ORIGINAL RESEARCH article
Taxonomic Richness and Diversity of Larval Fish Assemblages in the Oceanic Gulf of Mexico: Links to Oceanographic Conditions
- 1Department of Marine Biology, Texas A&M University, Galveston, TX, United States
- 2Department of Marine and Environmental Sciences, Nova Southeastern University, Dania Beach, FL, United States
- 3Department of Wildlife and Fisheries Sciences, Texas A&M University, College Station, TX, United States
Biodiversity enhances the productivity and stability of marine ecosystems and provides important ecosystem services. The aim of this study was to characterize larval fish assemblages in pelagic waters of the northern Gulf of Mexico (NGoM) and identify oceanographic conditions associated with areas of increased taxonomic richness (TF) and Shannon diversity (H’). Summer ichthyoplankton surveys were conducted in the NGoM in 2015 and 2016 using neuston net (surface layer; upper 1 m) and oblique bongo net (mixed layer; 0–100 m) tows. Over 17,000 fish larvae were collected over the two-year study, and 99 families of fish larvae were present. Catch composition in the surface layer was relatively similar to the mixed-layer catch, with carangids (jacks), scombrids (mackerels, tunas), and exocoetids (flyingfishes) being numerically dominant, while deep-pelagic species, including myctophids (lanternfishes), gonostomatids (bristlemouths), and sternoptychids (marine hatchetfishes), were present almost exclusively in the mixed layer samples. Generalized additive models were used to evaluate the effect of oceanographic conditions on ichthyoplankton abundance and biodiversity. Salinity and sea surface height (SSH) were the most influential oceanographic conditions, with higher occurrence, higher TF, and higher H’ all present in areas of lower salinity, and lower SSH. This study highlights the ecological importance of cyclonic mesoscale features and areas of upwelling as areas of increased biodiversity for larval fishes, and also indicates that the mixed layer in the NGoM is essential habitat for deep-pelagic fishes during the early life interval.
Pelagic fishes play an important role in open ocean ecosystems, and changes in their abundances can impact community structure and ecosystem stability (Cury, 2000; Myers, 2003; Myers and Worm, 2003). Declines in the abundances of pelagic fishes are often attributed to overfishing (Ward and Myers, 2005) but other types of anthropogenic disturbance (e.g., habitat loss or degradation) and climate change also influence their distribution and abundance (Lehodey et al., 2006; Rijnsdorp et al., 2009). New management approaches that focus on ecosystem-level processes rather than single stocks or species are necessary to effectively mitigate past overexploitation and better understand the drivers of community change in pelagic ecosystems (Pikitch et al., 2004).
Research on the early life stages of pelagic fishes is important because it can provide information on spawning locations, spawning stock biomass, and population-level processes (Houde, 2002). Unfortunately, studies on larvae and juvenile fishes during the first few months of life are limited or non-existent for many open ocean species despite the fact that biological data on these stages are needed to better assess and monitor recruitment variability. Temporal and spatial trends in the distribution and abundance of fish larvae can be used to identify environmental factors that affect early life survival (Nonaka et al., 2000). Moreover, changes in the distribution, abundance, and assemblage composition can also be indicative of changing oceanographic conditions (Hernandez et al., 2010; Carassou, 2012), including anthropogenic disturbances such as the Deepwater Horizon oil spill (Rooker et al., 2013; Kitchens and Rooker, 2014). To date, information on the early life ecology and the environmental drivers of abundance of pelagic fishes in the Northern Gulf of Mexico (NGoM) is incomplete for most taxa. This is particularly true when considering the numerically dominant deep-pelagic taxa, and such information is needed to fill in data gaps regarding factors that influence the distribution, abundance, and population dynamics of pelagic species (Richardson, 2008).
The pelagic environment in particular provides unique challenges for locating areas of high biodiversity because the geographic location of mesoscale features and associated conditions are dynamic in time and space (Marchese, 2015). As a result, management of pelagic ecosystems requires multifaceted approaches that couple ecology and oceanography (Game et al., 2009; Lewison et al., 2015). Despite increased awareness of the importance of biodiversity, our understanding of biological communities in pelagic ecosystems is incomplete (Mittermeier et al., 2011). Identifying areas of high taxonomic richness (TF) and diversity and the oceanographic conditions that create or maintain areas of elevated biodiversity are critical because species-rich ecosystems are considered more stable and less likely to collapse compared to species-poor ecosystems (Bakun, 2006; Worm et al., 2006). Increased biodiversity also has a positive impact on ecosystem services and functions, such as resource use efficiency, nutrient cycling, and higher fisheries yields, and can stabilize ecosystems against regime shifts (Gamfeldt et al., 2014; Rocha et al., 2015).
As a model system, the NGoM offers many advantages for evaluating the biodiversity and structure of larval fish assemblages. Most notably, the oceanic component of this region is generally considered oligotrophic, but gets occasional injections of nutrient discharges from the Mississippi-Atchafalaya River System (MARS) that lead to higher productivity (Dagg and Breed, 2003). This supports primary and secondary production and high fishery yields of “coastal pelagic” taxa (Browder, 1993). Surrounding the MARS plume, densities of fish larvae may reach up to 20 times higher than reported for other areas of the GoM (Grimes and Finucane, 1991; Richards, 1993). In addition, the Loop Current and associated mesoscale features in the NGoM can concentrate fish eggs and larvae, particularly along fronts associated with divergent (cyclonic), and convergent (anticyclonic) eddies (Richards, 1993; Shulzitski et al., 2015). These mesoscale features play an important role in regulating the spatial distribution of ichthyoplankton (Karnauskas et al., 2013), and a higher northern intrusion of the Loop Current has been shown to increase the abundance of fish larvae in the NGoM (Lindo-Atichati, 2012). The Loop Current is generally associated with higher salinity and warmer waters. In particular, cyclonic features (cold core) often enhance production through upwelling, leading to increased foraging opportunities for fish larvae, and are thus assumed to serve as critical nursery habitat for several taxa of pelagic fishes (Richardson et al., 2010).
