Richness and endemism of the freshwater fishes of Mexico

 

Topiltzin Contreras-MacBeath 1, Marlem Brito Rodríguez 2, Valentino Sorani 3, Chris Goldspink 4 & Gordon McGregor Reid 5

 

1 Centro de Investigaciones Biológicas, Universidad Autónoma del Estado de Morelos, México

2 Facultad de Ciencias Biológicas, Universidad Autónoma del Estado de Morelos, México

3 Centro de Investigación en Biodiversidad y Conservación, Laboratorio Interdisciplinario de Sistemas de Información Geográfica, Universidad Autónoma del Estado de Morelos, C.P. 62260, Morelos, México

4 Manchester Metropolitan University, All Saints Building, All Saints,
Manchester, M15 6BH, UK

5 Chester Zoo, Upton-by-Chester, Chester CH2 1LH, UK

1 topis@uaem.mx (corresponding author), 2 merlam_14@hotmail.com, 3 vsorani@yahoo.com.mx, 4 CGoldspink@aol.com,5 gordonr@chesterzoo.org

 

 

Abstract: A study of richness and endemism of the freshwater fishes of Mexico, was carried out in order to identify hotspots and inform conservation efforts. This was done by mapping and overlaying individual species distributions by means of geographical information systems based on museum data. The study was able to confirm several previously proposed centres of freshwater fish richness (Southeastern Mexico, the Mesa Central, the Bravo-Conchos river system and the Panuco and Tuxpan-Nautla rivers).  Seven areas with high ‘Corrected Weighted Endemism’ Index values were identified, with the valley of Cuatrociénegas recognized as a true centre. An alarming result was the identification of a “Ghost” centre of endemism (Llanos El Salado) in southwestern Nuevo León, where six endemic cyprinodont species are all ‘extinct’ or ‘extinct in the wild’.  Forty-nine single site endemics that are distributed all over Mexico were identified.  The Chichancanab lagoon in the border between Yucatan and Quintana Roo, where a flock composed of six endemic cyprinodonts is present needs special mention. Three hotspots of richness plus endemism were found in Mexico, the most important of which is the Mesa Central where impacts by human activities have had a detrimental effect on fish populations.

 

Keywords: Conservation, hotspots, ichthyodiversity, Meso-America, species.

 

 

Spanish Abstract Resumen: Se realizó un estudio de la riqueza y endemismo de los peces dulceacuícolas de México, con la finalidad de identificar “hotspots” y dirigir esfuerzos de conservación. Lo anterior se llevó a cabo mediante el mapeo y la superposición de las distribuciones de especies con el uso de sistemas de información geográfica y bases de datos de colecciones científicas. Los resultados confirman varios centros de endemismos propuestos previamente (Sudeste mexicano, la Mesa central, el sistema Bravo-Conchos, así como el de los ríos Panuco y Tuxpan-Nautla). Se identificaron además siete áreas con altos valores en el Índice de Endemismo Ponderado, siendo el Valle de Cuatro Ciénegas un verdadero Centro. Un resultado alarmante fue el haber encontrado un centro de endemismo “fantasma” (Llanos El Salado) al Sudoeste de Nuevo León, donde seis especies de Cyprinodóntidos endémicos están ahora extintos o extintos en la naturaleza. Se encontraron además cuarenta y nueve especies endémicas a una sola localidad. Destaca el caso de la laguna de Chichancanab ubicada en la frontera de los estados de Yucatán y Quintara Roo, donde existe un grupo compuesto de seis especies de Cyprinodóntidos. Se encontraron tres “hotspots” de riqueza y endemismo, dentro de los que destaca la Mesa central, donde los impactos de las actividades humanas han tenido un fuerte impacto sobre las poblaciones de peces.

 

 

 

doi: http://dx.doi.org/10.11609/JoTT.o3633.5421-33  |  ZooBank: urn:lsid:zoobank.org:pub:6D0D9D42-7628-4BFB-9273-48A8A32D4700

 

Editor: Rajeev Raghavan, Conservation Research Group (CRG), St. Albert’s College, Kochi, India.          Date of publication: 26 February 2014 (online & print)

 

Manuscript details: Ms # o3633 | Received 22 May 2013 | Final received 06 February 2014 | Finally accepted 08 February 2014

 

Citation: Contreras-MacBeath, T., M.B. Rodríguez, V. Sorani, C. Goldspink & G.M. Reid (2014). Richness and endemism of the freshwater fishes of Mexico. Journal of Threatened Taxa 6(2): 5421–5433; http://dx.doi.org/10.11609/JoTT.o3633.5421-33

 

Copyright: © Contreras-MacBeath et al. 2014. Creative Commons Attribution 3.0 Unported License. JoTT allows unrestricted use of this article in any medium, reproduction and distribution by providing adequate credit to the authors and the source of publication.

