The target species (Aphia minuta and Pseudaphya ferreri) of the transparent goby fishery on Mallorca Island (Balearic Islands, western Mediterranean) are currently discarded when the maximum daily catch is exceeded or when the sorting process is unworkable. The mortality suffered by this discarded fraction remains unknown, although it may be important for resource management. Accordingly, the aims of this study were to (1) assess the environmental drivers of the relative post-release survival of the discarded target species and (2) test the correlations between post-release survival and two behavior-related variables (swimming speed and its increase after a stimulus, assessed via video recording). To do so, mortality of the target species from 47 hauls sampled under normal fishing boat operations was monitored when the gear was onboard and after a few hours. At the reference level (an average depth of 25.7 m and temperature of 15.7 ºC), the immediate survival was 99.9% (95% CI: 97.9 to 100%), but the estimated post-release survival decreased to 47.2% (33.8 to 65.8%). Relative post-release mortality doubled when the water temperature increased by 2.8 ºC or when the fishing depth increased up to 32 m. Furthermore, the swimming speed of the target species was significantly correlated with the estimated post-release survival; thus, this vitality metric may offer a promising strategy for more easily estimating post-release mortality in other fisheries.
Citation: Gil MdM, Palmer M, Morey G, Manjabacas A, Pastor E, Díaz-Gil C, et al. (2020) Assessing relative post-release mortality for the transparent goby fishery: Environmental drivers and the utility of vitality metrics. PLoS ONE 15(4): e0230357. https://doi.org/10.1371/journal.pone.0230357
Editor: Heather M. Patterson, Department of Agriculture, Water and the Environment, AUSTRALIA
Received: July 8, 2019; Accepted: February 27, 2020; Published: April 9, 2020
Copyright: © 2020 Gil et al. This is an open access article distributed under the terms of the Creative Commons Attribution License, which permits unrestricted use, distribution, and reproduction in any medium, provided the original author and source are credited.
Data Availability: All relevant data are within the manuscript and its Supporting Information files.
Funding: This research received funding from the European Commission’s Horizon 2020 Research and Innovation Programme under the Grant Agreement No. 634495 for the Science, Technology, and Society Initiative to Minimize Unwanted Catches in European Fisheries (MINOUW). The funder had no role in study design, data collection and analysis, decision to publish, or preparation of the manuscript.
Competing interests: The authors have declared that no competing interests exist.
A large proportion of global commercial fishery catches are discarded and returned to the sea due to regulatory, economic or other reasons . Discards constitute a waste of natural resources, and they negatively affect both the sustainability of marine ecosystems and the economic viability of fisheries [2, 3]. Therefore, the problem of discarding in European fisheries has received increasing public attention , and the current Common Fisheries Policy promotes measures for the reduction and/or elimination of discards (Regulation EU No 1380/2013 of the European Parliament and the Council on the Common Fisheries Policy).
The implementation of ecosystem-based fishery management and the need to restrict harvest levels have highlighted issues relating to discard mortality [5, 6]. Therefore, to fully assess the effects of fishing at the individual, population and ecosystem scales, it is necessary to quantify the levels of discarding and associated rates of fishery-induced mortality . The fraction of the catch that may survive when released is highly variable, depending on species, gear, depth, water temperature or fish size [5, 6, 8]. In some cases, very high survival rates have been reported [9, 10].
However, properly estimating discard survival is challenging. Estimating survival from the proportion of catches that are alive when onboard (i.e., assuming that any released fish will survive) has been demonstrated to be a naïve approach . A larger post-release mortality rate than expected according to the survival observed at the time of release could occur because released fish can suffer sublethal effects (e.g., masked injuries or barotrauma) that may eventually result in delayed mortality from predation, physiological stress, or disease . In fact, post-release survival (i.e., the long-term survival of the fishes subjected to the fishing process and subsequently released to the sea) is reduced by both immediate mortality (i.e., the mortality when the gear comes onboard) and delayed mortality (i.e., the mortality suffered after fish have been released as a result of the fishing process). Accordingly, one of the most commonly used approaches for assessing post-release mortality is to monitor mortality by keeping a sample of the catch in captivity, although this method can introduce some potential biases and has some logistical difficulties . Tagging- or telemetry-based methods can be alternatively implemented to estimate survival, but they also have drawbacks, mainly related to tag size and tag-induced effects [13, 14]. Alternatively, the use of several measures of activity, reflex response or injury level as proxies of post-release survival has also been proposed , and this method has proven useful in some cases, as well as producing rapid results and being low cost .
The mortality observed in captivity can be attributed to fishing-related mortality and handling-related mortality. Therefore, in the absence of control fish (i.e., individuals that were not subject to the fishing process but have experienced the same handling and captivity protocol), the cause of mortality cannot be determined; however, genuine controls are unfeasible in many, if not all, cases . Therefore, mortality relative to some reference level is often assessed instead . This possibility is certainly relevant because it allows an accurate evaluation of the putative drivers of post-release mortality. The factors that may affect discard mortality are diverse. For example, gear type or other technicalities related to the fishing strategy, such as catch size, on-deck handling practices or duration of air exposure, are likely relevant [9, 16–18]. The inability to avoid predators may also severely reduce post-release survival . Finally, several environmental factors, such as temperature, sea conditions, depth-related barotrauma and biological factors including species, size, physical injuries and physiological stress, have been reported to affect post-release mortality [6, 9, 16]. Proper assessment of the role of all of these drivers may allow enhancement of post-release survival by modifying fishing practices.
