Wildlife conservation may involve management interventions to achieve both population and ecosystem goals. One type of conservation intervention, translocation, has become an important tool for rebuilding the abundance, expanding the geographical range, and improving the genetic diversity of wild populations (Griffith et al., Reference Griffith, Scott, Carpenter and Reed1989; Pimm et al., Reference Pimm, Dollar and Bass2006; Seddon et al., Reference Seddon, Armstrong and Maloney2007; Van Houtan et al., Reference Van Houtan, Halley, van Aarde and Pimm2009; Batson et al., Reference Batson, Gordon, Fletcher and Manning2015). For critically-reduced, dispersal-limited, or highly fragmented populations, translocation is among the most effective methods to rebuild populations (Sarrazin & Barbault, Reference Sarrazin and Barbault1996; Fischer & Lindenmayer, Reference Fischer and Lindenmayer2000). In addition to recovering populations, translocation may also help to restore degraded ecosystems. Reestablishing key grazers or top predators, for example, can restore important ecological functions that are critical to ecosystem health (Berger et al., Reference Berger, Stacey, Bellis and Johnson2001; Beschta & Ripple, Reference Beschta and Ripple2009; Seddon et al., Reference Seddon, Griffiths, Soorae and Armstrong2014).
Although the conservation benefits of translocation are often clear, its implementation may be challenging. Successfully capturing and moving wild individuals may involve practical and logistical hurdles, particularly if the source populations are severely depleted (Miller et al., Reference Miller, Ralls, Reading, Scott and Estes1999). Translocation programmes may also be complicated by political, socioeconomic and legal conflicts (Loomis, Reference Loomis2006; Massei et al., Reference Massei, Quy, Gurney and Cowan2010). The success of such efforts may further be constrained by the behaviour of the species themselves, as relocated animals may behave unpredictably and ultimately not assimilate within their targeted sites (Ruth et al., Reference Ruth, Logan, Sweanor, Hornocker and Temple1998; Carswell et al., Reference Carswell, Speckman, Gill, Larson, Bodkin and VanBlaricom2015). Successful translocation programmes must overcome such challenges.
In addition to translocation, rescue and rehabilitation programmes can be useful in wildlife conservation efforts. At the most basic level, such programmes can collect pivotal data to inform management about vulnerable demographics and hazards populations encounter that lead to stranding (Van Houtan et al., Reference Van Houtan, Hargrove and Balazs2010; Nicholson et al., Reference Nicholson, Mayer, Staedler, Fujii, Murray and Johnson2018). Beyond this, the temporary captive care and rehabilitation of stranded individuals has been a part of species conservation and reintroduction efforts for a number of species categorized as Threatened or Endangered under the Endangered Species Act, such as Hawaiian monk seals Monachus schauinslandi and manatees Trichechus manatus (Gilmartin et al., Reference Gilmartin, Sloan, Harting, Johanos, Baker, Breese and Ragen2011; Norris, Reference Norris2011; Adimey et al., Reference Adimey, Ross, Hall, Reid, Barlas, Keith Diagne and Bonde2016). Although such programmes have faced numerous obstacles and criticisms, often these stem from a systematic lack of data on post-release survival, or formal analysis of the population and ecosystem impacts of releasing rehabilitated individuals (Guy et al., Reference Guy, Curnoe and Banks2013).
In this study we focus on a specific type of translocation, reintroduction, which involves moving animals within the species' historical range for the purpose of enhancing and expanding the population (Kleiman et al., Reference Kleiman, Price, Beck, Feistner, Mace and Olney1994). Southern sea otters are currently categorized as Threatened under the Endangered Species Act (USFWS, 2003), and their distribution is limited to 500 km of the central California coastline (Fig. 1; Tinker & Hatfield, Reference Tinker and Hatfield2016). The population remains concentrated in the geographical center of its distribution, where densities have been historically high, and this region is believed to be at carrying capacity (Laidre et al., Reference Laidre, Jameson and Demaster2001; Tinker et al., Reference Tinker, Bentall and Estes2008). Beyond this core area, a number of threats appear to be limiting the population from naturally expanding into unoccupied portions of its historical range and thus impeding greater recovery (Tinker et al., Reference Tinker, Bentall and Estes2008; Lafferty & Tinker, Reference Lafferty and Tinker2014; Tinker & Hatfield, Reference Tinker and Hatfield2016; Nicholson et al., Reference Nicholson, Mayer, Staedler, Fujii, Murray and Johnson2018).
