aid in our understanding of the evolution of biodiversity from both ecological and physiological perspectives.
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We would like to thank the Mexican federal government for collection permits. Zachary Cress, Chi-Cheng Wat, Holly Kindsvater, Heather Chance and Rich Serva assisted with thermal tolerance experiments. We thank John Morrongiello for comments on the manuscript. The study was supported by NSF grant IOS-0923825 to GGR and a National Research Service Award to SWC. ZWC was supported by NSF DDIG IOS-1011613, NSF IGERT-0654377 to the Applied Biodiversity Science program at TAMU and by Consejo Nacional de Ciencia y Tecnologia Mexico – Clave 0127310 grant in basic science to William Scott Monks. We are grateful to Rich Serva and the American Livebearer Association for equipment and for assistance with fish husbandry. All testing and animal care was in accordance with Animal Use Protocols reviewed and approved by Texas A&M University IACUC.
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Table S1 List of collection sites.
Table S2 Environmental variables used to construct ENMs and estimates of the relative contribution of each variable (%) to the Maxent model for each species.
Table S3 X. birchmanni allele frequencies in different hybrid populations from SNP markers genotyped in Culumber et al. (2011).
Table S4 Principal components on X. birchmanni allele frequencies in hybrid populations at four SNP loci.
Table S5 Discriminant function analysis to differentiate X. malinche, X. birchmanni, and hybrid sites based on environmental conditions.
Table S6 X. birchmanni allele frequencies in hybrid populations used for temporal analyses.
Table S7 (A) Full table of ANOVA for cold tolerance along the elevational gradient. (B) Full table of ANOVA for heat tolerance.
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