 

Funding: Mexican Education Ministry through PROMEP and the Noth England Zoological Society.

 

Competing Interest: The authors declare no competing interests.

 

Author Contribution: Topiltzin Contreras-MacBeath coordinated the study and participated in each step. C.R. Goldspink, and Gordon McGregor Reid participated in the design, management and implementation of the study, its research objectives and the provision of academic rigour.  Marlem Brito Rodríguez participated in spatial analysis, integration of the freshwater fish data base of Mexico, richness map, endemism map and final cartography.  Valentino Sorani participated in spatial analysis methodology development and manuscript revision.

 

Author Details: Topiltzin Contreras is head of the Conservation Biology Research Group at the “Universidad Autónoma del Estado de Morelos” in Mexico, he is also Chair of the IUCN/SSC Freshwater Conservation Sub-Committee, he is also currently Minister for Sustainable Development of the Government of Morelos, Mexico. C.R.Goldspink, previously worked for the International Biological Programme (Netherlands) Freshwater Section but currently involved with local and worldwide conservation issues. Particular research interests include the management of isolated lakes in North West England and the potential threats from invasive species and climatic change. Senior Lecturer at the Manchester Metropolitan University. Gordon McGregor Reid is the former Director General Director of Chester Zoo, and Former Chair of the IUCN/SSC Freshwater Fish Specialist Group. Valentino Sorani is head of the Interdisciplinary GIS Laboratory of the Research Center in Biodiversity and Conservation of the “Universidad Autónoma del Estado de Morelos”. Professor of GIS. Expert in land planning, remote sensing and spatial analysis. Marlem Brito Rodríguez is responsible for the GIS area of the Interdisciplinary GIS Laboratory of the Research Center in Biodiversity and Conservation of the “Universidad Autónoma del Estado de Morelos”. She is an expert in remote sensing, cartography and spatial data bases.

 

Acknowledgements:  We would like to thank CONABIO for providing access to their databases, as well as the GBIF for their records.

 

 

 

For figures, images, tables -- click here

 

 

Introduction

 

Mexico is the southern most country of North America, extending into the Isthmus of Tehuantepec.  It has a total area of 1,964,375km2 and is bounded by a coastline of 7,828km to the west (Pacific) and 3,294km to the east, which includes parts of the Gulf of Mexico and the Caribbean (CNA 2008).  The country has a wide range of terrestrial habitats and formations consisting of volcanic mountain ranges and extensive arid deserts, and is estimated to contain at least 10% of the known world terrestrial biodiversity including plants, reptiles, amphibians and mammals (Espinosa et al. 2008).  This taxonomic diversity reflects the wide range of habitats represented in Mexico, regional differences in climate and its position between the Nearctic and Neotropical biogeographical regions (Morrone 2005).

Similarly, a wide range of aquatic systems occurs across the country with over 50 large rivers and 70 large lakes represented.  The rivers Yaqui, Fuerte, Mezquital, Lerma-Santiago, and Balsas drain into the Pacific, whilst the Bravo, Pánuco, Papaloapan, Grijalva and Usumacinta rivers drain into the Gulf of Mexico (Lara-Lara et al. 2008).  There are over 70 lakes ranging in size from 10–100 km2.  Lake Chapala in Jalisco is the largest lake, followed by Cuitzeo and Pátzcuaro in Michoacán, Catazajá in Chiapas, del Corte in Campeche, Bavicora and Bustillos in Chihuahua, and Catemaco in Veracruz.  Though, there have been various studies on the distribution of plants and animals across the country (Ramamoorthy et al. 1993, Flores-Villela & Gerez 1994, Koleff & Soberón 2008) there have been relatively few studies on aquatic biota (Domínguez-Domínguez et al. 2006b; Huidobro et al. 2006; Aguilar-Aguilar et al. 2008).  The freshwater fish fauna is particularly diverse with more than 616 species described of which 264 are endemic (examples of some Mexican freswater fish species are shown in images 1–7).   A further 115 species are known to be exotics (Miller et al. 2009).  In spite of this diversity there have been very few attempts to formally describe regional differences in fish species assemblages to better inform conservation action.

