Amphibians and Reptiles Associated With Urban and Peri-urban Landscapes in the Central Andes of Colombia

Amphibians and Reptiles Associated With Urban and Peri-urban Landscapes in the Central Andes of Colombia | Research Square window.SnipcartSettings = { analytics: { enabled: false } }; (function() { var accessVector = localStorage.getItem('access_vector') || ''; window.dataLayer = window.dataLayer || []; if (accessVector) { window.dataLayer.push({ user: { profile: { profileInfo: { snid: accessVector } } } }); } })(); (function(w,d,s,l,i){w[l]=w[l]||[];w[l].push({'gtm.start':new Date().getTime(),event:'gtm.js'});var f=d.getElementsByTagName(s)[0],j=d.createElement(s),dl=l!='dataLayer'?'&l='+l:'';j.async=true;j.src='https://www.googletagmanager.com/gtm.js?id='+i+dl;f.parentNode.insertBefore(j,f);})(window,document,'script','dataLayer','GTM-K279D39R'); Browse Preprints In Review Journals COVID-19 Preprints AJE Video Bytes Research Tools Research Promotion AJE Professional Editing AJE Rubriq About Preprint Platform In Review Editorial Policies Our Team Advisory Board Help Center Sign In Submit a Preprint Cite Share Download PDF Research Article Amphibians and Reptiles Associated With Urban and Peri-urban Landscapes in the Central Andes of Colombia Erika Alejandra Cardona-Galvis, Jose J. Henao-Osorio, L. Santiago Caicedo-Martínez, and 3 more This is a preprint; it has not been peer reviewed by a journal. https://doi.org/ 10.21203/rs.3.rs-7464640/v1 This work is licensed under a CC BY 4.0 License Status: Under Review Version 1 posted 13 You are reading this latest preprint version Abstract The accelerated loss of biodiversity is one of the major concerns for conservation actions. In Colombia, much of the urban and cultivated areas are concentrated in the Andean region, a global biodiversity hotspot that retains less than 15% of its original forest cover. In this region, biodiversity studies are not often performed in urban environments. Here, this study present information about the diversity and composition of amphibians and reptiles in green areas of the municipality of Manizales, in the Central Andes of Colombia. To document the diversity and changes in the presence of amphibians and reptiles in the green and urbanized areas of Manizales, we performed fieldwork, literature searches and review of specimens from biological collections. Additionally, we incorporated a spatial analysis of ecological connectivity based on the Local Climate Zones (LCZ) classification. We recorded 30 species (10 amphibians, 20 reptiles), 16 endemic to Colombia, and two threatened species. Strabomantidae was the most diverse amphibian family (5 spp.), while for reptiles it was Colubridae (11 spp.). Field surveys yielded 291 individuals across 17 species, with Pristimantis thectopternus being the most abundant amphibian and Pholidobolus marianus the most common reptile. Species richness showed moderate positive correlation with area, though the smallest site exhibited the highest species density. LCZ analysis revealed significant landscape fragmentation. Reptiles demonstrated greater urban tolerance than amphibians. Our results highlight the critical importance of conserving urban green areas and the utility of LCZ for biodiversity conservation planning in rapidly urbanizing Andean ecosystems. Amphibian Andes Conservation Local Climate Zones Reptile Urban ecosystems Figures Figure 1 Figure 2 Figure 3 Figure 4 Introduction The exponential growth of the world's human population for more than 100 years has raised the rate of transformation of natural habitats in urban, industrial, or cultivated areas (Ripple et al. 2017 ; Zabel et al. 2019 ; Hughes et al. 2023 ). During the next 30 years, the global human population will reach a number close to 9.7 billion people, of which about 68% are likely to settle in metropolitan areas (United Nations 2022 ; LaRota-Aguilera and Marull 2023 ). From 1992 to 2000, around 190,000 km 2 of natural environments were transformed into urban areas, and between 2000 and 2030 an additional 290,000 km 2 it is estimated be transformed at global scale (McDonald et al. 2020 ). Increasing urbanization in natural areas are often associated with a decrease in species diversity (McKinney 2002 , 2006 ; Santos and Tellería 2006 ; Elmqvist et al. 2013 ). However, urban environments may also exhibit greater heterogeneity at smaller spatial scales than rural environments, becoming important habitats for many species (Keinath et al. 2023 ). In the Neotropics, the Andes are recognized as one of the world’s biodiversity hotspots due to its exceptional species richness and high levels of endemism, making it a global conservation priority (Kattan et al. 2004 ; Antonelli et al. 2009 ; Hazzi et al. 2018 ). In recent years, there has been greater interest in understanding the dynamics that characterize biodiversity in urban environments in this region (Delgado-V and Correa-H 2013; MacGregor-Fors 2013 ; Vanegas-Guerrero et al. 2016 ; Ramalho et al. 2018 ; Demartín et al. 2024 ). However, for the Andes there are still large information gaps that prevent a more precise understanding of which species may or may not persist in highly anthropized environments (Vanegas-Guerrero et al. 2016 ). To fill these information gaps and better understand the spatial dynamics and ecological connectivity of urban environments, the Local Climate Zones (LCZ) classification (Stewart and Oke 2012 ; Bechtel et al. 2015 ) can be integrated along with the information of the diversity of species. LCZ’s allow distinguishing between dense urban zones, open residential areas, artificial vegetation covers, and natural forested zones, facilitating the evaluation of potential ecological corridors and barriers for biodiversity (Han et al. 2024 ). The Andean region of Colombia, part of the Northern Andes (Josse et al. 2009 ), retains less than 15% of its original forest cover, primarily due to the expansion of the agricultural frontier and the grow of major population centers (Gentry 1993 ; Etter and Wyngaarden 2000 ; Armenteras et al. 2003 , 2011 ). Despite this, the Northern Andes is characterized by high biological diversity, and a high number of endemism (Kattan et al. 2004 ), being considered a key priority area for biodiversity conservation (Myers et al. 2000 ; Josse et al. 2009 ; Tognelli et al. 2019 ). Within the Northern Andes, the municipality of Manizales (571.8 km 2 , >434,403 inhabitants; (DANE 2018; Giraldo-Ospina and Vásquez-Varela 2021 ), is an intermediate-sized city located in the Central Cordillera of Colombia, in the Coffee Growing Region. Its rugged terrain results in fragmented urban development and reduced mountain connectivity (Giraldo-Ospina and Vásquez-Varela 2020 ). In Manizales, sub-Andean Forest remnants have been consolidated under the "Ecopark Network" and areas of environmental interest, which includes peri-urban forest relicts and other green areas within or near the city (Rojas-Morales 2012 ; Giraldo-Ospina and Vásquez-Varela 2021 ). Private households in the urban area of Manizales increased by about 25% between 2005 and 2018 (DANE 2018), highlighting the need for accurate information on biodiversity and its distribution in environments strongly affected by population growth. In the last 30 years, studies have been conducted that highlight the high biological richness in various vertebrate groups in Manizales such as birds (Walker 1996 ), reptiles (Rojas-Morales 2012 ; Rojas-Morales et al. 2014 ), and bats (Rosero-Taramuel et al. 2023 ), but research focused on estimate the diversity of amphibians and reptiles inhabiting urban and peri-urban landscapes in the city of Manizales are scarce (e.g., Rojas-Morales 2012 ; Rojas-Morales et al. 2014 ; Toro-Restrepo 2023 ; Vanegas-Guerrero et al. 2016 ; Ramírez-Chaves et al. 2022 ). Additionally, there has been no comprehensive assessment the diversity of amphibians and reptiles across the different LCZ, leaving a significant gap in understanding how these urban landscape classifications influence amphibian and reptile communities. The information gaps have hindered the establishment of monitoring, habitat connection studies, and the prioritization of species for conservation in urban and peri-urban environments. Furthermore, amphibians and reptiles are among the vertebrates most affected by habitat modifications due to their ectotherm condition, their low vagility, the aversion that some species generate in people (i.e., snakes; Lynch 2012 ), as well as a dependence on humid environments by amphibian species (Vanegas-Guerrero et al. 2016 ). Although information on the presence of certain amphibian and reptile species is available for some areas within Manizales, the relationship between biodiversity patterns and different LCZ has not been systematically evaluated. This knowledge gap represents a key opportunity for our research to establish these associations and understand how urban landscape characteristics influence amphibian and reptile distribution. For these reasons, our study aimed to document the amphibian and reptile diversity in the Ecopark network and areas of environmental interest of Manizales and asses the connectivity of habitats and number of species detected in different LCZ´s. Although this research focuses on a local scale, the results will serve as a fundamental basis for future large-scale studies in the Andes, a region of exceptional amphibian and reptile diversity and conservation priority. Our working hypothesis is that smaller and more isolated areas will support lower species richness and show dominance of only one or two species, such as generalist or disturbance-tolerant species. Material and methods Study area This study was conducted in the municipality of Manizales, Department of Caldas, which is located on the western flank of the Central Cordillera of the Andes of Colombia. It has a minimum elevation of 800 m and a maximum of 3800 m (Verhelst et al. 2001). Geographically, it includes areas whitin the middle Cauca River basin, as well as highland ecosystems such as Andean, sub- and high-Andean forests, and páramo vegetation dominated by Espeletia (Kattan and Alvarez-López 1996; Aceituno et al. 2013). Due to its wide altitudinal range, the presence of fertile volcanic soils and a wide variety of water tributaries, it is an ideal environment for the development of agricultural activities, as well as for biodiversity (Rojas-Morales et al. 2011; Rojas-Morales 2012; Rosero-Taramuel et al. 2023). In the study area, we selected several sampling points including remnants of forests (in a state of succession and some fragments of vegetation typical of the Andean zone) located in the interior and periphery of the urban matrix, in the urban area and surrounding of Manizales. These remanants have been catalogued as i) protected areas called "Ecoparks" (Ecoparques in Spanish) (Arango-B et al. 2007), and ii) environmental interest areas, including the Recinto del Pensamiento, and Cerro Sancancio. All areas are located in an elevational range between 1700 and 2500 m. The selected Ecoparks and environmental interest areas are part of urban and peri-urban landscapes (Fig. 1). The urban landscapes are: (1) Jardín Botánico de la Universidad de Caldas (hereafter referred to as Jardín Botánico) (2150 m elevation; area: 7 ha), (2) Bosque Popular El Prado (2030 m; area: 22.7 ha); (3) Cerro Sancancio (1890-2200; area: 74 ha). The peri-urban landscapes included: (4) Los Alcázares-Arenillo (1730-1960 m; located in the southwest of the urban area of Manizales, with an area of 35.7 ha); (5) Los Yarumos (2150 m; located northwest of the city with an approximate area of 35.8 ha); (6) Monteleón (2200 m; located in the northwest of the municipality of Manizales with about 25.9 ha); (7) Recinto del Pensamiento (2250 m; located to the east of the city of Manizales with about 179 ha). No fieldwork was conducted at the Recinto del Pensamiento; however, it was included because herpetological specimens from this site are housed in the collections of the Centro de Museos, Museo de Historia Natural, Universidad de Caldas (MHN-UCa). Amphibian and reptile diversity and threatened category To determine the richness of amphibians and reptiles we conducted field work in the Ecoparks and the environmental interest areas of Manizales during 24 January to 20 April of 2022, and in the first week of November of 2023. In all sampling sites, we used the visual and acoustic encounter sampling method, removing rocks, logs and leaf litter, in addition to checking shrubs and grasslands for amphibians and reptiles in the different microhabitats. Field surveys were carried out between 13:00 and 21:00 h during each sampling day (Veith et al. 2004; Rueda et al. 2006; Aguirre-León 2011), with each site sampled for four consecutive days a two-person team. We identified the vouchers by comparisons with specimens deposited in the Amphibian Collection (MHN-UCa-Am) and Reptile Collection (MHN-UCa-R) of the Centro de Museos, Museo de Historia Natural, Universidad de Caldas. Vouchers were collected under permits granted by the Corporación Autónoma Regional de Caldas (CORPOCALDAS), and the Autoridad Nacional de Licencias Ambientales (ANLA) to the Universidad de Caldas, as stipulated in resolution No. 02497 of December 31, 2018, updated by resolution No. 000026 of January 9, 2024. Besides recorded individuals at the field, we also reviewed 235 additional specimens housed in the MHN-UCa, originally collected in the study area between 1985 and 2024. To complete the information, we included some photographic records with good resolution obtained by Ecoparks and areas of environmental interest staff, and literature information from previous studies in remnant forests of the city of Manizales (i.e., Rojas-Morales and González-Durán 2011; Rojas-Morales 2012; Rojas-Morales et al. 2014; Toro-Restrepo 2023; Ramírez-Chaves et al. 2022). For the taxonomic classification, we followed to Uetz et al. (2025) non-avian Reptiles and Frost (2024) for amphibians. We compiled the threatened category for each species according to the Red List of Threatened Species of the International Union for Conservation of Nature (IUCN 2025). We listed the endemic species following to Uetz et al. (2025) for reptiles and Frost (2024) for amphibians. Taxonomic diversity analysis To calculate the taxonomic diversity of amphibians and reptiles in each Ecopark and the environmental interest areas, we performed alpha and beta diversity analyses using R software (version 4.4.2; R Core Team, 2024). We grouped the species recorded at each site to estimate the local richness (alpha diversity) (Table S1), and general richness by summing all sites (Gamma diversity). The analyses were based on abundance data obtained during fieldwork and were performed separately for amphibians and reptiles. Also, we calculated effective species diversity using the iNEXT package (Hsieh et al. 2016). We calculate Beta diversity to quantify species turnover and nestedness (following Baselga 2010), among the different Ecoparks. The Jaccard index is decomposed into its components: turnover (βJTU) and nestedness (βJNE); total beta (βJAC) resulting of the sum of βJTU and βJNE (Baselga 2010). Additionally, to assess the average beta diversity across all study sites, we estimated multiple beta diversity using the betapart package (Baselga 2012). Exploration of diversity changes and ecological connectivity using Local Climate Zones (LCZ) To explore changes in amphibian and reptile diversity across the Ecoparks and areas of environmental interest, we estimated the species richness per km 2 , the dominancy patterns of species in each area, and the degree of isolation of each site. We evaluated the relationship between site area and two ecological variables: species richness and abundance. Given the small sample size (n = 6) and the potential violation of the normality, we applied a nonparametric Spearman correlation test. This analysis was performed in R software (version 4.4.2) using the “cor.test()” function (R Core Team, 2024). To assess the ecological connectivity between Ecoparks and areas of environmental interest, we used the Local Climate Zone (LCZ) classification scheme (Stewart and Oke 2012; Bechtel et al. 2015). For this, we used the urban climates map of Manizales, developed by Roncancio and Stewart (2022), which classifies the city’s territory according to the LCZ framework. The LCZ classification, originally proposed by Stewart and Oke (2012) allows for the spatial categorization of urban landscapes based on land cover and urban form. For this study, we considered the following LCZ categories: LCZ 2 (Compact midrise), LCZ 3 (Compact lowrise), LCZ 5 (Open midrise), LCZ 6 (Open lowrise), LCZ 9 (Sparsely built), LCZ A (Dense trees), LCZ B (Scattered trees), and LCZ D (Low plants). We particularly focused on LCZ A and B, as these categories are associated with higher vegetative cover and potential for wildlife movement. By overlaying the LCZ classification over the urban matrix shapefile of Manizales, we explored whether Ecoparks are spatially connected or isolated in the urban landscape. This approach allows for more precise identification of potential connectivity corridors or areas requiring restoration to improve biodiversity conservation in urban contexts. We integrated the diversity analyses (alpha and beta) into this spatial framework to evaluate how taxonomic diversity patterns relate to landscape connectivity and LCZ characteristics. We also estimated the number of amphibian and reptiles that can be found in each LCZ observed in Manizales, analysing species richness and beta diversity across the various climate zones. This analysis helps to identify which LCZ types may serve as refugee or barriers for different amphibians and reptile species and provides insights into potential conservation priorities for the urban landscape. Based on this classification, we identified potential connections corridors between each site, prioritizing routes that traverse LCZ A and B categories, and described spatial continuity, highlighting areas where natural cover may be insufficient to support ecological flows. To do this, the shortest linear distances between the study areas were drawn and the different LCZs present in each line were described in detail. This allowed for the calculation of a percentage of the LCZ classification corresponding to the built form and/or natural cover of each drawn line. Additionally, by employing records from the Amphibian and Reptile Collections of the MHN-UCa, we identified the LCZ types that may currently be used by amphibians and reptiles beyond the Ecoparks and designated environmental interest areas (Table S2). This approach integrates landscape ecology principles with urban climatic zoning, providing a spatially explicit framework for understanding how urbanization patterns affect the distribution and conservation potential for amphibians and reptiles in the study area. Results Diversity of amphibians and reptiles and threatened category Our field surveys yielded a total of 291 individuals, belonging to seven amphibian and 10 reptile species (Table S1). We obtained 231 amphibian records through visual and acoustic encounter surveys, while reptile sampling yielded 60 records. Among amphibians, P . thectopternus was the most abundant species with 102 records, distributed across nearly all study areas except in the site 4 (Los Alcázares-Arenillo). Alpha diversity analyses revealed that site 3 (Cerro Sancancio) presented the highest observed richness (6), followed by site 1 (5; Jardín Botánico). Sample completeness (SC) was elevated for most amphibian sites, reaching values of 1 at sites 1, 3, 4 and 5 (Los Yarumos) (Table S2). Site 2 (Bosque Popular el Prado) showed slightly lover completeness (SC = 0.9744), while site 6 had the lowest completeness (SC = 0.8364). In terms of Shannon diversity for amphibians, site 1 showed the highest values (q1 = 4.3285), followed by site 4 (q1= 2.9486), and site 3 (q1 = 2.8346) (Table 2). Simpson index values showed a more equitable distribution in site 1 (q2 = 3.8136), compared to other sites. For reptiles, Pholidobolus marianus was the most abundant species with 23 records found across all sampling areas (Table S1). Alpha diversity analyses showed that site 4 presented the highest values for both Shannon diversity (H’ = 4.0579) and Simpson diversity (D = 3.6119), followed by site 3 (H’ = 3.0678, D = 2.5745). Sites 5 and 6 showed observed richness of three and two species respectively, with variable diversity values (Table 2). Overall, sampling was acceptable to good for reptiles (SC > 0.84). Sites 2 and 6 achieved complete sample completeness (SC = 1) despite low sample sizes, indicating that all present species were captured, though increased sampling effort would be recommended for validation. Site 3 (SC = 0.8485) showed probability of undetected species, suggesting that sampling effort could be improved (Table S2). The review of specimens from the MHN-UCa collections included five species (which were also recorded during our field surveys): Dendropsophus columbianus , Leucostethus aff. fraterdanieli , Pristimantis achatinus, P. thectopternus , and P. paisa . Additionally, the literature review and photographic records added three amphibian species (Table 1). Among these, Nynphargus grandisonae and Centrolene savagei were recorded exclusively through photographic evidence, while Gastrotheca nicefori was documented through photographs and acoustic encounters (Fig. 2). For reptiles, we confirmed 18 reptile species based on the review of specimens and the compilation of information from the literature (Table 1). Photographic records further confirmed the presence of 11 reptile species in the study areas (Fig. 3). Of the total species documented, 16 are restricted to Colombia, and two of them ( Riama columbiana and Lepidoblepharis williams i) are currently classified as Endangered according to the IUCN Red List. Through the combination of all study methodologies, we recorded a total of 30 amphibian and reptile species in the Ecoparks and areas of environmental interest. For amphibians, we identified 10 species belonging to six genera and five families (Table 1). The families with the highest species richness were Strabomantidae with five species, and Centrolenidae with two, while Dendrobatidae, Hemiphractidae, and Hylidae, were represented by a single species (Table 1; Fig. 2). We found differences in species richness among the study sites (Table 1). Sites 1 and 5 showed the highest amphibian richness, with seven and six species, respectively. Some species were documented exclusively in specific sites; for instance, Gastrotheca nicefori and Nymphargus grandisonae , were only recorded in Los Yarumos, while Pristimantis w-nigrum was only recorded in the Jardín Botánico. For reptiles, 20 species belonging to 14 genera and seven families were recorded (Table 1). Anolidae (three species) was the lizard family with the highest number of representatives in the urban and peri-urban areas of Manizales. For snakes, Colubridae was the most diverse family with 10 species (Fig. 3). Similar to amphibians, reptile species richness varied among sites. Of the 20 recorded reptile species, 11 were documented in urban areas and 16 in peri-urban areas. Notably, the endemic Atractus manizalesensis , were recorded only in the Jardín Botánico, while seven snake species were recorded only in peri-urban landscapes (Table 1). Diversity changes and ecological connectivity using Local Climate Zones (LCZ) Most reptiles recorded in our study were observed within forested areas (LCZ A, B). However, species within the genera Atractus , Anolis and Pholidobolus are commonly observed in highly anthropized zones near the study areas (LCZ 2, 3 and 9) (Table 3). In particular, the cases of Atractus biseriatus , A. lehmanni , and Pholidobolus marianus , which were documented in multiple urban locations corresponding to compact midrise zones (LCZ 2), compact lowrise zones (LCZ 3), and sparsely built areas (LCZ 9). The analysis of species richness in relation to Ecopark size showed a moderate positive correlation (Spearman’s r = 0.44, p-value = 0.38, Fig. 4A), indicating a tendency for larger areas to host greater amphibian and reptile diversity. A similar pattern was observed for total abundance (Spearman’s r = 0.60, p-value = 0.24, Fig. 4B), where larger areas generally hosted greater numbers of individuals. Although neither correlation was statistically significant, both Spearman’s r values suggest a potential positive association between site area and amphibian and reptile diversity, consistent with expectations from island biogeography theory and urban habitat fragmentation patterns. However, the case of the Jardín Botánico stands out: despite being the smallest area evaluated (0.07 km 2 ), it presented the highest species density with 128.57 species/km 2 (1.28 species/ha) (Table S3), hosting nine different species with a relatively equal distribution of dominance between Pristimantis paisa (26.67%), Leucostethus aff. fraterdanieli , and Pholidobolus marianus (both with 15.56%). Alpha and beta diversity results reveal patterns directly related to the spatial configuration and connectivity of the assessed sites. The high differentiation of species communities between sites (βJAC = 0.8548 for reptiles, βJAC = 0.6274 for amphibians) indicates that 84% for reptiles and 63% for amphibians (Table 4), of total diversity is due to species turnover between locations. This pattern of high turnover suggests that each site maintains relatively unique assemblages, possibly due to the barriers imposed by the surrounding urban matrix. The dominance pattern among sites revealed that Pristimantis thectopternus was the most abundant species in four of the six sites locations evaluated (sites 2, 3, 5 and 6), with percentages ranging from 56.41% to 69.57% (Table S1, S3), contrasting with the greater evenness observed at site 1 (Simpson’s index D = 3.8136 for amphibians). This variation in the dominance structure between sites is related to the different connectivity conditions: site 1, which presents greater Shannon diversity (H' = 4.3285) and evenness, could benefit from better connectivity conditions or greater habitat heterogeneity. This dominance may be related to its ability to adapt to different habitat conditions within urban forest fragments. Species of ground snakes ( Atractus ) showed a marked presence in the urban environment surrounding the Ecoparks, with records distributed mainly in compact lowrise and midrise areas (LCZ 2 and LCZ 3) (Table 3). The low nestedness component (βJNE = 0.1120 for reptiles, βJNE = 0.2032 for amphibians) compared to species turnover indicates that species loss does not follow a predictable pattern based on fragment size (Table 4), but is more closely related to the specific characteristics of each site and its degree of isolation. The turnover component was considerably higher for reptiles (βJTU = 0.7429) than for amphibians (βJTU = 0.4242), suggesting that reptiles are more sensitive to effects of fragmentation and isolation between Ecoparks and areas of environmental interest. The analysis of potential ecological corridors between the sites, based on the LCZ classification, showed significant fragmentation of the urban landscape (Table 5). The most favorable corridor in terms of natural cover was identified between Cerro Sancancio (site 3), Bosque Popular El Prado (site 2), and Los Yarumos (site 5; corridor 15, Fig. 1, Table 5), with 95.99% of its linear distance (5,107.7 m) corresponding to natural cover categories (LCZ A, B, D, and F). However, this corridor has a total length of 5,321 m, which represents a considerable distance for amphibian and reptile species with limited dispersal capabilities. Similarly, the corridor between Los Yarumos and Monteleón (site 6; corridor 8, Table 5, Fig. 1) has a high percentage of natural cover (92.03%), but its linear distance of 3,254 m also poses a significant barrier to amphibian and reptile mobility. Although we identified potential corridors with a high proportion of natural areas (LCZ A and B) (Table 5), the extension of these corridors and the predominance of urban matrices (LCZ 2, 3, 5, and 6) in critical sections severely limit functional connectivity for both amphibians and reptiles (Fig. 1), reflecting the high differentiation of assemblages, mainly among reptiles (βJTU = 0.7429) (Table 4). This suggests that each site acts as an island with limited species exchange, explaining both the high observed beta diversity and the site-specific dominance patterns. Shorter connections between Ecoparks, such as those linking the Jardín Botánico with Cerro Sancancio (283–391 m), have significant percentages of built-up areas (between 40.48% and 84.64%), compromising their functionality as effective corridors (Table 5). These shorter corridors could function as transit zones for some species, particularly reptiles such as Atractus spp. and P. marianus, which have demonstrated some tolerance to urbanized environments. Discussion A total of 10 amphibians and 20 reptiles were documented in the study area, representing 28% of the amphibian and 55% of the reptile species for the south-central region of Caldas (Rojas-Morales et al. 2014 ); highlighting the role of the different local landscapes in the maintenance of different species. However, the species richness of amphibians and reptiles found in the study area is low in relation to that found in nearby well-preserved rural areas such as Parque Nacional Natural Selva de Florencia, Reserva Natural Privada Riomanso and Reserva Forestal Protectora Bosques de la Central Hidroeléctrica de Caldas (Acosta-Galvis et al. 2006 ; Acosta-Galvis 2009 ; Duarte-Marín et al. 2018 ; Gómez-Salazar et al. 2017 ). This pattern is consistent with global trends showing reduced biodiversity in urban areas compared to natural environments (McKinney 2006 ; Elmqvist et al. 2013 ). Nevertheless, some studies have documented contrasting patterns where urban areas can support higher species richness than expected (Hamer and McDonnell 2008 , 2010 ; Banville and Bateman 2012 ). Positive outcomes are often associated with strategic urban planning that prioritizes habitat quality, vegetation structural complexity, and connectivity between green spaces, demonstrating that urbanization effects on amphibians and reptiles are not universally negative and can be mitigated through appropriate management practices (Hamer and McDonnell 2008 , 2010 ; Banville and Bateman 2012 ). The presence of 16 endemic species (53,3% of total recorded species) underscores the conservation value of urban green areas in the Colombian Andes. This level of endemism is particularly noteworthy given the highly modified nature of the urban landscape and reinforces the critical importance of maintaining these forest fragments for regional biodiversity conservation (Myers et al. 2000 ; Hazzi et al. 2018 ). Among our records, Riama columbiana and Lepidoblepharis williams i stand out as species of particular conservation concern, categorized as Endangered (EN) according to the IUCN ( 2025 ). Both species were observed in the Jardín Botánico, Los Yarumos and Monteleón Ecoparks, representing one of the few documented populations in adjacent urban environments. The consistent presence of both species at these sites presents a significant opportunity for conservation action and ecological research. We recommend establishing long-term monitoring programs to asses population dynamics, habitat requirements, and potential threats to this species within urban contexts. Additionally, the presence of other endemic species such as Atractus manizalesensis and Pristimantis paisa further emphasizes the conservation priority of these urban forest remnants. The relative scarcity of threatened species in our inventory may reflect the resilience of urban-tolerant species or possible local extinctions of more sensitive taxa (Pereyra et al. 2021 ). This pattern warrants further investigation through comparison with historical records and assessment of species that may have been lost from the urban landscape over time. Our results revealed a complex relationship between habitat area and species richness, with a moderate positive correlation suggesting that area alone is not the sole determinant of biodiversity in urban environments. The exceptional case of the Jardín Botánico, which despite being the smallest area exhibited the highest species density, indicates that habitat quality, microhabitat heterogeneity, and connectivity may be more critical factors than patch size (Keinath et al. 2023 ; Marsh et al. 2024 ). This finding partially contradicts our initial hypothesis, suggesting that additional factors such as microhabitat heterogeneity, conservation status, proximity to areas like Cerro Sancancio, and the presence of water bodies may be more important determinants than area size for maintaining viable amphibian and reptile populations in urban environments. The presence of water bodies, varied topography, and maintained vegetation structure in the Jardín Botánico likely contribute to its high species density (Callaghan et al. 2019 ). These results align with studies on other urban environments showing that small but well-managed green spaces can support disproportionately high biodiversity (Lepczyk et al. 2017 ; Callaghan et al. 2019 ); and urban planning should prioritize habitat quality enhancement and microhabitat diversity rather than focusing solely on increasing that size of green spaces (Marsh et al. 2024 ). We also found a clear pattern of differential urban tolerance between amphibians and reptiles. Most records in highly urbanized areas (LCZ 2, 3 and 9) correspond to reptiles, particularly species of the genera Atractus , Anolis , and Pholidobolus marianus. Urban records outside of Ecoparks correspond mainly to reptiles, especially ground snakes ( Atractus ) and stick lizards like Pholidobolus marianus (Table 3 ), suggesting that reptiles may be more adaptable to urban environments compared to amphibians, likely due to their reduced dependence on specific humidity requirements and water bodies for reproduction (Hamer and McDonnell 2008 ). The concentration of urban records between the Jardín Botánico, Cerro Sancancio, and Los Yarumos (Fig. 1 ) indicates that these areas, despite the intervening urban matrix, may function as a fragmented ecological complex for some species with greater tolerance to disturbance. The dominance of the Northern Cordilleras Robber Frog ( Pristimantis thectopternus ) across multiple sites indicates that direct-developing species with broader ecological tolerances are better suited to persist in fragmented urban landscapes (Hamer and McDonnell 2008 ). This aligns with global patterns showing that species with specialized habitat requirements or complex life cycles are disproportionately affected by urbanization (McKinney 2006 ). The LCZ analysis revealed severe fragmentation of the urban landscape, with most potential corridors between Ecoparks and environmental interest areas, exceeding dispersal distances for amphibians and reptiles (Smith and Green 2005 ). Even the most favourable corridor identified (between Cerro Sancancio, Bosque Popular el Prado, and Los Yarumos) spans over 5 km, representing a significant barrier for species with limited mobility. The concentration of urban records in areas between Jardín Botánico, Cerro Sancancio, and Los Yarumos suggest that these sites may function as loosely connected ecological network for disturbance-tolerant species. However, the intervening urban matrix (dominated by LCZ 2 and 3) likely prevents movement for most amphibian species and limits connectivity for all but the most urban-adapted reptiles (Marsh et al. 2024 ). Despite the presence of scattered green areas in the urban matrix of Manizales, the ecological connectivity for amphibians and reptiles is severely compromised by habitat fragmentation. Targeted management interventions could improve this situation. Conservation strategies should focus on improving the permeability of shorter corridors, particularly those connecting the Jardín Botánico with other sites, where tolerant species such as ground snakes ( Atractus spp.) and the stick lizard, Pholidobolus. marianus could facilitate gene flow between fragmented populations. Species of Atractus might exhibit adaptability to urbanized environments (Rojas-Morales 2012 ), with multiple species documented in compact residential areas (LCZ 2 and 3). Urban tolerance may relate to their fossorial habitats, small size, allowing them to exploit urban microhabitats unavailable to larger or more specialized species (Lettoof et al. 2023 ). Similarly, P. marianus showed consistent presence across all study sites and urban areas, suggesting high ecological flexibility within this genus. Finally, the moderate positive correlation between area size and species richness (r = 0.44) and total abundance (r = 0.60), although not statistically significant, reinforces the importance of maintaining and expanding existing urban green areas while improving their functional connectivity. The substantial representation of species of amphibians and reptiles within the urban environments evaluated underscores both the conservation value of urban green spaces and the potential for well-planned cities to server as refugia for regional biodiversity in highly modified landscapes (Lepczyk et al. 2017 ). Conclusions We highlight several critical conservation priorities: (1) protection and enhancement of existing Ecoparks and environmental interest areas, particularly the Cerro Sancancio (site 3), Jardín Botánico (site 1) and Los Alcázares-Arenillo (site 4), which harbours the highest amphibians and reptiles species; (2) implementation of corridor restoration projects to improve connectivity between forest fragments, with special attention to reducing the permeability barriers in shorter connections; (3) establishment of monitoring programs for endemic and threatened species; and (4) integration of biodiversity considerations into urban planning processes using LCZ mapping as a tool for identifying priority areas for conservation action. Severe fragmentation revealed by our connectivity analysis, coupled with the high betta diversity (driven primarily by species turnover), indicates that current green infrastructure is insufficient to maintain long-term viable populations for most species. Strategic habitat restoration focusing on corridors with high natural cover percentages (> 90%) but excessive length should be prioritized to enhance functional connectivity across the urban landscape. The differential responses observed between amphibians and reptiles, with reptiles showing higher turnover and greater urban tolerance, should inform targeted conservation strategies that consider that specific ecological requirements and dispersal limitations of each taxonomic group. Declarations Acknowledgments We appreciate the support provided by the members of the Natural History Laboratory during the different sampling days. JJHO, LSCM and HFAM thank The Mohamed bin Zayed Species Conservation Fund for the grant to carry out the project "Current threats and conservation status of three species of Harlequin toad (Anura, Bufonidae, Atelopus ) in the Andes of Colombia" (Project N° 222529372) that during its development has contributed to the generation of knowledge about the fauna of amphibians and reptiles in several areas of the coffee region, including the city of Manizales. We thank the Interadministrative Agreement N° 2110200953 signed between the Alcaldía de Manizales, CORPOCALDAS and the Universidad de Caldas, for the planning and execution of the Expedición Manizales + Biodiversa carried out in the urban and peri-urban forests of Manizales, Caldas, Colombia. Author contributions EACG: Conceptualization, investigation, data curation, formal analysis, manuscript writing, revision and editing. JJHO: Conceptualization, data curation, manuscript writing, revision and editing. 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Nat Commun 10(1):2844. https://doi.org/10.1038/s41467-019-10775-z Tables Table 1 Amphibians and reptiles recorded Ecoparks and areas of environmental interest of the city of Manizales, Colombia. Sites: (1) Jardín Botánico, (2) Bosque Popular El Prado, (3) El Cerro Sancancio, (4) Los Alcázares-Arenillo, (5) Los Yarumos, (6) Monteleón, (7) Recinto del Pensamiento. Its conservation status is described by the IUCN: Least Concern (LC); Data Deficient (DD); Endangered (EN). Voucher specimens are housed at the MNH-UCa Amphibians (Am) and Reptiles (R) collections Taxon Localities Threat category (IUCN) Endemic Vouchers or type of record Amphibia, Anura Centrolenidae Nymphargus grandisonae (Cochran & Goin, 1970) 5 LC Photographs Centrolene savagei (Ruiz & Lynch, 1991) 4, 5, 6 LC x Photographs Dendrobatidae Leucostethus aff . fraterdanieli (Silverstone, 1971) 1, 2, 4, 5, 6 LC x Am-416-418, 447-452, 832-835, visual encounter, Rojas-Morales et al. (2021) Hemiphractidae Gastrotheca nicefori Gaige, 1933 5 LC Photographs, acoustic encounter Hylidae Dendropsophus columbianus (Boettger, 1892) 1, 4 LC x Am-186-191, 347-348, 350, visual encounter, Blandón-Marín (2006) Strabomantidae Pristimantis achatinus (Boulenger, 1898) 1, 2, 3, 4, 5 LC Am-349, 353, 1134, 1876, visual encounter, Escobar-Vargas et al. (2016) Pristimantis erythropleura (Boulenger, 1896) 3 LC x Am-1779, Visual encounter Pristimantis paisa (Lynch & Ardila-Robayo, 1999) 1, 2, 3, 4, 5, 6 LC x Am-827-830, visual encounter Pristimantis thectopternus (Lynch, 1975) 1, 2, 3, 5, 6, 7 LC x Am-706, 1871, visual encounter, Pristimantis w-nigrum (Boettger, 1892) 1 LC Toro-Restrepo 2023 Reptilia, Squamata, Sauria Gekkonidae Lepidoblepharis duolepis Ayala & Castro, 1983 4 LC x R-205, 341, 532-535, visual encounter Lepidoblepharis williamsi Ayala & Serna , 1986 1 EN x R-210-211, 341, 975-977, visual encounter Gymnophthalmidae Pholidobolus marianus (O'Shaughnessy, 1879) 1, 2, 4, 5, 6 LC R-531, 1039, visual encounter, photographs Riama columbiana (Andersson, 1914) 5, 6 EN x R-920, Visual encounter, photographs Anolidae Anolis antonii (Boulenger, 1908) 1, 4, 5 LC x R-680-683, visual encounter Anolis quimbaya (Moreno-Arias, Méndez-Galeano, Beltrán & Vargas-Ramírez, 2023) 2, 5, 7 LC x R-487, 801, Photographs Anolis ventrimaculatus Boulenger, 1911 1, 3 LC R-1190, Visual encounter Reptilia, Serpentes Colubridae Atractus biseriatus Prado, 1941 1, 5 DD x R-530, visual encounter, Photographs Atractus lehmanni Boettger, 1898 1, 5 3 DD x R-1026, 1092, 11110, 1139, 1191 visual encounter, Photographs Atractus manizalesensis Prado, 1940 1 LC x R-209, visual encounter Chironius monticola Roze, 1952 4 LC R-186 Clelia equatoriana (Amaral, 1924) 1, 4 LC R-1022, Rojas-Morales (2012) Dipsas sanctijoannis (Boulenger, 1911) 4, 5 LC x Photographs, Rojas-Morales & Escobar-Lasso (2010) Erythrolamprus bizona Jan, 1863 4 LC R-072, 185 Erythrolamprus epinephelus (Cope, 1862) 1, 5 LC R-290, 334, 337; photographs, Rojas-Morales (2012), visual encounter Imantodes cenchoa (Linnaeus, 1758) 6 LC R-047, photographs, Rojas-Morales et al. (2014) Lampropeltis micropholis (Cope, 1860) 5 LC Photographs, Rojas-Morales (2012) Elapidae Micrurus mipartitus (Duméril, Bibron & Duméril, 1854) 4 LC R-104 Viperidae Bothriechis schlegelii (Berthold, 1846) 4, 5 LC Visual encounter, photographs Leptotyphlopidae Trilepida joshuai (Dunn, 1944) 1, 5 LC x R-162, 468, 1249, photographs, Rojas-Morales (2012), Rojas-Morales & Gonzáles-Dúran (2011) Table 2 Alpha diversity of amphibians and reptiles at six localities of Manizales, Central Andes of Colombia: (1) Jardín Botánico, (2) Bosque Popular El Prado, (3) Cerro Sancancio, (4) Los Alcázares-Arenillo, (5) Los Yarumos, (6) Monteleón. Observed values for three diversity indices are presented Amphibians Reptiles Site Index Observed Observed 1 Species richness 5.0000 4.0000 Shannon diversity 4.3285 2.9543 Simpson diversity 3.8136 2.5862 2 Species richness 4.0000 1.0000 Shannon diversity 2.5335 1.0000 Simpson diversity 2.1627 1.0000 3 Species richness 6.0000 4.0000 Shannon diversity 2.8346 3.0678 Simpson diversity 1.9042 2.5745 4 Species richness 4.0000 5.0000 Shannon diversity 2.9486 4.0579 Simpson diversity 2.4994 3.6119 5 Species richness 4.0000 3.0000 Shannon diversity 2.0042 2.7495 Simpson diversity 1.5238 2.5714 6 Species richness 3.0000 2.0000 Shannon diversity 1.8946 2.0000 Simpson diversity 1.5152 2.0000 Table 3 Amphibian and reptile species are recorded in urban areas or surrounding Ecoparks or areas of environmental interest in Manizales, along with their respective Local Climate Zone (LCZ). LCZ 2: Compact midrise; LCZ 3: Compact lowrise; LCZ 5: Open midrise; LCZ 6: Open lowrise; LCZ 9: Sparsely built: LCZ A: Dense