Sea otters have long been recognized as a keystone species throughout the North Pacific (Estes & Palmisano, Reference Estes and Palmisano1974; Estes & Duggins, Reference Estes and Duggins1995). After being hunted to near-extinction (Kenyon, Reference Kenyon1969), their gradual recovery in a variety of near shore habitats (including rocky subtidal areas, soft-sediment communities, and seagrass dominated estuaries) has resulted in trophic upgrades such as increased kelp abundance and improved sea grass health (Estes et al., Reference Estes, Terborgh, Brashares, Power, Berger and Bond2011; Hughes et al., Reference Hughes, Eby, Van Dyke, Tinker, Marks, Johnson and Wasson2013). Thus, a proactive management approach that targets reintroduction of sea otters to historical areas would benefit population recovery and ecosystem restoration.
To circumvent many of the hurdles for translocation and rehabilitation programmes, we propose that, in certain cases, stranded or orphaned juvenile animals can be reared and utilized as a source population for reintroductions, in lieu of captured wild animals. Most orphaned sea otter pups strand with acute symptoms of maternal separation (i.e. dehydration, hypothermia and/or hypoglycemia), rather than severe injury or chronic disease. Therefore, they may be restored to normal health with basic medical intervention and husbandry care. Successful rehabilitation of these pups is also dependent on a surrogacy programme, which uses non-releasable adult female sea otters as surrogate mothers to provide care for the pups (Fig 2a; Nicholson et al., Reference Nicholson, Mayer, Staedler and Johnson2007). Because of their young age at stranding, orphaned pups are unlikely to have established fidelity to their maternal home ranges, and may be released into novel habitats (Ralls et al., Reference Ralls, Eagle and Siniff1996). Because these juveniles learn the required survival behaviours, such as socialization and foraging skills, from surrogate sea otter mothers we propose that we can maximize survival of these juvenile animals on release while minimizing the risk of human habituation (Nicholson et al., Reference Nicholson, Mayer, Staedler and Johnson2007).
Here, we present the results of a long-term, experimental study aimed at examining the feasibility of a reintroduction programme for sea otters, the demographic viability of surrogate-reared juveniles, and the efficacy of their reintroduction for reestablishing sea otter populations in unoccupied habitats. We use demographic analyses to answer if surrogate-reared sea otters differ in survival and reproduction from their wild counterparts. We then use the resulting vital rate estimates to parameterize an individual-based simulation model that we use to estimate the magnitude of population growth predicted over a 15-year period attributable to the surrogate-reared sea otters and their subsequent reproductive output. By comparing model predictions to survey-based estimates of population dynamics over this same period, we answer the question of how much the release of surrogate-reared sea otters contributed to local population recovery in Elkhorn Slough. Based on the answers to these questions, we discuss the broader management implications of our findings as they relate to stimulating sea otter range expansion in California, aiding in recovery of the subspecies and restoring ecological function to degraded ecosystems.
Study area and sea otter population
Elkhorn Slough is a 12 km2 tidal wetland adjoining Monterey Bay in central California (Fig. 1a,b) that is characterized by soft-sediment and muddy benthic substrate, intermittent eelgrass Zostera marina communities, and smaller tidal channels surrounded by pickleweed Salicornia virginica (Hughes et al., Reference Hughes, Eby, Van Dyke, Tinker, Marks, Johnson and Wasson2013). This coastal estuary was selected as the release site for this study as it already contained a small otter population (Fig. 1d), abundant prey resources, and accessible vantage points and waterways to ensure continuous monitoring of released animals. Initial recolonization of Elkhorn Slough by sea otters began in the mid 1980s (Kvitek et al., Reference Kvitek, Fukayama, Anderson and Grimm1988), but the population fluctuated as a result of immigration and emigration of males during the 1990s (Fig. 1d; Tinker & Hatfield, Reference Tinker and Hatfield2016). In 2000 the first pup born in Elkhorn Slough was observed (T.R. Kiekhefer et al., unpubl. data).
