- Open Access
Latitudinal diversity patterns of Chilean coastal fishes: searching for causal processes
© Navarrete et al.; licensee Springer. 2014
- Received: 14 August 2013
- Accepted: 31 December 2013
- Published: 26 March 2014
Several particular aspects of diversity patterns of Chilean littoral fishes are still poorly understood, and existing studies within this scope are fundamentally based on bibliographic compilations. In this study, we use empirical data to assess whether the diversity patterns of fish fauna along 4000 km of the Chilean coast (20°–55° S)can be explained in relation to the environmental latitudinal gradient. Fish were collected from intertidal pools and subtidal habitats (<35 m). Analyses focused on the spatial scales of diversity patterns and latitudinal breaks in species diversity, comparing the observed patterns among intertidal and subtidal habitats. Correlations between variance in environmental factors and species richness were calculated.
Richness was positively autocorrelated at spatial scales <1000 km. Overall, richness was observed to progressively decrease toward higher latitudes, but values for intertidal fish in particular decreased towards the north and south from the point of maximum richness. This is a pattern that has already been recorded for other intertidal organisms. Similarity was seen to decrease with distance, and turnover point for intertidal fishes was high around 30°–32° S, while northern species disappeared between 36°–39° S. Subtidally, there is an invasion of subantarctic species between 53°–55° S.
Environmental variables are significant to the diversity patterns recorded. However, richness variations could result from many types of variables acting together and not from one single factor.
- α and β-diversity
- Endemic species
- Intertidal fishes
- Latitudinal diversity gradient
- Marine biogeography
Species richness is the fundamental and most intuitive expression of biological diversity and represents the number of coexisting species (i.e., with overlapping ranges) on a particular spatial scale (Magurran 2004). Despite its apparent simplicity, spatial variation in the number of species in the latitudinal gradient generates one of the canonical patterns in ecology (Blackburn and Gaston 1996), where it is shown that richness increases towards the tropics in a wide variety of taxa (Rosenzweig 1995). Notwithstanding these well-known latitudinal patterns of species richness, the mechanisms associated with their generation still remain unclear. For a couple of decades, several studies have changed the traditional focus of analysis of local species richness, or α-diversity (e.g., Harrison et al. 1992; Blackburn and Gaston 1996; Koleff and Gaston 2002; Rodríguez and Arita 2004; Qian et al. 2005; Soininen et al. 2007), and highlighted the need for additional research on species turnover across local habitat, or β-diversity (Whittaker 1972). The study of species turnover helps to better describe the dynamics of diversity between communities, which allows a better estimate than studying only α-diversity (Soininen et al. 2007). This is why complementary analyses of α and β-diversity can help with the understanding and identification of the underlying processes that control diversity patterns at different spatial scales as well as promote the development of hypotheses related to general patterns of diversity (Ricklefs 1987; Castilla et al. 2004).
The coast of Chile has received much attention from scientists interested in studying biogeographic patterns in both its flora and fauna (e.g., Sebens and Paine 1979; Santelices 1980; Jaramillo 1982; Brattström and Johanssen 1983; Brattström 1990; Lancellotti and Vásquez 2000; Ojeda et al. 2000; Thiel 2002; Valdovinos et al. 2003; Moreno et al. 2006; Fernández et al. 2009; Broitman et al. 2011; Rivadeneira et al. 2011; and see Miloslavich et al. 2011 on the marine biodiversity of South America). This can be explained by a series of particular characteristics of the Chilean littoral, most notably its long latitudinal extension of approximately 4,200 km of coastline (Ojeda et al. 2000), which is strongly influenced by the Humboldt Current System (Thiel et al. 2007). In addition, the Chilean coast has marked differences within its length. It is practically continuous and fully exposed to the prevailing southwesterly winds from Arica (18° 20′ S) to the northern part of Chiloé Island (ca. 41° 45′ S), while from Chiloé to Cape Horn (ca. 56° S), it is highly fragmented, forming a large number of islands and protected channels (Ahumada et al. 2000; Ojeda et al. 2000), thus representing one of the regions with the highest amount of intertidal habitat in the world (Pequeño et al. 1995). These characteristics create a sharp temperature gradient and a wide variability of current, wind-induced upwelling conditions and environments along the latitudinal axis (Ahumada et al. 2000; Broitman et al. 2001; Camus 2001; Thiel et al. 2007). Such factors could affect the geographic distribution and abundance of the organisms that inhabit it, influencing the observed patterns of diversity.