Here, we assess the attributes of the NGoM as early life habitat of pelagic fishes, including deep-pelagic taxa, with a special emphasis on identifying areas, and oceanographic conditions that support larval fish assemblages with high TF and Shannon diversity (H’). When determining biodiversity of the pelagic environment, it is well recognized that mesopelagic fauna (depth range: 200 to 1000 m) of both invertebrates and fishes, frequent the upper 200 m of the water column, or epipelagic zone during all life stages through diel vertical migration (Richards, 1993). In response, deep-pelagic fish taxa may be important determinants of TF and H’ in the epipelagic zone, and an objective of this study was to quantify linkages between fishes typically associated with these two different zones of the water column. We also coupled TF and H’ with physicochemical and biological factors using generalized additive models (GAMs) to evaluate the relative importance of oceanographic conditions on biodiversity, which provides a means for identifying regions and conditions that support species-rich assemblages of fish larvae in the NGoM. We hypothesize that biodiversity hotspots for larval fishes (high TF and H’) in the NGoM will occur primarily in convergence zones (frontal features).
Materials and Methods
Ichthyoplankton surveys were conducted in June and July over two consecutive years (2015, 2016) in a sampling corridor that ranged from 27.0–28.0°N and 88.0–91.0°W. The sampling corridor contained 48 stations located on transects at both 27.0°N and 28.0°N, with stations along each transect approximately 15 km apart (Figure 1), which represents an area sampled continuously for the past decade to assess larval recruitment variability of pelagic fishes, including billfishes, tunas, dolphinfishes, and swordfish (e.g., Rooker et al., 2012, 2013; Kitchens and Rooker, 2014; Cornic et al., 2018). Near-surface sampling was conducted with a 1 × 2 m neuston net rigged with a 1200 μm mesh. Neuston net tows were conducted in the upper 1 m of the water column (surface layer) at each station, and each tow was approximately 10 min in duration. In addition, oblique bongo net tows were conducted from between 0–100 + m of the water column (mixed layer) at each station; paired bongo nets were rigged with 333-μm mesh and 500-μm mesh nets. Although different mesh sizes were used for surface and mixed layer sampling, catch composition is known to be similar between the mesh sizes and gears with similar tow profiles (Richards, 1993; Randall et al., 2015), which allows for general comparisons of assemblage structure and diversity between the two distinct regions of the water column. All tows were performed at a vessel speed of approximately 2.5 knots, and the volume of water sampled during each tow was determined by equipping nets with General Oceanics flowmeters (Model 2030R, Miami, FL, United States).
Figure 1. Sampling sites (black dots) of the June and July ichthyoplankton cruises performed in 2015 and 2016 in the Northern Gulf of Mexico.
Sargassum (kg/m3) collected in the neuston nets and invertebrates in the neuston and combined bongo nets (kg/m3) were separated, weighed, and recorded. Samples from neuston and combined 333-μm mesh and 500-μm bongo tows were preserved in a 100% ethanol solution for transport back to the lab. Sea surface temperature (SST, °C), salinity, and dissolved oxygen (mg/L) were measured at the surface of each station using a Sonde 6920 Environmental Monitoring System (YSI Inc., Yellow Springs, Ohio, United States). Other oceanographic parameters at each station were determined using remotely sensed data accessed through Copernicus Marine Environmental Monitoring Service1 and the marine geospatial ecology toolbox (version 0.8a44) in ArcGIS (version 10.0). Sea surface height (SSH, m) data were calculated weekly at a resolution of 1/4 degree using satellite altimetry measurements (GLOBAL_ANALYSIS_PHYS_001_020) from Copernicus2. Distance to the Loop Current was estimated by measuring the linear distance from the edge of the feature (km), based on the 20-cm SSH contour following Randall et al. (2015) using the Spatial Analyst toolbox in ArcGIS. Water depth at each station was estimated from NOAA National Geophysical Data Center using the GEODAS US Coastal Relief Model Grid with a grid cell size of 3 arc-s3.
Samples from each station were sorted under Leica MZ stereomicroscope in the laboratory and fish larvae were isolated and preserved in 70% ethanol solution. All fish larvae were identified to family through visual identification following keys in Richards (2006), with family used as the taxonomic level for assessing biodiversity (Hernandez et al., 2013). Although TF and H’ were estimated from identification to family level, genetic approaches such as High resolution Melting Analysis and Polymerase chain reaction were often used to determine species identification for certain taxa, which provided confirmation of assignments to the family level for all individuals assayed (Smith et al., 2009). Issues that led to identification of unknown specimens included trawl damage to the specimen and/or individuals too small to accurately identify. Damaged samples had either a significant amount of tissue missing or only part of the body was found. Individuals with a total standard length of less than 2 mm were too small to accurately identify in some cases.
Two diversity measures were applied to the larval fish assemblages. Species richness (S) is commonly used to represent total number of species per sample but here we estimated TF as the number of families present in each sample. Similarly, Shannon diversity (H’) was based on diversity at the family level following the equation
where n is the total number of individuals and fi is the number of individuals for each family.
Diversity measures TF and H’ were used for statistical testing, with each station consisting of both surface layer and mixed layer samples. A two-way analysis of variance (ANOVA) was used to examine effects of station location and month-year date with separate models developed using TF and H’ as dependent variables. A Bonferroni adjustment was used to account for multiple testing to decrease chances for a Type I error. Two-way ANOVAs were also used to examine inter- and intra-annual differences in both TF and H’ for surface layer, mixed layer, and combined samples. Tukey’s honestly significant difference (HSD) test was used to test for post hoc differences among means. All statistical analyses were run using R (version 3.4.2) with alpha set at 0.05 (Wood, 2011; Oksanen et al., 2017).
Generalized additive models were used to examine the influence of oceanographic factors for varying time periods (month, year) on TF and H’. Explanatory variables used in GAMs were month, year, SST, SSH, distance to Loop Current boundary, salinity (SAL), dissolved oxygen (DO), depth, invertebrate biomass, and Sargassum biomass. GAMs are extensions of general linear models and allow fixed effects to be modeled by using a smoothing function (Guisan et al., 2002). General GAM construction follows the equation:
Where E[y] equals the expected values of the response variable (TF or H’), g represents the link function, β0 equals the intercept, x represents one of k explanatory variables, and Sk represents the smoothing function of each respective explanatory variable. In addition to oceanographic data collected at each station described earlier, remotely sensed data (SSH, distance to Loop Current) were included as explanatory variables in GAMs. Spatial autocorrelation was not deemed to be an issue for fixed stations given the dynamic nature of oceanographic conditions across our sampling corridor. A manual procedure was used to identify influential variables on TF and H’, and the final model for each diversity measure was based on minimizing the Akaike information criterion (AIC). Collinearity among variables was examined using Spearman’s test and variance inflation factor (VIF), (ρ > 0.60 and VIF > 5); collinearity was not found to be an issue thus all environmental variables were tested. A manual backward stepwise selection process was used to remove explanatory variables that did not influence TF or H’ based models. Stepwise selection ended when all remaining variables were significant (p > 0.05) or the AIC value started to increase when non-significant variables were removed. Percent deviance explained (DE) was calculated for each model to examine overall fit. Once the final model was selected, each variable was removed individually to see the response in ΔAIC, and ΔDE in order to assess the relative importance of each predictor variable following Rooker et al. (2012).
