Abstract Toxic pollutants such as crude oil have direct negative effects for a wide array of marine life. While mortality from acute exposure to oil is obvious, sub-lethal consequences of exposure to petroleum derivatives for growth and reproduction are less evident and sub-lethal effects in fish populations are obscured by natural environmental variation, fishing, and measurement error. We use fisheries independent surveys in the Gulf of Alaska to examine the consequences of the 1989 Exxon Valdez oil spill (EVOS) for demersal fish. We delineate areas across a range of exposure to EVOS and use spatio-temporal models to quantify the abundance of 53 species-groups over 31 years. We compare multiple community metrics for demersal fish in EVOS and Control areas. We find that areas more exposed to EVOS have more negative trends in total groundfish biomass than non-EVOS areas, and that this change is driven primarily by reductions in the abundance of the apex predator guild. We show no signature of increased variability or increased levels of synchrony within EVOS areas. Our analysis supports mild consequences of EVOS for groundfish communities, but suggests that long time-series and assessments of changes at the community level may reveal sub-lethal effects in marine communities. Introduction Major environmental disasters such as oil spills are a persistent concern to marine ecosystems worldwide, with major oil disasters striking coastal seas throughout the past century and affecting all oceans. In United States coastal waters alone between 1973 and 2011, nearly 2.7 million m3 of oil were accidentally released, though annual release rates have dropped substantially over the past 20 years (Ramseur, 2010). Particularly well publicized spills include the Santa Barbara, CA oil spill of 1969 (Squire, 1992), the Amoco Cadiz spill off France in 1978 (Conan et al., 1982), the Exxon Valdez spill in 1989 (Paine et al., 1996; Peterson et al., 2003), and the Deepwater Horizon spill of 2010 (Camilli et al., 2010). Oil spills can have long-lasting impacts on marine ecological systems from the intertidal to the deep sea and from plankton to fish to marine mammals (Conan et al., 1982; Paine et al., 1996; Peterson et al., 2003). The effects of petroleum contamination on marine communities are varied and complex. Documented effects range from the acute and direct (e.g. toxicological effects that cause serious injury or immediate death; Garrott et al., 1993; Piatt and Ford, 1996) to the gradual and indirect, including negative consequences for growth, development, and reproduction (Hicken et al., 2011; Monson et al., 2011; Rice et al., 2001). In recent years, a consensus has developed indicating that even relatively low levels of exposure can have considerable fitness consequences for individuals (Collier et al., 1993; Hicken et al., 2011; Incardona et al., 2015; Sørhus et al., 2016). While laboratory studies have found negative consequences of petroleum related contaminants, connecting individual level studies to population or community level effects in natural populations has proved difficult (Peterson, 2001; Peterson et al., 2003; Awkerman et al., 2016; but see Fodrie et al., 2014) primarily because information on important components of the ecosystem before the spill are often lacking. Additionally, natural environmental variation—both spatial and temporal—can obscure signatures of oil impacts in marine communities, spatial-temporal heterogeneity of fishing pressures may confound oil effects, and sparse biological sampling may result in insufficient power to detect the biological effects of an oil spill (Paine et al., 1996). The Exxon Valdez oil spill (hereafter “EVOS”) in March 1989 spilled ∼257 000 barrels (36 000 t) of crude oil into Prince William Sound, Alaska (Paine et al., 1996; Wolfe et al., 1994). In the months following the spill, oil was advected by wind and currents to the southwest, spreading into the Gulf of Alaska (GOA). While the dispersal path and distribution of oil in the water column and sediments remains uncertain, the approximate distribution and extent of surface oil (Short and Heintz, 1997; Wolfe et al., 1994) and oiled beaches are documented (Figure 1; NOAA, 1997). Furthermore, oil from EVOS reached a wide range of habitats and species; oil was observed both directly in some deep water trawls (Armstrong et al., 1995) and metabolites associated with petroleum exposure were detected in invertebrate and fish species across a vast spatial area (Collier et al., 1993; Short and Heintz, 1997; Sol et al., 2000; Marty et al., 2003;). Estimates by Wolfe et al. (1994) suggest ∼20% of the oil reached the sediments in Prince William Sound and the GOA. Also, EVOS oil remains in the environment to the present day: oil has been documented many years after the spill along shorelines (Peterson et al., 2003; Short et al., 2007) and detected through metabolites in sampled fish (Jewett et al., 2002). Figure 1 View largeDownload slide Map of study region with discrete areas for comparison of demersal groundfish communities. Shorelines with documented oiling from EVOS are highlighted in red. Numbered areas designate focal areas in the 50–150 m depth range and are coloured based on their categorical exposure to EVOS. Dashed lines delineate four areas used to collate groundfish catch statistics with circled letters defined as: P = Prince William Sound, C = Cook Inlet, K = Kodiak, and A = Alaska