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Introduction

The arrival of massive amounts of pelagic Sargassum spp. has caused changes in the natural benthic dynamics of Caribbean coastal ecosystems for the last nine years (Gower, Young & King, 2013; Schell, Goodwin & Siuda, 2015). Pelagic Sargassum is a complex of two species, namely S. fluitans and S. natans (Oyesiku & Egunyomi, 2014). Since 2011, extensive masses of Sargassum appeared in unusual ways in oceanic waters off northern Brazil (De Széchy et al., 2012; Sissini et al., 2017), along the West Indies and Caribbean coasts (Gower, Young & King, 2013) from Trinidad to the Dominican Republic (Rodríguez-Martínez, van Tussenbroek & Jordán-Dahlgren, 2016; van Tussenbroek et al., 2017), and along the west African coast from Sierra Leone to Ghana (Smetacek & Zingone, 2013). Wang et al. (2019) recorded that for June 2018, wet biomass reached more than 20 million tons in the Caribbean Sea and Central Atlantic Ocean.

The Mexican Caribbean shores faced atypical massive mats of pelagic Sargassum in the summer of 2015 (van Tussenbroek et al., 2017; Cuevas, Uribe-Martínez & Liceaga-Correa, 2018; Arellano-Verdejo, Lazcano-Hernandez & Cabanillas-Terán, 2019). There was a subsequent decrease during 2016 and 2017, but for most of 2018 and thus far in 2019 influx has increased again. Several studies revealed that these massive mats of Sargassum have a new possible distribution source different from the historic North Atlantic Recirculation Region (NARR) known as “The Sargasso Sea” (Schell, Goodwin & Siuda, 2015). Instead, the most probable origin of the massive influx on the Caribbean shores is the North Equatorial Recirculation Region (NERR) (Johnson et al., 2013; Schell, Goodwin & Siuda, 2015). High oceanic temperatures and nutrient inputs (Franks, Johnson & Ko, 2016; Wang et al., 2018), among other oceanographic coupled patterns such as changes of surface currents, are the most probable causes of this new region of Sargassum flourishment (Johnson et al., 2013; Gower, Young & King, 2013; Sissini et al., 2017). A recent study by Wang et al. (2019) revealed that increases of pelagic Sargassum are driven by upwelling off West Africa during the boreal winter and by Amazon River discharge during the spring and summer. The authors state that recurrent blooms in the Caribbean Sea and tropical Atlantic are likely, highlighting the importance for understanding their effects on existing ecosystems for future planning.

Changes in habitat structure can directly influence trophic dynamics (Hunter & Price, 1992; Sweatman, Layman & Fourqurean, 2017) and have been shown to cause synergistic effects on coral reefs (Smetacek & Zingone, 2013). For example, harmful macroalgae blooms have been recognized as drivers of degradation in coral reef habitats (Lapointe et al., 2005). This has effects on the diversity of reef biota (Bauman et al., 2010; Louime, Fortune & Gervais, 2017) like variations in the sea urchin populations (Lapointe et al., 2010). The carbon and nitrogen flow by macroalgae blooms likely has adverse effects at different scales. Such disturbances from Sargassum, coupled with pre-existing threats on coral reefs, add to the drivers of Anthropocene reef degradation (Alvarez-Filip et al., 2011; Cramer et al., 2012).

The massive decomposition of Sargassum has negative impacts not only on tourism and local fisheries, but on nearshore ecosystems (Solarin et al., 2014; Louime, Fortune & Gervais, 2017). However, few studies assess the trophic impact of Sargassum blooms on benthic communities. Pelagic Sargassum and their attached epiphytic algae can contribute new organic matter to these communities (Rooker, Turner & Holt, 2006; Wang et al., 2018). Therefore, we consider whether or not these new sources of nitrogen and carbon act in a detrimental manner on the trophic chain of benthic communities. The beaching and decomposing of massive Sargassum mats produce hypoxia in near-shore coral reef communities (Rodríguez-Martínez et al., 2019). This effect coupled with high hydrogen sulfide and ammonium concentrations have been shown to cause faunal mortality in the Mexican Caribbean (Rodríguez-Martínez et al., 2019). As a consequence, the coastal environment becomes even more sensitive to degradation agents. To assess these issues, we included measurements of dissolved oxygen in our study.