Although most biogeographic studies conducted on the Chilean coast gather bibliographic information that includes studies using different criteria and methodologies, both for selecting target groups and for analyzing data, these studies generally recognize two faunal groups (Camus 2001), a warm temperate region north of 42° S and a cold temperate region south of 42° S. Furthermore, between these two regions (between 30° S and 42° S), the existence of a transition area and species mix has been proposed (Dahl 1960; Dell 1971; Brattström and Johanssen 1983). However, the fact that measures of diversity are scale-dependent (Lopez De Casenave et al. 2007) leads us to interpret the results of studies based on bibliographic compilations with caution, precisely because of differences in the methodologies used for data collection.
Ojeda et al. (2000) put together an extensive bibliographic database with unpublished personal data, to understand the biogeography of marine fish from the Southeast Pacific. They found that littoral fish diversity remains fairly constant along the coast down to around 40° S, declining south of this latitude. They detected two biogeographic regions along the Chilean coast, with a break between them at 40° S. In the present study, our goal was to continue with this work by using empirical fish data from rocky intertidal and subtidal habitats through standardized methodologies, thus providing great interpretative value to our results, as it keeps the sampling error term constant. This also avoids, for example, the potential bias implicit in data from bibliographic compilations (i.e., avoiding methodological differences), which has also been done by other recent studies (see Thiel 2002; Häussermann and Försterra 2005; Rivadeneira et al. 2011).
Our objectives were to determine the existence of latitudinal patterns in the richness (i.e., α-diversity) and turnover (i.e., β-diversity) of rocky intertidal and subtidal fish species off the coast of Chile. Additionally, we assessed whether such patterns can be explained by the latitudinal gradient, determining which spatial scales dominate these patterns of variation. Finally, we tried to identify whether there are breaks in richness patterns, assessing whether they are related independently or associated to the environmental variables representative of Chile's coastal ocean and/or to the result of colonization, dispersal, and adaptation processes of ancestral fish taxa that gave rise to what we now recognize as the fish fauna of the Chilean littoral.
Species richness, sites and sampling dates of intertidal (Int) and subtidal (Sub) fishes (<35 m deep)
1997, May 1998 to May 1999
July 1996 to November 1997
July 1996 to November 1997
March 1989 to September 1990
March 1994 to July 1996
1997 to 2005 (bimonthly)
September 1998 to January 1999
1975 to 1976
1987, 1991 and 1992
January 1960 to April 1975
October 1995, November 1992
October to November 1996
January to July 1980, April 1992
1987 to 1988
Fish data are available in the FIP Project no. 2004–28 in the website of the Fondo de Investigación Pesquera (http://www.fip.cl/Archivos/Hitos/Informes/inffinal%202004-28.pdf).
In this study, we consider intertidal fishes to be those that live their postlarval lives, or part of them, in the intertidal zone (see Gibson and Yoshiyama 1999). These fishes were collected from rocky intertidal pools at each study site. Sampling consisted of suctioning off the water contained in the pool during the tidal ebb by using a 5 HP portable water pump. The hose nozzle was placed perpendicularly at the bottom of the pool to prevent the fish from being sucked up by the pump. Once the water was extracted, BZ 20 benzocaine fish anesthetic was applied both in the crevices and under the rocks, facilitating capture with hand nets (Hernández-Miranda and Ojeda 2006).
Subtidal fish samplings were conducted by visual surveys along bathymetric transects between 0 and 35-m deep and with three fish collecting nets (3 × 50 m) composed of five panels (graduated sizes of openings 10 to 50 mm) placed at random on the bottom, perpendicular to the coastline, between 5 and 18-m deep. The nets were placed at the sampling sites 1 h after sunrise and withdrawn 1 h after sunset (see Angel and Ojeda 2001).
Latitudinal gradient in species richness
We conducted a series of regression analyses focused on defining the order in the polynomial regression model between the number of species and latitude-longitude. To do this, first, second, and third order models were sequentially adjusted. The coefficient of determination r2 was evaluated to determine the degree of explanation of the latitudinal component on the spatial variation of fish diversity. To rank the models, we use Akaike information criteria (AIC) and the weighted version of the AIC criteria (AICw) was used to estimate the probabilities of each model being the best model in terms of AIC, given the data and the set of fitted models (Wagenmakers and Farrell 2004).