Peninsula. Figure 1 View largeDownload slide Map of study region with discrete areas for comparison of demersal groundfish communities. Shorelines with documented oiling from EVOS are highlighted in red. Numbered areas designate focal areas in the 50–150 m depth range and are coloured based on their categorical exposure to EVOS. Dashed lines delineate four areas used to collate groundfish catch statistics with circled letters defined as: P = Prince William Sound, C = Cook Inlet, K = Kodiak, and A = Alaska Peninsula. Quantifying the consequences of EVOS requires consideration of both environmental variability and other human impacts on the GOA. The EVOS occurred within a high latitude coastal shelf system that is influenced by complex bathymetry with seasonal, interannual, and decadal variability (Stabeno et al., 2016). The region is influenced by substantial freshwater inputs, vigorous coastal currents that generate eddies, topographic steering, entrainment of offshore production at the heads of gullies, and complex frontal structure (Royer et al., 2001; Stabeno et al., 2016). While major atmospheric forces such as the Pacific Decadal Oscillation (PDO) substantially affect GOA, the timing of the EVOS coincided with a well-documented shift in climate conditions in 1988/1989 which broadly affected the Alaskan ocean conditions (Bond et al., 2003; Di Lorenzo et al., 2008). At smaller spatial scales, episodic storm events impact water column stability which affects the timing of spring blooms and the disruption of the provisioning of nutrients to the surface in summer (Henson, 2007; Hollowed et al., 2007). These complex environmental processes influence survival and dispersal of fish across the coastal shelf via direct impacts on the availability of preferred habitats and indirect impacts on seasonal primary production, spatial patterns of the quality and quantity of zooplankton in the region, and encounter rates between predators and prey. In addition to environmental variation, post-juvenile groundfish in the GOA have been exposed to spatially and temporally heterogeneous patterns in commercial fishing over the past half century. Five main events have impacted the spatial and temporal patterns of fishing: (i) foreign fisheries depleted rockfish (primarily Pacific ocean perch, Sebastes alutus) populations in the late 1960s and early 1970s prior to United States harvest restrictions and populations slowly recovered throughout the 1990s (Hulson et al., 2014); (ii) domestication of the fisheries and exclusion of the foreign fleet between 1985 and 1990 (Megrey and Wespestad, 1990); (iii) the establishment of individual fishing quotas (IFQs) in the sablefish (Anoplopoma fimbria) and Pacific halibut (Hippoglossus stenolepis) fisheries in 1995 (NPFMC and NMFS, 1992; Pautzke and Oliver, 1997); (iv) a series of Bering Sea and pollock (Gadus chalcogrammus) allocation and management actions culminating in the passage of the American Fisheries Act (Felthoven, 2002; North Pacific Fishery Management Council (NPFMC), 2001); and (v) implementation of the Steller sea lion (Eumetopias jubatus) mitigation measures which established no trawl zones around haulouts and rookeries and implementation of seasonal quotas for sea lion prey (2001; McBeath, 2004). Quantifying the relative contribution of EVOS, natural environmental variability, and fisheries to population and community change is difficult (Peterson et al., 2003). Direct negative effects of EVOS on charismatic species such as marine mammals (Garrott et al., 1993) and birds (Piatt and Ford, 1996) are well documented. Additionally, some longer-term signals of oil impacts have been described for other species and habitats (Monson et al., 2011; Short et al., 2007). However, ecological systems are extraordinarily complex and theory suggests that many ecosystem-level consequences of an event like EVOS are the result of indirect interactions and complex species-by-environment interactions (Peterson, 2001; Peterson et al., 2003). Thus, a retrospective examination of the ecological consequences of EVOS after 25 years is warranted. Here we examine an understudied community in the context of EVOS—demersal fish communities of the central and western GOA—to explore community responses to the EVOS spill over a large geographic area in the context of a dynamic ocean environment and fisheries. Demersal fish communities were exposed to EVOS as oil swept west out of Prince William Sound (Figure 1, Collier et al.,1993, Sol et al.,2000). While the extent and exposure of fish communities to oil is somewhat uncertain, it is clear that some areas were exposed to significant amounts of oil while similar habitats in other areas were left unexposed. We leverage this spatial gradient in exposure to contrast demersal fish communities over the past 30 years (1984–2015) and compare groundfish communities in areas across a gradient of EVOS exposure. Specifically, we develop and apply a suite of spatio-temporal models to a fishery-independent groundfish survey and calculate a range of community metrics for demersal fish communities. Then we compare both spatial and time-series patterns of areas that experienced a range of exposure to EVOS to identify any potential EVOS-related signal in changes to the groundfish community. Rather than focus on a detailed analysis of individual species as has been done previously (Rice et al., 2001; Deriso et al., 2008; Monson et al., 2011; but see