A total of 17,091 larvae (N = 9,551 in 2015 and N = 7,540 in 2016) comprising 99 families were collected over 2 years of sampling in the NGoM (Table 1). The top five families by percent composition in 2015 from the surface layer accounted for over 70% of the larvae collected: carangids (jacks), clupeids (herrings), exocoetids (flyingfishes), scombrids (mackerels and tunas), and istiophorids (billfishes). For the mixed layer in 2015, myctophids (lanternfishes), scombrids, carangids, gonostomatids (bristlemouths), and gobiids (gobies) were the dominant families by percent composition (Table 1). General trends in catch percent composition persisted in 2016 and numerically dominant families in the surface layer were carangids, exocoetids, scombrids, istiophorids, and hermiramphids (halfbeaks), with carangids alone accounting for nearly 40% of the larvae collected. Deep-pelagic taxa again dominated the mixed layer from 2016 with 41% of the catch comprised of myctophids, gonostomatids, and bregmacerotids (codlets) larvae. A small percentage of the fish larvae collected (∼6%) could not be positively identified because of damage or the larvae were too small.
Table 1. Catch data of larvae in the northern Gulf of Mexico in 2015 and 2016 from surface (0–1 m with neuston tows) and mixed layer (0–100 + m with oblique bongo tows).
Distinct differences in the percent composition of certain families were observed between months for both surface and mixed layer samples; albeit certain taxa were consistently high in both June and July (Table 1). In the surface layer, exocoetids accounted for the largest percentage of the total catch in June 2015 and June 2016 compared to July 2015 and July 2016, whereas carangids were most common in the surface layer in July 2015 and July 2016 as compared to June 2015 and June 2016. July 2015 had a high percent composition of clupeids compared to June 2015 and June and July of 2016. Myctophids dominated the mixed layer for both months and years sampled except July 2015, when scombrids were the dominant taxa in the mixed layer. Scombrids were abundant for other years and months sampled. Carangids were consistently in the top three families based on percent composition and consistently caught in all months and years in both surface and mixed layer samples (Table 2).
Table 2. Catch data of top eight larval families in the northern Gulf of Mexico in 2015 and 2016 from surface (0–1 m with neuston tows) and mixed layer (0–100 + m with oblique bongo tows).
Of the 99 families collected, the percent frequency of occurrence by station of 44 families was greater than 10% in either surface or mixed layer samples in 2015 or 2016 (Table 1), representing high diversity across stations. In the surface layer, exoceotids, carangids, scombrids, and hemiramphids were relatively common and present at the majority of stations sampled across both years (Table 1). Several families were also common to the mixed layer with percent frequency of occurrence from combined years being over 50%, including myctophids, bregmacerotids, and scombrids. Certain taxa were common in 1 year but conspicuously less common in the other year sampled, in particular scombrids and carangids.
Biodiversity: TF and H’
Taxonomic richness in the surface layer and mixed layer varied between the 2 years surveyed (ANOVA, p < 0.001), with mean TF per station being higher in 2015 (6.3 ± 2.8) than 2016 (4.6 ± 3.2) for the surface station, and similarly, with mean TF per station being higher for the mixed layer in 2015 (12.4 ± 4.6) than 2016 (10.7 ± 4.7; Figure 2). Mean TF per station was similar between June (5.9 ± 2.6) and July (5.2 ± 3.5) surveys (ANOVA, p > 0.05) for surface stations. Mean TF per station in the mixed layer was significantly higher in June (12.9 ± 4.2) than July (10.4 ± 4.9) surveys (ANOVA, p < 0.001).
Figure 2. Comparison of taxonomic richness (TF) and Shannon diversity (H’) of all ichthyoplankton collected in the surface (0–1 m with neuston tows) and mixed layer samples (0–100 + m with oblique bongo tows) in 2015 and 2016 in the Northern Gulf of Mexico. Error bars represent standard error of the mean.
Shannon diversity (H’) in the surface layer and mixed layer (Figure 2) was different between years (ANOVA, p < 0.001), with mean H’ per station being higher in 2015 (1.4 ± 0.4 surface, 2.0 ± 0.4 mixed) than 2016 (1.2 ± 0.6 surface, 1.7 ± 0.5 mixed). Mean H’ was significantly different between months as well for both layers (ANOVA, p < 0.05), with June (1.3 ± 0.4 surface, 2.0 ± 0.3 mixed) being higher than July (1.0 ± 0.6 surface, 1.8 ± 0.5 mixed).
Both TF and H’ varied spatially in the NGoM, with the most pronounced horizontal trend occurring between the north and south sampling transects and in areas impacted by MARS (Figure 3), where salinity was lower. In general, mean TF and H’ was higher along the northern transect (28.0°N) across all months and years sampled (Figure 2). In both 2015 and 2016, the northern transect had higher mean TF (10.5 and 9.1) and mean H’ (1.8 and 1.4), compared to TF (8.2 and 6.4), and H’ (1.6 and 1.2) for the southern transect (27.0°N). Marked differences were observed in both indices between surface and mixed layer samples (Figure 2). In 2015 and 2016, mean TF (12.4 and 10.9), and H’ (2.0 and 1.8) were higher in the mixed layer compared to mean TF (6.3 and 4.8) and H’ (1.4 and 0.9) in the surface layer, which is not surprising given that oblique bongo tows in the mixed layer sample a significantly larger fraction of the water column. In 2015, areas of high TF were associated with the Loop Current boundary. June and July of 2015 had the highest northern intrusion of the Loop Current, while the 2016 July Loop Current had already detached into a large, anticyclonic Loop Current eddy. In 2015, areas of high TF and H’ were located near the Loop Current boundary.