trees; LCZ B; Scattered trees; LCZ D: Low plants. Records taken from the Amphibian and Reptile Collection of the MHN-UCa Taxon LCZ Amphibia Anura Bufonidae Rhinella horribilis (Wiegmann, 1833) LCZ 6 Reptilia Squamata Sauria Gekkonidae Hemidactylus garnotii Duméril & Bibron, 1836 LCZ 3, LCZ 5 Gymnophthalmidae Pholidobolus marianus (Ruthven, 1921) LCZ 2, LCZ 3, LCZ 5, LCZ 9 Anolidae Anolis antonii (Boulenger, 1908) LCZ 3 Serpentes Colubridae Atractus biseriatus Prado, 1941 LCZ 2, LCZ 3, LCZ 6 Atractus lehmanni Boettger, 1898 LCZ 3, LCZ 9, LCZ B Atractus manizalesensis Prado, 1940 LCZ 2, LCZ 3, LCZ 9 Chironius monticola Roze, 1952 LCZ 6 Clelia equatoriana (Amaral, 1924) LCZ 3, LCZ B Dipsas sanctijoannis (Boulenger, 1911) LCZ A, LCZ D Erythrolamprus bizona Jan, 1863 LCZ 3, LCZ 9 Erythrolamprus epinephelus (Cope, 1862) LCZ 2, LCZ 3 Lampropeltis micropholis (Cope, 1860) LCZ A Elapidae Micrurus mipartitus (Duméril, Bibron & Duméril, 1854) LCZ D Leptotyphlopidae Trilepida joshuai (Dunn, 1944) LCZ 3 Table 4 Components of beta diversity for amphibians and reptiles among sampling sites within the municipality of Manizales, Central Andes of Colombia Taxon Total beta diversity (βJAC) Turnover (βJTU) Nestedness (βJNE) Amphibians 0.6274 0.4242 0.2032 Reptiles 0.8548 0.7429 0.1120 Table 5 Characterization of potential corridors between Ecoparks and areas of environmental interest in Manizales according to their LCZ composition. LCZ 2: Compact midrise; LCZ 3: Compact lowrise; LCZ 5: Open midrise; LCZ 6: Open lowrise; LCZ 8: Large lowrise; LCZ 9: Sparsely built: LCZ A: Dense trees; LCZ B; Scattered trees; LCZ D: Low plants; LCZ F: Bare soil or sand ID Potential corridors Total linear distance (m) LCZ Built form Built distance (m) Built percentage LCZ Land Cover Cover distance (m) Cover percentage 1 Jardín Botánico - Cerro Sancancio 283 2, 3, 9 114.57 40.48% A, B, D 168.43 59.52% 2 Jardín Botánico - Cerro Sancancio 319 2, 3 270.00 84.64% A 49.00 15.36% 3 Jardín Botánico - Cerro Sancancio 391 2, 3, 5 259.90 66.47% A, B, D 131.10 33.53% 4 Yarumos - Monteleón 556 2, 3, 5, 6, 8, 9 465.80 83.78% B, D 90.20 16.22% 5 Yarumos - Monteleón 580 2, 3, 5, 6, 8, 9 504.10 86.91% B, D 75.90 13.09% 6 Yarumos - Monteleón 1854 3, 9 199.30 10.75% A, B, D 1654.70 89.25% 7 Yarumos - Monteleón 652 2, 3, 6, 9 185.10 28.39% A, B, D 466.90 71.61% 8 Yarumos - Monteleón 3254 8, 9 259.40 7.97% A, B, D, F 2994.60 92.03% 9 Jardín Botánico - Yarumos 1137 2, 3, 6 908.00 79.86% A, B, F 229.00 20.14% 10 Jardín Botánico - Yarumos 1325 2, 3, 6 1018.50 76.87% A, B, F 306.50 23.13% 11 Jardín Botánico - Monteleón 1633 2, 3, 6, 9 1368.70 83.82% A, B 264.30 16.18% 12 Jardín Botánico - Monteleón 1730 2, 3, 6 1467.80 84.84% A, B, F 262.20 15.16% 13 Jardín Botánico - Alcázares 3088 2, 3, 6, 8 2277.50 73.75% A, B, D 810.50 26.25% 14 Alcázares - Cerro Sancancio 3921 2, 3, 5, 6 2423.00 61.80% A, B, D, F 1498.00 38.20% 15 Cerro Sancancio - Bosque Popular - Yarumos 5321 3, 6, 8 213.30 4.01% A, B, D, F 5107.70 95.99% 16 Alcázares - Monteleón 3180 2, 3, 5, 8 1808.50 56.87% A, B, D 1371.50 43.13% Additional Declarations No competing interests reported. Supplementary Files Supplementarymaterials.docx Cite Share Download PDF Status: Under Review Version 1 posted Editorial decision: Revision requested 20 Nov, 2025 Reviews received at journal 18 Nov, 2025 Reviews received at journal 14 Nov, 2025 Reviews received at journal 09 Nov, 2025 Reviewers agreed at journal 01 Oct, 2025 Reviewers agreed at journal 01 Oct, 2025 Reviews received at journal 29 Sep, 2025 Reviewers agreed at journal 29 Sep, 2025 Reviewers agreed at journal 03 Sep, 2025 Reviewers invited by journal 02 Sep, 2025 Editor assigned by journal 27 Aug, 2025 Submission checks completed at journal 27 Aug, 2025 First submitted to journal 26 Aug, 2025 You are reading this latest preprint version Research Square lets you share your work early, gain feedback from the community, and start making changes to your manuscript prior to peer review in a journal. As a division of Research Square Company, we’re committed to making research communication faster, fairer, and more useful. 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Also discoverable on Platform About Our Team In Review Editorial Policies Advisory Board Help Center Resources Author Services Accessibility API Access RSS feed Manage Cookie Preferences © Research Square 2026 | ISSN 2693-5015 (online) Privacy Policy Terms of Service Do Not Sell My Personal Information {"props":{"pageProps":{"initialData":{"identity":"rs-7464640","acceptedTermsAndConditions":true,"allowDirectSubmit":false,"archivedVersions":[],"articleType":"Research Article","associatedPublications":[],"authors":[{"id":510938070,"identity":"0dfe5bed-e7b7-4cc8-bd1c-fdcc00bae613","order_by":0,"name":"Erika Alejandra Cardona-Galvis","email":"data:image/png;base64,iVBORw0KGgoAAAANSUhEUgAAAZAAAAAyAQMAAABI0h/eAAAABlBMVEX///8AAABVwtN+AAAACXBIWXMAAA7EAAAOxAGVKw4bAAABBUlEQVRIiWNgGAWjYLACHjDJ3MCQwGADZDA2HiBSCyNISxqYQYIWBobDYCZeLfzsh599eFNxR17e/WCbxIM/5+3Wth8G2lJjE41Li2RPmvHMOWeeGW48k9gmkdh2O3nbmUSglmNpuQ04tBjcYDBm5m07zLixIbHZILHhdrLZAaAWxobDOLXY32D/DNJiv7H/YbNBwp9zyWbnH+LXYiDBA7Ylcb5EYuODBLYDdmY3CNgicSanmHHOmcPJGyQeNj5IbEtOMLsBtCUBj1/4249vZnhTcdh2fn/ygYM//tjZm51Pf/jgQ40NTi0IFx6A0IlglQmElIOAPNRQe2IUj4JRMApGwcgCAMHHaeHu2soSAAAAAElFTkSuQmCC","orcid":"","institution":"University of Caldas","correspondingAuthor":true,"prefix":"","firstName":"Erika","middleName":"Alejandra","lastName":"Cardona-Galvis","suffix":""},{"id":510938074,"identity":"54f290d6-d52e-4f59-a0fd-4eb6a9aac66f","order_by":1,"name":"Jose J. Henao-Osorio","email":"","orcid":"","institution":"University of Caldas","correspondingAuthor":false,"prefix":"","firstName":"Jose","middleName":"J.","lastName":"Henao-Osorio","suffix":""},{"id":510938075,"identity":"60023be2-d468-48ac-b721-7b598b1151ce","order_by":2,"name":"L. Santiago Caicedo-Martínez","email":"","orcid":"","institution":"University of Caldas","correspondingAuthor":false,"prefix":"","firstName":"L.","middleName":"Santiago","lastName":"Caicedo-Martínez","suffix":""},{"id":510938078,"identity":"e1e8f358-2bc6-4e36-a796-55b86424148e","order_by":3,"name":"Héctor F. Árias-Monsalve","email":"","orcid":"","institution":"University of Caldas","correspondingAuthor":false,"prefix":"","firstName":"Héctor","middleName":"F.","lastName":"Árias-Monsalve","suffix":""},{"id":510938080,"identity":"8cc2f51c-7014-4fef-8d93-1c527bc0adcb","order_by":4,"name":"Julián A. Rojas-Morales","email":"","orcid":"","institution":"University of Caldas","correspondingAuthor":false,"prefix":"","firstName":"Julián","middleName":"A.","lastName":"Rojas-Morales","suffix":""},{"id":510938083,"identity":"2f008d02-a8da-41cc-b00e-8d32b5ad6686","order_by":5,"name":"Héctor E. Ramírez-Chaves","email":"","orcid":"","institution":"University of Caldas","correspondingAuthor":false,"prefix":"","firstName":"Héctor","middleName":"E.","lastName":"Ramírez-Chaves","suffix":""}],"badges":[],"createdAt":"2025-08-26 15:53:17","currentVersionCode":1,"declarations":"","doi":"10.21203/rs.3.rs-7464640/v1","doiUrl":"https://doi.org/10.21203/rs.3.rs-7464640/v1","draftVersion":[],"editorialEvents":[],"editorialNote":"","failedWorkflow":false,"files":[{"id":90906721,"identity":"7cf4a90b-1262-4717-91ed-4424b15c218f","added_by":"auto","created_at":"2025-09-09 13:12:05","extension":"png","order_by":1,"title":"Figure 1","display":"","copyAsset":false,"role":"figure","size":933418,"visible":true,"origin":"","legend":"\u003cp\u003eConnectivity of Ecoparks and areas of environmental interest through Local Climate Zones (LCZ) in urban and peri-urban landscapes of Manizales, Caldas, Colombia. Study sites: (1) Jardín Botánico, (2) Bosque Popular El Prado, (3) Cerro Sancancio, (4) Los Alcázares-Arenillo, (5) Los Yarumos, (6) Monteleón, and (7) Recinto del Pensamiento. LCZ classification layer based on Roncancio and Stewart (2022)\u003c/p\u003e","description":"","filename":"floatimage1.png","url":"https://assets-eu.researchsquare.com/files/rs-7464640/v1/db7d1d6db04311d2fc8d612c.png"},{"id":90908784,"identity":"f23ecf04-69dd-413b-9b0f-1d7690c7be07","added_by":"auto","created_at":"2025-09-09 13:28:05","extension":"jpeg","order_by":2,"title":"Figure 2","display":"","copyAsset":false,"role":"figure","size":759981,"visible":true,"origin":"","legend":"\u003cp\u003ePhotographic records of some amphibian species found in the municipality of Manizales, Central Andes of Colombia. a. \u003cem\u003eCentrolene savagei\u003c/em\u003e; b. \u003cem\u003eNymphargus grandisonae\u003c/em\u003e; c. \u003cem\u003ePristimantis achatinus\u003c/em\u003e; d. \u003cem\u003ePristimantis erythropleura\u003c/em\u003e; e. \u003cem\u003ePristimantis paisa\u003c/em\u003e; f. \u003cem\u003ePristimantis thectopternus\u003c/em\u003e; g. \u003cem\u003eLeucostethus\u003c/em\u003e aff. \u003cem\u003efraterdanieli\u003c/em\u003e; h. \u003cem\u003eGastrotheca nicefori\u003c/em\u003e; i. \u003cem\u003eDendropsophus columbianus\u003c/em\u003e. Photographs by Héctor F. Árias-Monsalve, Julián A. Rojas-Morales, and Jose. J. Henao-Osorio\u003c/p\u003e","description":"","filename":"floatimage2.jpeg","url":"https://assets-eu.researchsquare.com/files/rs-7464640/v1/528de73d231d90b2ac17cd5c.jpeg"},{"id":90905345,"identity":"3ece3a8f-1660-4052-9207-bb1b07cdb64e","added_by":"auto","created_at":"2025-09-09 13:04:05","extension":"jpeg","order_by":3,"title":"Figure 3","display":"","copyAsset":false,"role":"figure","size":682703,"visible":true,"origin":"","legend":"\u003cp\u003ePhotographic records of some reptile species found in the municipality of Manizales, Central Andes of Colombia. a. \u003cem\u003eAnolis antonii\u003c/em\u003e; b. \u003cem\u003eAnolis quimbaya\u003c/em\u003e; c. \u003cem\u003eLepidoblepharis duolepis\u003c/em\u003e; d. \u003cem\u003ePholidobolus marianus\u003c/em\u003e; e. \u003cem\u003eRiama columbiana\u003c/em\u003e; f. \u003cem\u003eAtractus lehmanni\u003c/em\u003e; g. \u003cem\u003eErythrolamprus epinephelus\u003c/em\u003e; h. \u003cem\u003eLampropeltis micropholis\u003c/em\u003e; i. \u003cem\u003eBothriechis schelegelii.\u003c/em\u003e Photographs by Héctor F. Árias-Monsalve and Jose. J. Henao-Osorio\u003c/p\u003e","description":"","filename":"floatimage3.jpeg","url":"https://assets-eu.researchsquare.com/files/rs-7464640/v1/206f169d569955b728304076.jpeg"},{"id":90905340,"identity":"32fb62e9-59b1-43fc-843e-c3c807004477","added_by":"auto","created_at":"2025-09-09 13:04:05","extension":"png","order_by":4,"title":"Figure 4","display":"","copyAsset":false,"role":"figure","size":72647,"visible":true,"origin":"","legend":"\u003cp\u003eRelationship between Ecopark area and amphibian and reptile diversity. a. Scatterplot showing the correlation between Ecopark size (km\u003csup\u003e2\u003c/sup\u003e) and species richness (r = 0.44). c. Scatterplot showing the correlation between Ecopark size and total abundance of individuals (r = 0.60). Study sites: (1) Jardín Botánico, (2) Bosque Popular El Prado, (3) Cerro Sancancio, (4) Los Alcázares-Arenillo, (5) Los Yarumos, (6) Monteleón\u003c/p\u003e","description":"","filename":"floatimage4.png","url":"https://assets-eu.researchsquare.com/files/rs-7464640/v1/0f7599a936ceffd8737e4dc0.png"},{"id":90910175,"identity":"8ab3be63-0944-4d97-bfbb-e7c1722398bb","added_by":"auto","created_at":"2025-09-09 13:36:07","extension":"pdf","order_by":0,"title":"","display":"","copyAsset":false,"role":"manuscript-pdf","size":3560131,"visible":true,"origin":"","legend":"","description":"","filename":"manuscript.pdf","url":"https://assets-eu.researchsquare.com/files/rs-7464640/v1/b7f8ee54-bc82-4579-add6-9bddf970e2cf.pdf"},{"id":90907094,"identity":"07c6232d-a92f-498e-8215-3fdad1c76ab4","added_by":"auto","created_at":"2025-09-09 13:20:05","extension":"docx","order_by":0,"title":"","display":"","copyAsset":false,"role":"supplement","size":33357,"visible":true,"origin":"","legend":"","description":"","filename":"Supplementarymaterials.docx","url":"https://assets-eu.researchsquare.com/files/rs-7464640/v1/342b65b509082affb1b18c48.docx"}],"financialInterests":"No competing interests reported.","formattedTitle":"\u003cp\u003eAmphibians and Reptiles Associated With Urban and Peri-urban Landscapes in the Central Andes of Colombia\u003c/p\u003e","fulltext":[{"header":"Introduction","content":"\u003cp\u003eThe exponential growth of the world's human population for more than 100 years has raised the rate of transformation of natural habitats in urban, industrial, or cultivated areas (Ripple et al. \u003cspan citationid=\"CR52\" class=\"CitationRef\"\u003e2017\u003c/span\u003e; Zabel et al. \u003cspan citationid=\"CR72\" class=\"CitationRef\"\u003e2019\u003c/span\u003e; Hughes et al. \u003cspan citationid=\"CR32\" class=\"CitationRef\"\u003e2023\u003c/span\u003e). During the next 30 years, the global human population will reach a number close to 9.7\u0026nbsp;billion people, of which about 68% are likely to settle in metropolitan areas (United Nations \u003cspan citationid=\"CR66\" class=\"CitationRef\"\u003e2022\u003c/span\u003e; LaRota-Aguilera and Marull \u003cspan citationid=\"CR38\" class=\"CitationRef\"\u003e2023\u003c/span\u003e). From 1992 to 2000, around 190,000 km\u003csup\u003e2\u003c/sup\u003e of natural environments were transformed into urban areas, and between 2000 and 2030 an additional 290,000 km\u003csup\u003e2\u003c/sup\u003e it is estimated be transformed at global scale (McDonald et al. \u003cspan citationid=\"CR44\" class=\"CitationRef\"\u003e2020\u003c/span\u003e). Increasing urbanization in natural areas are often associated with a decrease in species diversity (McKinney \u003cspan citationid=\"CR45\" class=\"CitationRef\"\u003e2002\u003c/span\u003e, \u003cspan citationid=\"CR46\" class=\"CitationRef\"\u003e2006\u003c/span\u003e; Santos and Teller\u0026iacute;a \u003cspan citationid=\"CR60\" class=\"CitationRef\"\u003e2006\u003c/span\u003e; Elmqvist et al. \u003cspan citationid=\"CR19\" class=\"CitationRef\"\u003e2013\u003c/span\u003e). However, urban environments may also exhibit greater heterogeneity at smaller spatial scales than rural environments, becoming important habitats for many species (Keinath et al. \u003cspan citationid=\"CR37\" class=\"CitationRef\"\u003e2023\u003c/span\u003e).\u003c/p\u003e\u003cp\u003eIn the Neotropics, the Andes are recognized as one of the world\u0026rsquo;s biodiversity hotspots due to its exceptional species richness and high levels of endemism, making it a global conservation priority (Kattan et al. \u003cspan citationid=\"CR36\" class=\"CitationRef\"\u003e2004\u003c/span\u003e; Antonelli et al. \u003cspan citationid=\"CR5\" class=\"CitationRef\"\u003e2009\u003c/span\u003e; Hazzi et al. \u003cspan citationid=\"CR30\" class=\"CitationRef\"\u003e2018\u003c/span\u003e). In recent years, there has been greater interest in understanding the dynamics that characterize biodiversity in urban environments in this region (Delgado-V and Correa-H 2013; MacGregor-Fors \u003cspan citationid=\"CR42\" class=\"CitationRef\"\u003e2013\u003c/span\u003e; Vanegas-Guerrero et al. \u003cspan citationid=\"CR67\" class=\"CitationRef\"\u003e2016\u003c/span\u003e; Ramalho et al. \u003cspan citationid=\"CR49\" class=\"CitationRef\"\u003e2018\u003c/span\u003e; Demart\u0026iacute;n et al. \u003cspan citationid=\"CR17\" class=\"CitationRef\"\u003e2024\u003c/span\u003e). However, for the Andes there are still large information gaps that prevent a more precise understanding of which species may or may not persist in highly anthropized environments (Vanegas-Guerrero et al. \u003cspan citationid=\"CR67\" class=\"CitationRef\"\u003e2016\u003c/span\u003e). To fill these information gaps and better understand the spatial dynamics and ecological connectivity of urban environments, the Local Climate Zones (LCZ) classification (Stewart and Oke \u003cspan citationid=\"CR62\" class=\"CitationRef\"\u003e2012\u003c/span\u003e; Bechtel et al. \u003cspan citationid=\"CR12\" class=\"CitationRef\"\u003e2015\u003c/span\u003e) can be integrated along with the information of the diversity of species. LCZ\u0026rsquo;s allow distinguishing between dense urban zones, open residential areas, artificial vegetation covers, and natural forested zones, facilitating the evaluation of potential ecological corridors and barriers for biodiversity (Han et al. \u003cspan citationid=\"CR29\" class=\"CitationRef\"\u003e2024\u003c/span\u003e).\u003c/p\u003e\u003cp\u003eThe Andean region of Colombia, part of the Northern Andes (Josse et al. \u003cspan citationid=\"CR34\" class=\"CitationRef\"\u003e2009\u003c/span\u003e), retains less than 15% of its original forest cover, primarily due to the expansion of the agricultural frontier and the grow of major population centers (Gentry \u003cspan citationid=\"CR23\" class=\"CitationRef\"\u003e1993\u003c/span\u003e; Etter and Wyngaarden \u003cspan citationid=\"CR21\" class=\"CitationRef\"\u003e2000\u003c/span\u003e; Armenteras et al. \u003cspan citationid=\"CR7\" class=\"CitationRef\"\u003e2003\u003c/span\u003e, \u003cspan citationid=\"CR8\" class=\"CitationRef\"\u003e2011\u003c/span\u003e). Despite this, the Northern Andes is characterized by high biological diversity, and a high number of endemism (Kattan et al. \u003cspan citationid=\"CR36\" class=\"CitationRef\"\u003e2004\u003c/span\u003e), being considered a key priority area for biodiversity conservation (Myers et al. \u003cspan citationid=\"CR47\" class=\"CitationRef\"\u003e2000\u003c/span\u003e; Josse et al. \u003cspan citationid=\"CR34\" class=\"CitationRef\"\u003e2009\u003c/span\u003e; Tognelli et al. \u003cspan citationid=\"CR63\" class=\"CitationRef\"\u003e2019\u003c/span\u003e).\u003c/p\u003e\u003cp\u003eWithin the Northern Andes, the municipality of Manizales (571.8 km\u003csup\u003e2\u003c/sup\u003e, \u0026gt;434,403 inhabitants; (DANE 2018; Giraldo-Ospina and V\u0026aacute;squez-Varela \u003cspan citationid=\"CR25\" class=\"CitationRef\"\u003e2021\u003c/span\u003e), is an intermediate-sized city located in the Central Cordillera of Colombia, in the Coffee Growing Region. Its rugged terrain results in fragmented urban development and reduced mountain connectivity (Giraldo-Ospina and V\u0026aacute;squez-Varela \u003cspan citationid=\"CR24\" class=\"CitationRef\"\u003e2020\u003c/span\u003e). In Manizales, sub-Andean Forest remnants have been consolidated under the \"Ecopark Network\" and areas of environmental interest, which includes peri-urban forest relicts and other green areas within or near the city (Rojas-Morales \u003cspan citationid=\"CR53\" class=\"CitationRef\"\u003e2012\u003c/span\u003e; Giraldo-Ospina and V\u0026aacute;squez-Varela \u003cspan citationid=\"CR25\" class=\"CitationRef\"\u003e2021\u003c/span\u003e). Private households in the urban area of Manizales increased by about 25% between 2005 and 2018 (DANE 2018), highlighting the need for accurate information on biodiversity and its distribution in environments strongly affected by population growth.\u003c/p\u003e\u003cp\u003eIn the last 30 years, studies have been conducted that highlight the high biological richness in various vertebrate groups in Manizales such as birds (Walker \u003cspan citationid=\"CR71\" class=\"CitationRef\"\u003e1996\u003c/span\u003e), reptiles (Rojas-Morales \u003cspan citationid=\"CR53\" class=\"CitationRef\"\u003e2012\u003c/span\u003e; Rojas-Morales et al. \u003cspan citationid=\"CR56\" class=\"CitationRef\"\u003e2014\u003c/span\u003e), and bats (Rosero-Taramuel et al. \u003cspan citationid=\"CR58\" class=\"CitationRef\"\u003e2023\u003c/span\u003e), but research focused on estimate the diversity of amphibians and reptiles inhabiting urban and peri-urban landscapes in the city of Manizales are scarce (e.g., Rojas-Morales \u003cspan citationid=\"CR53\" class=\"CitationRef\"\u003e2012\u003c/span\u003e; Rojas-Morales et al. \u003cspan citationid=\"CR56\" class=\"CitationRef\"\u003e2014\u003c/span\u003e; Toro-Restrepo \u003cspan citationid=\"CR64\" class=\"CitationRef\"\u003e2023\u003c/span\u003e; Vanegas-Guerrero et al. \u003cspan citationid=\"CR67\" class=\"CitationRef\"\u003e2016\u003c/span\u003e; Ram\u0026iacute;rez-Chaves et al. \u003cspan citationid=\"CR50\" class=\"CitationRef\"\u003e2022\u003c/span\u003e). Additionally, there has been no comprehensive assessment the diversity of amphibians and reptiles across the different LCZ, leaving a significant gap in understanding how these urban landscape classifications influence amphibian and reptile communities. The information gaps have hindered the establishment of monitoring, habitat connection studies, and the prioritization of species for conservation in urban and peri-urban environments.\u003c/p\u003e\u003cp\u003eFurthermore, amphibians and reptiles are among the vertebrates most affected by habitat modifications due to their ectotherm condition, their low vagility, the aversion that some species generate in people (i.e., snakes; Lynch \u003cspan citationid=\"CR41\" class=\"CitationRef\"\u003e2012\u003c/span\u003e), as well as a dependence on humid environments by amphibian species (Vanegas-Guerrero et al. \u003cspan citationid=\"CR67\" class=\"CitationRef\"\u003e2016\u003c/span\u003e). Although information on the presence of certain amphibian and reptile species is available for some areas within Manizales, the relationship between biodiversity patterns and different LCZ has not been systematically evaluated. This knowledge gap represents a key opportunity for our research to establish these associations and understand how urban landscape characteristics influence amphibian and reptile distribution. For these reasons, our study aimed to document the amphibian and reptile diversity in the Ecopark network and areas of environmental interest of Manizales and asses the connectivity of habitats and number of species detected in different LCZ\u0026acute;s. Although this research focuses on a local scale, the results will serve as a fundamental basis for future large-scale studies in the Andes, a region of exceptional amphibian and reptile diversity and conservation priority. Our working hypothesis is that smaller and more isolated areas will support lower species richness and show dominance of only one or two species, such as generalist or disturbance-tolerant species.