Wiens et al., 1996; Jewett et al., 1999), we assess aspects of the demersal fish community and analyse available information for signals of EVOS impacts within the context of environmental and management change. Our work complements existing research focused on detailed assessments for tactical management (Hollowed et al., 2000) and multi-species studies exploring spatial patterns of groundfish communities and their response to climatic shifts (Mueter and Norcross, 2002; Mueter and Megrey, 2005; Mueter et al., 2009; Holsman et al., 2016). Material and methods Data To assess spatial and temporal patterns in groundfish communities we used fisheries independent surveys conducted by the Alaska Fisheries Science Center (AFSC) between 1984 and 2015. The AFSC used the same sampling methodology and bottom trawl gear over the time series (stratified random sampling design; Armistead and Nichol, 1990; Stauffer, 2004). The mean latitude and longitude coordinates of each survey tow were converted to a Cartesian coordinate system (Alaska Albers equal area conic), which was compatible with existing EVOS geospatial data layers, and conserves area and distance for accurate spatial calculations. We limited our analyses to trawls set at depths shallower than 600 m because that depth was consistently surveyed throughout the time-series and because we focus on shallow demersal groundfish communities (see below). We used 7601 individual hauls between 1984 and 2015. We applied our models to 53 species groups. These groups represent species that were observed in at least 3% of the tows (>230 tows). 50 of these groups represent individual species and three represent species complexes that were not identified to species separately during field sampling throughout the survey extent (Supplementary Table S1). For brevity, we subsequently refer to these species and species-groups collectively as “species”. Statistical model We constructed separate models for each groundfish species to understand the spatial and temporal patterns of occurrence and abundance. We estimated a model for each species independently and subsequently combined the model outputs to generate a suite of multi-species metrics of the groundfish communities. We first present the statistical model and then describe the spatio-temporal metrics of groundfish communities. In all models, we used catch per unit effort (CPUE; kg ha−1) observed on each trawl as the response variable. Because most species were absent from a large number of observed trawls, we separately modelled the presence and distribution of species density, adopting a delta-GLMM approach with two sub-models (Maunder and Punt, 2004; Shelton et al., 2014). Probability of occurrence, πit(s), of the ith species in year t for a set of locations s, was modelled using a binomial GLMM with logit link, log it[πit(s)] = Xt(s)βi+ɛit(s) (1) where Xt(s) represents a matrix of fixed effect covariates at locations s in year t, βirepresents a vector of coefficients for species i, and ɛit(s) represents a vector of spatial random effects that follow a first-order autoregressive process: ɛits∼MVNormal[ρiɛit-1(s),Φi(s)] (2) where ρ represents the degree of autoregression in encounter probabilities and Φ represents spatial covariation in random effects (discussed below). Throughout the methods, we use bold lowercase symbols to represent vectors and bold uppercase to indicate matrices. Random effects were assumed to be autoregressive to account for variation not explicitly included in our model (e.g. variation due to the environment or population processes such as density dependence). Note that because trawl surveys were not conducted annually but triennially (1984–1999) or biennially (1999–2015) the autoregressive term refers to the date of the previous survey year, not the previous calendar year. We constructed an analogous model to describe the distribution of CPUE conditional on the catch of at least one individual and describe this “positive” model in Supplementary Material S1. For all models we used available haul-level information about bottom depth(m) and included both linear and quadratic terms for log(depth) in the occurrence and positive models (Shelton et al., 2014; Tolimieri et al., 2015). We centred log(depth) by subtracting the mean log(depth) across all tows. We also considered two models for fixed year effects: (i) we estimated a single intercept, and (ii) we allowed for a distinct intercept for each year. As the intercept scales the occurrence or conditional CPUE, respectively for the entire region, the single intercept model treats the spatial field as being the same across all years, whereas models with variable intercepts allow the spatial field to have the same shape, but increase or decrease by a constant intercept in each year (translating to increases or decreases in occurrence or density). For brevity, we provide technical details of the spatio-temporal random effects and estimation in the online supplementary (Supplementary Material S1). We fit a total of four models for each species: two occurrence models and two positive models. For each submodel (occurrence, positive), we estimated one model with a single intercept and one with a year-specific intercept. Models were compared using posterior predictive plots and deviance information criterion (DIC) to select models for each species. Data, code, and additional output from this modelling is publicly available on