Figure 3. Shannon index (H’; black) and taxonomic richness (TF; white) of larvae collected in June and July of 2015 and 2016 in the Northern Gulf of Mexico. Circles represent diversity of larvae per station. Location of the Loop Current and warm eddies is represented in red and cold core eddies are represented in blue.
Fish Habitat Modeling
Final TF–based (AIC = 835.0, DE = 37.8%) and H’-based (AIC = 224.5, DE = 40.9%) GAMs for collections from the surface layer included all environmental variables tested: SST, SSH, salinity, dissolved oxygen, invertebrate biomass, and distance to Loop Current, while Sargassum biomass was additionally included in the neuston net samples (Table 3). Based on ΔAIC and ΔDE (%), salinity (ΔAIC = 13.0, ΔDE = 5.0%), Sargasum biomass (ΔAIC = 4.6, ΔDE = 4.1%), and invertebrate biomass (ΔAIC = 8.2, ΔDE = 3.7%) were the most influential explanatory variables in the TF-based GAM. Dissolved oxygen (ΔAIC = 21.2, ΔDE = 7.8%) was again influential in the H’-based GAM along with SST (ΔAIC = 5.8, ΔDE = 4.1%) and SSH (ΔAIC = 5.0, ΔDE = 2.3%), albeit to a lesser degree. Responses plots from GAMs indicated that TF and H’ for fish larvae in the surface layer were higher at high sea surface temperatures (>28°C), lower sea surface heights (0.3–0.5 m), lower salinity, higher invertebrate biomass, farther from the Loop Current, and at lower Sargassum biomass (Figures 4, 5).
Table 3. Akaike information criterion (AIC), deviance explained (DE), and variables retained in the final GAMs based on taxonomic richness (TF), and Shannon diversity (H’) for surface samples (0–1 m with neuston tows), and mixed layer samples (0–100 + m with oblique bongo tows) collected in 2015 and 2016.
Figure 4. Response plots for 2015 oceanographic variable of the surface sample (0–1 m with neuston tows) taxonomic richness (TF) from full generalized additive model (GAM). Plots include sea surface temperature (°C), sea surface height (m), salinity, dissolved oxygen (mg/L), invertebrate biomass (kg m–3), distance to Loop Current (km), and Sargassum density (kg m–3). Solid lines represent smoothed values and the shaded area represents 95% confidence intervals. Dashed line displayed at y = 0 on response plots.
Figure 5. Response plots for 2015 oceanographic variable of the surface sample (0–1 m with neuston tows) Shannon diversity (H’) from full generalized additive model (GAM). Plots include sea surface temperature (°C), sea surface height (m), salinity, dissolved oxygen (mg L–1), invertebrate biomass (kg m–3), distance to Loop Current (km), and Sargassum density (kg m–3). Solid lines represent smoothed values and the shaded area represents 95% confidence intervals. Dashed line displayed at y = 0 on response plots.
Final TF- (AIC = 995.9, DE = 41.8%) and H’ – (AIC = 131.6, DE = 42.6%) based GAMs for collections from the mixed layer also included all environmental variables tested (Table 3). Based on ΔAIC and ΔDE (%), salinity (ΔAIC = 12.8, ΔDE = 3.5%), invertebrate biomass (ΔAIC = 10.5, ΔDE = 2.4%), and SST (ΔAIC = 6.2, ΔDE = 2.1%) were the most influential explanatory variables in the TF-based GAM. SST (ΔAIC = 15.8, ΔDE = 6.3%) in the H’-based GAM along with SSH (ΔAIC = 12.3, ΔDE = 6.1%) and invertebrate biomass (ΔAIC = 4.4, ΔDE = 2.0%) were the most influential variables (Table 3). Responses plots from GAMs indicated that TF and H’ for fish larvae in the mixed layer were higher at SSTs above 28°C, lower sea surface heights (0.3–0.5 m), lower salinity, higher invertebrate biomass, and farther from the Loop Current (Figures 6, 7).
Figure 6. Response plots for 2016 oceanographic variable of the bongo net taxonomic richness (TF) from full generalized additive model (GAM). Plots include sea surface temperature (°C), sea surface height (m), salinity, dissolved oxygen (mg L–1), invertebrate biomass (kg m–3), and distance to Loop Current (km). Solid lines represent smoothed values and the shaded area represents 95% confidence intervals. Dashed line displayed at y = 0 on response plots.
Figure 7. Response plots for 2016 oceanographic variable of the bongo net Shannon diversity (H’) from full generalized additive model (GAM). Plots include sea surface temperature (°C), sea surface height (m), salinity, dissolved oxygen (mg L–1), invertebrate biomass (kg m–3), and distance to Loop Current (km). Solid lines represent smoothed values and the shaded area represents 95% confidence intervals. Dashed line displayed at y = 0 on response plots.
Larvae of epipelagic and mesopelagic species were collected throughout our sampling corridor in both surface and mixed layer samples. Common epipelagic fishes (e.g., carangids, exocoetids, and scombrids) accounted for almost half of the fish percent composition assemblage in surface waters, and the dominance of larval taxa that inhabit the epipelagic zone as adults has also been reported in ichthyoplankton surveys of the Straits of Florida (Richardson et al., 2010), tropical Atlantic Ocean (Katsuragawa et al., 2014), and the Pacific Ocean (Vilchis et al., 2009). Densities of these taxa were markedly higher than any mesopelagic taxon collected (e.g., myctophids∼ 0.1 larvae 1000 m–3) in the surface layer. In contrast, mesopelagic fishes, most notably myctophids, bregmacerotids, and gonostomatids, dominated percent composition collections in the mixed layer, with myctophids alone accounting for nearly one quarter of the larval fish assemblage in the upper 100 m and present at high densities (>40 larvae 1000 m–3). These results are consistent with the findings that mesopelagic larval fishes dominated the catch composition in the mixed layer of other regions in the Atlantic Ocean, including the Mediterranean Sea (Alemany et al., 2010; Torres et al., 2011). Direct comparisons with other studies are limited because the majority of surveys using comparable sampling gears focused on specific taxa rather than the entire family level ichthyoplankton assemblage (e.g., Rooker et al., 2013; Kitchens and Rooker, 2014; Randall et al., 2015); however, an earlier study by Richards (1993) characterized the ichthyoplankton assemblage in the NGoM using bongo net tows to 200 m with an observed TF of 100, of which our study is highly similar (TF = 99). They also reported that myctophids, carangids, and gonostomatids were commonly collected in the upper 200 m, supporting our observation that the mixed layer represents important habitat of mesopelagic fishes during the early life period.