Evaluating consumers and resources through a trophic approach by tracking the relationships between consumers and prey provides relevant information on the trophic structure and dynamics of a benthic community (Minagawa & Wada, 1984; Vanderklift, Kendrick & Smit, 2006; Behmer & Joern, 2008). Stable isotopes of carbon (δ13C) and nitrogen (δ15N) have been used in marine ecosystems to determine the feeding habits of species (Peterson & Fry, 1987), nutrient migrations within food webs, trophic position of organisms and their contribution at all trophic levels (Vander Zanden & Rasmussen, 1996). It is also possible to trace the origin and transformation of the ingested organic matter and to detect changes in the trophic positions of organisms that coexist in the same habitat (Hobson, 1999; Vanderklift, Kendrick & Smit, 2006; Rodríguez-Barreras et al., 2016).

Stable carbon and nitrogen isotope ratios provide time-integrated information regarding feeding relationships and energy flow through food webs (DeNiro & Epstein, 1981; Peterson & Fry, 1987; Vander Zanden & Rasmussen, 2001). Moreover, stable isotopes can be used to study the trophic niche breadth of a species (Bearhop et al., 2004; Parnell et al., 2010; Phillips et al., 2014). This is directly influenced by consumers and resource input, providing a quantitative assessment of trophic conditions (Newsome et al., 2007; Boecklen et al., 2011). Stable isotope analyses are useful for assessing the health of ecosystems because it is possible to associate the consumers trophodynamics and niche breadth with habitat disturbances (Layman et al., 2007b; Hamaoka et al., 2010). It is also possible to detect changes in the trophic spectrum from anthropogenic impacts or unusual conditions that cause shifts in ecosystems (Wing et al., 2008; Prado, Alcoverro & Romero, 2010; Tomas, Box & Terrados, 2011). In light of the massive arrival of pelagic macroalgae, sea urchin herbivory is a good model to understand variability in the benthic trophic chain, as sea urchins are considered generalist consumers with a plastic feeding habit (Lawrence, 1975; Vanderklift, Kendrick & Smit, 2006). Echinoids have the capability to modify the community structure through foraging behaviour (Carpenter, 1986; Hay & Fenical, 1988; Sala et al., 1998; Eklöf et al., 2008). Thus, the relative position of δ13C vs. δ15N echinoids displayed in a bi-plot can give insights about organism responses to niche shifts, diet variability and habitat modification (Layman et al., 2007a; Layman et al., 2007b; Layman et al., 2012; Sweatman, Layman & Fourqurean, 2017).

The effect of Sargassum and their leachates on the diet of D. antillarum can improve our understanding on the impact on trophic ecology of one of the most important sea urchins of the Mexican Caribbean. The main reason to focus this study on D. antillarum is that this species is and was the major shallow-hard-bottom grazer in our study sites (Jorgensen, Espinoza-Ávalos & Bahena-Basave, 2008; Jordán-Garza et al., 2008). One of the most dramatic events in the Caribbean resulted from the pathogen-driven reduction in the populations of D. antillarum (Lessios et al., 1984) with detrimental ecological consequences like coral-algal phase-shifts. The southern part of Quintana Roo is not an exception encompassing with the effects of the abrupt coastal development and watershed pollution as key drivers along the Costa Maya (Arias-González et al., 2017).

The overarching aim of this study was to determine variations in the relative proportions of carbon and nitrogen of assimilated algal resources and the niche breadth of D. antillarum under massive influx of drifting Sargassum spp. vs. no influx of Sargassum at back reefs. We also aimed to determine whether pelagic Sargassum was a substantial source of energy for D. antillarum. To do this, we compared δ15N and δ13C values of D. antillarum with and without influx of Sargassum to track changes in this species trophic ecology (diet, trophic position and niche breadth). Ultimately, we tested the hypothesis that an influx in Sargassum in coastal ecosystem creates a significant change in the available algal sources and a shift in the trophic structure.