Dryad, doi:10.5061/dryad.j3t86. Generating predictive densities for each species Predictions for the two sub-models for each species were used to project densities for each species for the GOA. We projected model estimates to the centroid of each 2 × 2 km grid cell covering the entire GOA out to the 600 m isobath from 1000 Monte Carlo samples for each species. We then combined the occurrence and positive models to generate an unconditional expectation for CPUE for each grid cell. Such sampling from the joint posterior distribution properly accounts for uncertainty in these estimates. We then calculate the unconditional expectation for CPUE of species i at time t and location s by multiplying each sample from the independent occurrence and positive models. Specifically, for the gth Monte Carlo sample, the unconditional CPUE estimate is πitgs·μitgs and has units kg ha−1. Defining areas for comparison across the Gulf of Alaska We identified eleven areas across the GOA to compare groundfish communities through time (Figure 1). Each area was bounded by the 50 and 150 m bathymetric isopleths, and by natural bathymetric breaks (canyons) resulting in irregularly shaped areas that ranged in size from 1352 km2 to over 8000 km2 (Table 1, Figure 1). Because of the bathymetry, some focal areas were divided by narrow channels while others are separated by large distances. The focal areas span a range of habitats with differing exposures to EVOS, environmental disturbance, and fishing effort (Figure 1; Wolfe et al., 1994; Short and Heintz, 1997). While there is evidence from both direct observation of surface oil as well as shorelines documented to be oiled that GOA areas were exposed to oil (NOAA, 1997), most EVOS oil had weathered significantly by the time it entered the GOA (e.g. evaporation of the acutely toxic monoaromatics; decreased bioavailability because of increased tar ball formation from weathering) meaning the acute toxicity of EVOS in GOA water was reduced relative to Prince William Sound (Short and Harris, 1996; Rice et al., 2007). In GOA, weathered oil accumulated into wind rows, ultimately transitioning to tar balls through continued weathering, resulting in reduced bioavailability to embryos and larval fish in the upper water column (Rice et al., 2007; Short and Harris, 1996). Of the estimated 30% of the spilled oil entering the gulf, most transitioned to tar balls, while about a fifth weathered and sank as particles to the bottom sediments, over a large area (Wolfe et al.,1994). Table 1 Attributes for 11 focal areas. Focal area km2 Qualitative exposure to EVOS Catch region 1 8 364 Zero Prince William Sound 2 2 136 Low Prince William Sound 3 1 820 Medium Prince William Sound 4 1 352 Medium Cook Inlet 5 2 100 Medium Cook Inlet 6 4 572 Low Kodiak 7 7 064 Zero Kodiak 8 5 280 Zero Kodiak 9 2 792 Zero Kodiak 10 3 732 Zero Kodiak 11 7 840 Zero Alaska Penninsula Focal area km2 Qualitative exposure to EVOS Catch region 1 8 364 Zero Prince William Sound 2 2 136 Low Prince William Sound 3 1 820 Medium Prince William Sound 4 1 352 Medium Cook Inlet 5 2 100 Medium Cook Inlet 6 4 572 Low Kodiak 7 7 064 Zero Kodiak 8 5 280 Zero Kodiak 9 2 792 Zero Kodiak 10 3 732 Zero Kodiak 11 7 840 Zero Alaska Penninsula All areas bounded by 50 and 150 m bathymetric isopleths and by natural bathymetric breaks (canyons). Catch regions were illustrated in Figure 1 and correspond to statistical catch areas for longline and trawl fisheries used to document fishery removals. For our focal areas, the east-most area (area 1) was wholly unexposed to EVOS oil as currents and wind drove EVOS oil west out of Prince William Sound. Areas 3, 4, and 5 were exposed to the main flow of weathered oil that escaped Prince William Sound. Parts of areas 2 and 6 received some exposure, but the majority was thought to have travelled down Shelikof Strait, inside of Kodiak Island. Areas 7–11 may have been slightly exposed to EVOS, but direct observations of oil and oceanographic models suggest minimal or no impact for these areas (Short and Heintz, 1997; Wolfe et al., 1994). Thus our comparison areas bracket the spill spatially and provide areas with more and less exposure to EVOS. To understand the contribution of fisheries exploitation to changes in groundfish communities, we collated catch records for groundfish in the central GOA. Because of differences in catch location reporting requirements among species and across time, we compiled catch statistics for four broad areas encompassing all of our focal areas: Prince William Sound, Cook Inlet, Kodiak, and Alaska Penninsula (Figure 1). We obtained vessel-level total fishing catch data from the Commercial Fisheries Entry Commission (CFEC; https://www.cfec.state.ak.us, last accessed 5 May 2017) for years 1985–2014 and calculated the total groundfish mass sold from trawl and longline fisheries for each area in each year. Because harvest regions differ substantially in area, we standardized the catch to metric tons per km2 to facilitate direct comparisons among areas. To examine environmental variation we calculated summaries for bottom temperature each area in survey years between 1990 and 2015. We used observed bottom temperatures from the trawl survey locations as the response variable and used a generalized additive model (GAM) to predict bottom temperature. We used a smooth of log(water depth) and an independent tensor product smooth of Cartesian coordinates (Alaska Albers equal area