We used surrogate-reared juvenile sea otters (n = 37, Table 1) that had stranded as orphans from birth to 7 weeks of age between 2002 and 2015 (see Supplementary Material 1 for details of surrogacy methods). Our sample size was limited, in part, by the availability of surrogate mothers, but this increased as the study progressed (Fig. 2c). Comparative longitudinal data from an additional 178 wild-captured southern sea otters were available from concurrent tagging studies in Elkhorn Slough (n = 26) and outer coast populations in Monterey and Big Sur (n = 152). Detailed methods and results from these field studies are presented elsewhere (Tinker et al., Reference Tinker, Jessup, Staedler, Murray, Miller and Burgess2019; Tinker et al., Reference Tinker, Hatfield, Harris and Ames2016; Tinker et al., Reference Tinker, Tomoleoni, LaRoche, Bowen, Miles and Murray2017). All study animals had surgically implanted VHF radio transmitters for radio-telemetry and coloured flipper tags for visual monitoring (Siniff & Ralls, Reference Siniff and Ralls1991).
1 Year individual released.
2 Year individual died or was last seen alive.
3 1, known mortality; 0, alive at end of study or fate unknown.
Release and field monitoring
Surrogate-reared individuals were released at 0.5–1.5 years of age, which is approximately comparable to ages at which wild pups are successfully weaned (Riedman et al., Reference Riedman, Estes, Staedler, Giles and Carlson1994). We released single individuals within the slough, with 1–4 releases annually (Fig. 2d). The first 2 weeks after each release were treated as a conditioning period, or soft-release. During this period individuals were located and monitored daily via radio telemetry and visual observation. Individuals that were not foraging successfully (as indicated by observational data, deteriorating body condition or decreased energy level), or that exhibited symptoms of elevated stress (e.g. stereotypical pacing, vocalizing, or unproductive offshore travel) were recaptured, returned to normal health, and re-released. For the purposes of subsequent survival analyses, this 2-week point represented the time-origin of entry for each individual.
All study animals (wild-captured and released juveniles) were regularly monitored (1–5 times per week) with radio telemetry and visual observations from release until death, disappearance, or until the end of the study. Premature VHF radio failure combined with tag loss meant that the fates of some of the surrogate-reared animals were unknown (Table 1). For visually resighted females, we recorded reproductive status (whether a female had a dependent pup) and pup age (Siniff & Ralls, Reference Siniff and Ralls1991). Depending on the frequency of visual resights for each female, there was a small possibility of missing the births of pups that died or were abandoned soon after parturition. Success of each pup, defined as whether it survived to weaning at 6 months (Riedman et al., Reference Riedman, Estes, Staedler, Giles and Carlson1994) was also recorded whenever possible.
Although the survival and partial reproductive histories of many of the surrogate-reared animals was documented, many animals had unknown fates and/or partially unknown reproductive histories, and post-weaning survival and reproductive output of their pups was entirely unknown. Thus, it was not possible to quantify the total contribution of surrogate-reared animals to population dynamics based solely on a book-keeping summation of known data. To best utilize known-fate data that were available, while accounting for uncertainty in un-observed demographic transitions of surrogate-reared animals and their descendants, we developed an individual-based model to simulate the demographic transitions of individual sea otters within Elkhorn Slough over time (DeAngelis & Mooij, Reference DeAngelis and Mooij2005). An individual-based model specifies all individual outcomes (whether each individual survives or reproduces) at discrete time steps, as opposed to simply tracking total abundance or the abundance of age-classes within the population. In the case of released juveniles, some outcomes were known and therefore deterministic in the model. For individuals in the population with partially-known or unknown survival and reproductive histories (including descendants of the surrogate-reared animals), individual fates were treated as stochastic events with probabilities defined by the age- and sex-specific survival and reproductive rates for the appropriate class of each animal. Individual-based model parameter estimates are summarized below; see Supplementary Material 2 for additional details.