Spatial scales of autocorrelation of alpha diversity
Moran's I autocorrelation index was estimated (Sokal and Oden 1978) for different distance classes covering the entire study area. The number of distance classes was selected based on the extent and grain (i.e., separation between sites) obtained with the spatial database. Autocorrelation analysis and construction of correlograms were performed using the SAAP-PC program version 4.3 (Wartenberg 1989), and significance was evaluated using the Bonferroni correction.
Distance decay in similarity of species composition
Each sampling site can be specified in terms of the composition of species present in it, as well as its spatial position or particular geographic coordinates. Therefore, two sites can be compared using both perspectives, that is, estimating the differences in species composition using an index that uses the number of shared species (e.g., β-diversity or similarity indices), and estimating the geographical or Euclidean distance separating the sites. In this study, we used the Mantel test (Mantel 1967) to evaluate the correlation between the two matrices. The statistics of the Mantel test are standardized to r. Since each element in both matrices is not independent, the significance of r was evaluated using permutations. This was done by constructing a reference distribution rD, which is obtained by randomly reassigning the similarity value between sites to a different distance and repeating the calculation of r. In this study, 1,000 permutations of the geographical distance matrix were used. The Jaccard index (J) was used as a measure of similarity between sites to calculate the biological matrix, and Euclidean distance was used to calculate the spatial distance matrix. The Jaccard index was expressed as 1 − J to obtain a measure that reflects the expected pattern of full similarity 1 − J = 1 and dissimilarity 1 − J = 0 (Rivadeneira et al. 2002). The analysis was performed with the computer program PC-ORD (McCune and Mefford 1999) using 1,000 permutations for the Monte Carlo method as a procedure to obtain the distribution of random data rD.
Distribution ranges and latitudinal breaks in species diversity patterns
Data matrices were produced with the presence and absence of subtidal and intertidal species along the latitudinal axis. To identify latitudinal breaks in species richness, we perform a hierarchical cluster analysis using UPGMA as linkage method and 1 − Jaccard similarity coefficients as distance metric (Ojeda et al. 2000) using Systat® v12 software. Validity of the optimal clustering configuration was evaluated by bootstrapping 1,000 times the presence/absence matrix and estimating at each step the root mean square standard deviation (RMSSTD) across sites within each cluster. The similarity recorded at the minimum values of RMSSTD can be regarded as the similarity level greater than that expected by chance alone. In addition, using 1 − Jaccard's coefficient, we plotted the similarity between pairs of adjacent sites along the coast of Chile for both fish assemblages. Finally, we also illustrate the location where species evidenced limit to their range distributions by calculating the index ΔS (ΔS = SLat i − SLat i + 1) between site at the latitude i with the southward adjacent site located at the latitude i + 1. Thus, ΔS = 1 when a species is present in the northern but is absent in the adjacent southward site and ΔS = −1 when the species is absent in the northern site but present in the southward site. Plotting positive and negative ΔS values along latitude, we explore the location of southern limit to northern species and northern limits of the southern species.
Relationship of biogeographic patterns with environmental variables
There are few sources of environmental information along the Chilean coast over the spatial scales involved in this study; therefore, it was difficult to obtain exact matching data in terms of study period or spatial location of the study sites along the coast (also see Astorga et al. 2003; Valdovinos et al. 2003; Fernández et al. 2009). Thus, historical records of annual mean sea surface temperatures (SST) estimated for each degree of latitude from of each study site were compiled from the NOAA monthly data set (http://ferret.wrc.noaa.gov/Ferret/). Chlorophyll-a concentrations (Chl-a, mg m−3) estimated for the first 12 km cross-shore per degree of latitude from each study front was calculated by using 8-day averages, available from SeaWiFs satellite images between 1997 and 2000 (Thomas 1999; Fernández et al. 2009). The continental shelf area was relatively estimated by digitizing a 1:106 scale Lambert Zenithal Azimuthal equal area projection map down to the 200-m isobath (Astorga et al. 2003). For intertidal species, this area may represent the area where juvenile stages develop, while for subtidal species, it represents the habitat where they concentrate, providing a relatively good representation of the biogeographical pattern of fish distribution in Chilean coastal habitats.