conic) to predict bottom temperature in each year. Changes in the within year timing of the survey are not thought to be a major driver of temperature variation (Armistead and Nichol, 1990; Stauffer, 2004). We then calculated the average temperature in each area for each year and an across-year mean bottom temperature. We examined deviations from the across-year mean to look for area-specific trends in bottom temperature. Ideally, we would have data on a wide range of potential environmental covariates for our analyses but environmental covariates that are variable among our focal areas are very limited; broad scale environmental indices like the Pacific Decadal Oscillation are constant across our focal areas. Community metrics For each area, we summarized the groundfish community by constructing four community metrics from the single-species spatio-temporal models (individual metrics are described below). We hypothesized that any effect of EVOS would manifest differentially across species with multiple life-history and functional attributes, so we focused on community metrics that reflected species groups with different characteristics. For each metric, we summarized the predicted CPUE for each species in each year in each region using 1000 Monte Carlo draws for each 2 × 2 km grid cell. We combined information across grid cells within each area to generate an index-standardized mean estimate (and uncertainty) for unconditional CPUE (Shelton et al., 2014; Ward et al., 2015, Ono et al.,2016). Thus for each metric in each area, we have a time-series of predictions for each species for 1984–2015. We combined these species-specific metrics to generate multi-species community metrics for each area in each year. We describe the multi-species metrics and how they map onto expected EVOS impacts in turn. Total biomass. This was the simplest attribute and reflected the sum of all 53 fish species estimated by the spatio-temporal model. We hypothesized that total biomass would exhibit an overall decline if EVOS initiated a decrease in productivity as a result of chronic, sublethal effects that negatively affect recruitment, reproduction, growth, or survival at the community scale. Feeding guild. We defined guilds for GOA groundfish based on the categorization of species primary feeding habitat: pelagic (P) or benthic (B) foragers (Aydin et al., 2007; Gaichas et al., 2009). In addition, we categorized the eight largest and most voracious fish predators in the system as apex (A) predators (including e.g. Lingcod, Ophiodon elongates, and Pacific halibut; Supplementary Table S1). As the majority of EVOS oil in these habitats was thought to be weathered tar balls on the benthos, not suspended in the water column, we hypothesized that benthic feeders would be the most likely guild to exhibit a response to EVOS, though apex predators may respond indirectly via foodweb connections. Diet classification. We classified species based on their published dietary preferences. We use published diet data for each species (Aydin et al., 2007) to classify the dominant prey type for each species. We defined species diet as predominantly invertebrate (>80% of diet is invertebrates; I), pre-dominantly fish (>80% of diet is fish; F), or generalist (diet is between 20 and 80% for both fish and invertebrates). Recruitment interval. Hydrocarbon effects are documented to be particularly detrimental to early life-stages of fish (Hicken et al., 2011; Incardona et al., 2015; Sørhus et al., 2016). However, as the trawl survey only catches individuals that are generally longer than 15 cm standard length, the lag between the exposure of larvae to the oil and when juvenile fish are observed in the survey will vary among species. Therefore we divided species into three groups by the number of years expected between parturition and achieving a size of 20 cm (a size at which survey capture efficiency is close to one). We categorized this interval as short (<2 years), medium (2–4 years), or long (>4 years). We defined the interval using published parameters for the von Bertalanffy growth curve (retrieved from www.fishbase.org) and generated a predicted age to reach 20 cm. For species with multiple estimates of k and L∞ we used the median estimate. For a few species, we could not find published growth parameters. In these cases we used available estimates from similar species in the same family. Surface waters were undeniably impacted by EVOS oil in 1989 and pelagic eggs, larvae, and juvenile fish were potentially exposed. We hypothesize that shorter recruitment interval species will exhibit an immediate effect of EVOS while longer recruitment interval species will exhibit delayed effects. For all community metrics, we present four summaries to describe their change over time. First we present the raw time-series for each focal area to visually examine for evidence of a perturbation provided by EVOS. Second, to compare among areas exposed to varying amounts of oil, we calculate a linear trend for each area post-spill (1990–2015). To calculate the trend, we used the mean value of the metric derived from MCMC sampling for each area and year and weighted by the inverse of the variance derived from MCMC. Weights represent the uncertainty in the value of each metric in each year-area combination. Third, we compared the variability of each metric during the post-spill period using the coefficient of variation (CV). We calculated the