In this study, we attempt to identify and define regional differences in biodiversity in terms of the ‘hotspot’ approach which has proved successful in identifying areas of conservation importance elsewhere in the world (Myers 1988, 1990; Myers et al. 2000).  Both species number (richness) and endemism are used in defining the ‘hotspot’ approach by combining two independent measures of biodiversity.  Myers (2003) had stressed that “there is an urgent need to document freshwater ecosystems which could prove to be one of the most species-rich hotspots, certainly in terms of fish and one of the most severely threatened of all hotspots”.  Freshwater ecosystems therefore provide ideal candidates for applying the biodiversity hotspot approach (Mittermeier et al. 2010).

Thus, the main aim of the current study was to re-evaluate the status of freshwater fishes in Mexico in terms of their species richness and degree of endemism, and identify and map local ‘hotspots’ to further direct conservation planning and debate in the country. Large-scale studies of this kind on freshwater fish have largely been confined to Brazil and Africa (Nogueira et al. 2010; Darwall et al. 2011).

 

 

Methods

 

The analysis used during this study was based on the geographical procedures employed by Aguilar-Aguilar et al. (2008). This consisted of developing geo-referenced distribution records for the freshwater fishes found in Mexico.  Empirical data were derived from the National Mexican Biodiversity Authority (CONABIO) and records held by the Global Biodiversity Information Facility (GBIF).  These sources yielded 36,174 countrywide records and maps for 563 of the 650 known species listed for the country.  These data, which account for ca. 86% of the total fish fauna, also included many of the introduced or exotic species (Contreras-MacBeath 2014).

For each species, spatial records were converted to a vector format using ArcGis 9.3 and superimposed onto a 1:4,000,000 scale map of Mexico obtained from the geo-information module of CONABIO.  Each map was then compared to previously published species accounts (Miller et al. 2009) and those mentioned in Fishbase (Froese & Pauly 2010) to eliminate inconsistencies and false positives (Fielding & Bell 1997).  Of the total records examined, 358 were rejected representing 1% of the total.  A grid map of Mexico was then produced consisting of 249 grid cells assigned 1–31 from west to east and from A to M North to South.  Each 1oX1o grid cell equivalent to 12,345km2 was subsequently converted to raster format.  This marker allowed a comparison of the geographical layers.  Once the grid was obtained, each grid-cell was assigned consecutive numbers from 1 to 249.

For evaluation, data of each species was transformed to raster format, obtaining a matrix in binary format, with grid-cells with a value of “1” where the species was present and “0” where it was not.  This grid was then combined with the distributional ranges of each species using the “combine” command of Arc Info 7.0, which from a series of rasters, creates a new one that shows in its database all the possible combinations among all the rasters used in the operation.

The end result was a coverture in matricial format with an associated table that contains 534 columns, each representing a species, and 249 lines that represent grid-cells.  In this way, presence and absence information was available for every species in each grid-cell.  The total for each line represented species richness in each grid-cell, while the total for each column indicated the distributional range for each species.  With this information, a map of Mexico was constructed showing species richness in three categories: Low (1–30 species), medium (31–60 species) and high (61–90 species).

The endemism analysis was based on the ‘Corrected Weighted Endemism’ Index CWEI (Crisp et al. 2001; Linder 2001; Aguilar-Aguilar et al. 2008) using 216 of the 264 known Mexican endemic species, because of the availability of point data.  To calculate the Weighted Endemism Index (WEI), each species was weighted for the inverse of its range such that each endemic species in a grid-cell had a maximum ‘weight’ of 1; if a species was present in three grid-cells, it has a weight of 0.33 and one in 30 grid-cells has a weight of 0.03.  To calculate the value for each grid-cell, the weight values for all the species in that grid-cell was added so that cells with a high number of restricted range species had a higher score than grid-cells with fewer restricted range species (Linder 2001).  To correct for the correlation with species richness, and to generate the CWEI, the ‘weighted’ endemism was divided by the total number of species in a grid-cell (Crisp et al. 2001).  A map that differentiates between areas of low, moderate and high endemism was subsequently produced with the results of this analysis.

Due to the fact that the former is a coarse analysis that considers relatively large areas, and that it is known that some Mexican freshwater fish species have highly restricted distribution ranges that would not be identified by this means, we further analyzed single site endemics (extant species) separately, so as to have a finer view of endemism.