The direction and magnitude of each bivariate relationship between environmental variables and species richness was estimated with the Pearson product–moment correlation coefficient, using the Bonferroni correction. Subsequently, the contribution of each environmental variable to the total variance of the spatial diversity variation pattern was evaluated using the squared semi-partial correlation (sr2) in a multiple regression model (Tabachnik and Fidell 1989; Astorga et al. 2003).
When the sum of the pure effect of each variable (i.e., pure effect measured by the squared semi-partial correlation sr2 and represented by the symbol Σ in the tables) corresponds to the coefficient of determination (r2) of the regression model that includes all of these variables, we can conclude that the environmental effects are additive. However, any difference between sr2 and r2 can be attributed to synergistic effects or interaction between environmental variables.
In the case of multiple relationships, and given that diversity is the result of interactive processes, the data have been processed on a logarithmic scale, thus allowing for the application of regression models under the assumption of additivity of the effects involved in the analysis. Since multicollinearity between environmental variables is possible in this multiple regression analysis (e.g., SST with chlorophyll concentration), automatic methods were not applied in the selection of regression models (e.g., stepwise). Instead, models were developed sequentially, by manually adding variables as the r2 value increased from the previous model. In addition, we compared all resulting models using the AIC and weighted AIC (AICw) to parsimoniously order the selected models. In this study, we only report the models with one to five parameters, maximizing r2 with their corresponding AIC and AICw.
Latitudinal gradient in species richness
Summary of regression analysis of first, second and third order between fish species richness and latitude
Spatial scales of autocorrelation of alpha diversity
Distance decay in similarity of species composition
There is a clear pattern of decline in similarity from short to longer distances between sites in both intertidal and subtidal fish (Figure 2B). This was reflected by negative values for the overall Mantel coefficient of −0.79 for intertidal fish and of −0.81 for subtidal fish. In both cases, it was seen that despite the large distances involved, total dissimilarity in species richness was never recorded between the pairs of sites.
Distribution ranges and latitudinal breaks in species diversity patterns
Relationship of biogeographic patterns with environmental variables
Squared semi-partial correlation and multiple correlation of spatial and environmental variables
Squared semi-partial correlation
F (1, 5)
Σ sr2 = 0.15
Σ sr2 = 0.32
Analysis of the order of entry into the model of each explanatory variable and its importance
Variables included in the models
For subtidal fish, it was observed that the most important variable was the continental shelf area with r2 = 0.745 (Table 4). This slightly increased when the squared component of chlorophyll-a (Chl-a2) was added (to r2 = 0.799). However, the coefficient of determination substantially increased to 0.862 when latitude and temperature were included (i.e., four-parameter model).
It is clear that richness of littoral fishes on the Chilean coast is not constant along the latitudinal axis and, overall, a progressive decrease in richness toward higher latitudes can be observed. This general pattern was also described by Ojeda et al. (2000) for Chilean coastal bony fish and Chondrichthyes. For both of these groups, richness values are relatively constant from northern Chile to about 40° to 42° S, from which there is a marked decrease southward. In the current study, in agreement with Ojeda et al. (2000), a marked decrease of species south of ca. 40° S was observed, as well as a constant richness of subtidal fish north of this point. However, for intertidal fish, richness peaked between 32° and 36° S, which is a pattern that has been previously recorded for intertidal peracarids at mid-latitudes along the Chilean coast (Thiel 2002; Rivadeneira et al. 2011). From this zone of maximum richness, the numbers of species decrease both northward and southward. Such decrease is more pronounced at higher latitudes. This result suggests that although overall fish richness decreases with increasing latitude, particular assemblages associated with intertidal habitats may show breaks in this trend.