Material & Methods

Study sites

We determined the stable isotopes of carbon and nitrogen for D. antillarum at three reef lagoons (Mahahual, Xahuayxol, and Xcalak) with different distances from the beach to the reef crest (Fig. 1). The main strategy implemented by local authorities at some beaches with the massive arrival of macroalgae included the removal and disposal of Sargassum in the highest part of the beach or in places determined ex profeso. This contributed to a continuous accumulation of Sargassum masses on the beach. However, the Sargassum removal was not quantified and the information regarding removal included here is only preliminary.

Study sites.

Figure 1: Study sites.

Study area and sampling localities at the south coast of Quintana Roo: Mahahual (A), Xahuayxol (B) and Xcalak (C). The green polygon represents the marine protected area Parque Nacional Arrecifes de Xcalak (PNAX). Figure credit: Alejandro A. Aragón-Moreno.

Mahahual (18°42′16.96″N 87°42.619′W) is located in the northern part of the Mesoamerican Barrier Reef System (MBRS) in the state of Quintana Roo. Mahahual is a former fishing village but during the last two decades has undergone reef degradation due to anthropogenic impact (Martínez-Rendis et al., 2016). It has a narrow reef lagoon (230–450 m). Sargassum management in this locality was active through removing it from the beach and ex situ disposition.

Xahuayxol (18°30′21.78″N; 87°45′24.84″W) located south of Mahahual, has a larger reef lagoon measuring 300 to 500 m from the beach to the reef crest. Sargassum was not removed from the beach in any systematic way and remained accumulated on the shore. This reef is the northern limit of the marine protected area Parque Nacional Arrecifes de Xcalak (PNAX) and human activities are less salient than in Mahahual (Schmitter-Soto et al., 2018).

Xcalak (18°14′7.68″N; 87°50′1.46″W), at the southern limit of the Mexican Caribbean, is part of PNAX since 2000. It is also part of the MBRS (Hoffman, 2009). It has a wide reef lagoon (950–1,200 m), and Sargassum was accumulated along the shore in large amounts. There was active but less intense Sargassum management in place at Xcalak, where final disposal was in situ on the highest part of beach.

At all sampled sites, the dominant forcing mechanism was reef lagoon circulation from wave action (Mariño-Tapia et al., 2010). In our study area, during the period from June to August has the wave orbital velocity over the threshold of motion (Maldonado-Sánchez et al., 2019), indicating active circulation in the reef lagoons.

Collecting and processing data

This study covers two periods: Under Sargassum effect (USE) during the months of July–August 2015 and without Sargassum effect (WSE) in July–August 2016. USE sampling for stable isotope analysis included drifting Sargassum (mixture of S. fluitans and S. natans), turf associated pelagic Sargassum, benthic macroalgae, local turf and 19 individuals of D. antillarum. WSE sampling included benthic macroalgae, local turf and 15 individuals of D. antillarum (see sampling details ST1). Samples sizes were based on previous studies to obtain sufficient data for statistical analysis (Rodríguez, 2003; Tomas et al., 2006; Wing et al., 2008; Rodríguez-Barreras et al., 2016). The sampling sites were at coastal lagoons in the back reef zone (section c, Fig. 2), zone with no visible presence of Sargassum leachates (van Tussenbroek et al., 2017) and where D. antillarum is distributed (Steneck & Lang, 2003; Jorgensen, Espinoza-Ávalos & Bahena-Basave, 2008; Jordán-Garza et al., 2008; Maldonado-Sánchez, 2018).

Lagoon reef-scape showing the sections with Sargassum blooms.

Figure 2: Lagoon reef-scape showing the sections with Sargassum blooms.