To identify possible conservation ‘hotspots’ of richness plus endemism, the two previous maps were combined by creating two raster maps both with the same grid size, a grid position, and the same geo-reference, the first for species richness and the second for species endemism.  A cross operation was performed by overlaying the two raster maps by comparing cells at the same positions in both maps and keeping track of all the combinations that occur between the values or classes in both maps.  A cross-table and the output cross-map were obtained.  The results were stored in an output cross-table and an output cross-map.  In the table associated with the output raster, a new item was created containing a unique value for all the possible combinations of the two input classes, as well as the class number and description of the first input map (richness) and those of the second input map (endemism) which makes it possible to identify every single combination.  The number of pixels occurring for each combination was counted, as well as the areas of the combinations calculated.  A biodiversity quality indicator was then defined by assigning to every combination a value, following the decision rule:

IF Vr + Ve < 4 then BQI = poor else if 4≤ Vr + Ve ≤5 then BQI = medium else BQI = high

This provided the basis for the production of a map, which correlates richness and endemism.

 

 

Results and Discussion

 

Distribution and range

Fish species records were obtained from 235 of the 249 grid-cells covering Mexico which represented 94.3% of the country area.  Those areas without confirmed records are shown in Figure 2 as white squares and are generally associated with arid regions of country, namely the provinces of El Salado and Mapimi.

In terms of distribution patterns, species varied from having very restricted distributions occurring in only one grid cell (23.3% of the total) up to those, which were widely represented across the country (Fig. 1 ).  Ten species are represented in 45 to 66 of the grid cells, namely Astyanax aeneus (66 cells), Astyanax mexicanus (65), Micropterus salmoides (62), Poecilia mexicana (60), Poecilia sphenops (55), Gambusia affinis (54), Lepomis macrochirus (51), Oreochromis mossambicus (47), Heterandria bimaculata (46) and Sphoeroides annulatus (45).  Astyanax aeneus was the most widely represented species, occurring in 66 cells equivalent to ca. 491,093km2 or 26.5% of the country area.

Many of the widely dispersed species correspond to the distribution maps previously described by Miller et al. (2009) and Froese & Pauly (2010), reflecting natural geographical boundaries.  These species include Astyanax aeneus, Astyanax mexicanus, Poecilia mexicana, Sphoeroides annulatus and possibly Poecilia sphenops, if sites with populations of un-determined taxonomic status are included (Miller et al. 2009).    Other widely distributed species are those, which are known to be associated with human activities, especially aquaculture.  The Cichlid Oreochromis mossambicus (commonly referred to as Mozambique Tilapia) is now the seventh most widely distributed freshwater fish in Mexico.  In addition, four native species, which have had relatively small original distributions in Mexico, have now been translocated to many other parts of the country.  Species such as Micropterus salmoides and Lepomis macrochirus have both been widely stocked for sport fishing (Contreras-MacBeath et al. 1998) and Gambusia affinis is often used for the control of mosquito larvae (Miller et al. 2009). Similarly, Heterandria bimaculata has spread through aquaculture activities (Contreras-MacBeath et al. 1998).  It is alarming that half of the ten most widely distributed freshwater fishes of Mexico are exotics (Gozlan et al. 2010).

In contrast, 124 species (23.3% of the total) have ranges restricted to only one cell.  Most of these restricted species are from five families comprising 67% of the total namely, Poeciliidae (19 spp), Atherinopsidae (16 spp), Cyprinodontidae (12 spp), Cyprinidae (11 spp) and Goodeidae (9 spp).

When examined by their range areas, it is apparent that the overall pattern for all species is skewed to the right (Fig. 1), consistent with the generalized model described by Gaston (1998).  That is, most species have a relatively small range size and a few have relatively large range size.  This pattern has been observed for many other taxonomic species assemblages (Bell 2001; Jetz & Rahbek 2002).

For Mexico, Ceballos (2001) found that that 50% of mammal species and 8% of birds could be considered as ‘rare’ based on the criterion (50,000km2) employed by IUCN. Similar results were found for reptiles and amphibians (Ceballos 2001), which correspond to the value, observed here for fish.  Thus based on the 50,000km2 criterion, 57% of Mexican freshwater fish should be considered as rare.

Moreover, if each 1o grid cell is equivalent to 12,345km2, then 100 species found within this category (19%) roughly fit the criterion of ‘restricted range’ species proposed by Nogueira et al. (2010) who found that of the 2587 freshwater fish species known for Brazilian freshwaters, 819 (32%) had distribution ranges not exceeding 10,000km2.  Similar to Brazil, these values could be used in the identification of site-scale conservation priorities in Mexico.