These peaks of intertidal fish species richness at temperate latitudes, where richness can apparently vary without a particular trend at intermediate latitudes, could be widespread in fish living in these environments. Prochazka et al. (1999) collected bibliographic information on intertidal fish from different temperate and tropical regions of the world, and despite the possible bias and lack of representation associated with such diverse bibliography, there is still no clear indication of a decrease in richness with increasing latitude, at least not at intermediate latitudes. This particular pattern may be the result of underlying processes related to the particular and highly variable conditions of the intertidal environment, specifically tide pools. In this environment, the observed pattern emerges from the specific characteristics of the resident fish fauna, whose species are usually small and cryptic in habit and coloration. These characteristics are generally considered to be specialized to intertidal life (Horn et al. 1999). Similarly, other marine organisms have shown variations in the pattern of decreasing species at higher latitudes. For example, it has been reported that the total number of sublittoral benthic macroalgae and invertebrate species tends to increase steadily towards the south of Chile (Santelices 1980; Brattström and Johanssen 1983; Lancellotti and Vásquez 2000; Fernández et al. 2009; Rivadeneira et al. 2011). For macroalgae, this pattern results from an increase in the contribution of species of subantarctic origin toward the south (Santelices 1980).
Our results show that both richness and species composition between study sites are structured. Richness is positively autocorrelated up to about 1,000 km of separation between sites for both fish assemblages. This reveals that the richness of sites separated by >1,000 km has no dependencies, thus indicating the spatial range of influence of local richness values. As with the number of species, similarity between sites decreases depending on the distance between them. However, no paired comparison between locations showed complete dissimilarity of fish fauna, even between the end locations of the range of study. This can be explained by the presence of species that are distributed all along the Chilean coast and which are therefore common to all locations. Among these species, both Chondrichthyes and bony fish are found in the subtidal environment, while these widespread species are represented only by bony fish in the intertidal zone. Certainly, the pattern generated in intertidal and subtidal fish corresponds to a balance between species maintenance, loss, and entry, in addition to the presence of endemic species with a reduced distribution range (Ojeda et al. 2000).
The fact that there are latitudinal breaks in intertidal fish richness with a progressive decline in the number of species above 33° S and a steady decline in species turnover from north to south indicates that these patterns emerge more from species loss than from changes in the specific composition. However, the precise increase of richness at 33° S may be due to the appearance of species endemic to the Chilean intertidal zone starting at 20° S (i.e., Helcogrammoides chilensis (Cancino 1960)) and 32° S (e.g., Bovichthys chilensis Regan, 1913; Auchenionchus microcirrhis (Valenciennes 1836); Helcogrammoides cunninghami (Smitt 1898). Please refer to Appendix one in Ojeda et al. 2000), which is a similar pattern found for intertidal peracarids, and due to the possible overlap of northern and southern species (see Thiel 2002). At the other end of the latitudinal gradient, the fact that richness stabilizes and turnover substantially increases starting at 48° S may be due to the entry of new species originating in the south (e.g., Agonopsis chiloensis (Jenyns 1840), Notothenia spp.). These new species build up assemblages different from those recorded at lower latitudes (e.g., from 33° to 46° S), which can be due to the possible effect of the dispersive barrier of the Peninsula Taitao around 48° S, as it has also been observed for other invertebrate marine taxa (Häussermann and Försterra 2005; Wichmann et al. 2012). Regarding subtidal fish, the break at 39° S suggests that there is an area of high diversity and low turnover between 36° and 41° S, with a significant level of endemic species. The observed decrease in species richness south of 38° to 40° S is primarily due to a marked loss of species of subtropical origin, represented mainly by herbivores (e.g., Aplodactylus punctatus Valenciennes, 1832). However, specific turnover substantially increases, which is possibly the combined effect of both the loss and entry of new species (but to a lesser extent to the amount lost) of sub-Antarctic origin, mainly from the Zoarcidae and Nototheniidae families (Ojeda et al. 2000). A similar pattern has also been documented for polychaetes (see Moreno et al. 2006).
The biogeographical aspects of the fish fauna of the eastern South Pacific had already been discussed by Mead (1970), who noted that there is no such fish fauna that originated on these shores. Accordingly, we can observe that it sprung from the colonization and adaptation of various taxa of tropical and subantarctic origin. In addition, Mead (1970) proposed that the observed pattern of species decline at higher latitudes was mainly due to the absence of species of subtropical origin, primarily herbivorous fish belonging to the advanced Perciformes. The possible explanation for this was lack of time for these taxa to have evolved and adapted to the cold temperate conditions since the last glacial period. However, there is evidence of organisms within the advanced Perciformes that have in fact been able to adapt to cold temperate conditions, being these fish strict carnivores or omnivores. Therefore time is not a sufficient explanation for the observed pattern within the advanced Perciformes, with particular restrictions on herbivore feeding modes, which are more likely to occur in temperate and cold waters (see Floeter et al. 2005).