\u003c/p\u003e"},{"header":"Material and methods","content":"\u003cp\u003e\u003cstrong\u003eStudy area\u003c/strong\u003e\u003c/p\u003e\n\u003cp\u003eThis study was conducted in the municipality of Manizales, Department of Caldas, which is located on the western flank of the Central Cordillera of the Andes of Colombia. It has a minimum elevation of 800 m and a maximum of 3800 m (Verhelst et al. 2001). Geographically, it includes areas whitin the middle Cauca River basin, as well as highland ecosystems such as Andean, sub- and high-Andean forests, and p\u0026aacute;ramo vegetation dominated by \u003cem\u003eEspeletia\u003c/em\u003e (Kattan and Alvarez-L\u0026oacute;pez 1996; Aceituno et al. 2013). Due to its wide altitudinal range, the presence of fertile volcanic soils and a wide variety of water tributaries, it is an ideal environment for the development of agricultural activities, as well as for biodiversity (Rojas-Morales et al. 2011; Rojas-Morales 2012; Rosero-Taramuel et al. 2023).\u003c/p\u003e\n\u003cp\u003eIn the study area, we selected several sampling points including remnants of forests (in a state of succession and some fragments of vegetation typical of the Andean zone) located in the interior and periphery of the urban matrix, in the urban area and surrounding of Manizales. These remanants have been catalogued as i) protected areas called \u0026quot;Ecoparks\u0026quot; (Ecoparques in Spanish) (Arango-B et al. 2007), and ii) environmental interest areas, including the Recinto del Pensamiento, and Cerro Sancancio. All areas are located in an elevational range between 1700 and 2500 m. The selected Ecoparks and environmental interest areas are part of urban and peri-urban landscapes (Fig. 1). The urban landscapes are: (1) Jard\u0026iacute;n Bot\u0026aacute;nico de la Universidad de Caldas (hereafter referred to as Jard\u0026iacute;n Bot\u0026aacute;nico) (2150 m elevation; area: 7 ha), (2) Bosque Popular El Prado (2030 m; area: 22.7 ha); (3) Cerro Sancancio (1890-2200; area: 74 ha). The peri-urban landscapes included: (4) Los Alc\u0026aacute;zares-Arenillo (1730-1960 m; located in the southwest of the urban area of Manizales, with an area of 35.7 ha); (5) Los Yarumos (2150 m; located northwest of the city with an approximate area of 35.8 ha); (6) Montele\u0026oacute;n (2200 m; located in the northwest of the municipality of Manizales with about 25.9 ha); (7) Recinto del Pensamiento (2250 m; located to the east of the city of Manizales with about 179 ha). No fieldwork was conducted at the Recinto del Pensamiento; however, it was included because herpetological specimens from this site are housed in the collections of the Centro de Museos, Museo de Historia Natural, Universidad de Caldas (MHN-UCa).\u003c/p\u003e\n\u003cp\u003e\u003cstrong\u003eAmphibian and reptile diversity and threatened category\u003c/strong\u003e\u003c/p\u003e\n\u003cp\u003eTo determine the richness of amphibians and reptiles we conducted field work in the Ecoparks and the environmental interest areas of Manizales during 24 January to 20 April of 2022, and in the first week of November of 2023. In all sampling sites, we used the visual and acoustic encounter sampling method, removing rocks, logs and leaf litter, in addition to checking shrubs and grasslands for amphibians and reptiles in the different microhabitats. Field surveys were carried out between 13:00 and 21:00 h during each sampling day (Veith et al. 2004; Rueda et al. 2006; Aguirre-Le\u0026oacute;n 2011), with each site sampled for four consecutive days a two-person team. We identified the vouchers by comparisons with specimens deposited in the Amphibian Collection (MHN-UCa-Am) and Reptile Collection (MHN-UCa-R) of the Centro de Museos, Museo de Historia Natural, Universidad de Caldas. Vouchers were collected under permits granted by the Corporaci\u0026oacute;n Aut\u0026oacute;noma Regional de Caldas (CORPOCALDAS), and the Autoridad Nacional de Licencias Ambientales (ANLA) to the Universidad de Caldas, as stipulated in resolution No. 02497 of December 31, 2018, updated by resolution No. 000026 of January 9, 2024.\u003c/p\u003e\n\u003cp\u003eBesides recorded individuals at the field, we also reviewed 235 additional specimens housed in the MHN-UCa, originally collected in the study area between 1985\u003cstrong\u003e\u0026nbsp;\u003c/strong\u003eand 2024. To complete the information, we included some photographic records with good resolution obtained by Ecoparks and areas of environmental interest staff, and literature information from previous studies in remnant forests of the city of Manizales (i.e., Rojas-Morales and Gonz\u0026aacute;lez-Dur\u0026aacute;n 2011; Rojas-Morales 2012; Rojas-Morales et al. 2014; Toro-Restrepo 2023; Ram\u0026iacute;rez-Chaves et al. 2022). For the taxonomic classification, we followed to Uetz et al. (2025) non-avian Reptiles and Frost (2024) for amphibians. We compiled the threatened category for each species according to the Red List of Threatened Species of the International Union for Conservation of Nature (IUCN 2025). We listed the endemic species following to Uetz et al. (2025) for reptiles and Frost (2024) for amphibians.\u003c/p\u003e\n\u003cp\u003e\u003cstrong\u003eTaxonomic diversity analysis\u003c/strong\u003e\u003c/p\u003e\n\u003cp\u003eTo calculate the taxonomic diversity of amphibians and reptiles in each Ecopark and the environmental interest areas, we performed alpha and beta diversity analyses using R software (version 4.4.2; R Core Team, 2024). We grouped the species recorded at each site to estimate the local richness (alpha diversity) (Table S1), and general richness by summing all sites (Gamma diversity). The analyses were based on abundance data obtained during fieldwork and were performed separately for amphibians and reptiles. Also, we calculated effective species diversity using the iNEXT package (Hsieh et al. 2016).\u0026nbsp;\u003c/p\u003e\n\u003cp\u003eWe calculate Beta diversity to quantify species turnover and nestedness (following Baselga 2010), among the different Ecoparks. The Jaccard index is decomposed into its components: turnover (\u0026beta;JTU) and nestedness (\u0026beta;JNE); total beta (\u0026beta;JAC) resulting of the sum of \u0026beta;JTU and \u0026beta;JNE (Baselga 2010). Additionally, to assess the average beta diversity across all study sites, we estimated multiple beta diversity using the betapart package (Baselga 2012).\u003c/p\u003e\n\u003cp\u003e\u003cstrong\u003eExploration of diversity changes and ecological connectivity using Local Climate Zones (LCZ)\u003c/strong\u003e\u003c/p\u003e\n\u003cp\u003eTo explore changes in amphibian and reptile diversity across the Ecoparks and areas of environmental interest, we estimated the species richness per km\u003csup\u003e2\u003c/sup\u003e, the dominancy patterns of species in each area, and the degree of isolation of each site. We evaluated the relationship between site area and two ecological variables: species richness and abundance. Given the small sample size (n = 6) and the potential violation of the normality, we applied a nonparametric Spearman correlation test. This analysis was performed in R software (version 4.4.2) using the \u0026ldquo;cor.test()\u0026rdquo; function (R Core Team, 2024).\u003c/p\u003e\n\u003cp\u003eTo assess the ecological connectivity between Ecoparks and areas of environmental interest, we used the Local Climate Zone (LCZ) classification scheme (Stewart and Oke 2012;\u0026nbsp;Bechtel et al. 2015). For this, we used the urban climates map of Manizales, developed by Roncancio and Stewart (2022), which classifies the city\u0026rsquo;s territory according to the LCZ framework. The LCZ classification, originally proposed by Stewart and Oke (2012) allows for the spatial categorization of urban landscapes based on land cover and urban form. For this study, we considered the following LCZ categories: LCZ 2 (Compact midrise), LCZ 3 (Compact lowrise), LCZ 5 (Open midrise), LCZ 6 (Open lowrise), LCZ 9 (Sparsely built), LCZ A (Dense trees), LCZ B (Scattered trees), and LCZ D (Low plants). We particularly focused on LCZ A and B, as these categories are associated with higher vegetative cover and potential for wildlife movement.\u0026nbsp;\u003c/p\u003e\n\u003cp\u003eBy overlaying the LCZ classification over the urban matrix shapefile of Manizales, we explored whether Ecoparks are spatially connected or isolated in the urban landscape. This approach allows for more precise identification of potential connectivity corridors or areas requiring restoration to improve biodiversity conservation in urban contexts. We integrated the diversity analyses (alpha and beta) into this spatial framework to evaluate how taxonomic diversity patterns relate to landscape connectivity and LCZ characteristics.\u0026nbsp;\u003c/p\u003e\n\u003cp\u003eWe also estimated the number of amphibian and reptiles that can be found in each LCZ observed in Manizales, analysing species richness and beta diversity across the various climate zones. This analysis helps to identify which LCZ types may serve as refugee or barriers for different amphibians and reptile species and provides insights into potential conservation priorities for the urban landscape. Based on this classification, we identified potential connections corridors between each site, prioritizing routes that traverse LCZ A and B categories, and described spatial continuity, highlighting areas where natural cover may be insufficient to support ecological flows. To do this, the shortest linear distances between the study areas were drawn and the different LCZs present in each line were described in detail. This allowed for the calculation of a percentage of the LCZ classification corresponding to the built form and/or natural cover of each drawn line. Additionally, by employing records from the Amphibian and Reptile Collections of the MHN-UCa, we identified the LCZ types that may currently be used by amphibians and reptiles beyond the Ecoparks and designated environmental interest areas (Table S2). This approach integrates landscape ecology principles with urban climatic zoning, providing a spatially explicit framework for understanding how urbanization patterns affect the distribution and conservation potential for amphibians and reptiles in the study area.\u003c/p\u003e"},{"header":"Results","content":"\u003cp\u003e\u003cstrong\u003eDiversity of amphibians and reptiles and threatened category\u003c/strong\u003e\u003c/p\u003e\n\u003cp\u003eOur field surveys yielded a total of 291 individuals, belonging to seven amphibian and 10 reptile species (Table S1). We obtained 231 amphibian records through visual and acoustic encounter surveys, while reptile sampling yielded 60 records. Among amphibians, \u003cem\u003eP\u003c/em\u003e. \u003cem\u003ethectopternus\u003c/em\u003e was the most abundant species with 102 records, distributed across nearly all study areas except in the site 4 (Los Alc\u0026aacute;zares-Arenillo). Alpha diversity analyses revealed that site 3 (Cerro Sancancio) presented the highest observed richness (6), followed by site 1 (5; Jard\u0026iacute;n Bot\u0026aacute;nico). Sample completeness (SC) was elevated for most amphibian sites, reaching values of 1 at sites 1, 3, 4 and 5 (Los Yarumos) (Table S2). Site 2 (Bosque Popular el Prado) showed slightly lover completeness (SC = 0.9744), while site 6 had the lowest completeness (SC = 0.8364). In terms of Shannon diversity for amphibians, site 1 showed the highest values (q1 = 4.3285), followed by site 4 (q1= 2.9486), and site 3 (q1 = 2.8346) (Table 2). Simpson index values showed a more equitable distribution in site 1 (q2 = 3.8136), compared to other sites.\u0026nbsp;\u003c/p\u003e\n\u003cp\u003eFor reptiles, \u003cem\u003ePholidobolus marianus\u003c/em\u003e was the most abundant species with 23 records found across all sampling areas (Table S1). Alpha diversity analyses showed that site 4 presented the highest values for both Shannon diversity (H\u0026rsquo; = 4.0579) and Simpson diversity (D = 3.6119), followed by site 3 (H\u0026rsquo; = 3.0678, D = 2.5745). Sites 5 and 6 showed observed richness of three and two species respectively, with variable diversity values (Table 2). Overall, sampling was acceptable to good for reptiles (SC \u0026gt; 0.84). Sites 2 and 6 achieved complete sample completeness (SC = 1) despite low sample sizes, indicating that all present species were captured, though increased sampling effort would be recommended for validation. Site 3 (SC = 0.8485) showed probability of undetected species, suggesting that sampling effort could be improved (Table S2).\u0026nbsp;\u003c/p\u003e\n\u003cp\u003eThe review of specimens from the MHN-UCa collections included five species (which were also recorded during our field surveys): \u003cem\u003eDendropsophus columbianus\u003c/em\u003e, \u003cem\u003eLeucostethus\u0026nbsp;\u003c/em\u003eaff.\u003cem\u003e\u0026nbsp;fraterdanieli\u003c/em\u003e, \u003cem\u003ePristimantis achatinus, P. thectopternus\u003c/em\u003e, and \u003cem\u003eP. paisa\u003c/em\u003e. Additionally, the literature review and photographic records added three amphibian species (Table 1). Among these, \u003cem\u003eNynphargus grandisonae\u0026nbsp;\u003c/em\u003eand \u003cem\u003eCentrolene savagei\u0026nbsp;\u003c/em\u003ewere recorded exclusively through photographic evidence, while \u003cem\u003eGastrotheca nicefori\u003c/em\u003e was documented through photographs and acoustic encounters (Fig. 2). For reptiles, we confirmed 18 reptile species based on the review of specimens and the compilation of information from the literature (Table 1). Photographic records further confirmed the presence of 11 reptile species in the study areas (Fig. 3). Of the total species documented, 16 are restricted to Colombia, and two of them (\u003cem\u003eRiama columbiana\u003c/em\u003e and\u0026nbsp;\u003cem\u003eLepidoblepharis williams\u003c/em\u003ei) are currently classified as Endangered according to the IUCN Red List.\u0026nbsp;\u003c/p\u003e\n\u003cp\u003eThrough the combination of all study methodologies, we recorded a total of 30 amphibian and reptile species in the Ecoparks and areas of environmental interest. For amphibians, we identified 10 species belonging to six genera and five families (Table 1). The families with the highest species richness were Strabomantidae with five species, and Centrolenidae with two, while Dendrobatidae, Hemiphractidae, and Hylidae, were represented by a single species (Table 1; Fig. 2). We found differences in species richness among the study sites (Table 1). Sites 1 and 5 showed the highest amphibian richness, with seven and six species, respectively. Some species were documented exclusively in specific sites; for instance, \u003cem\u003eGastrotheca nicefori\u003c/em\u003e and \u003cem\u003eNymphargus grandisonae\u003c/em\u003e, were only recorded in Los Yarumos, while \u003cem\u003ePristimantis w-nigrum\u003c/em\u003e was only recorded in the Jard\u0026iacute;n Bot\u0026aacute;nico.\u003c/p\u003e\n\u003cp\u003eFor reptiles,\u003cstrong\u003e\u0026nbsp;\u003c/strong\u003e20 species belonging to 14 genera and seven families were recorded (Table 1). Anolidae (three species) was the lizard family with the highest number of representatives in the urban and peri-urban areas of Manizales. For snakes, Colubridae was the most diverse family with 10 species (Fig. 3). Similar to amphibians, reptile species richness varied among sites. Of the 20 recorded reptile species, 11 were documented in urban areas and 16 in peri-urban areas. Notably, the endemic \u003cem\u003eAtractus manizalesensis\u003c/em\u003e, were recorded only in the Jard\u0026iacute;n Bot\u0026aacute;nico, while seven snake species were recorded only in peri-urban landscapes (Table 1).\u003c/p\u003e\n\u003cp\u003e\u003cstrong\u003eDiversity changes and ecological connectivity using Local Climate Zones (LCZ) \u0026nbsp; \u0026nbsp; \u0026nbsp; \u0026nbsp; \u0026nbsp; \u0026nbsp; \u0026nbsp; \u0026nbsp; \u0026nbsp; \u0026nbsp; \u0026nbsp; \u0026nbsp; \u0026nbsp; \u0026nbsp; \u0026nbsp; \u0026nbsp; \u0026nbsp; \u0026nbsp;\u0026nbsp;\u003c/strong\u003e\u003c/p\u003e\n\u003cp\u003eMost reptiles recorded in our study were observed within forested areas (LCZ A, B). However, species within the genera \u003cem\u003eAtractus\u003c/em\u003e, \u003cem\u003eAnolis\u003c/em\u003e and \u003cem\u003ePholidobolus\u003c/em\u003e are commonly observed in highly anthropized zones near the study areas (LCZ 2, 3 and 9) (Table 3). In particular, the cases of \u003cem\u003eAtractus biseriatus\u003c/em\u003e, \u003cem\u003eA. lehmanni\u003c/em\u003e, and \u003cem\u003ePholidobolus marianus\u003c/em\u003e, which were documented in multiple urban locations corresponding to compact midrise zones (LCZ 2), compact lowrise zones (LCZ 3), and sparsely built areas (LCZ 9).\u003c/p\u003e\n\u003cp\u003eThe analysis of species richness in relation to Ecopark size showed a moderate positive correlation (Spearman\u0026rsquo;s r = 0.44, p-value = 0.38, Fig. 4A), indicating a tendency for larger areas to host greater amphibian and reptile diversity. A similar pattern was observed for total abundance (Spearman\u0026rsquo;s r = 0.60, p-value = 0.24, Fig. 4B), where larger areas generally hosted greater numbers of individuals. Although neither correlation was statistically significant, both Spearman\u0026rsquo;s r values suggest a potential positive association between site area and amphibian and reptile diversity, consistent with expectations from island biogeography theory and urban habitat fragmentation patterns. However, the case of the Jard\u0026iacute;n Bot\u0026aacute;nico stands out: despite being the smallest area evaluated (0.07 km\u003csup\u003e2\u003c/sup\u003e), it presented the highest species density with 128.57 species/km\u003csup\u003e2\u003c/sup\u003e (1.28 species/ha) (Table S3), hosting nine different species with a relatively equal distribution of dominance between \u003cem\u003ePristimantis paisa\u003c/em\u003e (26.67%), \u003cem\u003eLeucostethus\u0026nbsp;\u003c/em\u003eaff.\u003cem\u003e\u0026nbsp;fraterdanieli\u003c/em\u003e, and \u003cem\u003ePholidobolus marianus\u003c/em\u003e (both with 15.56%). Alpha and beta diversity results reveal patterns directly related to the spatial configuration and connectivity of the assessed sites. The high differentiation of species communities between sites (\u0026beta;JAC = 0.8548 for reptiles, \u0026beta;JAC = 0.6274 for amphibians) indicates that 84% for reptiles and 63% for amphibians (Table 4), of total diversity is due to species turnover between locations. This pattern of high turnover suggests that each site maintains relatively unique assemblages, possibly due to the barriers imposed by the surrounding urban matrix.\u003c/p\u003e\n\u003cp\u003eThe dominance pattern among sites revealed that \u003cem\u003ePristimantis thectopternus\u003c/em\u003e was the most abundant species in four of the six sites locations evaluated (sites 2, 3, 5 and 6), with percentages ranging from 56.41% to 69.57% (Table S1, S3), contrasting with the greater evenness observed at site 1 (Simpson\u0026rsquo;s index D = 3.8136 for amphibians). This variation in the dominance structure between sites is related to the different connectivity conditions: site 1, which presents greater Shannon diversity (H\u0026apos; = 4.3285) and evenness, could benefit from better connectivity conditions or greater habitat heterogeneity. This dominance may be related to its ability to adapt to different habitat conditions within urban forest fragments. Species of ground snakes (\u003cem\u003eAtractus\u003c/em\u003e) showed a marked presence in the urban environment surrounding the Ecoparks, with records distributed mainly in compact lowrise and midrise areas (LCZ 2 and LCZ 3) (Table 3).\u003c/p\u003e\n\u003cp\u003eThe low nestedness component (\u0026beta;JNE = 0.1120 for reptiles, \u0026beta;JNE = 0.2032 for amphibians) compared to species turnover indicates that species loss does not follow a predictable pattern based on fragment size (Table 4), but is more closely related to the specific characteristics of each site and its degree of isolation. The turnover component was considerably higher for reptiles (\u0026beta;JTU = 0.7429) than for amphibians (\u0026beta;JTU = 0.4242), suggesting that reptiles are more sensitive to effects of fragmentation and isolation between Ecoparks and areas of environmental interest.\u0026nbsp;\u003c/p\u003e\n\u003cp\u003eThe analysis of potential ecological corridors between the sites, based on the LCZ classification, showed significant fragmentation of the urban landscape (Table 5). The most favorable corridor in terms of natural cover was identified between Cerro Sancancio (site 3), Bosque Popular El Prado (site 2), and Los Yarumos (site 5; corridor 15, Fig. 1, Table 5), with 95.99% of its linear distance (5,107.7 m) corresponding to natural cover categories (LCZ A, B, D, and F). However, this corridor has a total length of 5,321 m, which represents a considerable distance for amphibian and reptile species with limited dispersal capabilities. Similarly, the corridor between Los Yarumos and Montele\u0026oacute;n (site 6; corridor 8, Table 5, Fig. 1) has a high percentage of natural cover (92.03%), but its linear distance of 3,254 m also poses a significant barrier to amphibian and reptile mobility.\u0026nbsp;\u003c/p\u003e\n\u003cp\u003eAlthough we identified potential corridors with a high proportion of natural areas (LCZ A and B) (Table 5), the extension of these corridors and the predominance of urban matrices (LCZ 2, 3, 5, and 6) in critical sections severely limit functional connectivity for both amphibians and reptiles (Fig. 1), reflecting the high differentiation of assemblages, mainly among reptiles (\u0026beta;JTU = 0.7429) (Table 4). This suggests that each site acts as an island with limited species exchange, explaining both the high observed beta diversity and the site-specific dominance patterns. Shorter connections between Ecoparks, such as those linking the Jard\u0026iacute;n Bot\u0026aacute;nico with Cerro Sancancio (283\u0026ndash;391 m), have significant percentages of built-up areas (between 40.48% and 84.64%), compromising their functionality as effective corridors (Table 5). These shorter corridors could function as transit zones for some species, particularly reptiles such as \u003cem\u003eAtractus\u003c/em\u003e spp. and \u003cem\u003eP. marianus,\u003c/em\u003e which have demonstrated some tolerance to urbanized environments.