Mesopelagic fish larvae, particularly myctophids, bregmacerotids, and gonostomatids, were numerically dominant by percent composition in samples from the mixed layer. At night, juveniles and adults of these taxa are known to migrate from the mesopelagic zone to the epipelagic zone (D’Elia et al., 2016); Rodriguez et al. (2006) also reported high catches of mesopelagic fishes in the epipelagic zone of the Canaries-African Coastal Transition Zone. All samples were collected during the day and their presence in the upper 100 m of the water column suggests that the earliest life stages remain in the epipelagic zone in the daytime hours, and diel vertical migration between the zones commences later (Moku et al., 2003). Several midwater taxa, including species within these three families, hatch in the epipelagic zone and begin migration as they transition from larvae to juveniles (Watanabe et al., 2002). A large fraction of the individuals collected in our surveys from these families were relatively small (<5 mm SL) with many specimens appearing to be recently hatched, likely accounting for the high numbers of mesopelagic taxa in our bongo net collections from the mixed layer.
Taxonomic richness and Shannon diversity (H’) varied across the sampling corridor, with estimates of both diversity measures generally higher along the northern transect (28.0°N). It is possible, even likely, that TF and H’ were higher along the northern transect because this region borders the outer continental shelf, and thus both continental shelf and oceanic species are likely present in this region, with mixed communities leading to higher diversity. Many of the families of fish larvae collected along the northern transect in this study were indicative of continental shelf assemblages (McEachran and Fechhelm, 2010), and a greater presence of continental shelf species was often found at stations impacted by freshwater inflow (green water, lower salinity, and higher turbidity). That said, the northern transect stations were seaward of the continental shelf in slope waters where fish larvae of oceanic taxa (e.g., exocoetids, istiophorids, and scombrids) are known to occur. While the northern transect was essentially a mixed assemblage of both continental shelf and oceanic taxa, nearly all of the stations in the southern transect (27.0°N) were in oceanic waters, which explains the high abundances of exocoetids and scombrids. As a result, the larval fish assemblage was primarily comprised of oceanic species with limited contribution of continental shelf species, leading to lower overall diversity or reduced TF and H’ relative to stations in the northern transect.
Assemblage diversity also varied temporally and both TF and H’ were generally higher in June than July in both sampling years. In the surface layer, exocoetids, mullids, and clupeids comprised a significantly higher percentage of the assemblage in June for both years, while carangids and scombrids were higher in July. In the mixed layer, myctophids and bregmacerotids dominated the June assemblage while carangids and scombrids comprised a greater proportion of the catch in July. Temporal shifts in the abundance and assemblage composition of larval fishes are often attributed to seasonal patterns of spawning in the Gulf of Mexico (Sanvicente-Añorve et al., 1998), equatorial Atlantic Ocean (Mourato et al., 2014), and inland waters off Australia (King et al., 2016), but other factors such as the position of mesoscale features or oceanographic conditions are also known to influence presence and spatial distribution of fish larvae (Cowen et al., 2000; Randall et al., 2015; Cornic et al., 2018). Results of the present study are consistent with other studies conducted in the NGoM that indicate higher numbers of exocoetids in June (Randall et al., 2015) and higher numbers of scombrids in July (Cornic et al., 2018), with both studies attributing seasonal patterns in larval abundance to temporal variation in spawning activity. Carangids, myctophids, and bregmacerotids are known to display variable spawning throughout the year (Moku et al., 2003; Ditty et al., 2004; Namiki et al., 2007), and this may have contributed to observed temporal shifts in the presence of certain taxa in our collections. Inter-annual variability in the abundance and diversity of larval fishes are common and often associated with temporal shifts in the location of mesoscale features (Richardson et al., 2010; Rooker et al., 2013). In 2015, a higher northward penetration of the Loop Current corresponded with higher TF and H’, while the northward penetration of the Loop Current was reduced in 2016 and lower TF and H’ were observed. This suggests that diversity of the larval fish assemblage in this region is related to the northward extension of the Loop Current, perhaps due to physical convergence, as the Loop Current water itself is highly oligitrophic, and these results are consistent with previous studies (Rooker et al., 2012; Cornic et al., 2018).
The intrusion of the MARS also affects the distribution and abundance of fish larvae in the NGoM (Govoni et al., 1989; Grimes and Finucane, 1991), and a primary physicochemical indicator of MARS intrusion is salinity. In the present study, salinity was an important explanatory variable in both TF and H’ GAMs, indicating that assemblage diversity for larval fishes may be highly dependent on the spatial configuration of lower salinity intrusions from MARS. Freshwater discharge from MARS in the spring creates a salinity gradient in the NGoM that ranges from the river delta to the continental shelf over the summer months (Schiller et al., 2011; O’Connor et al., 2016). Stations with highest diversity of larval fishes were often found in areas with lower salinity, suggesting that areas impacted by freshwater inflow may serve as habitat for a wider range of taxa, including both continental shelf and oceanic species. We observed that both TF and H’ were higher in low salinity areas because both continental shelf taxa (serranids, lutjanids, and sciaenids) and oceanic taxa (exocoetids, scombrids, and istiophorids) were often present in collections, leading to higher diversity. Generally, the MARS plume is larger in area and outflow in June relative to July as the greatest amount of freshwater is discharged in the spring (Aulenbach et al., 2007). Results from this study showed higher diversity of larval fishes in our June surveys for both 2015 and 2016, suggesting that the influx of freshwater from the MARS impacted the assemblage composition and the location of areas with higher TF and H’. Moreover, 2015 had significantly higher diversity measures than 2016, which also appears associated with the MARS plume, as there was a greater freshwater discharge in 2015 (896,600 ft3 s–1) than in 2016 (539,150 ft3 s–1)4. MARS freshwater inflow into the oceanic ecosystem is also associated with an influx of nutrients that increase primary and secondary productivity (Lohrenz et al., 1997; O’Connor et al., 2016) and likely increases food opportunities for larval fishes. Thus, areas impacted by MARS may represent favorable habitat that supports growth and survival during early life (Grimes and Finucane, 1991), which may have also contributed to higher TF and H’ observed at stations influenced by MARS. This is consistent with findings that show physiochemical processes, such as salinity, have been shown to influence larval fish distribution and the interaction between larval fish and the surrounding environment ultimately determines survival and recruitment success (Fogarty et al., 1991; Bruce et al., 2001).