According to all of the above, and as a proof of concept for a strategy that could be applicable across diverse fisheries, the aims of this paper are twofold. First, the effects of two environmental variables (depth and temperature) on post-release survival were estimated via asymptotic extrapolation of data for short-term-monitored fish in captivity. Although the use of survival modeling is well established , here, we propose a time-varying mortality model and apply a Bayesian fitting approach that allows us to explore the effect of a number of covariates on the survival rate. Second, given that monitoring fish mortality is difficult, we demonstrated how to extract new vitality metrics based on video-recorded fish mobility. Finally, we evaluated the correlations between these new metrics and the estimated post-release survival to demonstrate the utility of the metrics. This methodology was applied to the target species (Aphia minuta and Pseudaphya ferreri) of the transparent goby fishery in the Balearic Islands (western Mediterranean).
Materials and methods
The transparent goby fishery in Mallorca is a small-scale fishery that uses special purse-seine nets over sand and gravel bottoms . The surrounding net is hauled at depths reaching 30 m inside bays during winter. The fishery is economically important, with an average annual gross revenue of 274,498 € on Mallorca Island  and high market prices (from 20 to 40 € per kg). The main target species is A. minuta (a 1-year-lifespan pelagic goby less than 60 mm long) , but another similarly sized Gobiidae (P. ferreri) is also caught. Due to their small size and great resemblance, these two species are usually marketed mixed under the commercial category of the most abundant species. These target species aggregate in shoals close to the bottom (5 to 40 m depth) of bays during the fishing season . Similar fisheries are operated along the Spanish and Italian coasts.
The fishery operates with specific licenses, gear controls, and closed seasons. A management plan was established in 2013 in accordance with European Union rules (Decree 44/2013). The total maximum catch per year for this fishery is 40,000 kg, usually 30 kg/day/boat for A. minuta and 50 kg/day/boat for P. ferreri. Landings can occur in only 11 fixed ports, and only 35 boats can operate with specific nets from December 15th to April 30th. In addition, a co-management committee was created with the participation of the public administration, fishers’ associations, researchers, and nongovernmental organizations. This committee periodically revises the daily catches and the fishing effort and, if required (for example, if the monthly threshold is not reached), implements more restrictive measures (i.e., closing days) for sustaining the sale price and resources .
The discarded fraction accounted for in this fishery is small (not exceeding 10% of the total catch) because sorting fish is technically difficult. Therefore, when discards are over a certain threshold, the entire catch is released (i.e., slipping); thus, such released catches remain unaccounted for in the maximum daily catch. The discarded fishes, i.e., those returned to the sea when the maximum daily catch is exceeded or when slipping is carried out, have an unknown survival rate.
A total of 19 sampling days were randomly selected during the fishing season from December 15th 2015, to April 30th 2016. Between one and three boats were selected at each of the five ports harboring most of the transparent goby fleet of Mallorca Island (Fig 1). A total of 47 hauls were sampled during this study, and usually 2 or 3 hauls were sampled on a given fishing trip. The trips were conducted under normal fishing operations: the mean duration of the tows was 35.1 min (range: 21–55 min), the mean towing speed was 0.5 knots, the codend mesh size was 3 mm, the mean fishing depth was 25.7 m, and the mean water temperature was 15.7 ºC.
For each sampled haul, both short-term survival monitoring and video recording (outlined below) were conducted. Fish (a mixture of A. minuta and P. ferreri) were collected just as the codend was brought onboard (t0) by an onboard observer. A random sample of fish was placed into a 15 liter plastic container with sea water and continuous aeration. The time of day, date, location, tow duration, sea conditions, depth and water temperature were recorded. Dead (unresponsive, immobile, and nonreflexive) animals were counted and separated from those that were alive in the container at t0.
At the end of the fishing trip, the containers with the collected samples were landed at the port. Then, at tf (time since the gear was brought onboard, which ranged between approximately 1 hour and 9 hours), the dead and alive individuals in each container were separated for later identification, counting and length measurement. The time of day, temperature and oxygen concentration of each container were recorded at tf. A random sample of fish remaining alive was video recorded (details provided below).
The swimming speed and the reaction to a stimulus of the individuals that came to port alive were estimated using the videos. A sample of ten randomly selected individuals per haul were recorded in a circular arena measuring 23 cm in diameter (Fig 2A). The entire trajectory of the individuals within the arena was recorded using a GoPro HERO 3 camera (GoPro, Colorado, USA). To avoid any lighting interference, the camera was mounted on the top of a larger, upside-down, black structure covering the arena (Fig 2B). Battery powered light-emitting diode lights were also mounted around the camera. The fish were given 5 min to acclimatize to the new container, after which the arena was video recorded for 10 min. The reaction to a stimulus was analyzed by dropping a piece of metal near the arena, which was accomplished using a magnetic release at the mid-time of the 10 min period. After video recording, all the animals were sacrificed and stored for later identification, counting and measurement.
Image of a video recording of ten individuals during the transparent goby fishery sampling (A) and image of the structure used for the video recordings (B).
The study was authorized by the Fisheries Department of the Balearic Government. All sampling, experimentation and euthanasia of individuals were carried out in strict accordance with the recommendations of Directive 2010/63/UE, adhering to Spanish law (RD53/2013, BOE n. 34, February 8th, 2013). Euthanasia was performed with electrical stunning, and all efforts were made to minimize suffering.
The survival model.
Preliminary inspection of the variability in the observed survival ratio at different times after the gear was brought onboard (t calculated as tf-t0) suggested that the survival probability to time t reached an apparently steady state at a level different from zero when t was relatively small (Fig 3). Such a pattern can be predicted by neither a conventional Weibull model nor a negative exponential model  because in such models, the lower long-term limit is zero survival.
Expected time dependence of the weibull mortality model (with different values of the model parameters; in red) , the special case of the negative exponential mortality model (in blue)  and the model proposed here (in black).