\u0026nbsp;\u003c/p\u003e"},{"header":"Discussion","content":"\u003cp\u003eA total of 10 amphibians and 20 reptiles were documented in the study area, representing 28% of the amphibian and 55% of the reptile species for the south-central region of Caldas (Rojas-Morales et al. \u003cspan citationid=\"CR56\" class=\"CitationRef\"\u003e2014\u003c/span\u003e); highlighting the role of the different local landscapes in the maintenance of different species. However, the species richness of amphibians and reptiles found in the study area is low in relation to that found in nearby well-preserved rural areas such as Parque Nacional Natural Selva de Florencia, Reserva Natural Privada Riomanso and Reserva Forestal Protectora Bosques de la Central Hidroel\u0026eacute;ctrica de Caldas (Acosta-Galvis et al. \u003cspan citationid=\"CR3\" class=\"CitationRef\"\u003e2006\u003c/span\u003e; Acosta-Galvis \u003cspan citationid=\"CR2\" class=\"CitationRef\"\u003e2009\u003c/span\u003e; Duarte-Mar\u0026iacute;n et al. \u003cspan citationid=\"CR18\" class=\"CitationRef\"\u003e2018\u003c/span\u003e; G\u0026oacute;mez-Salazar et al. \u003cspan citationid=\"CR26\" class=\"CitationRef\"\u003e2017\u003c/span\u003e). This pattern is consistent with global trends showing reduced biodiversity in urban areas compared to natural environments (McKinney \u003cspan citationid=\"CR46\" class=\"CitationRef\"\u003e2006\u003c/span\u003e; Elmqvist et al. \u003cspan citationid=\"CR19\" class=\"CitationRef\"\u003e2013\u003c/span\u003e). Nevertheless, some studies have documented contrasting patterns where urban areas can support higher species richness than expected (Hamer and McDonnell \u003cspan citationid=\"CR27\" class=\"CitationRef\"\u003e2008\u003c/span\u003e, \u003cspan citationid=\"CR28\" class=\"CitationRef\"\u003e2010\u003c/span\u003e; Banville and Bateman \u003cspan citationid=\"CR9\" class=\"CitationRef\"\u003e2012\u003c/span\u003e). Positive outcomes are often associated with strategic urban planning that prioritizes habitat quality, vegetation structural complexity, and connectivity between green spaces, demonstrating that urbanization effects on amphibians and reptiles are not universally negative and can be mitigated through appropriate management practices (Hamer and McDonnell \u003cspan citationid=\"CR27\" class=\"CitationRef\"\u003e2008\u003c/span\u003e, \u003cspan citationid=\"CR28\" class=\"CitationRef\"\u003e2010\u003c/span\u003e; Banville and Bateman \u003cspan citationid=\"CR9\" class=\"CitationRef\"\u003e2012\u003c/span\u003e).\u003c/p\u003e\u003cp\u003eThe presence of 16 endemic species (53,3% of total recorded species) underscores the conservation value of urban green areas in the Colombian Andes. This level of endemism is particularly noteworthy given the highly modified nature of the urban landscape and reinforces the critical importance of maintaining these forest fragments for regional biodiversity conservation (Myers et al. \u003cspan citationid=\"CR47\" class=\"CitationRef\"\u003e2000\u003c/span\u003e; Hazzi et al. \u003cspan citationid=\"CR30\" class=\"CitationRef\"\u003e2018\u003c/span\u003e). Among our records, \u003cem\u003eRiama columbiana\u003c/em\u003e and \u003cem\u003eLepidoblepharis williams\u003c/em\u003ei stand out as species of particular conservation concern, categorized as Endangered (EN) according to the IUCN (\u003cspan citationid=\"CR33\" class=\"CitationRef\"\u003e2025\u003c/span\u003e). Both species were observed in the Jard\u0026iacute;n Bot\u0026aacute;nico, Los Yarumos and Montele\u0026oacute;n Ecoparks, representing one of the few documented populations in adjacent urban environments. The consistent presence of both species at these sites presents a significant opportunity for conservation action and ecological research. We recommend establishing long-term monitoring programs to asses population dynamics, habitat requirements, and potential threats to this species within urban contexts. Additionally, the presence of other endemic species such as \u003cem\u003eAtractus manizalesensis\u003c/em\u003e and \u003cem\u003ePristimantis paisa\u003c/em\u003e further emphasizes the conservation priority of these urban forest remnants. The relative scarcity of threatened species in our inventory may reflect the resilience of urban-tolerant species or possible local extinctions of more sensitive taxa (Pereyra et al. \u003cspan citationid=\"CR48\" class=\"CitationRef\"\u003e2021\u003c/span\u003e). This pattern warrants further investigation through comparison with historical records and assessment of species that may have been lost from the urban landscape over time.\u003c/p\u003e\u003cp\u003eOur results revealed a complex relationship between habitat area and species richness, with a moderate positive correlation suggesting that area alone is not the sole determinant of biodiversity in urban environments. The exceptional case of the Jard\u0026iacute;n Bot\u0026aacute;nico, which despite being the smallest area exhibited the highest species density, indicates that habitat quality, microhabitat heterogeneity, and connectivity may be more critical factors than patch size (Keinath et al. \u003cspan citationid=\"CR37\" class=\"CitationRef\"\u003e2023\u003c/span\u003e; Marsh et al. \u003cspan citationid=\"CR43\" class=\"CitationRef\"\u003e2024\u003c/span\u003e). This finding partially contradicts our initial hypothesis, suggesting that additional factors such as microhabitat heterogeneity, conservation status, proximity to areas like Cerro Sancancio, and the presence of water bodies may be more important determinants than area size for maintaining viable amphibian and reptile populations in urban environments. The presence of water bodies, varied topography, and maintained vegetation structure in the Jard\u0026iacute;n Bot\u0026aacute;nico likely contribute to its high species density (Callaghan et al. \u003cspan citationid=\"CR14\" class=\"CitationRef\"\u003e2019\u003c/span\u003e). These results align with studies on other urban environments showing that small but well-managed green spaces can support disproportionately high biodiversity (Lepczyk et al. \u003cspan citationid=\"CR39\" class=\"CitationRef\"\u003e2017\u003c/span\u003e; Callaghan et al. \u003cspan citationid=\"CR14\" class=\"CitationRef\"\u003e2019\u003c/span\u003e); and urban planning should prioritize habitat quality enhancement and microhabitat diversity rather than focusing solely on increasing that size of green spaces (Marsh et al. \u003cspan citationid=\"CR43\" class=\"CitationRef\"\u003e2024\u003c/span\u003e).\u003c/p\u003e\u003cp\u003eWe also found a clear pattern of differential urban tolerance between amphibians and reptiles. Most records in highly urbanized areas (LCZ 2, 3 and 9) correspond to reptiles, particularly species of the genera \u003cem\u003eAtractus\u003c/em\u003e, \u003cem\u003eAnolis\u003c/em\u003e, and \u003cem\u003ePholidobolus marianus.\u003c/em\u003e Urban records outside of Ecoparks correspond mainly to reptiles, especially ground snakes (\u003cem\u003eAtractus\u003c/em\u003e) and stick lizards like \u003cem\u003ePholidobolus marianus\u003c/em\u003e (Table\u0026nbsp;\u003cspan refid=\"Tab3\" class=\"InternalRef\"\u003e3\u003c/span\u003e), suggesting that reptiles may be more adaptable to urban environments compared to amphibians, likely due to their reduced dependence on specific humidity requirements and water bodies for reproduction (Hamer and McDonnell \u003cspan citationid=\"CR27\" class=\"CitationRef\"\u003e2008\u003c/span\u003e). The concentration of urban records between the Jard\u0026iacute;n Bot\u0026aacute;nico, Cerro Sancancio, and Los Yarumos (Fig.\u0026nbsp;\u003cspan refid=\"Fig1\" class=\"InternalRef\"\u003e1\u003c/span\u003e) indicates that these areas, despite the intervening urban matrix, may function as a fragmented ecological complex for some species with greater tolerance to disturbance. The dominance of the Northern Cordilleras Robber Frog (\u003cem\u003ePristimantis thectopternus\u003c/em\u003e) across multiple sites indicates that direct-developing species with broader ecological tolerances are better suited to persist in fragmented urban landscapes (Hamer and McDonnell \u003cspan citationid=\"CR27\" class=\"CitationRef\"\u003e2008\u003c/span\u003e). This aligns with global patterns showing that species with specialized habitat requirements or complex life cycles are disproportionately affected by urbanization (McKinney \u003cspan citationid=\"CR46\" class=\"CitationRef\"\u003e2006\u003c/span\u003e).\u003c/p\u003e\u003cp\u003eThe LCZ analysis revealed severe fragmentation of the urban landscape, with most potential corridors between Ecoparks and environmental interest areas, exceeding dispersal distances for amphibians and reptiles (Smith and Green \u003cspan citationid=\"CR61\" class=\"CitationRef\"\u003e2005\u003c/span\u003e). Even the most favourable corridor identified (between Cerro Sancancio, Bosque Popular el Prado, and Los Yarumos) spans over 5 km, representing a significant barrier for species with limited mobility. The concentration of urban records in areas between Jard\u0026iacute;n Bot\u0026aacute;nico, Cerro Sancancio, and Los Yarumos suggest that these sites may function as loosely connected ecological network for disturbance-tolerant species. However, the intervening urban matrix (dominated by LCZ 2 and 3) likely prevents movement for most amphibian species and limits connectivity for all but the most urban-adapted reptiles (Marsh et al. \u003cspan citationid=\"CR43\" class=\"CitationRef\"\u003e2024\u003c/span\u003e). Despite the presence of scattered green areas in the urban matrix of Manizales, the ecological connectivity for amphibians and reptiles is severely compromised by habitat fragmentation. Targeted management interventions could improve this situation. Conservation strategies should focus on improving the permeability of shorter corridors, particularly those connecting the Jard\u0026iacute;n Bot\u0026aacute;nico with other sites, where tolerant species such as ground snakes (\u003cem\u003eAtractus\u003c/em\u003e spp.) and the stick lizard, \u003cem\u003ePholidobolus. marianus\u003c/em\u003e could facilitate gene flow between fragmented populations. Species of \u003cem\u003eAtractus\u003c/em\u003e might exhibit adaptability to urbanized environments (Rojas-Morales \u003cspan citationid=\"CR53\" class=\"CitationRef\"\u003e2012\u003c/span\u003e), with multiple species documented in compact residential areas (LCZ 2 and 3). Urban tolerance may relate to their fossorial habitats, small size, allowing them to exploit urban microhabitats unavailable to larger or more specialized species (Lettoof et al. \u003cspan citationid=\"CR40\" class=\"CitationRef\"\u003e2023\u003c/span\u003e). Similarly, \u003cem\u003eP. marianus\u003c/em\u003e showed consistent presence across all study sites and urban areas, suggesting high ecological flexibility within this genus.\u003c/p\u003e\u003cp\u003eFinally, the moderate positive correlation between area size and species richness (r\u0026thinsp;=\u0026thinsp;0.44) and total abundance (r\u0026thinsp;=\u0026thinsp;0.60), although not statistically significant, reinforces the importance of maintaining and expanding existing urban green areas while improving their functional connectivity. The substantial representation of species of amphibians and reptiles within the urban environments evaluated underscores both the conservation value of urban green spaces and the potential for well-planned cities to server as refugia for regional biodiversity in highly modified landscapes (Lepczyk et al. \u003cspan citationid=\"CR39\" class=\"CitationRef\"\u003e2017\u003c/span\u003e).\u003c/p\u003e"},{"header":"Conclusions","content":"\u003cp\u003eWe highlight several critical conservation priorities: (1) protection and enhancement of existing Ecoparks and environmental interest areas, particularly the Cerro Sancancio (site 3), Jard\u0026iacute;n Bot\u0026aacute;nico (site 1) and Los Alc\u0026aacute;zares-Arenillo (site 4), which harbours the highest amphibians and reptiles species; (2) implementation of corridor restoration projects to improve connectivity between forest fragments, with special attention to reducing the permeability barriers in shorter connections; (3) establishment of monitoring programs for endemic and threatened species; and (4) integration of biodiversity considerations into urban planning processes using LCZ mapping as a tool for identifying priority areas for conservation action. Severe fragmentation revealed by our connectivity analysis, coupled with the high betta diversity (driven primarily by species turnover), indicates that current green infrastructure is insufficient to maintain long-term viable populations for most species. Strategic habitat restoration focusing on corridors with high natural cover percentages (\u0026gt;\u0026thinsp;90%) but excessive length should be prioritized to enhance functional connectivity across the urban landscape. The differential responses observed between amphibians and reptiles, with reptiles showing higher turnover and greater urban tolerance, should inform targeted conservation strategies that consider that specific ecological requirements and dispersal limitations of each taxonomic group.\u003c/p\u003e"},{"header":"Declarations","content":"\u003cp\u003e\u003cstrong\u003eAcknowledgments\u003c/strong\u003e\u003c/p\u003e\n\u003cp\u003eWe appreciate the support provided by the members of the Natural History Laboratory during the different sampling days. JJHO, LSCM and HFAM thank The Mohamed bin Zayed Species Conservation Fund for the grant to carry out the project \u0026quot;Current threats and conservation status of three species of Harlequin toad (Anura, Bufonidae, \u003cem\u003eAtelopus\u003c/em\u003e) in the Andes of Colombia\u0026quot; (Project N\u0026deg; 222529372) that during its development has contributed to the generation of knowledge about the fauna of amphibians and reptiles in several areas of the coffee region, including the city of Manizales. We thank the Interadministrative Agreement N\u0026deg; 2110200953 signed between the Alcald\u0026iacute;a de Manizales, CORPOCALDAS and the Universidad de Caldas, for the planning and execution of the Expedici\u0026oacute;n Manizales + Biodiversa carried out in the urban and peri-urban forests of Manizales, Caldas, Colombia.\u003c/p\u003e\n\u003cp\u003e\u003cstrong\u003eAuthor contributions\u003c/strong\u003e\u003c/p\u003e\n\u003cp\u003e\u003cstrong\u003eEACG:\u0026nbsp;\u003c/strong\u003eConceptualization, investigation, data curation, formal analysis, manuscript writing, revision and editing.\u003cstrong\u003e\u0026nbsp;JJHO:\u0026nbsp;\u003c/strong\u003eConceptualization, data curation, manuscript writing, revision and editing. \u003cstrong\u003eLSCM:\u0026nbsp;\u003c/strong\u003eManuscript writing, data curation,\u003cstrong\u003e\u0026nbsp;\u003c/strong\u003ereview and editing.\u003cstrong\u003e\u0026nbsp;HFAM: \u0026nbsp;\u003c/strong\u003ePhotography, manuscript writing, review and editing. \u003cstrong\u003eJARM:\u0026nbsp;\u003c/strong\u003eFormal analysis, manuscript writing, review and editing.\u003cstrong\u003e\u0026nbsp;HERC:\u0026nbsp;\u003c/strong\u003eConceptualization, investigation, manuscript writing, revision, and editing\u003cstrong\u003e.\u003c/strong\u003e\u003c/p\u003e\n\u003cp\u003e\u003cstrong\u003eCompeting interests\u003c/strong\u003e\u003c/p\u003e\n\u003cp\u003eThe authors declare no personal, financial, or institutional conflicts of interest.\u0026nbsp;\u003c/p\u003e"},{"header":"References","content":"\u003col\u003e\n \u003cli\u003e Aceituno FJ, Loaiza N, Delgado-Burbano ME, Barrientos G (2013) The initial human settlement of Northwest South America during the Pleistocene/Holocene transition: Synthesis and perspectives. 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Version 2025-1. \u0026lt;https://www.iucnredlist.org\u0026gt;\u003c/li\u003e\n \u003cli\u003eJosse C, Cuesta F, Navarro G, Barrena V, Cabrera E, Chac\u0026oacute;n-Moreno E, Ferreira W, Peralvo M, Saito J, Tovar A (2009) Ecosistemas de los Andes del Norte y Centro: Bolivia, Colombia, Ecuador, Per\u0026uacute; y Venezuela. Secretar\u0026iacute;a General de la Comunidad Andina, Programa Regional ECOBONA\u0026ndash;Intercooperation, CONDESAN\u0026ndash;Proyecto P\u0026aacute;ramo Andino, Programa BioAndes, EcoCiencia, NatureServe, IAvH, LTA\u0026ndash;UNALM, ICAE\u0026ndash;ULA, CDC\u0026ndash;UNALM, RUMBOL SRL.\u003c/li\u003e\n \u003cli\u003eKattan GH, Alvarez-L\u0026oacute;pez H (1996) Preservation and management of biodiversity in fragmented landscapes in the Colombian Andes. In Forest patches in tropical landscapes. J. Schelhas \u0026amp; R. Greenberg, Eds. Washington, D. 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Cienc.\u003cem\u003e\u0026nbsp;\u003c/em\u003e36(140):435-449.\u0026nbsp;\u003c/li\u003e\n \u003cli\u003eMacGregor-Fors I (2013) Ecolog\u0026iacute;a Urbana: Experiencias en Am\u0026eacute;rica Latina. I. MacGregor Fors, Ed. ISBN: 978-607-00-6869-0. 130 p.\u003c/li\u003e\n \u003cli\u003eMarsh DM, Medina J, Wilkinson B (2024) Predicting amphibian and reptile distributions and species richness across urban parks in the eastern United States.\u0026nbsp;Urban Ecosyst\u0026nbsp;27:125-145. https://doi.org/10.1007/s11252-023-01437-6\u003c/li\u003e\n \u003cli\u003eMcDonald RI, Mansur AV, Ascens\u0026atilde;o F, Colbert M, Crossman K, Elmqvist T, Gonzalez A, G\u0026uuml;neralp B et al (2020) Research gaps in knowledge of the impact of urban growth on biodiversity. 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Nature 403(6772):853-858. https://doi.org/10.1038/35002501\u003c/li\u003e\n \u003cli\u003ePereyra LC, Akmentins, MS, Salica MJ, Quiroga MF, Moreno CE, Vaira M (2021)\u0026nbsp;Tolerant and avoiders in an urban landscape: anuran species richness and functional groups responses in the Yungas\u0026rsquo; forest of NW Argentina.\u0026nbsp;Urban Ecosyst\u003cem\u003e\u0026nbsp;\u003c/em\u003e24:141\u0026ndash;152. https://doi.org/10.1007/s11252-020-01025-y\u003c/li\u003e\n \u003cli\u003eRamalho WP, Silva JR, Soares PT, Ferraz D, Arruda FV, Prado VHM (2018) The anurans and squamates of a peri-urban Cerrado remnant in the State of Goi\u0026aacute;s, Central Brazil. Herpetology Notes 11(1):573-583.\u003c/li\u003e\n \u003cli\u003eRam\u0026iacute;rez-Chaves HE, Henao-Osorio JJ, Cardona-Galvis EA, Arias-Monsalve HF, Rojas-Morales JA (2022) Listado de los reptiles (Reptilia) del departamento de Caldas, Colombia. v1.0.\u003cem\u003e\u0026nbsp;\u003c/em\u003eUniversidad de Caldas. https://doi.org/10.15472/vxjiis\u003c/li\u003e\n \u003cli\u003eR Core Team (2024) R: A Language and Environment for Statistical Computing. R version\u0026nbsp;4.4.2.\u0026nbsp;R Foundation for Statistical Computing, Vienna, Austria. https://www.R-project.org/ \u0026nbsp;\u003c/li\u003e\n \u003cli\u003eRipple WJ, Wolf C, Newsome TM, Galetti M, Alamgir M, Crist E, Mahmoud MI, Laurance WF et al (2017) World Scientists\u0026rsquo; Warning to Humanity: A Second Notice. BioScience 67(12):1026-1028. https://doi.org/10.1093/biosci/bix125\u003c/li\u003e\n \u003cli\u003eRojas-Morales JA (2012) Snakes of an urban-rural landscape in the central Andes of Colombia: species composition, distribution, and natural history. Phyllomedusa: Journal of Herpetology 11(2):135-154. https://doi.org/10.11606/issn.2316-9079.v11i2p135-154\u003c/li\u003e\n \u003cli\u003eRojas-Morales JA, Gonz\u0026aacute;lez-Dur\u0026aacute;n GA (2011) Description of the colouration in life of \u003cem\u003eTricheilostoma joshuai\u003c/em\u003e (Serpentes, Leptotyphlopidae). \u0026iquest;A species tolerant of disturbed habitats? Salamandra 47(4):237-240.\u003c/li\u003e\n \u003cli\u003eRojas-Morales JA, Escobar-Lasso S, Guti\u0026eacute;rrez-C\u0026aacute;rdenas PDA (2011) Contribuci\u0026oacute;n al conocimiento de los anfibios de la regi\u0026oacute;n centro-sur de Caldas: primeros registros de ranas de cristal (Anura: Centrolenidae) para el municipio de Manizales, Colombia. Bol. Cient. Mus. Hist. Nat. Univ. Caldas 15(1):75-83.\u0026nbsp;\u003c/li\u003e\n \u003cli\u003eRojas-Morales JA, Arias-Monsalve HF, Gonz\u0026aacute;lez-Duran GA (2014) Anfibios y reptiles de la regi\u0026oacute;n centro-sur del departamento de Caldas, Colombia. 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In T\u0026eacute;cnicas de Inventario y Monitoreo para los Anfibios de la Regi\u0026oacute;n Tropical Andina. A. Angulo, J. Rueda-Almonacid, J. Rodr\u0026iacute;guez-Mahecha, \u0026amp; E. La Marca, Eds. Bogot\u0026aacute;, D. C.: Conservaci\u0026oacute;n Internacional- Panamericana Formas e Impresos S.A. 135-171.\u003c/li\u003e\n \u003cli\u003eSantos T, Teller\u0026iacute;a JL (2006) P\u0026eacute;rdida y fragmentaci\u0026oacute;n del h\u0026aacute;bitat: efecto sobre la conservaci\u0026oacute;n de las especies. Ecosistemas 15(2):3-12. Available: https://www.revistaecosistemas.net/index.php/ecosistemas/article/view/180.\u003c/li\u003e\n \u003cli\u003eSmith MA, Green DM (2005) Dispersal and the metapopulation paradigm in amphibian ecology and conservation: are all amphibian populations metapopulations? Ecography \u003cem\u003e28\u003c/em\u003e(1):110-128. https://doi.org/10.1111/j.0906-7590.2005.04042.x\u003c/li\u003e\n \u003cli\u003eStewart ID, Oke TR (2012)\u0026nbsp;Local climate zones for urban temperature studies. Bull. Amer. Meteor. Soc. 93(12):1879-1900. https://doi.org/10.1175/BAMS-D-11-00019.1\u003c/li\u003e\n \u003cli\u003eTognelli, MF, Anderson EP, Jim\u0026eacute;nez‐Segura LF, Chuctaya J, Chocano L, Maldonado‐Ocampo JA, Mesa‐Salazar L, Mojica JI et al (2019) Assessing conservation priorities of endemic freshwater fishes in the Tropical Andes region. Aquatic Conserv: Mar Freshw Ecosyst 29(7): 1123-1132. https://doi.org/10.1002/aqc.2971\u003c/li\u003e\n \u003cli\u003eToro-Restrepo B (2023) Contribuci\u0026oacute;n al conocimiento de la fauna asociada a los ecoparques de Manizales: Un aporte a las colecciones biol\u0026oacute;gicas del Museo de Historia Natural de la Universidad de Caldas. v1.1. No organization. Dataset/Occurrence. https://ipt.biodiversidad.co/permisos/resource?r=ecoparques_manizales\u0026amp;v=1.1\u003c/li\u003e\n \u003cli\u003eUetz P, Freed P, Aguilar R, Reyes F, Kudera J, Ho\u0026scaron;ek J (eds.) (2025) The Reptile Database, http://www.reptile-database.org, accessed [20/04/2025]\u0026nbsp;\u003c/li\u003e\n \u003cli\u003eUnited Nations. (2022). World Population Prospects 2022: Summary of Results.