 

Richness

The number of fish species found across the 249 grid cells varied from one up to 90 species per cell with an overall mean of 19 species per cell (Fig. 2).  In terms of richness, the grid-cell with the highest richness (S=90) was located in south-eastern Mexico within the Papaloapan River basin.  This includes Lake Catemaco, los Tuxtlas (Biosphere Reserve) and the coastal lagoon of Sontecomapan in the State of Veracruz.  Of the 90 species recorded, six were exotics, especially tilapias introduced for aquaculture.  The 86 remaining species were distributed amongst 27 families, the most speciose of which were Poeciliidae with 18 and Cichlidae with 10.  Both these groups represent 32% of the total fish diversity in the grid-cell.

If families are grouped according to Myer’s (1949) classification of freshwater fish based on their tolerance to salt water (primary, secondary and ‘peripheral’) (Berra 2007), ‘peripheral’ families dominate, with 22 families and 50 species, while there are only two primary families with five species and three secondary families with 29 species.  This clearly reflects the influence of the paleogeographical history of the region, as well as marine radiations and incursions into the freshwater fish fauna (Myers 1966; Miller et al. 2009).  This is consistent with what has also been described for the whole of North America (Lévźque et al. 2008).

From Fig. 2, it is evident that the highest values of species richness are found in four distinct centers formed by grid cells which correspond well with the ichthyofaunal provinces described earlier by Miller et al. (2009).

(1) The first center is localized in southeastern Mexico, with the largest number of species per grid-cell (62–90) concentrated in the Grijalva-Usumacinta, Coatzacoalcos and Papaloapan rivers (darkest color in the map).  This region corresponds with the area of highest availability of water in Mexico (Bunge 2010).  If the Yucatan Peninsula is included in this centre, 39 grid-cells are represented and this corresponds to the Usumacinta ichthyofaunal province (Miller et al. 2009).  These findings are in accordance with a similar analysis carried out for helminth parasites of freshwater fish (Aguilar-Aguilar et al. 2008).  This general pattern is also similar to that found for terrestrial vertebrates with the highest species richness in southeastern Mexico (Koleff & Soberón 2008).

This centre has 44 families and 265 species, 16 of which are exotics.  Within this group, the two most diverse families are Cichlidae and Poeciliidae with 42 and 40 species respectively. These are followed by the Gobiidae with 12, Eleotridae 11, and Ariidae, Cyprinodontidae and Gerreidae with 10 species each.  Perhaps due to the large river systems, availability of water and large floddplains (Aguilar 2003; Lara-Lara et al. 2008; Bunge 2010), there are species with large distributions, such as Sciades guatemalensis (34 grid cells), Astyanax aeneus (33) (Image 1), Cichlasoma urophthalmus (31), Poecilia mexicana (31), Gambusia yucatana (29), Belonesox belizanus (28), Rocio ocotal (28), Parachromis friedrichsthalii (27), Heterandria bimaculata (24) and Cichlasoma salvini (23).  By contrast, there are 71 species with distributions represented by only one grid-cell equivalent to 12,345km2.

(2) The second centre occurs in central Mexico mainly within the Lerma-Santiago river system, which corresponds to the central part of the Mesa Central ichthyofaunal province (Miller et al. 2009).  It has eight grid-cells that range from 33–52 species per cell, with the highest values concentrated in the region of Michoacan lakes (Patzcuaro & Cuitzeo) as well as Lake Chapala, which has been well documented previously (Domínguez-Domínguez et al. 2006b, Huidobro et al. 2006, Mercado-Silva et al. 2006).  This province also corresponds with the findings of Aguilar-Aguilar et al. (2008) for fish helminths.  It has 23 families and 122 species of freshwater fish, including 19 exotics. The most diverse family is Goodeidae with 25 species, but in the whole of the Mesa Central there are about 41 species (Domínguez-Domínguez et al. 2006a).  Other diverse families are Atherinopsidae, Poeciliidae and Cyprinidae, with 22, 13 and 12 species respectively. The two species with the widest distribution (eight grid-cells) are Goodea atripinnis, and the exotic Oreochromis mossambicus.  These are followed by a group of species with relatively wide distributions (seven grid-cells) such as Algansea tincella, Notropis sallaei, Chirostoma arge, Ilyodon whitei, Poeciliopsis infans, and the exotics Oreochromis aureus and Xiphophorus hellerii.  The last species is native to Mexico but not to to the Mesa Central (Miller et al. 2009), following the definition proposed by Copp et al. (2005).  In this region, there were 55 species having distributions within one grid-cell.