CV using the deviations from the linear trend to estimate the standard deviation and the overall mean abundance from 1990 to 2015. Beyond trends and variability, we used two metrics of synchrony for the groundfish community to compare areas classified as EVOS-affected (areas 2–6) and Control (areas 1, 7–11). We calculated community-wide synchrony, φ, for each area for the entire time period (Loreau and de Mazancourt, 2008). The parameter φ ranges between 0 (indicating uncorrelated fluctuations) and 1 indicating perfect synchrony. We compared φ among areas and used a permutation test to examine whether the calculated synchrony deviated significantly from a community in which all species are fluctuating independently (using the community.sync function in R package synchrony; Gouhier and Guichard, 2014). To examine if community synchrony changed over the time-series, we used a moving window approach, calculating φ in 9-year blocks for each area. A 9-year window ensures at least four survey points are included in each correlation calculation. For all of these analyses, we use the estimated mean density of each species in each area. Final, to ask if focal areas fluctuated in unison over the time-series, we calculated all pairwise Pearson product moment correlations among areas. As with φ we calculated both single pairwise correlation for the entire time-series and correlations using a 9-year moving window. Results We successfully estimated spatio-temporal models for 53 species (Supplementary Table S1) and generated predictions for each of the 2 × 2 km grid cells in the GOA. We then combined predicted densities into our multi-species metrics for each of the focal areas. Our analysis revealed substantial variation among areas across all community metrics (Supplementary Figure S1). For example, focal areas varied more than threefold in total biomass and the relative rank of individual areas tended to be stable through time; low biomass areas remained low biomass areas and high biomass areas remained high biomass areas, reflecting the well-known spatial variation in productivity across the GOA. In general, the raw time-series from three focal areas most exposed to EVOS do not appear visually different than other areas in the GOA. This is true for total biomass as well as all guilds, diet types, and recruitment categories (Supplementary Figure S1). Total catch from trawl and longline gear types also had substantial variation in groundfish communities among the four catch regions (Figure 2). Kodiak and Alaska Peninsula average catches were 2–4 times the catch in Cook Inlet or Prince William Sound per km2, and both the magnitude and ranking of regions with respect to catch were consistent over time (Figure 2). The initial increase in documented catches from 1985 to 1990 for all regions reflect, in part, the transition to an entirely U.S.-based fleet, not necessarily an increase in overall catch. Regardless, there is no evidence of changes in catch 1989 or 1990 in response to EVOS in any region and broadly speaking, total removals were relatively stable across the time-series after 1990. Figure 2 View largeDownload slide Top: Annual, area standardized groundfish catches for four major areas in the Gulf of Alaska. See Figure 1 for area definitions. Bottom: Bottom temperature deviations from long-term mean for each of the 11 focal areas. Focal EVOS areas are in red (areas 3, 4, and 5; Figure 1), remaining areas are in black. Figure 2 View largeDownload slide Top: Annual, area standardized groundfish catches for four major areas in the Gulf of Alaska. See Figure 1 for area definitions. Bottom: Bottom temperature deviations from long-term mean for each of the 11 focal areas. Focal EVOS areas are in red (areas 3, 4, and 5; Figure 1), remaining areas are in black. Estimates of bottom temperature derived from the trawl survey show substantial temporal variation but there was no indication that any of the focal areas systematically differed from a broader shared pattern (Figure 2). In particular, none of the EVOS focal areas stand out as notably different from the remaining areas (Figure 2). Examination of trends revealed negative linear trends in total biomass in EVOS exposed areas (Figure 3). The three most exposed areas had negative trends, the two areas classified as moderate EVOS exposure showed a negative and no trend, respectively, while Control areas had zero or positive trends. The pattern among areas in total biomass trend was not driven by a single group (Figure 3). Instead the negative trend in EVOS regions total biomass was associated with a negative trend in the apex predator guild (Guild A) and a lower (near zero) trend in the pelagic forager guild (Guild P) in areas most exposed to EVOS. There was not an obvious pattern in trend for diet types and the trend for recruitment categories; species with short times to recruitment (Short) generally had more negative trends. Figure 3 View largeDownload slide Estimated linear trend for the 11 groundfish regions. Areas hypothesized to be most affected by EVOS are shaded darkly, the marginal areas of EVOS exposure have lighter shading. Each row shows the community broken up based on guild, diet category, or recruitment interval. Note that the values of the y-axis vary among panels. Vertical bars represent ±1 standard error. Figure 3 View largeDownload slide Estimated linear trend for the 11 groundfish regions. Areas hypothesized to be most