Sea otter survival rates were estimated using longitudinal monitoring data described above, and a Bayesian proportional hazards model (Walsh et al., Reference Walsh, Dreitz and Heisey2015) to account for the effects of age, sex, and study group, following methods previously described for sea otters (Tinker et al., Reference Tinker, Tomoleoni, LaRoche, Bowen, Miles and Murray2017). Briefly, age-varying hazards for each sex were assumed to be continuous variables and estimated using non-parametric conditional auto-regressive methods (Sinha & Dey, Reference Sinha and Dey1997). Group effects were categorical variables and corresponded to additional hazards relative to a reference group (Outer Coast). Age–group interactions and age–sex interactions were also included. Survival outcomes for each otter, at 1 month intervals over the duration of the study, were represented as random Bernoulli trials and comprised binomial likelihoods maximized by a Bayesian Markov chain Monte Carlo algorithm (Heisey & Patterson, Reference Heisey and Patterson2006). Model convergence was evaluated and confirmed by examination of Markov chain Monte Carlo trace plots and the R-hat statistic (Gelman et al., Reference Gelman, Carlin, Stern, Dunson, Vehtari and Rubin2014). Age and sex-specific survival rates and 95% credible intervals were computed and examined graphically to determine whether there were differences in survivorship schedules between study groups.
We estimated per-capita annual birth rates (number of pups born per year per female) and weaning success rates (the probability a pup survives to weaning age of 6 months) from observational data of tagged female sea otters (wild and surrogate-reared). To estimate birth rates for each study group, we calculated the mean numbers of days between consecutive births for tagged females with three or more known consecutive pup births (and at least one pup successfully reared to weaning age). Based on previously published data (Jameson & Johnson, Reference Jameson and Johnson1993; Tinker et al., Reference Tinker, Doak, Estes, Hatfield, Staedler and Bodkin2006) we assumed birth rates among females were essentially constant after 3 years of age, whereas for 2-year-olds we arbitrarily set a value of 0.25 to reflect the fact that a small proportion of 2-year-old females do reproduce.
To estimate weaning success rate, we fitted a suite of generalized linear mixed models that related putative predictor variables to the binomial response variable of known weaning outcomes for individual tagged females (following Tinker et al., Reference Tinker, Doak, Estes, Hatfield, Staedler and Bodkin2006). As found in previous studies, the primary factor affecting weaning success was age of the mother (Tinker et al., 2013; Tinker et al., Reference Tinker, Tomoleoni, LaRoche, Bowen, Miles and Murray2017); however, we also wanted to test for differences among the three study groups. We evaluated eight functional models for calculating mothers' age- and group-specific weaning success, including various combinations of age effects (linear and higher order polynomials) and group differences, as well as simpler models excluding these main effects. We then compared Akaike information criteria (AIC) values to select the best-supported model (Burnham & Anderson, Reference Burnham and Anderson2002).
Net annual immigration rates
The net annual immigration rates for wild males and females were unavailable from longitudinal data, and could not be estimated independently from other tagging studies. Instead, we generated maximum-likelihood estimates by comparing expected population growth using the individual-based model to observed population dynamics, while varying the net immigration of both sexes. We calculated the likelihood of obtaining the observed population counts of sea otters and pups given a set of net immigration rates for each sex and then log-transformed the data and multiplied by −1 to obtain negative log-likelihoods. This was summed across study years and we then used a global optimization algorithm to determine the values of net immigration for males and females that minimized the cumulative log-likelihood estimate. These values were then used to parameterize individual-based model simulations, described below.
Individual-based model simulations
The model simulated demographic outcomes (survival, birth rate, weaning success) for all individual sea otters within the estuary population over a sequence of 15 time steps (1 step = 1 year) corresponding to the duration of the study (see Supplementary Material 3 for the pseudo-code describing a single iteration of the model) while accounting for the effects of age, sex, and study group. The model was initiated with a pool of 20 males, reflecting the observed population in Elkhorn Slough in 2002 (Tinker & Hatfield, Reference Tinker and Hatfield2016), and then iterated with 10,000 simulations to produce a distribution of results, from which the mean and 95% credible intervals of expected population abundances over time were calculated.
The individual-based model was used to generate expected population growth trajectories under four different hypothetical scenarios, all starting from an initial population of 20 independent males, and 0 independent females or pups: (1) no additions of surrogate-reared juveniles, and no immigration of wild females or males; (2) no additions of surrogate-reared juveniles, but immigration of wild females and males (see Supplementary Material 2 for estimation of immigration rates); (3) additions of surrogate-reared juveniles (according to actual release data), but no immigration of wild otters; and (4) a realistic scenario, allowing for additions of surrogate-reared juveniles (according to release data) as well as immigration of wild females and males. By comparing expected population growth under these four scenarios with observed counts, we were able to calculate the proportional contributions to population growth in Elkhorn Slough of surrogate-reared and wild otters and their progeny.
