High predation of marine turtle hatchlings near a coastal jetty
Introduction
In all ecosystems, predation is a key process that drives the dynamics of populations and structures communities (Estes, 1996; Preisser et al., 2005). Similar to many marine organisms, the life history stage in marine turtles immediately following hatching is likely to be the most vulnerable to predators (Heithaus, 2013). After successfully traversing the nesting beach, hatchling turtles enter nearshore waters where rates of predation within the first hour are thought to be high (Stancyk, 1982). However, relatively few studies have measured predation during this time and those that have done so have typically been confounded by the presence of an observer. In the past, the size of available tags relative to the small size of hatchlings has prevented passive tracking, so that most studies have used active tracking techniques where hatchlings have been followed by a snorkeler or observer on a small vessel (dinghy or kayak) (Frick, 1976; Witherington and Salmon, 1992; Gyuris, 1994; Pilcher et al., 2000; Stewart and Wyneken, 2004; Whelan and Wyneken, 2007). Most of these studies have reported levels of mortality below 10%, with some exceptions (e.g. Gyuris, 1994; Pilcher et al., 2000 and Reising et al., 2015). However, the presence of an observer (and a vessel) is likely to influence both the process of predation (Frick, 1976; Nowak et al., 2014) and also the behaviour of the turtle (Hendrickson, 1958). Given their relative sizes, predators such as reef fishes are likely to be very wary of the boat or snorkeler following the hatchling (Milinski, 1986). Indeed, some species have been reported to retreat or drop hatchlings when approached by a snorkeler (Frick, 1976). For these reasons, it is possible that active tracking may underestimate levels of hatchling predation in the nearshore.
The recent development of small acoustic tags combined with passive acoustic receiver arrays has now enabled the remote study of the movement patterns of turtle hatchlings as they disperse through the nearshore (Thums et al., 2013; Thums et al., 2016; Wilson et al., 2018). Research using this technology has shown that within 300āÆm of the shoreline, turtle hatchlings take a fast, directed path offshore, transiting these waters in about 10 to 15āÆmin. Importantly, tracks that do not follow these characteristic offshore routes, but in contrast linger and frequently change in direction, speed and tortuosity of movement, can provide evidence of consumption of tagged hatchlings by predators (Thums et al., 2016). Additionally, tags that cease movement can also represent predation where the tag is removed during prey handling by a predator (Khan et al., 2016). Thus, tracking hatchlings in a receiver array can monitor the movement of both hatchlings and their predators and allow for the calculation of predation rates, which are key questions in the movement ecology of marine megafauna (Hays et al., 2016).
Earlier studies have shown that hatchlings are predated more frequently in the nearshore when close to, or crossing, reef habitat (Frick, 1976; Witherington and Salmon, 1992; Gyuris, 1994; Pilcher et al., 2000), whereas predation tends to be lower when hatchlings cross areas of sand (Stewart and Wyneken, 2004; Whelan and Wyneken, 2007). This implies that rates of predation may be highest where benthic habitats provide refuges for fish. Given that man-made structures such as jetties, wharves, offshore platforms and pipelines are also known to support and attract large numbers of fish (Bohnsack, 1989; Rilov and Benayahu, 2000; Claisse et al., 2014; McLean et al., 2017), it seems possible that these could also increase predation rates on turtle hatchlings. Additionally, for navigation and/or operations during the night, these structures are often required to be lit, which can also attract large-bodied predatory fish (Becker et al., 2013). This could further increase predation rates on hatchlings as they are also attracted towards light sources at night (Thums et al., 2016; Wilson et al., 2018).
Here, we investigate the impacts of a jetty with artificial lights on the predation and nearshore movements of hatchlings of the endemic flatback turtle, Natator depressus, in northern Australia. Light pollution and the development of coastal infrastructure such as jetties and port facilities are recognised as primary threats to marine turtles around the world (Wallace et al., 2011). Several large rookeries of the flatback turtle are located close to industrial developments (Kamrowski et al., 2014) where large jetties have been built for the shipping of mineral and petroleum resources (Drenth, 2007; Department of Environment and Energy, 2017). Consequently, the possibility that these structures are attracting hatchlings (due to lighting) and fish (due to cover) and increasing hatchling predation rates, remains an unresolved and concerning question for the global management of turtle populations. We used acoustic tags and passive receiver arrays to document in-water predation on turtle hatchlings at differing distances from a jetty and in the presence and absence of artificial light. We hypothesised that predation rates would be higher closer to the jetty as it would provide cover for fish predators and that the attraction of hatchlings to lights on the jetty might increase this phenomenon. We also hypothesised that the attraction of hatchlings to light might decline with distance from the light source.
Section snippets
Study site
The study was conducted on the south-eastern side of Thevenard Island (21.456Ā°S, 115.002Ā°E), approximately 30āÆkm offshore from the town of Onslow, Western Australia (Fig. 1) where a flatback turtle nesting beach is located. Limestone reefs surround the island and beaches provide nesting habitat for green (Chelonia mydas), flatback (N. depressus) and hawksbill (Eretmochelys imbricata) turtles. We made use of a 90āÆm-long open pile jetty (constructed in 1991), that forms part of a recently
Environmental conditions during the study period
Ocean currents were tidally modulated and flowed to the west-southwest (mean (Ā±SD) direction 249.0āÆĀ±āÆ6.9Ā°) during the study period with a mean speed of 0.13āÆĀ±āÆ0.03āÆmāÆsā1 (Fig. A.1). Waves approached mainly from the east (median 104Ā° bearing, ranging from 70 to 128Ā°) with a mean height of 0.17āÆĀ±āÆ0.07āÆm (Fig. A.1). Mean water depth during the experiment was 2.63āÆĀ±āÆ0.11āÆm and water temperature was 30.34āÆĀ±āÆ0.17āÆĀ°C (Fig. A.1). Wind speed was higher on Night 1 (27.1āÆĀ±āÆ6.3āÆkmāÆhā1) than it was on the
Discussion
We used a passive acoustic tracking array to quantify rates of predation of marine turtle hatchlings in the nearshore with and without artificial lighting. Predation events were high across the study area (72%), but we found no obvious impact of artificial light on predation rates. This level of predation was substantially higher than that occurring at equivalent sites on the other side of the island (3ā23%) where there was no jetty (Wilson et al., 2018; Appendix D, Fig. A.6). The RUV
Conclusions
The impact of nearshore structures such as jetties on populations of marine turtles is largely unquantified. Our study suggests that they may pose a significant threat to the conservation and management of populations by sheltering predators that consume vulnerable hatchlings and likely other reef biota outside of the turtle hatching season. Although this predator addition and concentration may be localised, given the global footprint of such coastal infrastructure, the ecosystem effects may
Acknowledgements
We thank S. Warburton, A. Mason and M. Vo for their assistance in field experiments, C. Speed for lending RUVs, B. Vaughan and M. Birt for assisting with fish identification, V. Udyawer for providing R code for track animations, and to H. Pederson, M. Heupel, R. Harcourt, G. Hays and the anonymous reviewers for their valuable advice. We also thank DBCA staff and volunteers for collecting the nesting distribution data used here. All research protocols included in this paper have been approved by
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