(3) The third center is localized in northern Mexico, along the border with the United States, and corresponds to the Bravo-Conchos river system.  It comprises eight grid-cells that range from 32–57 species, the most diverse one of which includes the Rio Bravo delta and part of Laguna Madre.  This suggests that its high diversity is a reflection of the influence of the presence of many peripheral fish species.  It has 30 families and 122 species, with only three exotics.  The three most diverse families are Cyprinidae, Poeciliidae and Cyprinodontidae with 24, 14 and nine species respectively.  As in the previous region, species distributions range from 1–8 grid cells.  There are five species with a wide distribution, Astyanax mexicanus, Gambusia affinis, Ictalurus punctatus, Lepomis macrochirus and Micropterus salmoides, all native to the region.  However, 57 species have distributions which include only one grid-cell.

(iv) The fourth center is found in eastern Mexico along the central portion of the Gulf, and comprises the Pánuco and Tuxpan-Nautla rivers, the latter of which, corresponds to the Tamesi-Pánuco complex ichthyofaunal province.  It consists of seven grid-cells with a range of 33 –41 species.  It has 32 families and 125 species, 15 of which are exotics. The most diverse families are Poeciliidae and Cichlidae with 24 and 11 species respectively.  Three species are distributed throughout the whole centre (seven grid-cells), Astyanax mexicanus, Poecilia Mexicana and Herichthys cyanoguttatus. In the case of this last species, Miller et al. (2009) suggested that for this region it could be a different species.  There are also 53 species with distributions of only grid-cell.

There are three other grid-cells with relatively high values of species richness, two are along the Pacific coast, one in Guerrero and the other in Sinaloa, but this reflects the influence of ‘peripheral’ fish species. One of the highlighted grid-cells has 33 species and is located in central Mexico between the States of Morelos and México reflecting the influence of the higher Lerma and Balsas basins.  However, this high number of species is mainly due to the presence of 14 exotic species, which represent 42% of the total.  Based on native species alone, this cell would fall in the low richness category with only 19 species. Exotics species account for 64% of all species within the State of Morelos (Contreras-MacBeath et al. 1998).

 

Endemism

Based on the definitions applied here, Mexican endemics appear to be widely distributed across the country. Of the endemic species identified, 216 occurred within 174 of the 249 grid-cells (colored grid-cells Fig. 3) representing 70% of the country area.  There were also areas of moderate endemism throughout the country, but with no distinctive pattern apparent.

Based on the calculated indices (CWEI) of endemism, seven individual grid-cells showed high values.  These are highlighted in the map (dark color Fig. 3).  Most occur in northern Mexico and are associated with arid ecosystems, areas of relatively low species richness and with species of restricted distributions.  These grid-cells can be grouped in one of two categories.  Grid-cells 1 and 2 can be considered as true centers of endemism.

The first center of endemism (Fig. 2(1)) compromises the valley of Cuatrociénegas in central Coahuila, which is a 1,000km2 desert valley that has the greatest number of endemic species of any place in North America (Stein et al. 2000).  Much of its biotic diversity is associated with a complex array of thousands of geothermal springs, marshes, lakes and streams (Souza et al. 2006).  It has the highest richness of all the areas of endemism identified in this paper with 10 endemic fish species, but its high index of endemism is dependent on the presence of Cyprinella xanticara, Cyprinodon atrorus, Cyprinodon bifasciatus, Etheostoma lugoi, Gambusia longispinis, Herichthys minckleyi, Lucania interioris and Xiphophorus gordoni.  This is one of the eight globally outstanding freshwater ecoregions identified for Mexico by Revenga et al. (2000).

The second center of endemism (Fig. 2(2)) consists of two springs included in two endorheic basins in Southwestern Nuevo León; El Potosí (Ejido Catarino Rodríguez, Municipio de Galeana), which is the type locality for Cyprinodon alvarezi and Megupsilon aprorus (both now extinct in the wild) and the Ojo de Agua la Presa in Bolsón de Sandia which was inhabited by Cyprinodon veronicae, Cyprinodon longidorsalis (both now extinct in the wild), Cyprinodon inmemoriam and Cyprinodon ceciliae (both extinct). Due to the fact that all six species identified for this center are extinct or extinct in the wild, it is best regarded as a “ghost” center of endemism.  Eleven years ago, the freshwater ecosystems in this area, which roughly corresponds to “Llanos El Salado” ecoregion were regarded as vulnerable by Abell et al. (2000) but have now all disappeared due to water abstraction. Clearly, further studies are required to identify the stressors which have contributed to the extinction of these species, to avoid similar problems occurring elsewhere.  The remaining areas of endemism (compared to the valley of Cuatrociénegas and Llanos El Salado), are highlighted by values of CWEI due to the fact that they are in areas with low species richness of endemics, and those present have restricted distributions.