\u003c/li\u003e\n \u003cli\u003eVanegas-Guerrero J, Fern\u0026aacute;ndez C, Buitrago-Gonz\u0026aacute;lez W, Vargas-Salinas F (2016) Urban remnant forests: are they important for herpetofaunal conservation in Central Andes of Colombia? Herpetological Review 74(2):180-185.\u003c/li\u003e\n \u003cli\u003eVeith M, L\u0026ouml;tters S, Andreone F, R\u0026ouml;del M-O (2004) Measuring and monitoring amphibian diversity in tropical forests. II. Estimating species richness from standardized transect censing. Ecotropica 10:85-99.\u003c/li\u003e\n \u003cli\u003eVentura L, Strubbe D, Shwartz A (2024) Beyond the concrete jungle: The value of urban biodiversity for regional conservation efforts.\u0026nbsp;Science of The Total Environment\u0026nbsp;955:177222. https://doi.org/10.1016/j.scitotenv.2024.177222\u003c/li\u003e\n \u003cli\u003eVerhelst JC, Rodr\u0026iacute;guez JC, Orrego O, Botero JE, L\u0026oacute;pez JA, Franco VM, Pfeifer AM (2001) Aves del Municipio de Manizales-Caldas, Colombia. Biota Colombiana 2(3):265-284.\u003c/li\u003e\n \u003cli\u003eWalker HR (1996) Avifauna registrada en la parte alta de la microcuenca Palogrande (sector del Jard\u0026iacute;n Bot\u0026aacute;nico de la Universidad de Caldas). Bol. Cient. Mus. Hist. Nat. Univ. Caldas 1:11-15. Available: https://revistasojs.ucaldas.edu.co/index.php/boletincientifico/article/view/6177.\u003c/li\u003e\n \u003cli\u003eZabel F, Delzeit R, Schneider JM, Seppelt R, Mauser W, V\u0026aacute;clav\u0026iacute;k T (2019) Global impacts of future cropland expansion and intensification on agricultural markets and biodiversity. Nat Commun 10(1):2844. https://doi.org/10.1038/s41467-019-10775-z\u0026nbsp;\u003c/li\u003e\n\u003c/ol\u003e"},{"header":"Tables","content":"\u003cp\u003e\u003cstrong\u003eTable 1\u0026nbsp;\u003c/strong\u003eAmphibians and reptiles recorded Ecoparks and areas of environmental interest of the city of Manizales, Colombia. Sites: (1) Jard\u0026iacute;n Bot\u0026aacute;nico, (2) Bosque Popular El Prado, (3) El Cerro Sancancio, (4) Los Alc\u0026aacute;zares-Arenillo, (5) Los Yarumos, (6) Montele\u0026oacute;n, (7) Recinto del Pensamiento. Its conservation status is described by the IUCN: Least Concern (LC); Data Deficient (DD); Endangered (EN). Voucher specimens are housed at the MNH-UCa Amphibians (Am) and Reptiles (R) collections\u003c/p\u003e\n\u003cdiv align=\"\"\u003e\n \u003ctable border=\"0\" cellspacing=\"0\" cellpadding=\"0\" width=\"954\"\u003e\n \u003ctbody\u003e\n \u003ctr\u003e\n \u003ctd style=\"width: 509px;\"\u003e\n \u003cp\u003e\u003cstrong\u003eTaxon\u003c/strong\u003e\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 84px;\"\u003e\n \u003cp\u003e\u003cstrong\u003eLocalities\u003c/strong\u003e\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 107px;\"\u003e\n \u003cp\u003e\u003cstrong\u003eThreat category (IUCN)\u003c/strong\u003e\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 65px;\"\u003e\n \u003cp\u003e\u003cstrong\u003eEndemic\u003c/strong\u003e\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 189px;\"\u003e\n \u003cp\u003e\u003cstrong\u003eVouchers or type of record\u003c/strong\u003e\u003c/p\u003e\n \u003c/td\u003e\n \u003c/tr\u003e\n \u003ctr\u003e\n \u003ctd style=\"width: 509px;\"\u003e\n \u003cp\u003e\u003cstrong\u003eAmphibia, Anura\u003c/strong\u003e\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 84px;\"\u003e\u003cbr\u003e\u003c/td\u003e\n \u003ctd style=\"width: 107px;\"\u003e\u003cbr\u003e\u003c/td\u003e\n \u003ctd style=\"width: 65px;\"\u003e\u003cbr\u003e\u003c/td\u003e\n \u003ctd style=\"width: 189px;\"\u003e\u003cbr\u003e\u003c/td\u003e\n \u003c/tr\u003e\n \u003ctr\u003e\n \u003ctd style=\"width: 509px;\"\u003e\n \u003cp\u003e\u003cstrong\u003eCentrolenidae\u003c/strong\u003e\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 84px;\"\u003e\u003cbr\u003e\u003c/td\u003e\n \u003ctd style=\"width: 107px;\"\u003e\u003cbr\u003e\u003c/td\u003e\n \u003ctd style=\"width: 65px;\"\u003e\u003cbr\u003e\u003c/td\u003e\n \u003ctd style=\"width: 189px;\"\u003e\u003cbr\u003e\u003c/td\u003e\n \u003c/tr\u003e\n \u003ctr\u003e\n \u003ctd style=\"width: 509px;\"\u003e\n \u003cp\u003e\u003cem\u003eNymphargus grandisonae\u003c/em\u003e (Cochran \u0026amp; Goin, 1970)\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 84px;\"\u003e\n \u003cp\u003e5\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 107px;\"\u003e\n \u003cp\u003eLC\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 65px;\"\u003e\u003cbr\u003e\u003c/td\u003e\n \u003ctd style=\"width: 189px;\"\u003e\n \u003cp\u003ePhotographs\u003c/p\u003e\n \u003c/td\u003e\n \u003c/tr\u003e\n \u003ctr\u003e\n \u003ctd style=\"width: 509px;\"\u003e\n \u003cp\u003e\u003cem\u003eCentrolene savagei\u003c/em\u003e (Ruiz \u0026amp; Lynch, 1991)\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 84px;\"\u003e\n \u003cp\u003e4, 5, 6\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 107px;\"\u003e\n \u003cp\u003eLC\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 65px;\"\u003e\n \u003cp\u003ex\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 189px;\"\u003e\n \u003cp\u003ePhotographs\u003c/p\u003e\n \u003c/td\u003e\n \u003c/tr\u003e\n \u003ctr\u003e\n \u003ctd style=\"width: 509px;\"\u003e\n \u003cp\u003e\u003cstrong\u003eDendrobatidae\u003c/strong\u003e\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 84px;\"\u003e\u003cbr\u003e\u003c/td\u003e\n \u003ctd style=\"width: 107px;\"\u003e\u003cbr\u003e\u003c/td\u003e\n \u003ctd style=\"width: 65px;\"\u003e\u003cbr\u003e\u003c/td\u003e\n \u003ctd style=\"width: 189px;\"\u003e\u003cbr\u003e\u003c/td\u003e\n \u003c/tr\u003e\n \u003ctr\u003e\n \u003ctd style=\"width: 509px;\"\u003e\n \u003cp\u003e\u003cem\u003eLeucostethus\u0026nbsp;\u003c/em\u003eaff\u003cem\u003e. fraterdanieli\u003c/em\u003e (Silverstone, 1971)\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 84px;\"\u003e\n \u003cp\u003e1, 2, 4, 5, 6\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 107px;\"\u003e\n \u003cp\u003eLC\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 65px;\"\u003e\n \u003cp\u003ex\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 189px;\"\u003e\n \u003cp\u003eAm-416-418, 447-452, 832-835, visual encounter, Rojas-Morales et al. (2021)\u003c/p\u003e\n \u003c/td\u003e\n \u003c/tr\u003e\n \u003ctr\u003e\n \u003ctd style=\"width: 509px;\"\u003e\n \u003cp\u003e\u003cstrong\u003eHemiphractidae\u003c/strong\u003e\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 84px;\"\u003e\u003cbr\u003e\u003c/td\u003e\n \u003ctd style=\"width: 107px;\"\u003e\u003cbr\u003e\u003c/td\u003e\n \u003ctd style=\"width: 65px;\"\u003e\u003cbr\u003e\u003c/td\u003e\n \u003ctd style=\"width: 189px;\"\u003e\u003cbr\u003e\u003c/td\u003e\n \u003c/tr\u003e\n \u003ctr\u003e\n \u003ctd style=\"width: 509px;\"\u003e\n \u003cp\u003e\u003cem\u003eGastrotheca nicefori\u003c/em\u003e Gaige, 1933\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 84px;\"\u003e\n \u003cp\u003e5\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 107px;\"\u003e\n \u003cp\u003eLC\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 65px;\"\u003e\u003cbr\u003e\u003c/td\u003e\n \u003ctd style=\"width: 189px;\"\u003e\n \u003cp\u003ePhotographs, acoustic encounter\u0026nbsp;\u003c/p\u003e\n \u003c/td\u003e\n \u003c/tr\u003e\n \u003ctr\u003e\n \u003ctd style=\"width: 509px;\"\u003e\n \u003cp\u003e\u003cstrong\u003eHylidae\u003c/strong\u003e\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 84px;\"\u003e\u003cbr\u003e\u003c/td\u003e\n \u003ctd style=\"width: 107px;\"\u003e\u003cbr\u003e\u003c/td\u003e\n \u003ctd style=\"width: 65px;\"\u003e\u003cbr\u003e\u003c/td\u003e\n \u003ctd style=\"width: 189px;\"\u003e\u003cbr\u003e\u003c/td\u003e\n \u003c/tr\u003e\n \u003ctr\u003e\n \u003ctd style=\"width: 509px;\"\u003e\n \u003cp\u003e\u003cem\u003eDendropsophus columbianus\u003c/em\u003e (Boettger, 1892)\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 84px;\"\u003e\n \u003cp\u003e1, 4\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 107px;\"\u003e\n \u003cp\u003eLC\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 65px;\"\u003e\n \u003cp\u003ex\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 189px;\"\u003e\n \u003cp\u003eAm-186-191, 347-348, 350, visual encounter, Bland\u0026oacute;n-Mar\u0026iacute;n (2006)\u003c/p\u003e\n \u003c/td\u003e\n \u003c/tr\u003e\n \u003ctr\u003e\n \u003ctd style=\"width: 509px;\"\u003e\n \u003cp\u003e\u003cstrong\u003eStrabomantidae\u003c/strong\u003e\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 84px;\"\u003e\u003cbr\u003e\u003c/td\u003e\n \u003ctd style=\"width: 107px;\"\u003e\u003cbr\u003e\u003c/td\u003e\n \u003ctd style=\"width: 65px;\"\u003e\u003cbr\u003e\u003c/td\u003e\n \u003ctd style=\"width: 189px;\"\u003e\u003cbr\u003e\u003c/td\u003e\n \u003c/tr\u003e\n \u003ctr\u003e\n \u003ctd style=\"width: 509px;\"\u003e\n \u003cp\u003e\u003cem\u003ePristimantis achatinus\u003c/em\u003e (Boulenger, 1898)\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 84px;\"\u003e\n \u003cp\u003e1, 2, 3, 4, 5\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 107px;\"\u003e\n \u003cp\u003eLC\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 65px;\"\u003e\u003cbr\u003e\u003c/td\u003e\n \u003ctd style=\"width: 189px;\"\u003e\n \u003cp\u003eAm-349, 353, 1134, 1876, visual encounter, Escobar-Vargas et al. (2016)\u003c/p\u003e\n \u003c/td\u003e\n \u003c/tr\u003e\n \u003ctr\u003e\n \u003ctd style=\"width: 509px;\"\u003e\n \u003cp\u003e\u003cem\u003ePristimantis erythropleura\u003c/em\u003e (Boulenger, 1896)\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 84px;\"\u003e\n \u003cp\u003e3\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 107px;\"\u003e\n \u003cp\u003eLC\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 65px;\"\u003e\n \u003cp\u003ex\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 189px;\"\u003e\n \u003cp\u003eAm-1779, Visual encounter\u003c/p\u003e\n \u003c/td\u003e\n \u003c/tr\u003e\n \u003ctr\u003e\n \u003ctd style=\"width: 509px;\"\u003e\n \u003cp\u003e\u003cem\u003ePristimantis paisa\u003c/em\u003e (Lynch \u0026amp; Ardila-Robayo, 1999)\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 84px;\"\u003e\n \u003cp\u003e1, 2, 3, 4, 5, 6\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 107px;\"\u003e\n \u003cp\u003eLC\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 65px;\"\u003e\n \u003cp\u003ex\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 189px;\"\u003e\n \u003cp\u003eAm-827-830, visual encounter\u003c/p\u003e\n \u003c/td\u003e\n \u003c/tr\u003e\n \u003ctr\u003e\n \u003ctd style=\"width: 509px;\"\u003e\n \u003cp\u003e\u003cem\u003ePristimantis thectopternus\u003c/em\u003e (Lynch, 1975)\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 84px;\"\u003e\n \u003cp\u003e1, 2, 3, 5, 6, 7\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 107px;\"\u003e\n \u003cp\u003eLC\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 65px;\"\u003e\n \u003cp\u003ex\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 189px;\"\u003e\n \u003cp\u003eAm-706, 1871, visual encounter,\u003c/p\u003e\n \u003c/td\u003e\n \u003c/tr\u003e\n \u003ctr\u003e\n \u003ctd style=\"width: 509px;\"\u003e\n \u003cp\u003e\u003cem\u003ePristimantis w-nigrum\u003c/em\u003e (Boettger, 1892)\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 84px;\"\u003e\n \u003cp\u003e1\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 107px;\"\u003e\n \u003cp\u003eLC\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 65px;\"\u003e\n \u003cp\u003e\u0026nbsp;\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 189px;\"\u003e\n \u003cp\u003eToro-Restrepo 2023\u003c/p\u003e\n \u003c/td\u003e\n \u003c/tr\u003e\n \u003ctr\u003e\n \u003ctd style=\"width: 509px;\"\u003e\n \u003cp\u003e\u003cstrong\u003eReptilia, Squamata, Sauria\u003c/strong\u003e\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 84px;\"\u003e\u003cbr\u003e\u003c/td\u003e\n \u003ctd style=\"width: 107px;\"\u003e\u003cbr\u003e\u003c/td\u003e\n \u003ctd style=\"width: 65px;\"\u003e\u003cbr\u003e\u003c/td\u003e\n \u003ctd style=\"width: 189px;\"\u003e\u003cbr\u003e\u003c/td\u003e\n \u003c/tr\u003e\n \u003ctr\u003e\n \u003ctd style=\"width: 509px;\"\u003e\n \u003cp\u003e\u003cstrong\u003eGekkonidae\u003c/strong\u003e\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 84px;\"\u003e\u003cbr\u003e\u003c/td\u003e\n \u003ctd style=\"width: 107px;\"\u003e\u003cbr\u003e\u003c/td\u003e\n \u003ctd style=\"width: 65px;\"\u003e\u003cbr\u003e\u003c/td\u003e\n \u003ctd style=\"width: 189px;\"\u003e\u003cbr\u003e\u003c/td\u003e\n \u003c/tr\u003e\n \u003ctr\u003e\n \u003ctd style=\"width: 509px;\"\u003e\n \u003cp\u003e\u003cem\u003eLepidoblepharis duolepis\u003c/em\u003e Ayala \u0026amp; Castro, 1983\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 84px;\"\u003e\n \u003cp\u003e4\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 107px;\"\u003e\n \u003cp\u003eLC\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 65px;\"\u003e\n \u003cp\u003ex\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 189px;\"\u003e\n \u003cp\u003eR-205, 341, 532-535, visual encounter\u003c/p\u003e\n \u003c/td\u003e\n \u003c/tr\u003e\n \u003ctr\u003e\n \u003ctd style=\"width: 509px;\"\u003e\n \u003cp\u003e\u003cem\u003eLepidoblepharis williamsi\u0026nbsp;\u003c/em\u003eAyala \u0026amp; Serna\u003cem\u003e, 1986\u003c/em\u003e\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 84px;\"\u003e\n \u003cp\u003e1\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 107px;\"\u003e\n \u003cp\u003eEN\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 65px;\"\u003e\n \u003cp\u003ex\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 189px;\"\u003e\n \u003cp\u003eR-210-211, 341, 975-977, visual encounter\u003c/p\u003e\n \u003c/td\u003e\n \u003c/tr\u003e\n \u003ctr\u003e\n \u003ctd style=\"width: 509px;\"\u003e\n \u003cp\u003e\u003cstrong\u003eGymnophthalmidae\u003c/strong\u003e\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 84px;\"\u003e\u003cbr\u003e\u003c/td\u003e\n \u003ctd style=\"width: 107px;\"\u003e\u003cbr\u003e\u003c/td\u003e\n \u003ctd style=\"width: 65px;\"\u003e\u003cbr\u003e\u003c/td\u003e\n \u003ctd style=\"width: 189px;\"\u003e\u003cbr\u003e\u003c/td\u003e\n \u003c/tr\u003e\n \u003ctr\u003e\n \u003ctd style=\"width: 509px;\"\u003e\n \u003cp\u003e\u003cem\u003ePholidobolus marianus\u003c/em\u003e (O\u0026apos;Shaughnessy, 1879)\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 84px;\"\u003e\n \u003cp\u003e1, 2, 4, 5, 6\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 107px;\"\u003e\n \u003cp\u003eLC\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 65px;\"\u003e\u003cbr\u003e\u003c/td\u003e\n \u003ctd style=\"width: 189px;\"\u003e\n \u003cp\u003eR-531, 1039, visual encounter, photographs\u003c/p\u003e\n \u003c/td\u003e\n \u003c/tr\u003e\n \u003ctr\u003e\n \u003ctd style=\"width: 509px;\"\u003e\n \u003cp\u003e\u003cem\u003eRiama columbiana\u003c/em\u003e (Andersson, 1914)\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 84px;\"\u003e\n \u003cp\u003e5, 6\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 107px;\"\u003e\n \u003cp\u003eEN\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 65px;\"\u003e\n \u003cp\u003ex\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 189px;\"\u003e\n \u003cp\u003eR-920, Visual encounter, photographs\u003c/p\u003e\n \u003c/td\u003e\n \u003c/tr\u003e\n \u003ctr\u003e\n \u003ctd style=\"width: 509px;\"\u003e\n \u003cp\u003e\u003cstrong\u003eAnolidae\u003c/strong\u003e\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 84px;\"\u003e\u003cbr\u003e\u003c/td\u003e\n \u003ctd style=\"width: 107px;\"\u003e\u003cbr\u003e\u003c/td\u003e\n \u003ctd style=\"width: 65px;\"\u003e\u003cbr\u003e\u003c/td\u003e\n \u003ctd style=\"width: 189px;\"\u003e\u003cbr\u003e\u003c/td\u003e\n \u003c/tr\u003e\n \u003ctr\u003e\n \u003ctd style=\"width: 509px;\"\u003e\n \u003cp\u003e\u003cem\u003eAnolis antonii\u003c/em\u003e (Boulenger, 1908)\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 84px;\"\u003e\n \u003cp\u003e1, 4, 5\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 107px;\"\u003e\n \u003cp\u003eLC\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 65px;\"\u003e\n \u003cp\u003ex\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 189px;\"\u003e\n \u003cp\u003eR-680-683, visual encounter\u003c/p\u003e\n \u003c/td\u003e\n \u003c/tr\u003e\n \u003ctr\u003e\n \u003ctd style=\"width: 509px;\"\u003e\n \u003cp\u003e\u003cem\u003eAnolis quimbaya\u003c/em\u003e (Moreno-Arias, M\u0026eacute;ndez-Galeano, Beltr\u0026aacute;n \u0026amp; Vargas-Ram\u0026iacute;rez, 2023)\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 84px;\"\u003e\n \u003cp\u003e2, 5, 7\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 107px;\"\u003e\n \u003cp\u003eLC\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 65px;\"\u003e\n \u003cp\u003ex\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 189px;\"\u003e\n \u003cp\u003eR-487, 801, Photographs\u003c/p\u003e\n \u003c/td\u003e\n \u003c/tr\u003e\n \u003ctr\u003e\n \u003ctd style=\"width: 509px;\"\u003e\n \u003cp\u003e\u003cem\u003eAnolis ventrimaculatus\u003c/em\u003e Boulenger, 1911\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 84px;\"\u003e\n \u003cp\u003e1, 3\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 107px;\"\u003e\n \u003cp\u003eLC\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 65px;\"\u003e\u003cbr\u003e\u003c/td\u003e\n \u003ctd style=\"width: 189px;\"\u003e\n \u003cp\u003eR-1190, Visual encounter\u003c/p\u003e\n \u003c/td\u003e\n \u003c/tr\u003e\n \u003ctr\u003e\n \u003ctd style=\"width: 509px;\"\u003e\n \u003cp\u003e\u003cstrong\u003eReptilia, Serpentes\u003c/strong\u003e\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 84px;\"\u003e\u003cbr\u003e\u003c/td\u003e\n \u003ctd style=\"width: 107px;\"\u003e\u003cbr\u003e\u003c/td\u003e\n \u003ctd style=\"width: 65px;\"\u003e\u003cbr\u003e\u003c/td\u003e\n \u003ctd style=\"width: 189px;\"\u003e\u003cbr\u003e\u003c/td\u003e\n \u003c/tr\u003e\n \u003ctr\u003e\n \u003ctd style=\"width: 509px;\"\u003e\n \u003cp\u003e\u003cstrong\u003eColubridae\u003c/strong\u003e\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 84px;\"\u003e\u003cbr\u003e\u003c/td\u003e\n \u003ctd style=\"width: 107px;\"\u003e\u003cbr\u003e\u003c/td\u003e\n \u003ctd style=\"width: 65px;\"\u003e\u003cbr\u003e\u003c/td\u003e\n \u003ctd style=\"width: 189px;\"\u003e\u003cbr\u003e\u003c/td\u003e\n \u003c/tr\u003e\n \u003ctr\u003e\n \u003ctd style=\"width: 509px;\"\u003e\n \u003cp\u003e\u003cem\u003eAtractus biseriatus\u003c/em\u003e Prado, 1941\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 84px;\"\u003e\n \u003cp\u003e1, 5\u0026nbsp;\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 107px;\"\u003e\n \u003cp\u003eDD\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 65px;\"\u003e\n \u003cp\u003ex\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 189px;\"\u003e\n \u003cp\u003eR-530, visual encounter, Photographs\u003c/p\u003e\n \u003c/td\u003e\n \u003c/tr\u003e\n \u003ctr\u003e\n \u003ctd style=\"width: 509px;\"\u003e\n \u003cp\u003e\u003cem\u003eAtractus lehmanni\u003c/em\u003e Boettger, 1898\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 84px;\"\u003e\n \u003cp\u003e1, 5 3\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 107px;\"\u003e\n \u003cp\u003eDD\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 65px;\"\u003e\n \u003cp\u003ex\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 189px;\"\u003e\n \u003cp\u003eR-1026, 1092, 11110, 1139, 1191 visual encounter, Photographs\u003c/p\u003e\n \u003c/td\u003e\n \u003c/tr\u003e\n \u003ctr\u003e\n \u003ctd style=\"width: 509px;\"\u003e\n \u003cp\u003e\u003cem\u003eAtractus manizalesensis\u003c/em\u003e Prado, 1940\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 84px;\"\u003e\n \u003cp\u003e1\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 107px;\"\u003e\n \u003cp\u003eLC\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 65px;\"\u003e\n \u003cp\u003ex\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 189px;\"\u003e\n \u003cp\u003eR-209, visual encounter\u003c/p\u003e\n \u003c/td\u003e\n \u003c/tr\u003e\n \u003ctr\u003e\n \u003ctd style=\"width: 509px;\"\u003e\n \u003cp\u003e\u003cem\u003eChironius monticola\u003c/em\u003e Roze, 1952\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 84px;\"\u003e\n \u003cp\u003e4\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 107px;\"\u003e\n \u003cp\u003eLC\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 65px;\"\u003e\u003cbr\u003e\u003c/td\u003e\n \u003ctd style=\"width: 189px;\"\u003e\n \u003cp\u003eR-186\u003c/p\u003e\n \u003c/td\u003e\n \u003c/tr\u003e\n \u003ctr\u003e\n \u003ctd style=\"width: 509px;\"\u003e\n \u003cp\u003e\u003cem\u003eClelia equatoriana\u003c/em\u003e (Amaral, 1924)\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 84px;\"\u003e\n \u003cp\u003e1, 4\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 107px;\"\u003e\n \u003cp\u003eLC\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 65px;\"\u003e\u003cbr\u003e\u003c/td\u003e\n \u003ctd style=\"width: 189px;\"\u003e\n \u003cp\u003eR-1022, Rojas-Morales (2012)\u003c/p\u003e\n \u003c/td\u003e\n \u003c/tr\u003e\n \u003ctr\u003e\n \u003ctd style=\"width: 509px;\"\u003e\n \u003cp\u003e\u003cem\u003eDipsas sanctijoannis\u003c/em\u003e (Boulenger, 1911)\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 84px;\"\u003e\n \u003cp\u003e4, 5\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 107px;\"\u003e\n \u003cp\u003eLC\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 65px;\"\u003e\n \u003cp\u003ex\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 189px;\"\u003e\n \u003cp\u003ePhotographs, Rojas-Morales \u0026amp; Escobar-Lasso (2010)\u003c/p\u003e\n \u003c/td\u003e\n \u003c/tr\u003e\n \u003ctr\u003e\n \u003ctd style=\"width: 509px;\"\u003e\n \u003cp\u003e\u003cem\u003eErythrolamprus bizona\u003c/em\u003e Jan, 1863\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 84px;\"\u003e\n \u003cp\u003e4\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 107px;\"\u003e\n \u003cp\u003eLC\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 65px;\"\u003e\u003cbr\u003e\u003c/td\u003e\n \u003ctd style=\"width: 189px;\"\u003e\n \u003cp\u003eR-072, 185\u003c/p\u003e\n \u003c/td\u003e\n \u003c/tr\u003e\n \u003ctr\u003e\n \u003ctd style=\"width: 509px;\"\u003e\n \u003cp\u003e\u003cem\u003eErythrolamprus epinephelus\u003c/em\u003e (Cope, 1862)\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 