We successfully released and monitored 20 males and 17 females until death, censoring because of transmitter failure and flipper tag loss (i.e. unknown fate) or end of study (Table 1). For each individual, the number of releases before passing the 2-week conditioning phase was 1–4. Despite all individuals originally stranding in open coast habitats, 16 of 20 males (80%) and 15 of 17 females (88%) remained in Elkhorn Slough after release.
Longitudinal data on survival were available for a total of 215 tagged sea otters from three overlapping studies (Supplementary Table 1). We found no strong differences in hazard ratios between surrogate-reared and wild-captured otters in Elkhorn Slough or along the open coast (Supplementary Fig. 1). Hazards associated with age and sex differences varied among all study groups, resulting in inverted-U shape survival curves that are typical for sea otters and other large mammals (Fig. 3; Tinker et al., Reference Tinker, Tomoleoni, LaRoche, Bowen, Miles and Murray2017). Because there were no significant differences in survival among the three study groups overall, we used age- and sex-specific survival rates associated with wild-captured Elkhorn Slough otters to parameterize the individual-based model.
A total of 72 females were included in the analysis of per capita birth rates, including 62 otters from outer coast populations, four wild otters captured in Elkhorn Slough, and six surrogate-reared otters. Three additional surrogate-reared females who were known to have reproduced were excluded from the analysis either because they were too young to have given birth to a minimum of three pups or because consecutive births with at least one successfully weaned pup had not been recorded. As in previous studies of reproduction in sea otters (Riedman et al., Reference Riedman, Estes, Staedler, Giles and Carlson1994; Tinker et al., Reference Tinker, Doak, Estes, Hatfield, Staedler and Bodkin2006, Reference Tinker, Jessup, Staedler, Murray, Miller and Burgess2019), we found that birth rates were consistent across study groups, with mean values of 0.943–1.032 and overlapping 95% credible intervals (Table 2). As a result, the overall mean birth rate across study groups (0.998) was used to parameterize the model.
Weaning success rates were analysed using data from a total of 340 pup dependencies with known outcomes (success or failure) for 132 tagged females. Based on AIC comparison, the best supported model included both linear and non-linear effects of mother's age, but no effect of study group (Table 3). The best-fit generalized linear mixed model showed an increasing probability of weaning success with mother's age, reaching an asymptote by 6 years and then declining slightly for older females (Supplementary Fig. 2). Therefore, we used the mean age-specific values of weaning success for all study groups combined to parameterize the individual-based model.
1 Fixed effects evaluated include linear and higher order terms for mother's age, and the categorical effect of study group (outer coast vs Elkhorn Slough wild vs surrogate-reared). Individual tagged females were included as a random effect in all models.
2 AIC statistics are shown for each model, with the lowest AIC value indicating the best-supported model (bold typeface).
The maximum-likelihood analysis indicated relatively low annual net rates of immigration for males and females, with the value for females (λ F = 0.6 otters per year) less than one-third that for males (λ M = 2.5 otters per year; Supplementary Fig. 3). The individual-based model treated immigration as a stochastic Poisson process, with mean values corresponding to the maximum-likelihood estimates.
Individual-based model simulations
Model projections of population growth in Elkhorn Slough during 2002–2016 differed greatly depending on assumptions about introductions of surrogate-reared otters and net immigration of wild otters. The first scenario (no additions of surrogate-reared otters and no immigration of wild females and males) showed a steady decline in population abundance as the resident population of males died out and were not replaced (Fig. 4a). The second scenario (allowing for immigration of wild otters, but no addition of surrogate-reared juveniles) showed a slow exponential increase of both adults and pups, although the rate of increase was less than half that observed in the actual survey data (Fig. 4b). The third scenario (allowing for the additions of surrogate-reared juveniles and subsequent reproductive output, but no immigration of wild otters) also showed an exponential rate of increase in adults and pups, with a rate of increase higher than scenario 2, but still lower than that observed in actual survey data (Fig. 4c). The fourth scenario (allowing for additions of surrogate-reared juveniles and immigration of wild females and males) showed rapid exponential growth of both adults and pups, closely matching the survey data (Fig. 4d).