The third center (Fig. 3) occurs in the northern part of Coahuila, on the border with the United States.  This center is defined by two species: Gambusia krumholzi from Río de Nava and Prietella phreatophila from a series of caves in the same region.  Although both of these sites are found within part of the río Bravo basin, they are restricted to México.

Center (4) is triggered by Gambusia alvarezi, which is endemic to the Ojo de San Gregorio spring near Ciudad Parral Chihuahua and center (5) triggered by Cyprinodon fontinalis and Cyprinella bocagrande, both from Bolsón de los Muertos in Chihuahua.  Center (6) is localized in the Baja California Peninsula and is triggered by Gobiesox juniperoserrari, that is known only from a series of pools in Arroyo “Las Pocitas” in Baja California Sur.  Center (7) is localized to the south of the country in Río Tehuantepec, Atoyac basin in the State of Oaxaca, and is triggered by two species, Notropis imelda and Poeciliopsis lutzi.

 

Single site endemics

In order to understand in detail the distribution of endemic species, we set out to identify species with discrete distributions known only from one site.  From our analysis, we found that 43 species in 11 families can be regarded as single site endemics.  The most diverse family is Cyprinodontidae with 11 species, followed by Goodeidae (9), Cyprinidae (7), Cichlidae (5), Poeciliidae (3), Atherinopsidae and Heptapteridae with two species each, and then there are three families with one species each (Fundulidae, Profundulidae and Characidae) (Fig. 4).

Single site endemics are distributed all over the country (Fig. 5).  Some species have a very restricted distribution; for example Zoogoneticus tequila (Image 2) is now only found in a 4m diameter spring in Tehuchitlán Jalisco (De la Vega-Salazar et al. 2003) and Cyprinodon julimes from the Chihuahuan desert that occurs in a 742m2 thermal spring (De la Maza et al. 2010).  Others localized endemics are found in larger water bodies such as Bramocharax caballeroi restricted to Catemaco Lake in Veracruz with a surface area of 72.54km2 (Torres-Orozco & Sanatta 1998).  There are also other local endemics such as Poeciliopsis catemaco and Xiphophorus milleri which occur in Lake Catemaco, but these were not considered because they can also be found in streams and tributaries of the lake (Miller et al. 2009).

It is important to mention a species flock composed of six endemic species of Cyprinodonts (Cyprinodon beltrani, C. simus, C. maya, C. labiousus, C. esconditus & C. verecundus) occurs in Laguna Chichancanab in the border between Yucatan and Quintana Roo (García-Moreno et al. 2008), but their occurrence could not be identified by the methods used here CWEI method (Crisp et al. 2001).  There is also a small region in central-western Mexico, where there are several endemic species of the upper Río Ameca, (Yuriria amatlana, Allotoca goslinei, Algansea amecae, Ameca splendens and Zoogoneticus tequila) which could be treated as a center of endemism.  The last species mentioned above is now confined to a single small spring in Tehuchitlan Jalisco (De la Vega-Salazar et al. 2003; Magurran 2009).

 

Richness and endemism hotspots

In order to identify biodiversity hotspots (Myers 1988; Crisp et al. 2001; Aguilar-Aguilar et al. 2008; Myers et al. 2000), richness and endemism were correlated and a map constructed (Fig. 6). Three main hotspots with high values; (1) the Mesa Central, (2) the Central-southeastern and (3) the Lower Rio Bravo River were identified. These are aso priority areas for conservation in terms of their parasite biodiversity and threats by Aguilar et al. (2010).

Among these, the Mesa Central stands out and includes the headwaters of the Río Ameca and the Lerma-Chapala-Santiago system extending into the Río Pánuco basin.  This whole region includes four of the eight globally outstanding freshwater ecoregions described by Revenga et al. (2000) that are distributed along central Mexico.  This region has been described as transitional between the Nearctic and Neotropical provinces (Morrone 2005; Huidobro et al. 2006; Corona et al. 2007) and contributes to its high species richness and endemism for fish (Miller 2005). Within this region, two hotspots can be identified which have the highest value for the combination of richness and endemism.