84px;\"\u003e\n \u003cp\u003e1, 5\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 107px;\"\u003e\n \u003cp\u003eLC\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 65px;\"\u003e\u003cbr\u003e\u003c/td\u003e\n \u003ctd style=\"width: 189px;\"\u003e\n \u003cp\u003eR-290, 334, 337; photographs, Rojas-Morales (2012), visual encounter\u003c/p\u003e\n \u003c/td\u003e\n \u003c/tr\u003e\n \u003ctr\u003e\n \u003ctd style=\"width: 509px;\"\u003e\n \u003cp\u003e\u003cem\u003eImantodes cenchoa\u003c/em\u003e (Linnaeus, 1758)\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 84px;\"\u003e\n \u003cp\u003e6\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 107px;\"\u003e\n \u003cp\u003eLC\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 65px;\"\u003e\u003cbr\u003e\u003c/td\u003e\n \u003ctd style=\"width: 189px;\"\u003e\n \u003cp\u003eR-047, photographs, Rojas-Morales et al. (2014)\u003c/p\u003e\n \u003c/td\u003e\n \u003c/tr\u003e\n \u003ctr\u003e\n \u003ctd style=\"width: 509px;\"\u003e\n \u003cp\u003e\u003cem\u003eLampropeltis micropholis\u003c/em\u003e (Cope, 1860)\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 84px;\"\u003e\n \u003cp\u003e5\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 107px;\"\u003e\n \u003cp\u003eLC\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 65px;\"\u003e\u003cbr\u003e\u003c/td\u003e\n \u003ctd style=\"width: 189px;\"\u003e\n \u003cp\u003ePhotographs, Rojas-Morales (2012)\u0026nbsp;\u003c/p\u003e\n \u003c/td\u003e\n \u003c/tr\u003e\n \u003ctr\u003e\n \u003ctd style=\"width: 509px;\"\u003e\n \u003cp\u003e\u003cstrong\u003eElapidae\u003c/strong\u003e\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 84px;\"\u003e\u003cbr\u003e\u003c/td\u003e\n \u003ctd style=\"width: 107px;\"\u003e\u003cbr\u003e\u003c/td\u003e\n \u003ctd style=\"width: 65px;\"\u003e\u003cbr\u003e\u003c/td\u003e\n \u003ctd style=\"width: 189px;\"\u003e\u003cbr\u003e\u003c/td\u003e\n \u003c/tr\u003e\n \u003ctr\u003e\n \u003ctd style=\"width: 509px;\"\u003e\n \u003cp\u003e\u003cem\u003eMicrurus mipartitus\u003c/em\u003e (Dum\u0026eacute;ril, Bibron \u0026amp; Dum\u0026eacute;ril, 1854)\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 84px;\"\u003e\n \u003cp\u003e4\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 107px;\"\u003e\n \u003cp\u003eLC\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 65px;\"\u003e\u003cbr\u003e\u003c/td\u003e\n \u003ctd style=\"width: 189px;\"\u003e\n \u003cp\u003eR-104\u003c/p\u003e\n \u003c/td\u003e\n \u003c/tr\u003e\n \u003ctr\u003e\n \u003ctd style=\"width: 509px;\"\u003e\n \u003cp\u003e\u003cstrong\u003eViperidae\u003c/strong\u003e\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 84px;\"\u003e\u003cbr\u003e\u003c/td\u003e\n \u003ctd style=\"width: 107px;\"\u003e\u003cbr\u003e\u003c/td\u003e\n \u003ctd style=\"width: 65px;\"\u003e\u003cbr\u003e\u003c/td\u003e\n \u003ctd style=\"width: 189px;\"\u003e\u003cbr\u003e\u003c/td\u003e\n \u003c/tr\u003e\n \u003ctr\u003e\n \u003ctd style=\"width: 509px;\"\u003e\n \u003cp\u003e\u003cem\u003eBothriechis schlegelii\u003c/em\u003e (Berthold, 1846)\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 84px;\"\u003e\n \u003cp\u003e4, 5\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 107px;\"\u003e\n \u003cp\u003eLC\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 65px;\"\u003e\u003cbr\u003e\u003c/td\u003e\n \u003ctd style=\"width: 189px;\"\u003e\n \u003cp\u003eVisual encounter, photographs\u003c/p\u003e\n \u003c/td\u003e\n \u003c/tr\u003e\n \u003ctr\u003e\n \u003ctd style=\"width: 509px;\"\u003e\n \u003cp\u003e\u003cstrong\u003eLeptotyphlopidae\u003c/strong\u003e\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 84px;\"\u003e\u003cbr\u003e\u003c/td\u003e\n \u003ctd style=\"width: 107px;\"\u003e\u003cbr\u003e\u003c/td\u003e\n \u003ctd style=\"width: 65px;\"\u003e\u003cbr\u003e\u003c/td\u003e\n \u003ctd style=\"width: 189px;\"\u003e\u003cbr\u003e\u003c/td\u003e\n \u003c/tr\u003e\n \u003ctr\u003e\n \u003ctd style=\"width: 509px;\"\u003e\n \u003cp\u003e\u003cem\u003eTrilepida joshuai\u0026nbsp;\u003c/em\u003e(Dunn, 1944)\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 84px;\"\u003e\n \u003cp\u003e1, 5\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 107px;\"\u003e\n \u003cp\u003eLC\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 65px;\"\u003e\n \u003cp\u003ex\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 189px;\"\u003e\n \u003cp\u003eR-162, 468, 1249, photographs, Rojas-Morales (2012), Rojas-Morales \u0026amp; Gonz\u0026aacute;les-D\u0026uacute;ran (2011)\u003c/p\u003e\n \u003c/td\u003e\n \u003c/tr\u003e\n \u003c/tbody\u003e\n \u003c/table\u003e\n\u003c/div\u003e\n\u003cp\u003e\u0026nbsp;\u003c/p\u003e\n\u003cp\u003e\u003cstrong\u003eTable 2\u0026nbsp;\u003c/strong\u003eAlpha diversity of amphibians and reptiles at six localities of Manizales, Central Andes of Colombia: (1) Jard\u0026iacute;n Bot\u0026aacute;nico, (2) Bosque Popular El Prado, (3) Cerro Sancancio, (4) Los Alc\u0026aacute;zares-Arenillo, (5) Los Yarumos, (6) Montele\u0026oacute;n. Observed values for three diversity indices are presented\u003c/p\u003e\n\u003cdiv align=\"\"\u003e\n \u003ctable border=\"1\" cellspacing=\"0\" cellpadding=\"0\" width=\"381\"\u003e\n \u003ctbody\u003e\n \u003ctr\u003e\n \u003ctd style=\"width: 76px;\"\u003e\u003cbr\u003e\u003c/td\u003e\n \u003ctd style=\"width: 130px;\"\u003e\u003cbr\u003e\u003c/td\u003e\n \u003ctd style=\"width: 96px;\"\u003e\n \u003cp\u003e\u003cstrong\u003eAmphibians\u003c/strong\u003e\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 80px;\"\u003e\n \u003cp\u003e\u003cstrong\u003eReptiles\u003c/strong\u003e\u003c/p\u003e\n \u003c/td\u003e\n \u003c/tr\u003e\n \u003ctr\u003e\n \u003ctd style=\"width: 76px;\"\u003e\n \u003cp\u003e\u003cstrong\u003eSite\u003c/strong\u003e\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 130px;\"\u003e\n \u003cp\u003e\u003cstrong\u003eIndex\u003c/strong\u003e\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 96px;\"\u003e\n \u003cp\u003e\u003cstrong\u003eObserved\u003c/strong\u003e\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 80px;\"\u003e\n \u003cp\u003e\u003cstrong\u003eObserved\u003c/strong\u003e\u003c/p\u003e\n \u003c/td\u003e\n \u003c/tr\u003e\n \u003ctr\u003e\n \u003ctd rowspan=\"3\" style=\"width: 76px;\"\u003e\n \u003cp\u003e\u003cstrong\u003e1\u003c/strong\u003e\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 130px;\"\u003e\n \u003cp\u003eSpecies richness\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 96px;\"\u003e\n \u003cp\u003e5.0000\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 80px;\"\u003e\n \u003cp\u003e4.0000\u003c/p\u003e\n \u003c/td\u003e\n \u003c/tr\u003e\n \u003ctr\u003e\n \u003ctd style=\"width: 130px;\"\u003e\n \u003cp\u003eShannon diversity\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 96px;\"\u003e\n \u003cp\u003e4.3285\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 80px;\"\u003e\n \u003cp\u003e2.9543\u003c/p\u003e\n \u003c/td\u003e\n \u003c/tr\u003e\n \u003ctr\u003e\n \u003ctd style=\"width: 130px;\"\u003e\n \u003cp\u003eSimpson diversity\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 96px;\"\u003e\n \u003cp\u003e3.8136\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 80px;\"\u003e\n \u003cp\u003e2.5862\u003c/p\u003e\n \u003c/td\u003e\n \u003c/tr\u003e\n \u003ctr\u003e\n \u003ctd rowspan=\"3\" style=\"width: 76px;\"\u003e\n \u003cp\u003e\u003cstrong\u003e2\u003c/strong\u003e\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 130px;\"\u003e\n \u003cp\u003eSpecies richness\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 96px;\"\u003e\n \u003cp\u003e4.0000\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 80px;\"\u003e\n \u003cp\u003e1.0000\u003c/p\u003e\n \u003c/td\u003e\n \u003c/tr\u003e\n \u003ctr\u003e\n \u003ctd style=\"width: 130px;\"\u003e\n \u003cp\u003eShannon diversity\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 96px;\"\u003e\n \u003cp\u003e2.5335\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 80px;\"\u003e\n \u003cp\u003e1.0000\u003c/p\u003e\n \u003c/td\u003e\n \u003c/tr\u003e\n \u003ctr\u003e\n \u003ctd style=\"width: 130px;\"\u003e\n \u003cp\u003eSimpson diversity\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 96px;\"\u003e\n \u003cp\u003e2.1627\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 80px;\"\u003e\n \u003cp\u003e1.0000\u003c/p\u003e\n \u003c/td\u003e\n \u003c/tr\u003e\n \u003ctr\u003e\n \u003ctd rowspan=\"3\" style=\"width: 76px;\"\u003e\n \u003cp\u003e\u003cstrong\u003e3\u003c/strong\u003e\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 130px;\"\u003e\n \u003cp\u003eSpecies richness\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 96px;\"\u003e\n \u003cp\u003e6.0000\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 80px;\"\u003e\n \u003cp\u003e4.0000\u003c/p\u003e\n \u003c/td\u003e\n \u003c/tr\u003e\n \u003ctr\u003e\n \u003ctd style=\"width: 130px;\"\u003e\n \u003cp\u003eShannon diversity\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 96px;\"\u003e\n \u003cp\u003e2.8346\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 80px;\"\u003e\n \u003cp\u003e3.0678\u003c/p\u003e\n \u003c/td\u003e\n \u003c/tr\u003e\n \u003ctr\u003e\n \u003ctd style=\"width: 130px;\"\u003e\n \u003cp\u003eSimpson diversity\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 96px;\"\u003e\n \u003cp\u003e1.9042\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 80px;\"\u003e\n \u003cp\u003e2.5745\u003c/p\u003e\n \u003c/td\u003e\n \u003c/tr\u003e\n \u003ctr\u003e\n \u003ctd rowspan=\"3\" style=\"width: 76px;\"\u003e\n \u003cp\u003e\u003cstrong\u003e4\u003c/strong\u003e\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 130px;\"\u003e\n \u003cp\u003eSpecies richness\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 96px;\"\u003e\n \u003cp\u003e4.0000\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 80px;\"\u003e\n \u003cp\u003e5.0000\u003c/p\u003e\n \u003c/td\u003e\n \u003c/tr\u003e\n \u003ctr\u003e\n \u003ctd style=\"width: 130px;\"\u003e\n \u003cp\u003eShannon diversity\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 96px;\"\u003e\n \u003cp\u003e2.9486\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 80px;\"\u003e\n \u003cp\u003e4.0579\u003c/p\u003e\n \u003c/td\u003e\n \u003c/tr\u003e\n \u003ctr\u003e\n \u003ctd style=\"width: 130px;\"\u003e\n \u003cp\u003eSimpson diversity\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 96px;\"\u003e\n \u003cp\u003e2.4994\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 80px;\"\u003e\n \u003cp\u003e3.6119\u003c/p\u003e\n \u003c/td\u003e\n \u003c/tr\u003e\n \u003ctr\u003e\n \u003ctd rowspan=\"3\" style=\"width: 76px;\"\u003e\n \u003cp\u003e\u003cstrong\u003e5\u003c/strong\u003e\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 130px;\"\u003e\n \u003cp\u003eSpecies richness\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 96px;\"\u003e\n \u003cp\u003e4.0000\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 80px;\"\u003e\n \u003cp\u003e3.0000\u003c/p\u003e\n \u003c/td\u003e\n \u003c/tr\u003e\n \u003ctr\u003e\n \u003ctd style=\"width: 130px;\"\u003e\n \u003cp\u003eShannon diversity\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 96px;\"\u003e\n \u003cp\u003e2.0042\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 80px;\"\u003e\n \u003cp\u003e2.7495\u003c/p\u003e\n \u003c/td\u003e\n \u003c/tr\u003e\n \u003ctr\u003e\n \u003ctd style=\"width: 130px;\"\u003e\n \u003cp\u003eSimpson diversity\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 96px;\"\u003e\n \u003cp\u003e1.5238\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 80px;\"\u003e\n \u003cp\u003e2.5714\u003c/p\u003e\n \u003c/td\u003e\n \u003c/tr\u003e\n \u003ctr\u003e\n \u003ctd rowspan=\"3\" style=\"width: 76px;\"\u003e\n \u003cp\u003e\u003cstrong\u003e6\u003c/strong\u003e\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 130px;\"\u003e\n \u003cp\u003eSpecies richness\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 96px;\"\u003e\n \u003cp\u003e3.0000\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 80px;\"\u003e\n \u003cp\u003e2.0000\u003c/p\u003e\n \u003c/td\u003e\n \u003c/tr\u003e\n \u003ctr\u003e\n \u003ctd style=\"width: 130px;\"\u003e\n \u003cp\u003eShannon diversity\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 96px;\"\u003e\n \u003cp\u003e1.8946\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 80px;\"\u003e\n \u003cp\u003e2.0000\u003c/p\u003e\n \u003c/td\u003e\n \u003c/tr\u003e\n \u003ctr\u003e\n \u003ctd style=\"width: 130px;\"\u003e\n \u003cp\u003eSimpson diversity\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 96px;\"\u003e\n \u003cp\u003e1.5152\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 80px;\"\u003e\n \u003cp\u003e2.0000\u003c/p\u003e\n \u003c/td\u003e\n \u003c/tr\u003e\n \u003c/tbody\u003e\n \u003c/table\u003e\n\u003c/div\u003e\n\u003cp\u003e\u0026nbsp;\u0026nbsp;\u003c/p\u003e\n\u003cp\u003e\u003cstrong\u003eTable 3\u0026nbsp;\u003c/strong\u003eAmphibian and reptile species are recorded in urban areas or surrounding Ecoparks or areas of environmental interest in Manizales, along with their respective Local Climate Zone (LCZ). \u0026nbsp;LCZ 2: Compact midrise; LCZ 3: Compact lowrise; LCZ 5: Open midrise; LCZ 6: Open lowrise; LCZ 9: Sparsely built: LCZ A: Dense trees; LCZ B; Scattered trees; LCZ D: Low plants. Records taken from the Amphibian and Reptile Collection of the MHN-UCa\u003c/p\u003e\n\u003cdiv align=\"\"\u003e\n \u003ctable border=\"0\" cellspacing=\"0\" cellpadding=\"0\" width=\"564\"\u003e\n \u003ctbody\u003e\n \u003ctr\u003e\n \u003ctd style=\"width: 483px;\"\u003e\n \u003cp\u003e\u003cstrong\u003eTaxon\u003c/strong\u003e\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 81px;\"\u003e\n \u003cp\u003e\u003cstrong\u003eLCZ\u003c/strong\u003e\u003c/p\u003e\n \u003c/td\u003e\n \u003c/tr\u003e\n \u003ctr\u003e\n \u003ctd style=\"width: 483px;\"\u003e\n \u003cp\u003e\u003cstrong\u003eAmphibia\u003c/strong\u003e\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 81px;\"\u003e\u003cbr\u003e\u003c/td\u003e\n \u003c/tr\u003e\n \u003ctr\u003e\n \u003ctd style=\"width: 483px;\"\u003e\n \u003cp\u003e\u003cstrong\u003eAnura\u003c/strong\u003e\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 81px;\"\u003e\u003cbr\u003e\u003c/td\u003e\n \u003c/tr\u003e\n \u003ctr\u003e\n \u003ctd style=\"width: 483px;\"\u003e\n \u003cp\u003e\u003cstrong\u003eBufonidae\u003c/strong\u003e\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 81px;\"\u003e\u003cbr\u003e\u003c/td\u003e\n \u003c/tr\u003e\n \u003ctr\u003e\n \u003ctd style=\"width: 483px;\"\u003e\n \u003cp\u003e\u003cem\u003eRhinella horribilis\u0026nbsp;\u003c/em\u003e(Wiegmann, 1833)\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 81px;\"\u003e\n \u003cp\u003eLCZ 6\u003c/p\u003e\n \u003c/td\u003e\n \u003c/tr\u003e\n \u003ctr\u003e\n \u003ctd style=\"width: 483px;\"\u003e\n \u003cp\u003e\u003cstrong\u003eReptilia\u003c/strong\u003e\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 81px;\"\u003e\u003cbr\u003e\u003c/td\u003e\n \u003c/tr\u003e\n \u003ctr\u003e\n \u003ctd style=\"width: 483px;\"\u003e\n \u003cp\u003e\u003cstrong\u003eSquamata\u003c/strong\u003e\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 81px;\"\u003e\u003cbr\u003e\u003c/td\u003e\n \u003c/tr\u003e\n \u003ctr\u003e\n \u003ctd style=\"width: 483px;\"\u003e\n \u003cp\u003e\u003cstrong\u003eSauria\u003c/strong\u003e\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 81px;\"\u003e\u003cbr\u003e\u003c/td\u003e\n \u003c/tr\u003e\n \u003ctr\u003e\n \u003ctd style=\"width: 483px;\"\u003e\n \u003cp\u003e\u003cstrong\u003eGekkonidae\u003c/strong\u003e\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 81px;\"\u003e\u003cbr\u003e\u003c/td\u003e\n \u003c/tr\u003e\n \u003ctr\u003e\n \u003ctd style=\"width: 483px;\"\u003e\n \u003cp\u003e\u003cem\u003eHemidactylus garnotii\u003c/em\u003e Dum\u0026eacute;ril \u0026amp; Bibron, 1836\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 81px;\"\u003e\n \u003cp\u003eLCZ 3, LCZ 5\u003c/p\u003e\n \u003c/td\u003e\n \u003c/tr\u003e\n \u003ctr\u003e\n \u003ctd style=\"width: 483px;\"\u003e\n \u003cp\u003e\u003cstrong\u003eGymnophthalmidae\u003c/strong\u003e\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 81px;\"\u003e\u003cbr\u003e\u003c/td\u003e\n \u003c/tr\u003e\n \u003ctr\u003e\n \u003ctd style=\"width: 483px;\"\u003e\n \u003cp\u003e\u003cem\u003ePholidobolus marianus\u003c/em\u003e (Ruthven, 1921)\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 81px;\"\u003e\n \u003cp\u003eLCZ 2, LCZ 3, LCZ 5, LCZ 9\u003c/p\u003e\n \u003c/td\u003e\n \u003c/tr\u003e\n \u003ctr\u003e\n \u003ctd style=\"width: 483px;\"\u003e\n \u003cp\u003e\u003cstrong\u003eAnolidae\u003c/strong\u003e\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 81px;\"\u003e\u003cbr\u003e\u003c/td\u003e\n \u003c/tr\u003e\n \u003ctr\u003e\n \u003ctd style=\"width: 483px;\"\u003e\n \u003cp\u003e\u003cem\u003eAnolis antonii\u003c/em\u003e (Boulenger, 1908)\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 81px;\"\u003e\n \u003cp\u003eLCZ 3\u003c/p\u003e\n \u003c/td\u003e\n \u003c/tr\u003e\n \u003ctr\u003e\n \u003ctd style=\"width: 483px;\"\u003e\n \u003cp\u003e\u003cstrong\u003eSerpentes\u003c/strong\u003e\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 81px;\"\u003e\u003cbr\u003e\u003c/td\u003e\n \u003c/tr\u003e\n \u003ctr\u003e\n \u003ctd style=\"width: 483px;\"\u003e\n \u003cp\u003e\u003cstrong\u003eColubridae\u003c/strong\u003e\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 81px;\"\u003e\u003cbr\u003e\u003c/td\u003e\n \u003c/tr\u003e\n \u003ctr\u003e\n \u003ctd style=\"width: 483px;\"\u003e\n \u003cp\u003e\u003cem\u003eAtractus biseriatus\u003c/em\u003e Prado, 1941\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 81px;\"\u003e\n \u003cp\u003eLCZ 2, LCZ 3, LCZ 6\u003c/p\u003e\n \u003c/td\u003e\n \u003c/tr\u003e\n \u003ctr\u003e\n \u003ctd style=\"width: 483px;\"\u003e\n \u003cp\u003e\u003cem\u003eAtractus lehmanni\u003c/em\u003e Boettger, 1898\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 81px;\"\u003e\n \u003cp\u003eLCZ 3, LCZ 9, LCZ B\u003c/p\u003e\n \u003c/td\u003e\n \u003c/tr\u003e\n \u003ctr\u003e\n \u003ctd style=\"width: 483px;\"\u003e\n \u003cp\u003e\u003cem\u003eAtractus manizalesensis\u003c/em\u003e Prado, 1940\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 81px;\"\u003e\n \u003cp\u003eLCZ 2, LCZ 3, LCZ 9\u003c/p\u003e\n \u003c/td\u003e\n \u003c/tr\u003e\n \u003ctr\u003e\n \u003ctd style=\"width: 483px;\"\u003e\n \u003cp\u003e\u003cem\u003eChironius monticola\u003c/em\u003e Roze, 1952\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 81px;\"\u003e\n \u003cp\u003eLCZ 6\u003c/p\u003e\n \u003c/td\u003e\n \u003c/tr\u003e\n \u003ctr\u003e\n \u003ctd style=\"width: 483px;\"\u003e\n \u003cp\u003e\u003cem\u003eClelia equatoriana\u003c/em\u003e (Amaral, 1924)\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 81px;\"\u003e\n \u003cp\u003eLCZ 3, LCZ B\u003c/p\u003e\n \u003c/td\u003e\n \u003c/tr\u003e\n \u003ctr\u003e\n \u003ctd style=\"width: 483px;\"\u003e\n \u003cp\u003e\u003cem\u003eDipsas sanctijoannis\u003c/em\u003e (Boulenger, 1911)\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 81px;\"\u003e\n \u003cp\u003eLCZ A, LCZ D\u003c/p\u003e\n \u003c/td\u003e\n \u003c/tr\u003e\n \u003ctr\u003e\n \u003ctd style=\"width: 483px;\"\u003e\n \u003cp\u003e\u003cem\u003eErythrolamprus bizona\u003c/em\u003e Jan, 1863\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 81px;\"\u003e\n \u003cp\u003eLCZ 3, LCZ 9\u003c/p\u003e\n \u003c/td\u003e\n \u003c/tr\u003e\n \u003ctr\u003e\n \u003ctd style=\"width: 483px;\"\u003e\n \u003cp\u003e\u003cem\u003eErythrolamprus epinephelus\u003c/em\u003e (Cope, 1862)\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 81px;\"\u003e\n \u003cp\u003eLCZ 2, LCZ 3\u003c/p\u003e\n \u003c/td\u003e\n \u003c/tr\u003e\n \u003ctr\u003e\n \u003ctd style=\"width: 483px;\"\u003e\n \u003cp\u003e\u003cem\u003eLampropeltis micropholis\u003c/em\u003e (Cope, 1860)\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 81px;\"\u003e\n \u003cp\u003eLCZ A\u003c/p\u003e\n \u003c/td\u003e\n \u003c/tr\u003e\n \u003ctr\u003e\n \u003ctd style=\"width: 483px;\"\u003e\n \u003cp\u003e\u003cstrong\u003eElapidae\u003c/strong\u003e\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 81px;\"\u003e\u003cbr\u003e\u003c/td\u003e\n \u003c/tr\u003e\n \u003ctr\u003e\n \u003ctd style=\"width: 483px;\"\u003e\n \u003cp\u003e\u003cem\u003eMicrurus mipartitus\u003c/em\u003e (Dum\u0026eacute;ril, Bibron \u0026amp; Dum\u0026eacute;ril, 1854)\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 81px;\"\u003e\n \u003cp\u003eLCZ D\u003c/p\u003e\n \u003c/td\u003e\n \u003c/tr\u003e\n \u003ctr\u003e\n \u003ctd style=\"width: 483px;\"\u003e\n \u003cp\u003e\u003cstrong\u003eLeptotyphlopidae\u003c/strong\u003e\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 81px;\"\u003e\u003cbr\u003e\u003c/td\u003e\n \u003c/tr\u003e\n \u003ctr\u003e\n \u003ctd style=\"width: 483px;\"\u003e\n \u003cp\u003e\u003cem\u003eTrilepida joshuai\u0026nbsp;\u003c/em\u003e(Dunn, 1944)\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 81px;\"\u003e\n \u003cp\u003eLCZ 3\u003c/p\u003e\n \u003c/td\u003e\n \u003c/tr\u003e\n \u003c/tbody\u003e\n \u003c/table\u003e\n\u003c/div\u003e\n\u003cp\u003e\u0026nbsp;\u0026nbsp;\u003c/p\u003e\n\u003cp\u003e\u003cstrong\u003eTable 4\u0026nbsp;\u003c/strong\u003eComponents of beta diversity for amphibians and reptiles among sampling sites within the municipality of Manizales, Central Andes of Colombia\u003c/p\u003e\n\u003cdiv align=\"\"\u003e\n \u003ctable border=\"0\" cellspacing=\"0\" cellpadding=\"0\" width=\"433\"\u003e\n \u003ctbody\u003e\n \u003ctr\u003e\n \u003ctd style=\"width: 91px;\"\u003e\n \u003cp\u003e\u003cstrong\u003eTaxon\u003c/strong\u003e\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 137px;\"\u003e\n \u003cp\u003e\u003cstrong\u003eTotal beta diversity (\u0026beta;JAC)\u003c/strong\u003e\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 91px;\"\u003e\n \u003cp\u003e\u003cstrong\u003e\u0026nbsp;Turnover (\u0026beta;JTU)\u003c/strong\u003e\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 115px;\"\u003e\n \u003cp\u003e\u003cstrong\u003eNestedness (\u0026beta;JNE)\u003c/strong\u003e\u003c/p\u003e\n \u003c/td\u003e\n \u003c/tr\u003e\n \u003ctr\u003e\n \u003ctd style=\"width: 91px;\"\u003e\n \u003cp\u003eAmphibians\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd valign=\"top\" style=\"width: 