Combining these model results, the proportionate contributions of surrogate-reared otters and their reproductive output to population growth in Elkhorn Slough varied among years, but accounted for c. 55% of overall observed population growth, and 64% of pup production over the study period (Fig. 5, Supplementary Table 2).
This study highlights the potential role that reintroduced, surrogate-reared juvenile animals can play in enhancing population growth in new habitats. The surrogacy methods we used allowed naïve juveniles to be successfully returned to the wild with survival (Fig. 3) and reproductive rates (Table 2) similar to the native population. We also show that releasing a small number of surrogate-reared juveniles annually had substantial impacts on population growth in Elkhorn Slough (Fig. 4c). Our model results indicate that surrogate-reared otters and their descendants represented over half of the local population growth that occurred during the study period (Fig. 5) and that this growth cannot be explained without their contributions (Fig. 4). This rapid population growth in Elkhorn Slough also coincided with increased eelgrass cover and improved ecosystem health in the Elkhorn Slough as a result of the ecosystem services sea otters provide (Hughes et al., Reference Hughes, Eby, Van Dyke, Tinker, Marks, Johnson and Wasson2013).
The successful establishment of relocated sea otters observed in this study is in contrast to previous sea otter translocation efforts in California. In the 1980s, managers attempted to establish a refuge population of sea otters in the unpopulated and geographically-isolated Channel Islands, to ensure population persistence in the event of a catastrophic oil spill (Rathbun et al., Reference Rathbun, Hatfield and Murphey2000). Juvenile and adult sea otters were captured from the mainland population and translocated to the remote San Nicolas Island. Although there was abundant prey at the new location, most (up to 90%) of the otters either traversed open-ocean distances of > 100 km to return to their previous habitat, or disappeared entirely (Carswell, Reference Carswell2008). Our study is different from this example in several important ways. Firstly, our study location was adjacent to the geographical center of the sea otter range, on the California mainland (Fig. 1). Despite this proximity, however, the habitat was initially relatively unoccupied by otters, with only a small base of non-territorial males. Secondly, rather than working in a relatively pristine kelp forest ecosystem, such as San Nicolas Island, our site was a highly-impacted, shallow, coastal estuary. Thirdly, instead of seeding the habitat with wild otters, we released juveniles that were ecologically naïve, who were surrogate-reared in captivity after stranding (Fig. 2). These differences are important to consider for any future reintroduction efforts, and the role of established occupancy and habitat type on reintroduction success warrants additional study. Our findings suggest that the release of ecologically naïve juveniles was a viable alternative to capturing and relocating wild sea otters.
The comparable survival rates between surrogate-reared animals and their wild counterparts (Fig. 3) can be largely attributed to the surrogacy rearing methods and the soft-release protocol, which gave naïve juveniles the highest probability of successfully assimilating with the wild population. The use of surrogate sea otter mothers, as well as housing juveniles with other conspecifics, provided pups with an appropriate social context for developing important survival skills, such as foraging and tool-use, while minimizing the risk of human habituation (Nicholson et al., Reference Nicholson, Mayer, Staedler and Johnson2007). Surrogacy has been previously implemented in isolated cases to rear orphaned young that remain in captivity (e.g. Rogers, Reference Rogers1985; Ridgway et al., Reference Ridgway, Kamolnick, Reddy, Curry and Tarpley1995; Gaspar et al., Reference Gaspar, Lenzi, Reddy and Sweeney2000; Hoff et al., Reference Hoff, Tarou, Horton, Mayo and Maple2005). Our study is the first case in which surrogacy has been used to bolster a wild population. As seen in other rehabilitation programmes, soft-releases may also improve survival and reproductive performance (Mitchell et al., Reference Mitchell, Wellicome, Brodie and Cheng2011; Adimey et al., Reference Adimey, Ross, Hall, Reid, Barlas, Keith Diagne and Bonde2016). Most juveniles required at least one recapture and temporary return to captivity before successfully transitioning to the wild. This high degree of monitoring during the initial 2-week release period increased individual survival and assimilation into the wild population.