affected by EVOS are shaded darkly, the marginal areas of EVOS exposure have lighter shading. Each row shows the community broken up based on guild, diet category, or recruitment interval. Note that the values of the y-axis vary among panels. Vertical bars represent ±1 standard error. In contrast to the trend analysis, there were no obvious patterns of temporal variability in response to EVOS (Figure 4). Values for CV were relatively similar across all areas in all metrics, though there were two categories, pelagic foragers (Guild P) and invertebrate consumers (Diet type I), which exhibited a general decline in CV from east to west (from area 1 to area 11). Figure 4 View largeDownload slide Estimated coefficient of variation (CV) for each of the 11 areas. Areas hypothesized to be most affected by EVOS are shaded darkly, the marginal areas of EVOS exposure have lighter shading. Each row shows the community broken up based on guild, diet category, or recruitment interval. Note that the values of the y-axis vary among panels. Figure 4 View largeDownload slide Estimated coefficient of variation (CV) for each of the 11 areas. Areas hypothesized to be most affected by EVOS are shaded darkly, the marginal areas of EVOS exposure have lighter shading. Each row shows the community broken up based on guild, diet category, or recruitment interval. Note that the values of the y-axis vary among panels. Estimates of community-wide synchrony for the entire study region were low across all areas ( φ≤0.21 for all sites) and permutation tests revealed no significant difference at any area between estimated synchrony and simulated communities in which species undergo uncorrelated fluctuations (p > 0.10 for all areas). Sliding window analysis of community synchrony also showed no obvious changes in synchrony across the time series. There is a suggestion of a slight decline in synchrony for EVOS areas relative to Control areas (Supplementary Figure S2), but any difference is very minor. Similarly, we found no changes in synchrony measures when analyses were applied to individual guilds, diet types, or recruitment intervals (results not shown). Final, we found evidence of a time-varying signature in the cross-correlation between total biomass among EVOS areas and among Control areas (Figure 5). At the beginning and end of the time-series, correlations among EVOS, among Control, and between EVOS and Control areas, were indistinguishable. However, EVOS and Control area had positive correlations during the 1990–1999 window before both declined gradually over the next 20 years. Interestingly, during this period the cross-correlation between EVOS and Control areas decreased to become negative, indicating that biomass fluctuated in opposite directions between EVOS-affected and Control areas during these periods (Figure 5). Pairwise correlations for the entire time period were much lower than for the 1990–1999 span. Figure 5 View largeDownload slide (a) Time-series of cross-correlations for total biomass using a nine-year moving window. Red line shows median cross-correlation among areas outside of the main EVOS spill (“Control”; areas 1 and 7–11). Green line shows median cross-correlation of all pairwise correlations in areas within the EVOS zone (“EVOS”, areas 2–6). Blue line shows median cross-correlation between areas within EVOS and the Control areas (“EVOS-Control”). Shaded regions indicate the inter-quartile range. (b) Pairwise Pearson correlations between focal locations for total biomass for the period 1990–1999. Figure 5 View largeDownload slide (a) Time-series of cross-correlations for total biomass using a nine-year moving window. Red line shows median cross-correlation among areas outside of the main EVOS spill (“Control”; areas 1 and 7–11). Green line shows median cross-correlation of all pairwise correlations in areas within the EVOS zone (“EVOS”, areas 2–6). Blue line shows median cross-correlation between areas within EVOS and the Control areas (“EVOS-Control”). Shaded regions indicate the inter-quartile range. (b) Pairwise Pearson correlations between focal locations for total biomass for the period 1990–1999. Discussion Detecting oil spill impacts in marine ecosystems is simultaneously easy and difficult. Acute petroleum contamination can cause direct mortality (Monson et al., 2011; e.g. Piatt and Ford, 1996) that is immediately obvious, whereas subtle and chronic consequences can affect growth and development through a range of physiological pathways (e.g. Rice et al., 2001; Hicken et al., 2011; Incardona et al., 2015). But how such effects translate from individuals to communities remains poorly understood (Fodrie et al., 2014). Here we focused on an ecologically and economically important component of the marine community, demersal groundfish, to attempt to detect a signature of EVOS using 25 years of data following the spill. EVOS contaminated portions of the GOA as evidenced by both direct observations of oil, and evidence of exposure from sampled fish (Collier et al., 1993). Groundfish have largely been neglected in the context of EVOS following the conclusion of Armstrong et al. (1995) that EVOS did not cause sufficient direct mortality to affect substantial proportions of fish populations. Since Armstrong et al. (1995), however, there has been a paradigm shift in how researchers assess the consequences of petroleum contamination (Peterson et al., 2003) with increasing attention paid