137px;\"\u003e\n \u003cp\u003e0.6274\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd valign=\"top\" style=\"width: 91px;\"\u003e\n \u003cp\u003e0.4242\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd valign=\"top\" style=\"width: 115px;\"\u003e\n \u003cp\u003e0.2032\u003c/p\u003e\n \u003c/td\u003e\n \u003c/tr\u003e\n \u003ctr\u003e\n \u003ctd style=\"width: 91px;\"\u003e\n \u003cp\u003eReptiles\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd valign=\"top\" style=\"width: 137px;\"\u003e\n \u003cp\u003e0.8548\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd valign=\"top\" style=\"width: 91px;\"\u003e\n \u003cp\u003e0.7429\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd valign=\"top\" style=\"width: 115px;\"\u003e\n \u003cp\u003e0.1120\u003c/p\u003e\n \u003c/td\u003e\n \u003c/tr\u003e\n \u003c/tbody\u003e\n \u003c/table\u003e\n\u003c/div\u003e\n\u003cp\u003e\u0026nbsp;\u003cstrong\u003e\u003c/strong\u003e\u0026nbsp;\u003c/p\u003e\n\u003cp\u003e\u003cstrong\u003eTable 5\u0026nbsp;\u003c/strong\u003eCharacterization of potential corridors between Ecoparks and areas of environmental interest in Manizales according to their LCZ composition. LCZ 2: Compact midrise; LCZ 3: Compact lowrise; LCZ 5: Open midrise; LCZ 6: Open lowrise; LCZ 8: Large lowrise; LCZ 9: Sparsely built: LCZ A: Dense trees; LCZ B; Scattered trees; LCZ D: Low plants; LCZ F: Bare soil or sand\u003c/p\u003e\n\u003ctable border=\"1\" cellspacing=\"0\" cellpadding=\"0\" width=\"841\" class=\"fr-table-selection-hover\"\u003e\n \u003ctbody\u003e\n \u003ctr\u003e\n \u003ctd style=\"width: 37px;\"\u003e\n \u003cp\u003e\u003cstrong\u003eID\u003c/strong\u003e\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 208px;\"\u003e\n \u003cp\u003e\u003cstrong\u003ePotential corridors\u003c/strong\u003e\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 85px;\"\u003e\n \u003cp\u003e\u003cstrong\u003eTotal linear distance (m)\u003c/strong\u003e\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 85px;\"\u003e\n \u003cp\u003e\u003cstrong\u003eLCZ \u0026nbsp; \u0026nbsp; \u0026nbsp; \u0026nbsp; \u0026nbsp; \u0026nbsp; \u0026nbsp; \u0026nbsp; \u0026nbsp;Built form\u003c/strong\u003e\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 95px;\"\u003e\n \u003cp\u003e\u003cstrong\u003eBuilt distance (m)\u003c/strong\u003e\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 77px;\"\u003e\n \u003cp\u003e\u003cstrong\u003eBuilt percentage\u003c/strong\u003e\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 84px;\"\u003e\n \u003cp\u003e\u003cstrong\u003eLCZ \u0026nbsp; \u0026nbsp; \u0026nbsp; \u0026nbsp; \u0026nbsp; \u0026nbsp; \u0026nbsp; \u0026nbsp; \u0026nbsp; \u0026nbsp; \u0026nbsp; \u0026nbsp; \u0026nbsp; \u0026nbsp; \u0026nbsp; \u0026nbsp; \u0026nbsp; \u0026nbsp; \u0026nbsp; \u0026nbsp; \u0026nbsp; \u0026nbsp; \u0026nbsp; \u0026nbsp; \u0026nbsp; \u0026nbsp; \u0026nbsp;Land Cover\u003c/strong\u003e\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 85px;\"\u003e\n \u003cp\u003e\u003cstrong\u003eCover distance (m)\u003c/strong\u003e\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 85px;\"\u003e\n \u003cp\u003e\u003cstrong\u003eCover percentage\u003c/strong\u003e\u003c/p\u003e\n \u003c/td\u003e\n \u003c/tr\u003e\n \u003ctr\u003e\n \u003ctd style=\"width: 37px;\"\u003e\n \u003cp\u003e\u003cstrong\u003e1\u003c/strong\u003e\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 208px;\"\u003e\n \u003cp\u003eJard\u0026iacute;n Bot\u0026aacute;nico - Cerro Sancancio\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 85px;\"\u003e\n \u003cp\u003e283\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 85px;\"\u003e\n \u003cp\u003e2, 3, 9\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 95px;\"\u003e\n \u003cp\u003e114.57\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 77px;\"\u003e\n \u003cp\u003e40.48%\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 84px;\"\u003e\n \u003cp\u003eA, B, D\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 85px;\"\u003e\n \u003cp\u003e168.43\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 85px;\"\u003e\n \u003cp\u003e59.52%\u003c/p\u003e\n \u003c/td\u003e\n \u003c/tr\u003e\n \u003ctr\u003e\n \u003ctd style=\"width: 37px;\"\u003e\n \u003cp\u003e\u003cstrong\u003e2\u003c/strong\u003e\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 208px;\"\u003e\n \u003cp\u003eJard\u0026iacute;n Bot\u0026aacute;nico - Cerro Sancancio\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 85px;\"\u003e\n \u003cp\u003e319\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 85px;\"\u003e\n \u003cp\u003e2, 3\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 95px;\"\u003e\n \u003cp\u003e270.00\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 77px;\"\u003e\n \u003cp\u003e84.64%\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 84px;\"\u003e\n \u003cp\u003eA\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 85px;\"\u003e\n \u003cp\u003e49.00\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 85px;\"\u003e\n \u003cp\u003e15.36%\u003c/p\u003e\n \u003c/td\u003e\n \u003c/tr\u003e\n \u003ctr\u003e\n \u003ctd style=\"width: 37px;\"\u003e\n \u003cp\u003e\u003cstrong\u003e3\u003c/strong\u003e\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 208px;\"\u003e\n \u003cp\u003eJard\u0026iacute;n Bot\u0026aacute;nico - Cerro Sancancio\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 85px;\"\u003e\n \u003cp\u003e391\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 85px;\"\u003e\n \u003cp\u003e2, 3, 5\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 95px;\"\u003e\n \u003cp\u003e259.90\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 77px;\"\u003e\n \u003cp\u003e66.47%\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 84px;\"\u003e\n \u003cp\u003eA, B, D\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 85px;\"\u003e\n \u003cp\u003e131.10\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 85px;\"\u003e\n \u003cp\u003e33.53%\u003c/p\u003e\n \u003c/td\u003e\n \u003c/tr\u003e\n \u003ctr\u003e\n \u003ctd style=\"width: 37px;\"\u003e\n \u003cp\u003e\u003cstrong\u003e4\u003c/strong\u003e\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 208px;\"\u003e\n \u003cp\u003eYarumos - Montele\u0026oacute;n\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 85px;\"\u003e\n \u003cp\u003e556\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 85px;\"\u003e\n \u003cp\u003e2, 3, 5, 6, 8, 9\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 95px;\"\u003e\n \u003cp\u003e465.80\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 77px;\"\u003e\n \u003cp\u003e83.78%\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 84px;\"\u003e\n \u003cp\u003eB, D\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 85px;\"\u003e\n \u003cp\u003e90.20\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 85px;\"\u003e\n \u003cp\u003e16.22%\u003c/p\u003e\n \u003c/td\u003e\n \u003c/tr\u003e\n \u003ctr\u003e\n \u003ctd style=\"width: 37px;\"\u003e\n \u003cp\u003e\u003cstrong\u003e5\u003c/strong\u003e\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 208px;\"\u003e\n \u003cp\u003eYarumos - Montele\u0026oacute;n\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 85px;\"\u003e\n \u003cp\u003e580\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 85px;\"\u003e\n \u003cp\u003e2, 3, 5, 6, 8, 9\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 95px;\"\u003e\n \u003cp\u003e504.10\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 77px;\"\u003e\n \u003cp\u003e86.91%\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 84px;\"\u003e\n \u003cp\u003eB, D\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 85px;\"\u003e\n \u003cp\u003e75.90\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 85px;\"\u003e\n \u003cp\u003e13.09%\u003c/p\u003e\n \u003c/td\u003e\n \u003c/tr\u003e\n \u003ctr\u003e\n \u003ctd style=\"width: 37px;\"\u003e\n \u003cp\u003e\u003cstrong\u003e6\u003c/strong\u003e\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 208px;\"\u003e\n \u003cp\u003eYarumos - Montele\u0026oacute;n\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 85px;\"\u003e\n \u003cp\u003e1854\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 85px;\"\u003e\n \u003cp\u003e3, 9\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 95px;\"\u003e\n \u003cp\u003e199.30\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 77px;\"\u003e\n \u003cp\u003e10.75%\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 84px;\"\u003e\n \u003cp\u003eA, B, D\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 85px;\"\u003e\n \u003cp\u003e1654.70\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 85px;\"\u003e\n \u003cp\u003e89.25%\u003c/p\u003e\n \u003c/td\u003e\n \u003c/tr\u003e\n \u003ctr\u003e\n \u003ctd style=\"width: 37px;\"\u003e\n \u003cp\u003e\u003cstrong\u003e7\u003c/strong\u003e\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 208px;\"\u003e\n \u003cp\u003eYarumos - Montele\u0026oacute;n\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 85px;\"\u003e\n \u003cp\u003e652\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 85px;\"\u003e\n \u003cp\u003e2, 3, 6, 9\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 95px;\"\u003e\n \u003cp\u003e185.10\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 77px;\"\u003e\n \u003cp\u003e28.39%\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 84px;\"\u003e\n \u003cp\u003eA, B, D\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 85px;\"\u003e\n \u003cp\u003e466.90\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 85px;\"\u003e\n \u003cp\u003e71.61%\u003c/p\u003e\n \u003c/td\u003e\n \u003c/tr\u003e\n \u003ctr\u003e\n \u003ctd style=\"width: 37px;\"\u003e\n \u003cp\u003e\u003cstrong\u003e8\u003c/strong\u003e\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 208px;\"\u003e\n \u003cp\u003eYarumos - Montele\u0026oacute;n\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 85px;\"\u003e\n \u003cp\u003e3254\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 85px;\"\u003e\n \u003cp\u003e8, 9\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 95px;\"\u003e\n \u003cp\u003e259.40\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 77px;\"\u003e\n \u003cp\u003e7.97%\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 84px;\"\u003e\n \u003cp\u003eA, B, D, F\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 85px;\"\u003e\n \u003cp\u003e2994.60\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 85px;\"\u003e\n \u003cp\u003e92.03%\u003c/p\u003e\n \u003c/td\u003e\n \u003c/tr\u003e\n \u003ctr\u003e\n \u003ctd style=\"width: 37px;\"\u003e\n \u003cp\u003e\u003cstrong\u003e9\u003c/strong\u003e\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 208px;\"\u003e\n \u003cp\u003eJard\u0026iacute;n Bot\u0026aacute;nico - Yarumos\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 85px;\"\u003e\n \u003cp\u003e1137\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 85px;\"\u003e\n \u003cp\u003e2, 3, 6\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 95px;\"\u003e\n \u003cp\u003e908.00\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 77px;\"\u003e\n \u003cp\u003e79.86%\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 84px;\"\u003e\n \u003cp\u003eA, B, F\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 85px;\"\u003e\n \u003cp\u003e229.00\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 85px;\"\u003e\n \u003cp\u003e20.14%\u003c/p\u003e\n \u003c/td\u003e\n \u003c/tr\u003e\n \u003ctr\u003e\n \u003ctd style=\"width: 37px;\"\u003e\n \u003cp\u003e\u003cstrong\u003e10\u003c/strong\u003e\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 208px;\"\u003e\n \u003cp\u003eJard\u0026iacute;n Bot\u0026aacute;nico - Yarumos\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 85px;\"\u003e\n \u003cp\u003e1325\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 85px;\"\u003e\n \u003cp\u003e2, 3, 6\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 95px;\"\u003e\n \u003cp\u003e1018.50\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 77px;\"\u003e\n \u003cp\u003e76.87%\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 84px;\"\u003e\n \u003cp\u003eA, B, F\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 85px;\"\u003e\n \u003cp\u003e306.50\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 85px;\"\u003e\n \u003cp\u003e23.13%\u003c/p\u003e\n \u003c/td\u003e\n \u003c/tr\u003e\n \u003ctr\u003e\n \u003ctd style=\"width: 37px;\"\u003e\n \u003cp\u003e\u003cstrong\u003e11\u003c/strong\u003e\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 208px;\"\u003e\n \u003cp\u003eJard\u0026iacute;n Bot\u0026aacute;nico - 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Alc\u0026aacute;zares\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 85px;\"\u003e\n \u003cp\u003e3088\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 85px;\"\u003e\n \u003cp\u003e2, 3, 6, 8\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 95px;\"\u003e\n \u003cp\u003e2277.50\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 77px;\"\u003e\n \u003cp\u003e73.75%\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 84px;\"\u003e\n \u003cp\u003eA, B, D\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 85px;\"\u003e\n \u003cp\u003e810.50\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 85px;\"\u003e\n \u003cp\u003e26.25%\u003c/p\u003e\n \u003c/td\u003e\n \u003c/tr\u003e\n \u003ctr\u003e\n \u003ctd style=\"width: 37px;\"\u003e\n \u003cp\u003e\u003cstrong\u003e14\u003c/strong\u003e\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 208px;\"\u003e\n \u003cp\u003eAlc\u0026aacute;zares - Cerro Sancancio\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 85px;\"\u003e\n \u003cp\u003e3921\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 85px;\"\u003e\n \u003cp\u003e2, 3, 5, 6\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 95px;\"\u003e\n \u003cp\u003e2423.00\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 77px;\"\u003e\n \u003cp\u003e61.80%\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 84px;\"\u003e\n \u003cp\u003eA, B, D, F\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 85px;\"\u003e\n \u003cp\u003e1498.00\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 85px;\"\u003e\n \u003cp\u003e38.20%\u003c/p\u003e\n \u003c/td\u003e\n \u003c/tr\u003e\n \u003ctr\u003e\n \u003ctd style=\"width: 37px;\"\u003e\n \u003cp\u003e\u003cstrong\u003e15\u003c/strong\u003e\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 208px;\"\u003e\n \u003cp\u003eCerro Sancancio - Bosque Popular - Yarumos\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 85px;\"\u003e\n \u003cp\u003e5321\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 85px;\"\u003e\n \u003cp\u003e3, 6, 8\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 95px;\"\u003e\n \u003cp\u003e213.30\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 77px;\"\u003e\n \u003cp\u003e4.01%\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 84px;\"\u003e\n \u003cp\u003eA, B, D, F\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 85px;\"\u003e\n \u003cp\u003e5107.70\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 85px;\"\u003e\n \u003cp\u003e95.99%\u003c/p\u003e\n \u003c/td\u003e\n \u003c/tr\u003e\n \u003ctr\u003e\n \u003ctd style=\"width: 37px;\"\u003e\n \u003cp\u003e\u003cstrong\u003e16\u003c/strong\u003e\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 208px;\"\u003e\n \u003cp\u003eAlc\u0026aacute;zares - Montele\u0026oacute;n\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 85px;\"\u003e\n \u003cp\u003e3180\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 85px;\"\u003e\n \u003cp\u003e2, 3, 5, 8\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 95px;\"\u003e\n \u003cp\u003e1808.50\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 77px;\"\u003e\n \u003cp\u003e56.87%\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 84px;\"\u003e\n \u003cp\u003eA, B, D\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 85px;\"\u003e\n \u003cp\u003e1371.50\u003c/p\u003e\n \u003c/td\u003e\n \u003ctd style=\"width: 85px;\"\u003e\n \u003cp\u003e43.13%\u003c/p\u003e\n \u003c/td\u003e\n \u003c/tr\u003e\n \u003c/tbody\u003e\n\u003c/table\u003e\n\u003cp\u003e\u0026nbsp;\u003c/p\u003e"}],"fulltextSource":"","fullText":"","funders":[],"hasAdminPriorityOnWorkflow":false,"hasManuscriptDocX":true,"hasOptedInToPreprint":true,"hasPassedJournalQc":"","hasAnyPriority":false,"hideJournal":false,"highlight":"","institution":"","isAcceptedByJournal":false,"isAuthorSuppliedPdf":false,"isDeskRejected":"","isHiddenFromSearch":false,"isInQc":false,"isInWorkflow":false,"isPdf":false,"isPdfUpToDate":true,"isWithdrawnOrRetracted":false,"journal":{"display":true,"email":"[email protected]","identity":"urban-ecosystems","isNatureJournal":false,"hasQc":true,"allowDirectSubmit":false,"externalIdentity":"ueco","sideBox":"Learn more about [Urban Ecosystems](https://www.springer.com/journal/11252)","snPcode":"11252","submissionUrl":"https://submission.nature.com/new-submission/11252/3","title":"Urban Ecosystems","twitterHandle":"","acdcEnabled":true,"dfaEnabled":true,"editorialSystem":"em","reportingPortfolio":"Springer Hybrid","inReviewEnabled":true,"inReviewRevisionsEnabled":false},"keywords":"Amphibian, Andes, Conservation, Local Climate Zones, Reptile, Urban ecosystems","lastPublishedDoi":"10.21203/rs.3.rs-7464640/v1","lastPublishedDoiUrl":"https://doi.org/10.21203/rs.3.rs-7464640/v1","license":{"name":"CC BY 4.0","url":"https://creativecommons.org/licenses/by/4.0/"},"manuscriptAbstract":"\u003cp\u003eThe accelerated loss of biodiversity is one of the major concerns for conservation actions. In Colombia, much of the urban and cultivated areas are concentrated in the Andean region, a global biodiversity hotspot that retains less than 15% of its original forest cover. In this region, biodiversity studies are not often performed in urban environments. Here, this study present information about the diversity and composition of amphibians and reptiles in green areas of the municipality of Manizales, in the Central Andes of Colombia. To document the diversity and changes in the presence of amphibians and reptiles in the green and urbanized areas of Manizales, we performed fieldwork, literature searches and review of specimens from biological collections. Additionally, we incorporated a spatial analysis of ecological connectivity based on the Local Climate Zones (LCZ) classification. We recorded 30 species (10 amphibians, 20 reptiles), 16 endemic to Colombia, and two threatened species. Strabomantidae was the most diverse amphibian family (5 spp.), while for reptiles it was Colubridae (11 spp.). Field surveys yielded 291 individuals across 17 species, with \u003cem\u003ePristimantis thectopternus\u003c/em\u003e being the most abundant amphibian and \u003cem\u003ePholidobolus marianus\u003c/em\u003e the most common reptile. Species richness showed moderate positive correlation with area, though the smallest site exhibited the highest species density. LCZ analysis revealed significant landscape fragmentation. Reptiles demonstrated greater urban tolerance than amphibians. Our results highlight the critical importance of conserving urban green areas and the utility of LCZ for biodiversity conservation planning in rapidly urbanizing Andean ecosystems.\u003c/p\u003e","manuscriptTitle":"Amphibians and Reptiles Associated With Urban and Peri-urban Landscapes in the Central Andes of Colombia","msid":"","msnumber":"","nonDraftVersions":[{"code":1,"date":"2025-09-09 13:04:00","doi":"10.21203/rs.3.rs-7464640/v1","editorialEvents":[{"type":"communityComments","content":0},{"type":"decision","content":"Revision requested","date":"2025-11-20T15:53:30+00:00","index":"","fulltext":""},{"type":"editorInvitedReview","content":"","date":"2025-11-18T20:03:36+00:00","index":"hide","fulltext":""},{"type":"editorInvitedReview","content":"","date":"2025-11-14T13:45:50+00:00","index":"hide","fulltext":""},{"type":"editorInvitedReview","content":"","date":"2025-11-10T04:14:44+00:00","index":"hide","fulltext":""},{"type":"reviewerAgreed","content":"332545548411914854994914284998805347014","date":"2025-10-02T01:06:53+00:00","index":"hide","fulltext":""},{"type":"reviewerAgreed","content":"174220797800008194266599348556045795138","date":"2025-10-01T22:16:14+00:00","index":"hide","fulltext":""},{"type":"editorInvitedReview","content":"","date":"2025-09-29T18:05:33+00:00","index":"hide","fulltext":""},{"type":"reviewerAgreed","content":"289031992510217940898727389074100288688","date":"2025-09-29T11:11:29+00:00","index":"hide","fulltext":""},{"type":"reviewerAgreed","content":"50077550425665255954041919110262066930","date":"2025-09-03T14:22:30+00:00","index":"hide","fulltext":""},{"type":"reviewersInvited","content":"","date":"2025-09-03T03:37:27+00:00","index":"","fulltext":""},{"type":"editorAssigned","content":"","date":"2025-08-28T02:35:50+00:00","index":"","fulltext":""},{"type":"checksComplete","content":"","date":"2025-08-28T01:44:37+00:00","index":"","fulltext":""},{"type":"submitted","content":"Urban Ecosystems","date":"2025-08-26T15:48:44+00:00","index":"","fulltext":""}],"status":"published","journal":{"display":true,"email":"[email protected]","identity":"urban-ecosystems","isNatureJournal":false,"hasQc":true,"allowDirectSubmit":false,"externalIdentity":"ueco","sideBox":"Learn more about [Urban Ecosystems](https://www.springer.com/journal/11252)","snPcode":"11252","submissionUrl":"https://submission.nature.com/new-submission/11252/3","title":"Urban Ecosystems","twitterHandle":"","acdcEnabled":true,"dfaEnabled":true,"editorialSystem":"em","reportingPortfolio":"Springer Hybrid","inReviewEnabled":true,"inReviewRevisionsEnabled":false}}],"origin":"","ownerIdentity":"08d9c97a-6675-4792-810f-2bf6b5ed7d12","owner":[],"postedDate":"September 9th, 2025","published":true,"recentEditorialEvents":[],"rejectedJournal":[],"revision":"","amendment":"","status":"under-review","subjectAreas":[],"tags":[],"updatedAt":"2026-05-19T17:08:11+00:00","versionOfRecord":[],"versionCreatedAt":"2025-09-09 13:04:00","video":"","vorDoi":"","vorDoiUrl":"","workflowStages":[]},"version":"v1","identity":"rs-7464640","journalConfig":"researchsquare"},"__N_SSP":true},"page":"/article/[identity]/[[...version]]","query":{"redirect":"/article/rs-7464640","identity":"rs-7464640","version":["v1"]},"buildId":"8U1c8b4HqxoKbykW_rLl7","isFallback":false,"isExperimentalCompile":false,"dynamicIds":[84888],"gssp":true,"scriptLoader":[]}