The birth and weaning of pups were key indicators that surrogate-reared females had successfully reentered the wild population and contributed to additional population growth. Despite similar reproductive and weaning success rates among all study populations, surrogate-reared females contributed a greater proportion (64%) of the pup production than wild Elkhorn Slough females (Supplementary Table 2). Prior to the initiation of our study, Elkhorn Slough was predominantly occupied by a small group of transient males. Given this discrete population and low net immigration of females, the addition of surrogate-reared females apparently had disproportionate effects on initial reproduction.
We measured the impact of reintroduced individuals on a small population, which is vital to determining the efficacy of a reintroduction programme, through long-term monitoring and individual-based model simulations. Overall, the introduction of surrogate-reared juveniles contributed to more than half of the observed population growth in Elkhorn Slough (Fig. 5). There are at least three reasons for their substantial impacts. Firstly, surrogate-reared females appear to have been among the first to produce pups in Elkhorn Slough; thus, it is possible that these individuals acted as pioneers that triggered a shift in the Slough population from a seasonally abundant male area to a resident mixed-sex reproductive population. This pattern has also been observed at the periphery of sea otter ranges (Lafferty & Tinker, Reference Lafferty and Tinker2014). Secondly, almost 90% of surrogate-reared females and approximately 80% of males remained in Elkhorn Slough after release. The use of juvenile individuals without established ecological memory probably provided greater capacity to reintroduce sea otters into unfamiliar habitat within a historically-occupied region. Thirdly, at the start of the study Elkhorn Slough was probably primed for rapid sea otter population growth, with abundant prey, sheltered habitats that acted as nurseries for mothers and pups, and a small but established population that provided conspecifics from which juveniles could learn. Similar patterns of population segregation, survival and reproduction were observed in Clam Lagoon, a small estuary on Adak Island, Alaska (Tinker & Estes, Reference Tinker and Estes1996), indicating successful recolonization of estuaries is a repeatable endeavour.
The success of our study is promising and provides strong support for the use of surrogacy-based rehabilitation and reintroduction methods as an alternative to traditional translocations. However, the degree to which released surrogate-reared sea otters would affect regions without an existing population base is unknown. Here, we demonstrate how captive surrogate mothers raised wild-born, orphaned juveniles with the necessary skills to survive in the wild, allowing their successful release into novel habitats. This has been important for bolstering local populations within the existing sea otter range and has subsequently helped restore those ecosystems. Such methods may become increasingly relevant at and beyond the range edges, where the emergence of complex ecosystem changes (Moxley et al., Reference Moxley, Nicholson, Van Houtan and Jorgensen2019) is a challenge for the conservation of sea otters and fluctuating ecosystems.
This research was supported by generous contributions to the Monterey Bay Aquarium. C. DeAngelo, S. Hazan, D. Cori, M. Young, E. Lenihan, J. Hymer, G. Bentall, J. Stewart and numerous staff and volunteers provided animal care, field monitoring and logistical support throughout the 15 years of the study. The Marine Mammal Center and California Department of Fish and Wildlife, particularly M. Harris, assisted with sea otter stranding response. D. Casper and H. Harris contributed veterinary care and expertise. B. Van Wagenen of Ecoscan Resource Data, R. Eby, and other volunteers from the Elkhorn Slough National Estuarine Research Reserve located wayward otters. L. Carswell assisted with federal permits. The Moss Landing Harbor District and Elkhorn Slough National Estuarine Research Reserve authorized access and field operations. J. Yee and two anonymous reviewers provided critiques of the text.
Study design: KM, AJ, TT, KV; design of methods and collection of field monitoring data: KM, MS, TN, JF; provision of veterinary care: MM; model design and data analysis: TT; figure production: TT, KV; writing: KM, JF, TT, KV; revisions: all authors.
Conflicts of Interest
All research activities were authorized by the U.S. Fish and Wildlife Service. Any use of trade, firm, or product names is for descriptive purposes only and does not imply endorsement by the U.S. Government. The scope of the research outlined in this study and all protocols for use of live southern sea otters were approved by the Institutional Animal Care and Use Committee of the Monterey Bay Aquarium. Animal housing facilities complied with U.S. Department of Agriculture regulations governing welfare of marine mammals, and met Association of Zoos and Aquariums accreditation standards. This research abided by the Oryx guidelines on ethical standards.