Spatial variability in SSH and SST were also important drivers of TF and H’ in this study. GAMs indicated that diversity increased in areas with lower SSH (cold-core eddies) and mid-level water temperatures (28–30°C). Cold-core eddies are associated with upwelling, as cold, nutrient-rich waters in these features support higher primary productivity (Biggs et al., 1997), and assemblage diversity has been shown to increase in areas of elevated productivity in both marine and terrestrial ecosystems (Waide et al., 1999; Cardinale et al., 2002). Convergent zones where two mesoscale features meet are also responsible for aggregating plankton and are therefore favorable conditions for the survival of fish larvae in the GoM (Bakun, 2006) as well as several other marginals seas including the Mediterranean Sea (Alemany et al., 2010), Caribbean Sea (Erisman et al., 2017), and Gulf of California (Avendaño-Ibarra et al., 2013), potentially leading to the increased diversity of larval fishes along these features. In addition to the fronts physically transporting larvae to convergent zones, these zones also increase feeding opportunities for larvae, leading to higher survival rates (Bakun, 2006; Acha et al., 2018; Sato et al., 2018). Results from recent studies in the NGoM of pelagic larval fishes yield similar results, with billfishes, dolphinfishes, and tunas being associated with frontal features and convergent zones (Rooker et al., 2013; Kitchens and Rooker, 2014; Cornic et al., 2018).
Baseline estimates of biodiversity and assemblage structure are critical understanding the impacts of anthropogenic stressors on marine ecosystem, and this study serves as reference point for assessing the impacts of changing conditions onlarval fish assemblages in oceanic waters of the NGoM. Biodiversity hotspots of fish larvae in the NGoM were located in areas where continental shelf and oceanic communities coalesced, with TF and H’ highest along the northern transect due to the influence of both MARS and mesoscale oceanographic features (Loop Current), confirming that biodiversity hotspots for larval fishes (high TF and H’) in the NGoM will occur primarily in convergence zones (frontal features). As a result, factors that alter physicochemical conditions (i.e., freshwater inflow linked to MARS), or the geographic position of these oceanographic features (shifts in western boundary currents due to climate change; Chen et al., 2019) will ultimately influence assemblage diversity in the NGoM, possibly leading to broader changes in ecosystem structure and stability. Additionally, our assumption that fish larvae of numerically dominant families that use the epipelagic zone as adults (istiophorids, carangids, scombrids, and exocoetids, etc.) account for the majority of ichthyoplankton in the surface layer, while the mixed layer will have a significant contribution of mesopelagic taxa, was also supported. Mesopelagic families, particularly myctophids and gonostomatids were an important component of the mixed layer assemblage, and this finding highlights the ecological connectivity that occurs between epipelagic and deep pelagic zones.
Data Availability Statement
The data are publicly available through the Gulf of Mexico Research Initiative Information and Data Cooperative (GRIIDC) at https://data.gulfresearchinitiative.org (doi: 10.7266/N7PZ576R, doi: 10.7266/N72B8W3M, doi: 10.7266/N76M356C, and doi: 10.7266/N76W98G7).
The animal study was reviewed and approved by Institutional Animal Care and Use Committee.
CM, KC-S, MC, TS, and JR contributed to the design, collection, identification, and analysis of biological samples. CM and JR wrote the manuscript. All authors contributed to the article and approved the submitted version.
This research was made possible by a grant from The Gulf of Mexico Research Initiative.
Conflict of Interest
The authors declare that the research was conducted in the absence of any commercial or financial relationships that could be construed as a potential conflict of interest.
We thank all the scientists and crew who participated in the surveys and laboratory work conducted over the course of this project. In particular, a special thanks to M. Dance, J. Ditty, D. Johnson, J. Lee, L. Podsim, J. Plumlee, L. Randall, T. Richards, B. Saurez, C. Steffen, and D. Wells.
- ^ http://marine.copernicus.eu/
- ^ http://marine.copernicus.eu/services-portfolio/access-to-products/
- ^ http://www.ngdc.noaa.gov/mgg/gdas/gd_designagrid.html
- ^ https://waterdata.usgs.gov/
Acha, E. M., Ehrlich, M. D., Muelbert, J. H., Pájaro, M., Bruno, D., Machinandiarena, L., et al. (2018). “Ichthyoplankton associated to the frontal regions of the southwestern atlantic,” in Plankton Ecology of the Southwestern Atlantic: From the Subtropical to the Subantarctic Realm, eds M. S. Hoffmeyer, M. E. Sabatini, F. P. Brandini, D. L. Calliari, and N. H. Santinelli (Berlin: Springer International Publishing), 219–246. doi: 10.1007/978-3-319-77869-3_11
Alemany, F., Quintanilla, L., Velez-Belchi, P., Garcia, A., Corte’s, D., Rodríguez, J. M., et al. (2010). Characterization of the spawning habitat of Atlantic bluefin tuna and related species in the Balearic Sea (western Mediterranean). Prog. Oceanogr. 86, 21–38. doi: 10.1016/j.pocean.2010.04.014
Aulenbach, B. T., Buxton, H. T., Battaglin, W. T., and Coupe, R. H. (2007). Streamflow and Nutrient Fluxes of the Mississippi-Atchafalaya River Basin and Sub Basins for the Period of Record Through 2005. Open-File Report. 2007–1080. Reston, VA: U.S. Geological Survey.