Lagoon reef-scape showing the sections: a: decomposing Sargassum spp., Section b, leachates (dark brown water) and section c, back reef, areas without visible leachates. Based on van Tussenbroek et al. (2017).

Under Sargassum effect (USE) measurements

USE included measurements of dissolved oxygen (mg l−1) recorded with a calibrated Multi-parameter water quality checker HORIBA 50 at Mahahual, Xahuayxol and Xcalak. Measurements of dissolved oxygen were made at points distributed in three sections from areas with decomposing Sargassum (section a), leachates (section b -dark brown water-) and reef lagoon areas without Sargassum leachates (section c) (Fig. 2).

Pelagic Sargassum spp., turf (benthic turf and the associated turf to pelagic Sargassum) and macroalgae samples were collected in coral reef patches of section c (back reef zone) for each sampling site.

Under and without Sargassum effect (USE and WSE) measurements

We collected algal samples to obtain biomass, and for stable isotope analysis using nine quadrats (50 × 50 cm) per site. Pelagic Sargassum biomass was calculated based on sunken thalli and overlaid on reef substrates inside the quadrats. The quadrats were located randomly within the sea urchin habitat (radius of 15 m from collected echinoids). The substrate inside each quadrat was scrapped, carefully removed, collected in bags, and frozen for later analysis.

Macroalgae were identified according to Littler & Littler (2000). Analyses were performed to genus level. For biomass estimates samples were dried for 48 h in an oven at 60 °C. Samples were weighed with a digital balance (standard error = 0.0001 g). To determine D. antillarum differential algae assimilation considering USE and WSE, algae samples were pooled per site. The sampled echinoids and algal species for this study are not threatened. The collection permit was obtained from the Comisión Nacional de Acuacultura y Pesca (CONAPESCA, PPF/DGOPA-002/17).

The collected individuals of D. antillarum were at the same depth range (1.5–2.5 m) and only individuals greater than 5.0 cm in test diameter were collected to avoid any ontogenic effect. Samples were frozen shortly after collection and processed later at the laboratory. The muscles of Aristotle’s lanterns were carefully removed and washed from the stomach contents to estimate algal assimilation by D. antillarum because this tissue offers a time-integrated measure of carbon and nitrogen assimilated sources (Polunin et al., 2001; Ben-David & Schell, 2001; Phillips & Koch, 2002).

Macroalgae and local turf, pelagic Sargassum species (S. fluitans and S. natans), turf associated to pelagic Sargassum, and echinoids muscle samples were rinsed with filtered water, dried at 50 °C during 48 h, grounded to a fine powder and placed in glass vial for isotope analyses. To remove carbonates from some algal species (eg., Halimeda spp. Penicillus spp., etc.), the samples were washed with diluted HCl at 1 N prior to drying to avoid disturbance in the mass spectrometer reading.

A subsample of each algae and muscle (1mg) was taken to evaluate the 13C/12C and 15N/14N ratios using a Delta V Plus Mass Spectrometer. Catalyzers silvered cobaltous/cobaltic oxide and chromium oxide were used. Carbon and nitrogen samples were analysed in a dual isotope mode at the Centro Interdisciplinario de Ciencias Marinas from Instituto Politécnico Nacional. Isotope samples were loaded into tin-capsules and placed in a 50-position automated Zero Blank sample carousel on a COSTECH 4020 elemental analyzer. The carbon and nitrogen isotopic results were expressed in standard delta notation relative to Vienna Pee Dee Belemnite (VPDB) and to atmospheric air. δ 13 C = 13 C 12 C Sample 13 C 12 C Standard 1 × 1000

and δ 15 N = 15 N 14 N Sample 15 N 14 N Standard 1 × 1000 .

The standard deviations of δ13C and δ15N replicate analyses were estimated; the precision values were 0.2‰ for carbon and nitrogen isotope measurements. In addition, we calculated the trophic level (TL) according to Hobson & Welch (1992) for every individual of D. antillarum in each site, expressed as: TL = 1 + Nm Nb TEF .

