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USGS · 70221153

Tarentola annularis (white-spotted wall gecko)

Abstract

USA: CALIFORNIA: Orange Co.: San Juan Capistrano (33.51°N,117.66°W; WGS 84). 25 August 2020. Samuel Fisher, Chelsea Martin, Robert Fisher. Verified by Gregory B. Pauly. Natural History Museum of Los Angeles County (LACM 191974). New county record. One juvenile (33 mm SVL) was collected, and another juvenile was seen 40 m away. Another juvenile was also observed during a second visit to the site on 19 September 2020. Wall geckos were first documented at this site since at least 2019 by Gary Nafis (G. Nafis, pers. comm. and as posted on www.californiaherps.com; 23 Aug 2020). Given that multiple individuals were observed at this site over 2 mo, this appears to be an established population. Invasive T. annularis were first detected in California in Redlands, San Bernardino County in the early 2000s (Wilcox et al. 2014. Herpetol. Rev. 45:464). This new Orange County population is ca. 80 km SW of the other known California population. While T. annularis has not spread much in the downtown urban center in Redlands over the last 20 years (S. Fisher, unpubl. data), it is possible it might expand its range more rapidly in a less urbanized habitat if there were more landscaping and natural features present. The only other published records for North America are from Florida where they are also invasive, and they have been known since the 1990s from several locations and continued to spread (Krysko et al. 2016. IRCF Rept. Amphib. 23:110-143). In the native range of T. annularis their habitat consists of desert, indicating that even though they are able to breed and persist in coastal Orange County they may not be in the optimal habitat (Ibrahim 2004. Zool. Middle East 31:23–38). A potential concern is that if T. annularis becomes more widespread in Southern California, they could present a risk to endemic nocturnal rock-dwelling species such as Xantusia henshawi and Phyllodactylus nocticolus because T. annularis has been shown to engage in saurophagy (Ibrahim 2004, op. cit.). It is much larger than these species (X antusia henshawi SVL = 70 mm; Phyllodactylus nocticolus SVL = 63 mm; Tarentola SVL = 108 mm) and well adapted to desert habitats where it could be a potential predator or competitor.

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90° N90° S · 180° W ← longitude → 180° E
Source-reported bounding extent: 33.49330726228523° to 33.51477815748719° latitude; -117.67378807067873° to -117.65027046203613° longitude. This indicates report coverage, not an exact sampling location. View area on OpenStreetMap.

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BibTeXRIS

Samuel R Fisher, Chelsea E Martin, Robert N. Fisher. 2021. Tarentola annularis (white-spotted wall gecko). https://pubs.usgs.gov/publication/70221153

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No detection of Batrachochytrium salamandrivorans after non-native salamander putative pet release in Massachusetts, USA

The disease caused by the amphibian chytrid fungus Batrachochytrium salamandrivorans (Bsal) has caused mass mortality of salamanders across Europe (Stegen et al. 2017; amphibians are not known to be susceptible to the disease (Martel et al. 2014). Bsal puts North American amphibian biodiversity at risk (Martel et al. 2014; Gray et al. 2015) despite imports of potentially infected amphibians (USFWS 2016; WAPTR 2018; Grear et al. 2021). Recently, the U.S. has announced the finalization of the 2016 interim rule to the Lacey Act (USFWS 2016) to restrict imports of all species of salamanders from 20 genera to the list of injurious amphibians and has added 16 genera to the injurious amphibian list in a new interim rule in response to updated research on salamander susceptibility to Bsal infection (USFWS 2025). A large-scale survey across the USA failed to detect Bsal in over 10,000 individuals (Waddle et al. 2020), and ongoing efforts by North American colleges and universities are similarly conducting Bsal surveillance without more recent detection (e.g., Hyman and Hill 2024). Concerned amphibian and disease specialists nevertheless are preparing for a Bsal invasion into North America (Grant et al. 2017; Olson et al.2024). Despite the initial survey results, the risk of Bsal incursion into North America remains due to broad host susceptibility of North American amphibian species (Gray et al. 2023). The major driver of Bsal introduction risk in the U.S. is expected to be captive amphibian release (Cunningham et al. 2015; Grear et al. 2021). Bsal primarily affects salamanders but anuran species can also be vectors (e.g., Towe et al. 2021; Monzon et al. 2022; Gray et al. 2023; Olson et al. 2024), increasing the risk of a released amphibian carrying Bsal into the natural environment (Grear et al. 2021). An early survey of pet salamanders in the United States did not detect Bsal (Klocke et al. 2017), but even one animal released with Bsal could have a major effect on local amphibians. Early detection and rapid response can improve host outcomes (Bletz et al. 2024; Gray et al. 2018), but the lack of timely knowledge about unwanted release of non-native pets to natural systems causes inevitable delay. Herein, we describe our experience responding to a report of a released non-native amphibian species, common in the pet trade (Gerson 2012; Maximo et al. 2021). We suggest improvements to early detection and rapid response efforts for amphibians and amphibian disease

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