Avendaño-Ibarra, R., Godínez-Domínguez, E., Aceves-Medina, G., González-Rodríguez, E., and Trasviña, A. (2013). Fish larve response to biophysical changes in the gulf of California, Mexico (Winter-Summer). J. Mar. Sci. 2013, 1–17. doi: 10.1155/2013/176760
Bakun, A. (2006). Fronts and eddies as key structures in the habitat of marine fish larvae: opportunity, adaptive response and competitive advantage. Sci. Mari. 70(Suppl. 2), 105–122. doi: 10.3989/scimar.2006.70s2105
Bruce, B. D., Evans, K., Sutton, C. A., Young, J. W., and Furlani, D. M. (2001). Influence of mesoscale occeanographic processes on larval distribution and stock structure in jackass morwong (Nemadactylus macropterus: Cheilodactylidae). ICES J. Mar. Sci. 58, 1072–1080. doi: 10.1006/jmsc.2001.1099
Cornic, M., Smith, B. L., Kitchens, L. L., Bremer, J. R. A., and Rooker, J. R. (2018). Abundance and habitat associations of tuna larvae in the surface water of the Gulf of Mexico. Hydrobiologia 806, 29–46. doi: 10.1007/s10750-017-3330-0
Dagg, M. J., and Breed, G. A. (2003). Biological effects of Mississippi River nitrogen on the northern Gulf of Mexico-a review and synthesis. J. Mar. Syst. 43, 133–152. doi: 10.1016/j.jmarsys.2003.09.002
D’Elia, M., Warren, J. D., Rodriguez-Pinto, I., Sutton, T. T., Cook, A., and Boswell, K. M. (2016). Diel variation in the vertical distribution of deep-water scattering layers in the Gulf of Mexico. Deep Sea Res. Part I-Oceanogr. Res. Pap. 115, 91–102. doi: 10.1016/j.dsr.2016.05.014
Ditty, J. G., Shaw, R. F., and Cope, J. S. (2004). Distribution of carangid larvae (Teleostei: Carangidae) and concentrations of zooplankton in the northern Gulf of Mexico, with illustrations of early Hemicaranx amblyrhynchus and Caranx spp. larvae. Mar. Biol. 145, 1001–1014. doi: 10.1007/s00227-004-1381-z
Erisman, B., Heyman, W., Kobara, S., Ezer, T., Pittman, S., Aburto-Oropeza, O., et al. (2017). Fish spawning aggregations: where well-placed management actions can yield big benefits for fisheries and conservation. Fish Fish. 18, 128–144. doi: 10.1111/faf.12132
Game, E. T., Grantham, H. S., Hobday, A. J., Pressey, R. L., Lombard, A. T., and Beckley, L. E. (2009). Pelagic protected areas: the missing dimension in ocean conservation. Trends Ecol. Evol. 24, 360–369.
Gamfeldt, L., Lefcheck, J. S., Byrnes, J. E., Cardinale, B. J., Duffy, J. E., and Griffin, J. N. (2014). Marine biodiversity and ecosystem functioning: what’s known and what’s next? Oikos 124, 252–265. doi: 10.1111/oik.01549
Grimes, C. B., and Finucane, J. H. (1991). Spatial distribution and abundance of larval and juvenile fish, chlorophyll and macrozooplankton around the Mississippi River discharge plume, and the role of the plume in fish recruitment. Mar. Ecol. Prog. Ser. 75, 109–119. doi: 10.3354/meps075109
Guisan, A., Edwards, T. C., and Hastie, T. (2002). Generalized linear and generalized additive models in studies of species distributions: setting the scene. Ecol. Model. 157, 89–100. doi: 10.1016/s0304-3800(02)00204-1
Hernandez, F. J. Jr., Carassou, L., Graham, W. M., and Powers, S. P. (2013). Evaluation of the taxonomic sufficiency approach for ichthyoplankton community analysis. Mar. Ecol. Prog. Ser. 491, 77–90. doi: 10.3354/meps10475
Hernandez, F. J. Jr., Powers, S. P., and Graham, W. M. (2010). Seasonal variability in ichthyoplankton abundance and assemblage composition in the northern Gulf of Mexico off Alabama. Fish. Bull. 108, 193–207.
Katsuragawa, M., Dias, J. F., Harari, C., Namiki, C., and Zani-Teixeira, M. L. (2014). Patetrns in larval fish assemblaged under the influence of the Brazil Current. Cont. Shelf Res. 89, 103–117. doi: 10.1016/j.csr.2014.04.024
King, A. J., Gwinn, D. C., Tonkin, Z., Mahoney, J., Raymond, S., Beesley, L., et al. (2016). Using abiotic drivers of fish spawning to inform environmental flow management. J. Appl. Ecol. 53, 34–43. doi: 10.1111/1365-2664.12542
Lewison, R., Hobday, A. J., Maxwell, S., Hazen, E., Hartog, J. R., Dunn, D. C., et al. (2015). Dynamic ocean management: identifying the critical ingredients of dynamic approaches to ocean resource management. BioScience 65, 486–498. doi: 10.1093/biosci/biv018
Lohrenz, S. E., Fahnenstiel, G. L., Redalje, D. J., Lang, G. A., Chen, X., and Dagg, M. J. (1997). Variations in primary production of northern Gulf of Mexico continental shelf waters linked to nutrient inputs from the Mississippi River. Mar. Ecol. Prog. Ser. 155, 45–54. doi: 10.3354/meps155045
Mittermeier, R. A., Turner, W. R., Larsen, F. W., Brooks, T. M., and Gascon, C. (2011). “Global biodiversity conservation: the critical role of hotspots,” in Biodiversity Hotspots, eds F. Zachos and J. Habel (Berlin: Springer). doi: 10.1016/j.gecco.2014.12.008
Mourato, B. L., Hazin, F., Bigelow, K., Musyl, M., Carvalho, F., and Hazin, H. (2014). Spatio-temporal trends of sailfish, Istiophorus platypterus catch rates in relation to spawning ground and environmental factors in the equatorial and southwestern Atlantic Ocean. Fish. Oceanogr. 23, 32–44. doi: 10.1111/fog.12040
Namiki, C., Bonecker, A. C. T., and De Castro, M. S. (2007). Occurrence and abundance of three larval codlet species (Bregmacerotidae, Teleostei) in the Southwest Atlantic Ocean (12-22 degrees S). J. Appl. Ichthyol. 23, 136–141. doi: 10.1111/j.1439-0426.2006.00818.x
Nonaka, R. H., Matsuura, Y., and Suzuki, K. (2000). Seasonal variation in larval fish assemblages in relation to oceanographic conditions in the Abrolhos Bank region off eastern Brazil. Fish. Bull. 98, 767–784.