to the effects of low-level, sublethal consequences of oil toxicity in a range of marine fish species (Hicken et al., 2011; Incardona et al., 2012; Sørhus et al., 2016). We recognize that substantial amounts of oil enter the marine environment via natural seeps (National Research Council, 2003; Ramseur, 2010) in addition to surface oil spills such as EVOS. However, we view natural seeps as temporally invariant, background drivers of communities across the GOA whereas EVOS was a pulse of oil that affected a specific area at a particular time providing contrast to detect a signature of EVOS. As the signature of EVOS on demersal fish communities is expected to be indirect and complex, we adopted a community-level approach to examining the signature of EVOS in groundfish. Our approach showed that while EVOS and Control areas were indistinguishable in terms of temporal variability (CV) and measures of community synchrony, we demonstrated that EVOS-affected areas had a decreasing trend in total biomass relative to Control areas. This signal appears to be driven largely by declines of apex predators in the EVOS-affected areas, including important fisheries species such as Lingcod, Pacific cod (Gadus macrocephalus), and Pacific halibut and reduced trend of the pelagic foragers guild which includes, for example, Pacific hake (Merluccius productus) and multiple rockfish species (Sebastes spp.). In contrast to our expectations that benthic foragers would be most exposed to weathered oil, we observed no clear signal between EVOS and Control areas among benthic foragers. Inspection of fisheries removals (Figure 2) does not suggest obvious changes of a magnitude that could drive community wide changes in the groundfish community. Similarly, available bottom temperature data do not suggest variation among focal areas (Figure 2). We also found an increased correlation among EVOS and Control areas coincident with the expected time interval of maximum EVOS effects (1990–1999). We are not aware of any other shared driver among areas that would be hypothesized to produce such a pattern, though other unidentified potential drivers could exist. We suggest that our observed patterns in the groundfish community are consistent with a small reduction in the productivity of EVOS areas relative to Control areas. Estimates of overall biomass trend suggest a decline on the order of 1–2% per year (Figure 3) for EVOS areas. A slight but broad based impact is consistent with our current understanding of sublethal effects of oil on pelagic eggs and larvae that can lead to reduced fish fitness (e.g. reduced growth). Such signatures would be most evident only when examined across the entire community simultaneously, rather than on a species by species basis (Figure 3). Because of the longevity of many of the groundfish species, any effect of reduced reproduction, recruitment, or growth, would manifest itself in the community gradually over the span of years to decades. In the absence of data that can be brought to directly assess these proposed mechanisms (e.g. spatial time-series of recruitment or growth) the exact causes of these patterns must remain speculative. As with any large scale and long-term study, it is impossible to control all possible covariates to isolate the effects of an oil spill and we must acknowledge that the observed patterns could arise from unidentified processes. However, we control for as many aspects as possible. In some ways, our ability to detect strong EVOS effects may be a function of the data in hand; if the Alaska groundfish trawl survey were done annually, for example, perhaps estimates of observation error and other uncertainties would be reduced. We constrained our analysis to only include areas contained within a single biogeographic region so all areas share major oceanographic features (e.g. PDO). Our analysis of bottom temperature supports this interpretation. Oceanographic drivers outlined in the introduction contribute to variation in groundfish abundance and productivity but how intra-regional oceanographic forces impact our results is unclear. Final, we constructed statistical models that account for occurrence probability, density, and incorporate measurement error. Thus we feel confident that the signals detected represent real patterns. Overall, we must echo Armstrong et al.’s (1995) conclusion that the signature of EVOS was not major a impact on groundfish communities and other drivers such as environmental variability and fishing may mask any EVOS signal. However, our analysis does suggest that low-level, long term consequences of a major environmental perturbation are detectable in natural systems and that spatial analyses conducted over broad spatial and temporal scales provide a rigorous approach for identifying such signatures. Supplementary data Supplementary material is available at the ICESJMS online version of the manuscript. Acknowledgements This work resulted from the Gulf of Alaska Dynamics Working Group conducted at the National Center for Ecological Analysis and Synthesis (NCEAS), a Center funded by the University of California, Santa Barbara, the State of California, and the Gulf Watch Alaska program by grant # 12120120 from the Exxon Valdez Oil Spill Trustees Council. 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ICES Journal of Marine Science – Oxford University Press
Published: Jan 1, 2018
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