Specifically, the conventional exponential model assumes a constant mortality rate. Conversely, the variation in the number of fish dN/dt that are alive after a given time t from the time that the gear came onboard may be time varying: (1) where m(t) is mortality. The expected number of fish that survive after a given time t (i.e., N(t)) will be: (2)
Certainly, all fish will die at some point if they are kept in captivity for a very long time, but in this case, the estimated mortality will not only be related to fishing practice mortality but also result from the confounding effects of fishing, captivity conditions (e.g., infections or non-natural feeding) and even senescence. According to Gil et al. , time variation for the instantaneous mortality rate, m(t), can be modeled as: (3)
This model seems to be appropriate for describing the biological process of accumulated mortality related to fishing because it is maximal when fish come onboard at time t = 0 (m0), m(t) decreases toward a smaller asymptotic mortality (m∞) and τ determines the rate of change between m0 and m∞. We propose that in the short term and in the absence of other mortality-related processes, m∞ = 0 (i.e., stabilization of N), and thus: (4)
Finally, Nf, the number of fish remaining alive at any time, will be: (6) where S0 is the survival probability when the gear was onboard (i.e., the number of live fish from a sample of N0 individuals). Thus, the asymptotic survival (survival at a large t) will be given by: (7)
Provided that the survival patterns may be modulated by different drivers, the lineal dependence of S0 and m0 on different covariables was evaluated. Specifically, the covariables considered were: (8) where Depth is the depth at which the haul was operated (which may increase mortality due to barotrauma), Temp0 and Tempf are the water temperatures at the time the gear was brought onboard and at the time the dead/live fish were counted at port. In addition, a single level of random effects on m0 and on S0 (rnd1 and rnd2, respectively) was considered. Specifically, random (normally distributed with a zero mean and variance σ1 and σ2) variation between the hauls from the same fishing trip was modeled.
The mortality estimated with this model (Eq 5) could be influenced by captivity conditions, given that the use of true control fishes was unfeasible in this study. In such a case, mortality can be decomposed into fishing (mf) and handling (mh) mortality; i.e., assuming additive effects, M(t) = mf + mh. Nevertheless, the relative mortality rates of different groups of fish can be compared even when mh remains unknown . Here, fishing mortality under a given environmental condition was compared with fishing mortality under a reference environmental condition (mf.reference), which was defined at the average depth and temperature (Eq 8). Therefore, the handling mortality cancels out when modeling emf+mh / emf.reference+mh . Accordingly, the slope of any environmental effect on mf can be properly estimated even when an unknown mh has an additive effect.
Fitting the survival model.
The unknown parameters of the survival model were estimated using a Bayesian approach. The number of surviving fish when haul i was onboard (N0,i) was assumed to be the result of a binomial process of Ni trials (number of dead fish plus number of alive fish when the gear was onboard) with probability S0,i (Eq 8). The number of surviving fish after ti hours (Nf,i) was assumed to be the result of a Poisson process with mean Mi*N0,i. This combination of random processes was selected after comparing other combinations of binomial, Poisson and three alternative implementations of negative binomial processes (see Results). The reliability of all these alternative implementations was successfully evaluated via simulations, and the implementation details are provided in the (S1 R script).
A nearly noninformative gamma distribution (shape = 0.01, scale = 0.01) was assumed as a prior for τ and for the tolerance (1/variance) of the two random effects considered (hauls from the same trip; on S0 and on m0). Alternative implementations of these priors (uniform distribution) rendered the same results. Priors for all the parameters of the linear dependencies were assumed to be normally distributed with a zero mean and a very large variance (1016). Three Markov chain Monte Carlo (MCMC) chains were run using randomly selected initial values for each parameter within a reasonable interval, and conventional convergence criteria  were checked. The number of iterations selected for each run was 60,000 values per chain after convergence and thinning (1 of 50). The model was implemented with the R2jags package (http://cran.r-project.org/web/packages/R2jags/R2jags.pdf) in R software (at http://www.r-project.org/), which uses the samplers implemented in JAGS (http://mcmc-jags.sourceforge.net/) to move the MCMC chains. The R script and the input data are supplied as (S2 R script and S1 Input data).
Because the fishery targets two species (A. minuta and P. ferreri), preliminary analyses were aimed at estimating species-specific mortality. However, because the models used for those analyses failed to converge (see the Results section) and the two species are managed, fished and marketed together, here, we explore the fishing mortality patterns of the species ensemble.
Algorithm for tracking fish trajectories.
Manual tracking of object trajectories in a video by observers is a very time-consuming task. Currently, software enhancements for obtaining information about moving objects from videos are being increasingly implemented . In this study, Python (v2.7; https://www.python.org/) code was developed to automatically track fish trajectories, taking advantage of the image analysis functions implemented in the OpenCV library (v3.2; http://opencv.org/). The code is structured as object oriented, and each fish trajectory is treated as an independent object.
The algorithm was applied to each frame of the time studied in each video, i.e., two minutes before and two minutes after the stimulus. The circular arena was the region of interest in the image, and it was detected automatically in each frame using a threshold value in the grayscale image. In the first frame, the initial position of each tracked fish was selected manually. For the remaining frames, the fish was identified as a blob (i.e., a region of the image with a large likelihood of being a fish) in a binary image during the process of image segmentation. Given that illumination was not uniform in the region of interest, an adaptive threshold based on the weighted sum of neighboring pixel values achieved better results for image segmentation than did a unique threshold value. Fish shadows in the arena bottom could produce false fish detections during image segmentation, and only blobs with a certain area were considered. The center of mass for every blob and the Euclidean distance between each blob and each fish position in the previous frame were calculated. To assign a fish to a blob, the Munkres algorithm  was applied to the distance matrix between blobs and fish in the previous frame. Overlap between fish or problems in segmentation due to fish transparency or poor lighting conditions can generate a smaller number of blobs than fish. In such cases, the same fish position in the previous frame was assigned to the fish without blob matching, and the fish being tracked was labeled. The position of the fish labeled in such a way was solved in the next frames. The output of the code was the trajectory of all the fish in a video. Fish speed, measured as the difference between two consecutive positions, was extracted for all the frames and all the fish in each video. A few errors in the trajectories were detected when two or more fish overlapped (i.e., occlusions). However, these failures did not have a relevant impact on the mobility metrics because the average mobility among all the fish in any given video was estimated. Although other codes for fish tracking have been developed , the lighting conditions and the transparency of the fishes forced us to implement specific software for this study.