O’Connor, B. S., Muller-Karger, F. E., Nero, R. W., Hu, C. M., and Peebles, E. B. (2016). The role of Mississippi river discharge in offshore phytoplankton blooming in the northeastern Gulf of Mexico during August 2010. Remote Sens. Environ. 173, 133–144. doi: 10.1016/j.rse.2015.11.004
Oksanen, J., Guillaume, F., Blanchet, F., Friendly, M., Kindt, R., Legendre, P., et al. (2017). vegan: Community Ecology Package. R Package Version 2.4-4. Avaliable online at: https://CRAN.R-project.org/package=vegan (accessed July, 2019).
Randall, L. L., Smith, B. L., Cowan, J. H., and Rooker, J. R. (2015). Habitat characteristics of bluntnose flyingfish Prognichthys occidentalis (Actinopterygii. Exocoetidae), across mesoscale features in the Gulf of Mexico. Hydrobiologia 749, 97–111. doi: 10.1007/s10750-014-2151-7
Richardson, D. E., Llopiz, J. K., Guigand, C. M., and Cowen, R. K. (2010). Larval assemblages of large and medium-sized pelagic species in the Straits of Florida. Prog. Oceanogr. 86, 8–20. doi: 10.1016/j.pocean.2010.04.005
Rijnsdorp, A. D., Peck, M. A., Engelhard, G. H., Mollmann, C., and Pinnegar, J. K. (2009). Resolving the effect of climate change on fish populations. ICES J. Mar. Sci. 66, 1570–1583. doi: 10.1093/icesjms/fsp056
Rodriguez, J. M., Hernandez- Leon, S., and Barton, E. D. (2006). Vertical distriv=bution of fish larvae in the Canaries-African coastal transition zone in the summer. Mar. Biol. 149, 885–897. doi: 10.1007/s00227-006-0270-z
Rooker, J. R., Kitchens, L. L., Dance, M. A., Wells, R. J., Falterman, B., and Cornic, M. (2013). Spatial, temporal, and habitat-related variation in abundance of pelagic fishes in the Gulf of Mexico: potential implications of the deepwater horizon oil spill. PLoS One 8:e76080. doi: 10.1371/journal.pone.0076080
Rooker, J. R., Simms, J. R., Wells, R. J. D., Holt, S. A., Holt, G. J., Graves, J. E., et al. (2012). Distribution and habitat associations of billfish and swordfish larvae across mesoscale features in the Gulf of Mexico. PLoS One. 7:e34180. doi: 10.1371/journal.pone.0034180
Sato, M., Barth, J. A., Benoit-Bird, K. J., Pierce, S. D., Cowles, T. J., Brodeur, R. D., et al. (2018). Coastal upwelling fronts as a boundary for planktivorous fish distributions. Mar. Ecol. Prog. Ser. 595, 171–186. doi: 10.3354/meps12553
Schiller, R. V., Kourafalou, V. H., Hogan, P., and Walker, N. D. (2011). The dynamics of the Mississippi River plume: Impact of topography, wind and offshore forcing on the fate of plume waters. J. Geophys. Res. Oceans 116:C06029.
Shulzitski, K., Sponaugle, S., Hauff, M., Walter, K., D’Alessandro, E. K., and Cowen, R. K. (2015). Close encounters with eddies: oceanographic features increase growth of larval reef fishes during their journey to the reef. Biol. Lett. 11:20140746. doi: 10.1098/rsbl.2014.0746
Smith, B. L., Lu, C.-P., and Alvarado Bremer, J. R. (2009). High-resolution melting analysis (HRMA): a highly sensitive inexpensive genotyping alternative for population studies. Mol. Ecol. Resour. 10, 193–196. doi: 10.1111/j.1755-0998.2009.02726.x
Torres, A. P., Reglero, P., Balbin, R., Urtizberea, A., and Alemany, F. (2011). Coexistence of larvae of tuna species and other fish in the surface mixed layer in the NW Mediterranean. J. Plankton Res. 33, 1793–1812. doi: 10.1093/plankt/fbr078
Vilchis, L. I., Balance, L. T., and Watson, W. (2009). Temporal variability of neustonic ichthyoplankton assemblages of the eastern Pacific warm pool: can community structure be linked to climate variability? Deep Sea Res. I 56, 125–140. doi: 10.1016/j.dsr.2008.08.004
Waide, R. B., Willig, M. R., Steiner, C. F., Mittelbach, G., Gough, L., Dodson, S. I., et al. (1999). The relationship Between Productivity and Species Richness. Annu. Rev. Ecol. Systemat. 30, 257–300.
Watanabe, H., Kawaguchi, K., and Hayashi, A. (2002). Feeding habits of juvenile surface-migratory myctophid fishes (family Myctophidae) in the Kuroshio region of the western North Pacific. Mar. Ecol. Prog. Ser. 236, 263–272. doi: 10.3354/meps236263
Wood, S. N. (2011). Fast stable restricted maximum likelihood and marginal likelihood estimation of semiparametric generalized linear models. J. R. Stat. Soc. 73, 3–36. doi: 10.1111/j.1467-9868.2010.00749.x
Keywords: pelagic fishes, ichthyoplankton, mesopelagic, epipelagic, biodiversity, open ocean, Loop Current, Gulf of Mexico
Citation: Meinert CR, Clausen-Sparks K, Cornic M, Sutton TT and Rooker JR (2020) Taxonomic Richness and Diversity of Larval Fish Assemblages in the Oceanic Gulf of Mexico: Links to Oceanographic Conditions. Front. Mar. Sci. 7:579. doi: 10.3389/fmars.2020.00579
Received: 30 July 2019; Accepted: 22 June 2020;
Published: 10 July 2020.
Edited by:Michael Vecchione, National Oceanic and Atmospheric Administration (NOAA), United States
Reviewed by:Andrew Corso, College of William & Mary, United States
Andrew Richard Thompson, National Oceanic and Atmospheric Administration (NOAA), United States
Copyright © 2020 Meinert, Clausen-Sparks, Cornic, Sutton and Rooker. This is an open-access article distributed under the terms of the Creative Commons Attribution License (CC BY). The use, distribution or reproduction in other forums is permitted, provided the original author(s) and the copyright owner(s) are credited and that the original publication in this journal is cited, in accordance with accepted academic practice. No use, distribution or reproduction is permitted which does not comply with these terms.