Where Nm is the mean δ15N ratio of each sea urchin, Nb is average basis δ15N value of the algal community, and TEF is the given value for the trophic enrichment factor (TEF). We assumed a TEF of 2.4 following Moore & Semmens (2008).

Data analysis

Dissolved oxygen data were summarized to obtain average values (± standard error) by section (sections a, b, c in Fig. 2) and reef lagoons (Mahahual, Xahuayxol, and Xcalak). We evaluated differences among sections and at the reef lagoons (sections a, b, c, in Fig. 2). We plotted raw data of dissolved oxygen as a function of distance to coast to visualize the low to high values gradient related to that distances in every reef lagoon.

The relative contribution of algae to the diet of the sea urchins D. antillarum was estimated with a Bayesian isotopic mixing model (SIAR Parnell & Jackson, 2013), which included the isotopic signatures, fractionation and variability to estimate the probability distribution of the contribution of the food source to a mixture. This procedure supplied accurate information about the contribution of algal species to the sea urchin tissues, as it provided the proportion for every source and recognized the main sources as important components of the diet (Peterson, 1999; Fry, 2006; Wing et al., 2008) at three different sites, and under and without Sargassum effect. To run the model, the isotopic discrimination factor values used were 2.4 ± 1.6‰ (mean ± SD) for δ15N, and 0.4 ± 1.3‰ (mean ± SD) for δ13C (Minagawa & Wada, 1984; Fry & Sherr, 1989; Moore & Semmens, 2008; Cabanillas-Terán et al., 2016).

The following algal taxa/groups were considered for the mixing models analyses: Caulerpa, Codium, Dictyota, Halimeda, Laurencia, Lobophora, Padina, Penicillus, Sargassum polyceratum, Stypopodium, turf, and Udotea. The sources for the model were selected following the theoretical geometric assumptions of the mixing model according to Phillips et al. (2014) and Rodríguez-Barreras et al. (2015) to ensure reliable resources. Samples of D. antillarum did not require lipid extraction since C:N ratios of Aristotle lantern’s muscle were lower than 3.5 (Post et al., 2007).

We performed a comparison USE and WSE between the niche width and overlap for D. antillarum by using Stable Isotope Bayesian Ellipses in R (SIBER) (Jackson et al., 2011) from the SIAR package (Parnell & Jackson, 2013). This procedure performs metrics based on ellipses and provides the standard ellipse corrected area (SEAc) used as the trophic niche breadth and the overlap between ellipses, presuming that values close to 1 exhibit a higher trophic overlap. Models were run with 200,000 iterations and a burn in of 50,000.

Homogeneity and normality of variance were tested by performing a Kolmogorov–Smirnov and a Cochran’s test (Zar, 1999). Nitrogen data followed the premises of parametric analysis, but the carbon, dissolved oxygen and biomass data required a power transformation for reaching normality and homogeneity of variance (Box & Cox, 1964). We ran two-way ANOVA to evaluate dissolved oxygen data differences among sections in the reef lagoons and we performed a post hoc comparison using Tukey-HSD test. The functions aov and glm from the Gaussian family were used to test the differences in isotopic ratios of carbon and nitrogen values to compare the effect (WSE and USE) between sites and their interaction. Statistics were performed with α < 0.05 (R Core Team, 1.0.153, 2017).

Results

The dissolved oxygen values USE indicated that the effects of the leachates generated by the decomposition process, together with the organic material carried in their vegetal structures, reduced the values of dissolved oxygen in the reef lagoon water. The decomposing Sargassum area (section a, Fig. 2) showed an average range from 1.01 (S.E. ± 0.30) mg l−1at Xcalak to 1.88 (S.E. ± 0.37) mg l−1 at Mahahual. The leachates area (section b, Fig. 2) showed an average range from 2.42 (S.E. ± 0.32) mg l−1 at Xahuayxol to 3.66 (S.E. ± 0.42) mg l−1at Mahahual. The back reef area (section c, Fig. 2) showed an average range from 4.1 (S.E. ± 0.34) mg l−1at Mahahual to 4.8 (S.E. ± 0.22) mg l−1at Xcalak. The two-way ANOVA indicated significant differences between reef lagoons (p < 0.05) and sections (p < 0.01); Mahahual was significantly different to Xcalak, but Mahahual and Xcalak were not significantly different to Xahuayxol (Post-hoc HSD of Tukey test, 95% confidence). The three sections at the three reefs were significantly different, except the sections b and c of Mahahual (Post-hoc HSD of Tukey test, 95% confidence). Therefore dissolved oxygen data showed a gradient significantly different between sections. The overall values of dissolved oxygen displayed the lowest concentrations for section a, near the shoreline and higher values beyond the back reef section c (Fig. 3).