The position of each fish in every video frame was estimated from two minutes before until two minutes after the stimulus. The speed in each frame (v, mm/second) was extracted from those trajectories. To minimize temporal autocorrelation, the size of such speed data was reduced by averaging over 60 consecutive frames. Given that the frame rate was 20 frames per second, the time series actually analyzed for a given fish was composed of 40 speed measures before and 40 measures after the stimulus. The speed of fish i at moment t (vi,t) was assumed to be gamma distributed as: (9) (10) where and toli,BA are the fish-specific (i) and period-specific (either before or after the stimulus) mean speed and tolerance (i.e., inverse of the variance), respectively, and (11) where is the average speed of fish i before the stimulus, vmean.BEFORE is the average speed of all the fish from a given haul before the stimulus, ΔBi is a fish-specific random effect before the stimulus, is the average speed of fish i after the stimulus, ΔBA is the speed difference between vmean.BEFORE and the average speed of all the fish from a given haul after the stimulus, and ΔAi is a fish-specific random effect after the stimulus.
The parameters of this model were fitted using a Bayesian approach with noninformative priors and the same technical settings described above. toli,BA, tolB and tolA were assumed to be gamma distributed, and vmean.BEFORE and ΔBA were assumed to be normally distributed with a zero mean and a very large variance. An R script with the code for completing the analyses and the data input for one fish are provided as (S3 R script and S2 Input data).
Relating survival to vitality.
The relationships between the estimated asymptotic post-release survival rate and the vitality metrics were assessed using a simple linear model where the response variable was the logit-transformed survival rate (which was estimated as described above) and the putative explanatory variables were the two vitality metrics (vmean.BEFORE and ΔBA), t (hours since the gear was brought onboard), Depth and Tempf (i.e., the water temperature at port arrival). The best model in terms of the Akaike information criterion was selected using the step function in the R library Stats.
As mentioned above, a preliminary attempt to fit a species-specific survival model was made. The catch of a given haul was classified into one of three categories according to the fisher's expertise: 1) more than 90% of A. minuta, 2) more than 90% of P. ferreri or 3) mixed catch. However, the small number of species-specific hauls precluded any attempt to estimate species-specific mortality (the models failed to converge). Nevertheless, the environmental variables considered did not differ between categories 1 and 2 (one-way analysis of variance (ANOVA) for depth: P = 0.877; ANOVA for temperature when the haul was onboard: P = 0.825; and ANOVA for temperature at port: P = 0.121). Therefore, species composition seems unbiased in relation to the environmental variables considered. Moreover, the observed and expected patterns of mortality (Fig 4) did not suggest the existence of any species-specific bias or trend. Therefore, thereafter, hauls were pooled and species composition was ignored because the implicit assumption that fishing mortality patterns would be similar for both species seemed plausible. Thus, given that the two species are managed, fished and marketed together, here, we explore the fishing mortality patterns of the species ensemble.
Six of the 47 sampled hauls were excluded from the survival analyses because the oxygen concentration of the water container registered at port arrival was too low to guarantee that the handling mortality and the fish mobility were comparable to those of the other sampled hauls. The average number of fish sampled per haul was 189.6 ± 84.5 (mean ± sd). The average number of fish that were alive when the gear came onboard was 176.2 ± 89.0, which corresponded to an average percentage of 91.7%. The average number of fish remaining alive when they arrived at port (i.e., after t hours since the gear was brought onboard, being t = 4.9 ± 2.1 hours) decreased to 64.4 ± 47.9. The average percentage of fish remaining alive when t ≥ 4 hours after the gear came onboard was only 27.8%. Therefore, the observed survival rate appeared to be close to 100% just at the time when the gear was brought onboard, after which it quickly decreased and seemed to converge to a steady value after a few hours (Fig 5); thus, the observations seem to fit the conceptual model in Fig 3.
Each white point represents a haul at t0 (i.e., the time when the gear was brought onboard), and each black point represents a haul at t (i.e., the time since the gear was brought onboard). The survival probability is estimated as the ratio between the number of fish that were alive and the total number of fish surveyed.
The pooled data were successfully fitted to the survival model (Eqs 6 to 8). The binomial (for N0) and Poisson (for Nf) processes rendered the best results in terms of deviation information criteria. Noticeably, all of the implementations with negative binomial distributions (S1 R script) failed to converge. The median and 95% Bayesian credibility interval of parameters from the model are detailed in Table 1. Note that temperature seems to negatively affect only delayed survival (m0), and depth seems to negatively affect only immediate survival (S0).
This model reasonably explained the observed values (i.e., counts of live fish /total fish after ti hours; see Fig 4). In the case where no mortality source other than fishing mortality was in effect, the expected immediate survival probability for fish captured at the average sampled depth (25.7 m) and temperature (15.7 ºC) was 99.9% (95% credibility interval (CI) between 97.9% and 100%; Fig 6 and Eq 7), but the asymptotic delayed survival when fish were immediately released when the haul was onboard was 47.2% (95% CI between 33.8% and 65.8%). Note that this expected delayed survival is higher than the average observed survival rate (27.8%) because to emulate immediate release, Tempf (the temperature of the container at port arrival) was set to equal Temp0 (water temperature of the sea), which is always lower, and increasing temperature negatively affects delayed mortality (Table 1).
This is the reference pattern chosen for estimating relative survival.