One of the most assessed and discussed causal mechanisms proposed to explain the decrease in species richness toward high latitudes relates to the particular diet of the fishes. Since diet is subject to physiological restrictions based on water temperature, energetic requirements of herbivore fishes can be affected by low temperature of polar waters (see Floeter et al. 2005; Pulgar et al. 2005; Behrens and Lafferty 2007). Nevertheless, these studies do not agree on the net effect of temperature on fitness or on the dietary preference of omnivorous fish, although they do highlight the importance of the combined effect of temperature and type of diet (i.e., herbivorous, omnivorous, and carnivorous) on metabolic rate, rate of intake, and assimilation capability. For example, Pulgar et al. (2005) recorded that the omnivorous Girella laevifrons (Tschudi 1846) tended to prefer a diet of algae over an animal diet at lower temperatures, arguing that metabolic rate decreases at low-temperature degrees. However, both Floeter et al. (2005), who studied the surgeonfish Acanthurus bahianus Castelnau, 1855, as well as Behrens and Lafferty (2007), who studied Girella nigricans (Ayres, 1860), noted that decreases in temperature worked against those fish with herbivorous diets, thus being an omnivorous diet more efficient at low temperatures. This particular herbivore restriction suggests a selection against fish whose diet consists mainly of algae and could mostly explain the latitudinal pattern of decline in the richness recorded for this group of fish. This also coincides with declines in overall abundances of these fishes (Meekan and Choat 1997).
Some of the breaks recorded in the biogeographic patterns are consistent with changes in the environmental system of the Chilean coast. For example, the change in the width of the continental shelf at 33° S coincides with a break in both the number and composition of species. This has also been described for benthic molluscs on South Pacific coasts (Valdovinos et al. 2003), where changes in the geomorphology of the continental shelf south of 40° S latitude constitute the variable that best explains the increased richness recorded. However, our results, similar to Rivadeneira et al. (2011) regarding peracarids, indicate a decrease in richness with an increase in continental shelf area. The correlation between diversity patterns and factors such as the geomorphology of the continental shelf justifies the use of a biogeographic perspective, since it generally holds that much of the variation in species richness, and abundance can be explained by environmental variables. Nevertheless, as evidenced by our results, such variation could be the effect of several types of variables acting together. Therefore, it cannot be explained by simply adding the effects involved but rather by identifying the interactions between the environmental variables studied. Correlations of these variables with a common variable that has not been considered in this study would also contribute to elucidating what triggers richness variation. This raises the need for studies that include factors other than those discussed in this paper. For example, Colton and Swearer (2012) studied the coastal fish fauna of Victoria, Australia, and concluded that the particular conditions of currents, isotherms, and habitat discontinuities can determine the biogeographic breaks recorded in this area, also emphasizing the difficulty of attributing faunal breaks to single mechanisms. Meanwhile, Lucifora et al. (2012) showed the importance of oxygen concentration and oceanic fronts for the diversity of Chondrichthyes over the continental shelf in the southwest Atlantic. Thus, the highest diversity levels were recorded close to oceanic fronts, where different water masses converge and generate enormous biological productivity, due to the entrance of nutrients into the photic zone of the water column caused by turbulent mixing (Acha et al. 2004).
Although our results suggest that environmental variables may simultaneously affect richness, the relative significance of each variable may differ between fish from different habitats. This is precisely what was observed between the two littoral environments studied. While temperature and shelf width were the main factors underlying variations in intertidal fish richness (both independently and in combination), shelf area mainly affected subtidal fish richness variations (independently and together with latitude and temperature).
We are grateful to Bernardo Broitman for providing SST, Chl-a, and areal data and to Martin Thiel for valuable comments and suggestions on the manuscript. This study was funded by several FONDECYT projects and FONDAP-FONDECYT grant 15010001 CASEB to FPO. NAL acknowledges financial support from CONICYT-FONDECYT 1090624 and PIA-CONICYT ANILLOS ACT-132. AHN is currently funded by a CONICYT doctoral fellowship.
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