The first hotspot, consists of an area known as the “Bajo Lerma” (Díaz-Pardo et al. 1993) and includes headwaters of the Río Ameca and Lake Chapala.  It has 48 species of which 38 are Mexican endemics (79%).  The second hotspot is formed by two adjacent grid-cells that cover the “Medio Lerma”, including lakes Patzcuaro, Cuitzeo and Yuridia.  It has 63 species, of which 49 are Mexican endemics (77%).  Unfortunately, this region of Mexico has also been identified as one of the most seriously downgraded/impacted areas (rivers and lakes) by human activities (Bernal-Brooks 1998; Fisher et al. 2003; von Bertrab, 2003; Garrido et al. 2010).  This has had a negative impact on the native fish fauna of the region (De la Vega-Salazar 2006; Domínguez-Domínguez et al. 2006a; Domínguez-Domínguez et al. 2008; Mercado-Silva et al. 2009; Magurran 2009) and has resulted in the extinction of six species, namely Chirostoma bartoni, Chirostoma charari, Evarra bustamantei, Evarra eigenmanni, Evarra tlahuacensis and Skiffia francesae (Contreras-MacBeath 2005).

The Central-southeastern hotspot includes the area with most water resources in Mexico for the rivers Coatzacoalcos, Papaloapan and Grijalva-Usumacinta (CONAGUA 2008; Bunge 2010).  This hotspot is more relevant because of its richness of 208 species, rather than its endemics comprising of only 30 species (14.4%).  Maybe due to the abundance of water in this hotspot, as well as the relatively low human population, it is one of Mexico’s regions with lowest pollution as indicated by measures of Biochemical Oxygen Demand (BOD) and Chemical Oxygen Demand (COD) (CONAGUA 2010). Nevertheless, Rio Grijalva is highlighted as an area that has witnessed large habitat modifications due to the construction of four large dams (Garrido et al. 2000).  There are als two known extinct species in this hotspot namely Atherinella callida, Priapella bonita (Harrison & Stiassny 1999).

The last of the hotspots identified is a small area in northern Mexico that corresponds to the lower Rio Bravo. As in the former case, this hotspot is highlighted mainly by its richness of 90 species, rather than the occurrence of seven endemics (7.7%).  As with many Mexican freshwater ecosystems associated with arid regions, it has been severely impacted by human activities (Contreras-Balderas & Lozano-Vilano 1993).  Surveys have demonstrated that the original freshwater fish fauna has been retreating from the lower reaches and is being replaced by brackishwater and marine invaders (Contreras-Balderas et al. 2002).  This river which had a runoff of over 12,000 million cubic meters/year in 1962 had less than 2% of that figure in 2002 and was dry for months in the delta region, both in 2002 and 2004 (Contreras-Balderas et al. 2008).

 

 

Conclusions

 

Data on species richness and endemism are both crucial for identifying regional and national ‘hotspots’ and for directing conservation effort.  Identifying and mapping these centres by means of geographical information systems based on museum data have confirmed several previously identified centres of freshwater fish richness including those of southeastern Mexico, the Mesa Central, the Bravo-Conchos river system and the Panuco and Tuxpan-Nautla rivers.  A further seven areas with high CWEI endemism values have been identified including the valley of Cuatrociénegas recognized as a true centre.  Unfortunately, an important area previously identified as a center of endemism, has now been identified as a “Ghost” centre of endemism (Llanos El Salado) in southwestern Nuevo León, due to the loss of six endemic cyprinodont species that were previously present in this area.  In addition, 49 single location endemics were found to be widely dispersed across Mexico.  One site, the Chichancanab lagoon on the border between Yucatan and Quintana Roo, contains a flock of six endemic cyprinodonts. Many of the other single site endemics which are threatened species should be considered as areas triggering ‘Alliance for Zero Extinction’.  However, three hotspots of richness and endemism in Mexico including the Mesa Central have been seriously compromised by human activities that are very detrimental to fish species populations.

This study has provided a countrywide analysis of the distributional patterns of most of the known species of freshwater fish in Mexico, using the most up-to-date information available.  However, further work is required on a smaller scale to identify and resolve local conservation issues. However, our results, provide important baseline reference material which can stimulate further conservation initiatives and debate at both local and national level.  The next step is to complete the IUCN threat assessments for each species. When completed, it will be possible to cross-reference our findings with the distributional patterns of threatened species and define explicit conservation goals.  Our study has also shown that methods, which have previously been applied to terrestrial taxa, can also be applied successfully to aquatic taxonomic groups.

 

 

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