As mentioned above, these figures should be interpreted with caution because fishing mortality and handling mortality could be confounded. Nevertheless, the fishing mortality pattern relative to a reference (here, a haul deployed under the average environmental conditions of depth and temperature) provides unbiased estimates of fishing mortality due to environmental drivers. Thus, to facilitate the interpretation of the model predictions, the expected values of relative survival were estimated under different combinations of environmental conditions (depth and temperature) within the sampled ranges (Fig 7).
The reference level was a haul deployed under the average environmental conditions (represented as the dashed lines). The thick isoline represents the environmental combinations for which the expected fishing survival was the same as that for the reference level. The thin isolines represent the environmental combinations for which the expected fishing survival was the same regarding the reference level. For example, the isoline of 1.5 represents the environmental combinations for which it is expected that the survival rate will be 50% higher than that for the reference.
The resulting pattern suggests a relevant effect of both depth and temperature in such a way that a similar survival probability may result from either a warmer temperature in shallower waters (e.g., 16.2 ºC and 16 m) or a colder temperature in deeper waters (e.g., 14.5 ºC and 35 m). At the average depth, a temperature change of 2.8 ºC should either halve or double the expected fishing survival. At the average temperature, a depth up to 32 m should double the expected fishing survival. Changes of 10 m in depth would cause changes of approximately 20% in expected fishing survival.
The object-tracking algorithm successfully estimated the individual trajectories of the fish (S1 Video). As an example, the speed deviations of a given fish over 4 min are shown in Fig 8, where the parameters of the analyzed model are visually depicted. The Bayesian model (Eqs 9 to 11) successfully extracted the two vitality metrics (vmean.BEFORE, mean speed of all fish in a trial before the stimulus, and ΔBA, speed increase after the stimulus; Fig 8).
The black solid vertical line indicates the moment at which the sonorous stimulus occurred. The green solid horizontal line indicates the mean speed of all fish in a haul before the stimulus (vmean.BEFORE), the green dashed line indicates the mean speed of a given fish in a haul before the stimulus (i.e., ), the red solid line indicates the average speed of all the fish from a given haul after the stimulus, and the red dashed line presents the mean speed of a given fish after the stimulus (i.e., ). The distance between the green solid line and the green dashed line represents the parameter ΔBi, the distance between the red solid line and the red dashed line represents the parameter ΔAi, and the distance between the green solid line and the red solid line represents the parameter ΔBA.
The (between-haul) average of the (between-fish of a given haul) average speed was 9.5 mm/s, but the between-haul variability was large (95% quantile: 5.2 to 15.0 mm/s; Fig 9A). In some hauls, fish increased their speed after the stimulus, but in most of cases, the 95% CI for ΔBA included zero; thus, the before-after difference was not significant (Fig 9B).
Boxplot of the mean speed of all fish before the stimulus, vmean.BEFORE (A), and boxplot of the before-after speed difference, ΔBA (B), for each of the 37 recorded videos. A line within the box marks the median values, the boxes denote the 25 and 75% percentiles, and the bars represent the minimum and maximum nonoutlier values, respectively.
Survival vs vitality
Finally, after regressing the survival rate on several putative explanatory variables, the best model (Table 2) was composed of one of the vitality metrics (vmean.BEFORE, mean speed of all fish in a haul before the stimulus) and the depth and water temperature when the gear was brought onboard and when motility was evaluated.
Mortality of the target species
The present study introduces an approach for assessing the relative post-release mortality of two target species (A. minuta and P. ferreri) in the transparent goby fishery and the environmental drivers of post-release fish mortality. Usually, these species are returned to the sea when the maximum daily catch for a boat is exceeded or when the fraction of the catch to be discarded is large, which technically hinders fish sorting and promotes slipping. In these cases, the survival of released fish remains unknown, underestimating the total mortality caused by fishing. This underestimation may affect the proper management of the fishery, which is based on the periodic review of daily catches and fishing effort . The immediate mortality estimated in this study under average environmental conditions was low (average survival percentage of 99.9%, CI: 97.9–100%), but the asymptotic delayed mortality was considerably high (average survival percentage of 47.2%) and highly variable (CI between 33.8% and 65.8%).
However, any post-release fishing survival estimate involving some form of captive observation can be confounded by captivity-related mortality . Therefore, captivity-related mortality must be disentangled from genuine fishing-related mortality, which may be achieved by, for example, simultaneously monitoring captive fished and control individuals obtained by methods that ensure the lack of any deleterious fishing-related effects . However, it is very difficult to find a true control capture method resulting in no mortality . Due to the small size, fragility and behavioral ecology of the targeted species in the transparent goby fishery, it is virtually impossible to obtain a sample free of any of the effects of fishing. In the cases for which it is not possible to obtain true control fish, a generalized model can be used to compare the relative survival rates of different groups of fish, for example, fish caught using different capture methods or at different depths . In this way, true replicates of fish are used to obtain a correct measure of variation for survival rate estimation. In this study, the replicates (i.e., the hauls) were obtained over a range of capture depths and water temperatures, which guaranteed an adequate design and, consequently, precise evaluation of the putative drivers of post-release mortality.
The survival of released fish may be affected by several biological processes, such as barotrauma, temperature shock, desiccation/air exposure/anoxia, light-related damage to the eyes, trauma related to handling or alteration of antipredator behavior [6, 9, 19]. In the case of the target species in the transparent goby fishery, desiccation/air exposure/anoxia seems to be irrelevant because fish from the codend are immediately released into a barrel with sea water for sorting or are collected using a hand net with the net still in the water (the target species tend to remain near the surface, which facilitates sorting) . Furthermore, in the case of slipping, fish are directly released to the sea; thus, mortality related to desiccation/air exposure/anoxia or even to onboard handling should be considered negligible. Conversely, water temperature seems to have a major effect on survival. A change of 2.8 ºC in average temperature is expected to halve or double survival. The use of any fishing gear causes some degree of stress to fish, which is increased by interactions with several stressors, such as water temperature . The importance of temperature for the survival of discarded species has been shown in several studies at temperate and tropical latitudes [31–33]. Temperature controls virtually all physiological functions and plays a major role in the life history of all species by exerting a critical influence on growth, metabolism, reproduction, distribution, behavior and, ultimately, survival [34, 35]. Additionally, the levels of dissolved oxygen are depressed at higher water temperatures, which may cause additional physiological problems .
Depth may play a role complementary to that of temperature in the survival of target species of the transparent goby fishery. However, the effect of depth seems to be smaller because a change of 10 m in depth would cause changes of approximately 20% in expected fishing survival. The effect of changes in depth, which are accompanied by differences in pressure, temperature, and light conditions, on mortality increases with capture depth [6, 37]. In fact, this variable has been identified as the best predictor of release mortality in the majority of deepwater studies because of the injuries produced by changes in pressure (barotrauma) . However, in this study, the effect of depth was smaller than the effect of temperature, likely because the studied transparent goby fishery is located in relatively shallow waters (less than 30 m depth). In fact, current regulations do not allow fishing at depths greater than 30 m (Decree 19/2019, BOIB n. 35, March 16th, 2019). Therefore, the survival of the target species will likely be higher than half of the reference value at all the water temperatures occurring during the fishing season (see Fig 7).
Another factor that could affect the survival of the target species is their small body size. Size-specific mortality of discards, with smaller fish showing greater mortality, has been demonstrated in many studies [38, 39]. The increased sensitivity of smaller fish is generally attributed to fatigue from swimming and greater injury from abrasion . Additionally, core body temperature warms faster in smaller fish, making them more sensitive to temperature increases [32, 40]. Therefore, A. minuta and P. ferreri, given their small body size, with an average value of 2.34 ± 0.5 cm, could be considered fragile species with high sensitivity to fishing effects.
Technical innovations in survival estimation
Vitality metrics (i.e., those related to swimming speed or reaction to a sound stimulus) may provide a new method for estimating post-release mortality, thus precluding the need for long-term experiments. A very simple device can be implemented for video monitoring of fish trajectories. Several motion metrics, such as fish speed at any moment and fish responses to a stimulus, can be automatically extracted in real time from the videos. Here, we empirically demonstrated that a motion metric is correlated with post-release survival. Therefore, vitality metrics, once calibrated with survival likelihood estimates, can be used as mortality predictors. In this study, the swimming speed of the target species was correlated with post-release survival and thus could be considered a genuine vitality metric. However, reaction to the sound stimulus did not present a clear relationship with survival. The relationship between some reflexes and post-release mortality has been proven to be species-specific; i.e., all fish have reflexes, but these reflexes differ among species . For example, the vestibular-ocular response was identified as an impaired reflex in sockeye and pink salmon but not in coho salmon . Reflexes are neurological responses to external stimuli, although the synergistic effects of different stressors on reflex impairment are not yet fully understood. Therefore, future research that uncovers the links between physiological disturbance, reflex impairment and post-release mortality would be valuable for different species from both an applied and a fundamental perspective.
Implications for management
Ignoring the post-release mortality of discarded target species could be a relevant concern for the transparent goby fishery since this fishery is managed based on the catches per unit of effort from the previous month . Unfortunately, due to the impossibility of obtaining genuine control fish in this fishery, an estimate of absolute fishing-related post-release mortality remains elusive. However, the survival reported here could be considered a proxy for the lower bound of survival probability, as long as the captivity conditions have a negative effect (but see the discussion of the predation effects below). In such a case, the environmental drivers reported here still have management implications. For example, survival is expected to be higher than the reference survival at any depth when the temperature is approximately 15 ºC or lower. This temperature corresponds to those observed during most of the fishing season (February to March). Conversely, during the rest of the fishing season, the water temperature is > 15 ºC, and thus, the survival rate will be lower than the reference value, especially when fishing takes place at deeper locations. In such cases, the survival rate could be < 50%, depending on the effect of unknown handling mortality.
Therefore, as a rule of thumb, during the colder months (February to March), high survival is expected for the discarded target fishes, and return to the sea would be advisable because many of the released fish would contribute to enhancing population dynamics. However, during the warmer months of the fishing season, survival is expected to be low. In this case, other measures are recommended. Some fishers, when the maximum daily catch is exceeded, share the catch with other boats already fishing that have not met the maximum . The fishers claim to carry out this practice when the fish are mostly dead (probably during the warmer months), optimizing effort and maximizing the use of the resource. The results reported here support this practice because the target species show high mortality under certain environmental conditions. Therefore, recently, due to the fishers’ request and based on the results of this study, the local administration modified fishing regulations, allowing the practice of sharing the catch (Decree 19/2019). Accordingly, each pair of boats that wish to associate in order to share their excess catches must communicate this wish before the start of the fishing season. This practice is in accordance with the EU discard policy (Regulation EU No 1380/2013 of the European Parliament and the Council on the Common Fisheries Policy), which aims to reduce the number of discards returned to the sea. In fact, the practice of sharing allows for a reduction in the discards of a fishery that, due to the high sensitivity of the target species, suffers high mortality from the fishing process and, in turn, increases the profitability of fishing.
In any case, it should be noted that the rules of thumb outlined above do not take into account that captivity conditions could fail to account for other factors, for example, predation mortality. Predation could be promoted by deficits in orientation, swimming ability, feeding, schooling, social interactions, and predator evasion, increasing discard mortality [40, 42]. Therefore, further investigations should be carried out to obtain more reliable post-release mortality estimates.
In conclusion, the survival model proposed in this study reasonably explains the observed post-release mortality of the transparent goby fishery. Moreover, once the depth of capture and the water temperature are known, it is possible to estimate the delayed relative mortality of the target species by video recording the fish caught for a few minutes. This methodology can be quickly applied onboard and at a relatively low cost, although it is limited to relatively small species. Here, we have demonstrated the utility of this approach for a specific fishery, but it may be applicable to a wider range of fisheries for which discarding is a significant issue.
S1 Video. Fragment of a video recording where the estimated fish trajectories are shown.
This study is a result of the Associated Unit LIMIA-IMEDEA. We would like to thank the fishers of the transparent goby fishery for their cooperation, allowing the onboard observer and the collection of samples.
- 1. Dunn DC, Boustany AM, Halpin PN. Spatio-temporal management of fisheries to reduce by-catch and increase fishing selectivity. Fish Fish. 2011;12(1): 110–9. http://dx.doi.org/10.1111/j.1467-2979.2010.00388.x.
- 2. Kelleher K. Discards in the world’s marine fisheries. An update. Italy: FAO; 2005.
- 3. Viana M, McNally L, Graham N, Reid DG, Jackson AL. Ignoring discards biases the assessment of fisheries' ecological fingerprint. Biol Letters. 2013;9: 20130812. http://dx.doi.org/10.1098/rsbl.2013.0812.
- 4. Eliasen SQ, Papadopoulou K-N, Vassilopoulou V, Catchpole TL. Socio-economic and institutional incentives influencing fishers' behaviour in relation to fishing practices and discard. ICES J Mar Sci. 2013;71(5): 1298–307. http://doi.org/10.1093/icesjms/fst120.
- 5. Bell JD, Lyle JM. Post-capture survival and implications for by-catch in a multi-species coastal gillnet fishery. PLOS ONE. 2016;11(11): e0166632. http://dx.doi.org/10.1371/journal.pone.0166632. pmid:27861602
- 6. Davis MW. Key principles for understanding fish bycatch discard mortality. Can J Fish Aquat Sci. 2002;59(11): 1834–43. http://dx.doi.org/10.1139/f02-139.
- 7. Crowder LB, Murawski SA. Fisheries Bycatch: Implications for Management. Fisheries. 1998;23(6): 8–17. http://doi.org/10.1577/1548-8446(1998)023<0008:FBIFM>2.0.CO;2.
- 8. Broadhurst MK, Millar RB, Brand CP, Uhlmann SS. Mortality of discards from southeastern Australian beach seines and gillnets. Dis Aquat Organ. 2008;80(1): 51–61. http://doi.org/10.3354/dao01904. pmid:18714684
- 9. Méhault S, Morandeau F, Kopp D. Survival of discarded Nephropsnorvegicus after trawling in the Bay of Biscay. Fish Res. 2016;183: 396–400. http://dx.doi.org/10.1016/j.fishres.2016.07.011.
- 10. Revill A. Survival of discarded fish. A rapid review of studies on discard survival rates. DG MARE A2: Request for services Commitment No. S12.615631; 2012.
- 11. Rudershausen PJ, Buckel JA, Williams EH. Discard composition and release fate in the snapper and grouper commercial hook-and-line fishery in North Carolina, USA. Fisheries Manag Ecol. 2007;14(2): 103–13. http://doi.org/10.1111/j.1365-2400.2007.00530.x.
- 12. Gilman E, Suuronen P, Hall M, Kennelly S. Causes and methods to estimate cryptic sources of fishing mortality. J Fish Biol. 2013;83(4): 766–803. http://doi.org/10.1111/jfb.12148. pmid:24090548
- 13. ICES. Report of the Workshop on Methods for Estimating Discard Survival (WKMEDS). Denmark: ICES CM 2014/ACOM:51; 2014.
- 14. Pollock KH, Pine WE. The design and analysis of field studies to estimate catch-and-release mortality. Fisheries Manag Ecol. 2007;14: 123–30. http://doi.org/10.1111/j.1365-2400.2007.00532.x.
- 15. Davis MW. Fish stress and mortality can be predicted using reflex impairment. Fish Fish. 2010;11(1): 1–11. http://doi.org/10.1111/j.1467-2979.2009.00331.x.
- 16. Benoît HP, Plante S, Kroiz M, Hurlbut T. A comparative analysis of marine fish species susceptibilities to discard mortality: effects of environmental factors, individual traits, and phylogeny. ICES J Mar Sci. 2013;70(1): 99–113. http://doi.org/10.1093/icesjms/fss132.
- 17. Dapp DR, Walker TI, Huveneers C, Reina RD. Respiratory mode and gear type are important determinants of elasmobranch immediate and post-release mortality. Fish Fish. 2016;17(2): 507–24. http://doi.org/10.1111/faf.12124.
- 18. Tenningen M, Vold A, Olsen RE. The response of herring to high crowding densities in purse-seines: survival and stress reaction. ICES J Mar Sci. 2012;69(8): 1523–31. http://doi.org/10.1093/icesjms/fss114.
- 19. Albalat A, Collard A, Brucem C, Coates CJ, Fox CJ. Physiological condition, short-term survival, and predator avoidance behavior of discarded Norway lobsters (Nephropsnorvegicus). J Shellfish Res. 2016;35(4): 1053–65. http://dx.doi.org/10.2983/035.035.0428.
- 20. Iglesias M, Massutí E, Reñones O, Morales-Nin B. Three small-scale fisheries based on the island of Majorca (NW Mediterranean). Boll SocHist Nat Balears. 1994;37: 35–58.
- 21. Palmer M, Tolosa B, Grau AM, Gil MM, Obregón C, Morales-Nin B. Combining sale records of landings and fishers knowledge for predicting métiers in a small-scale, multi-gear, multispecies fishery. Fish Res. 2017;195: 59–70. http://dx.doi.org/10.1016/j.fishres.2017.07.001.
- 22. De Buen F. Notas a la familia Gobiidae. Observaciones sobre algunos géneros y sinopsis de las especies ibéricas. Spain: Instituto Español de Oceanografía; 1931.
- 23. Iglesias M, Morales-Nin B. Lifecycle of the pelagicgo by Aphia minuta (Pisces: Gobiidae). Sci Mar. 2001;65(3): 183–92. http://doi.org/10.3989/scimar.2001.65n3183.
- 24. Morales-Nin B, Grau AM, Aguilar JS, Gil MM, Pastor E. Balearic Islands boat seine fisheries: the transparent goby fishery an example of co-management. ICES J Mar Sci. 2017. http://dx.doi.org/10.1093/icesjms/fsw227.
- 25. Benoît HP, Capizzano CW, Knotek RJ, Rudders DB, Sulikowski JA, Dean MJ, et al. A generalized model for longitudinal short- and long-term mortality data for commercial fishery discards and recreational fishery catch-and-releases. ICES J Mar Sci. 2015;72(6): 1834–47. http://dx.doi.org/10.1093/icesjms/fsv039.
- 26. Gil MM, Palmer M, Grau A, Balle S. Many vulnerable or a few resilient specimens? Finding the optimal for reintroduction/restocking programs. PLOS ONE. 2015;10(9): e0138501. http://doi.org/10.1371/journal.pone.0138501. pmid:26394242
- 27. Royle J, Chandler RB, Sollmann R, Gardner B. Spatial capture-recapture. USA: Academic Press; 2013.
- 28. Yilmaz A, Javed O, Shah M. Object tracking: A survey. ACM ComputSurv. 2006;38(4): 13.
- 29. Munkres J. Algorithms for the assignment and transportation problems. J SocIndAppl Math. 1957;5(1): 32–8. http://doi.org/10.1137/0105003.
- 30. Marti-Puig P, Serra-Serra M, Campos-Candela A, Reig-Bolano R, Manjabacas A, Palmer M. Quantitatively scoring behavior from video-recorded, long-lasting fish trajectories. Environ Modell Softw. 2018;106: 68–76. http://doi.org/10.1016/j.envsoft.2018.01.007.
- 31. Davis MW, Olla BL. Stress and delayed mortality induced in Pacific halibut by exposure to hooking, net towing, elevated seawater temperature and air: Implications for management of bycatch. N Am J Fish Manage. 2001;21(4): 725–32. http://dx.doi.org/10.1577/1548-8675(2001)021<0725:SADMII>2.0.CO;2.
- 32. Davis MW, Olla BL, Schreck CB. Stress induced by hooking, net towing, elevated sea water temperature and air in sablefish: lack of concordance between mortality and physiological measures of stress. J Fish Biol. 2001;58: 1–15. http://doi.org/10.1111/j.1095-8649.2001.tb00495.x.
- 33. Giomi F, Raicevich S, Giovanardi O, Pranovi F, Di Muro P, Beltramini M. Catch me in winter! Seasonal variation in air temperature severely enhances physiological stress and mortality of species subjected to sorting operations and discarded during annual fishing activities. In: Davenport J, editor. Challenges to Marine Ecosystems. Developments in Hydrobiology. Netherlands: Springer; 2008. pp. 195–202.
- 34. Fry FEJ. The effect of environmental factors on the physiology of fish. In: Hoar WS, Randall DJ, editors. Fish Physiology. Environmental Relations and Behavior. VI. USA: Academic Press; 1971. pp. 1–98.
- 35. Olla BL, Davis MW, Schreck CB. Temperature magnified postcapture mortality in adult sablefish after simulated trawling. J Fish Biol. 1998;53: 743–51. http://doi.org/10.1111/j.1095-8649.1998.tb01829.x.
- 36. Arlinghaus R, Cooke SJ, Lyman J, Policansky D, Schwab A, Suski C, et al. Understanding the complexity of catch-and-release in recreational fishing: An integrative synthesis of global knowledge from historical, ethical, social, and biological perspectives. Rev Fish Sci. 2007;15(1–2): 75–167. http://doi.org/10.1080/10641260601149432.
- 37. Curtis JM, Johnson MW, Diamond SL, Stunz GW. Quantifying delayed mortality from barotrauma impairment in discarded red snapper using acoustic telemetry. Mar Coast Fish. 2015;7(1): 434–49. http://doi.org/10.1080/19425120.2015.1074968.
- 38. Suuronen P, Perez-Comas JA, Lehtonen E, Tschernij V. Size-related mortality of herring (Clupeaharengus L.) escaping through a rigid sorting grid and trawl codend meshes. ICES J Mar Sci. 1996;53(4): 691–700. http://doi.org/10.1006/jmsc.1996.0088.
- 39. Uhlmann SS, Theunynck R, Ampe B, Desender M, Soetaert M, Depestele J. Injury, reflex impairment, and survival of beam-trawled flatfish. ICES J Mar Sci. 2016;73(4): 1244–54. http://doi.org/10.1093/icesjms/fsv252.
- 40. Davis MW, Olla BL. Mortality of lingcod towed in a net as related to fish length, seawater temperature, and air exposure: A laboratory bycatch study. N Am J Fish Manage. 2002;22(4): 1095–104. http://doi.org/10.1577/1548-8675(2002)022<1095:MOLTIA>2.0.CO;2.
- 41. Raby GD, Donaldson MR, Hinch SG, Patterson DA, Lotto AG, Robichaud D, et al. Validation of reflex indicators for measuring vitality and predicting the delayed mortality of wild coho salmon bycatch released from fishing gears. J Appl Ecol. 2012;49(1): 90–8. http://doi.org/10.1111/j.1365-2664.2011.02073.x.
- 42. Raby GD, Packer JR, Danylchuk AJ, Cooke SJ. The understudied and underappreciated role of predation in the mortality of fish released from fishing gears. Fish Fish. 2014;15(3): 489–505. http://dx.doi.org/10.1111/faf.12033.