Dissolved Oxygen values under Sargassum effect (USE).

Figure 3: Dissolved Oxygen values under Sargassum effect (USE).

Dissolved oxygen (mgl−1) values along the distance to shoreline at (A) Mahahual (blue), (B) Xahuayxol (purple) and (C) Xcalak (green) considering the sections depicted in Fig. 2: dissolved oxygen <2 mgl−1: decomposing Sargassum spp; dissolved oxygen between 2–4 mgl−1: leachates (dark brown water) and dissolved oxygen > 4 mgl−1: back reef, areas without visible leachates.

Biomass, δ15N and δ13C of macroalgae

Biomass data for benthic taxa displayed no significant differences between USE and WSE, but significant differences were found among localities (ANOVA, df = 2, F = 8.24, p < 0.0001). Mahahual had the highest mean benthic biomass values (55.2 dry weight m−2) followed by Xahuayxol with (38.8 dry weight m−2) and Xcalak (16 dry weight m−2 ±). WSE biomass average values for local benthic algae ranged from 3.01 dry weight m−2 ±0.95 (Codium spp. at Xcalak) to 133.50 dry weight m−2 ±30.29 (Halimeda spp. at Mahahual). USE values ranged from 7.75 dry weight m−2 ±5.4 (Caulerpa at Xcalak) to 145.99 dry weight m−2 ± 36.21 (Halimeda spp. at Mahahual, Table 1). Genus-level biomass of pelagic taxa showed no significant differences per site neither at genus level, however Sargassum fluitans displayed the highest biomass values.

Under and without Sargassum effect values revealed significant differences in overall benthic algae values of δ15N (ANOVA, df = 1, F = 20.27, p < 0.0001). Specifically under Sargassum blooms most of the algae exhibited isotopic signatures with significantly depleted δ15N like Dictyota and turf across the lagoon reef sites (Table 2). The overall macroalgal δ15N under Sargassum fluctuated from 0.023 to 2.08‰. At Xcalak Caulerpa displayed the highest mean values of nitrogen with 2.02 ± 0.08‰. Local Turf USE displayed negative values and overall turf values fluctuated from −0.97‰ to 0.42‰. Xahuayxol displayed the most negative δ15N mean value of local turf (−0.51 ± 0.02‰). Without Sargassum effect the mean algal genus δ15N fluctuated from 0.06 ± 0.08 with Penicillus at Xcalak, and Xahuayxol displayed the highest mean value of δ15N with Caulerpa (5.68 ± 0.01‰) (Table 2).

As for δ13C USE ratios fluctuated from −21.98 to −9.23‰ and WSE from −20.90 to −5.65‰. Considering only the algae presented in both sampling periods (WSE and USE) there was no significant difference in δ13C among sites (ANOVA, df = 2, F = 0.55, p > 0.05) neither was significant difference analysing the effect (ANOVA, df = 1, F = 1.14, p > 0.05) and their interaction (ANOVA, df = 2, F = 0.86, p > 0.05).

Overall USE pelagic Sargassum δ13C values fluctuated from −17.95‰ to −15.24‰. S. natans exhibited the most negative mean values of δ13C (−17.44 ± 0.71‰) at Mahahual (Table 2). There was no difference in δ13C among sites (ANOVA, df = 2, F = 0.05, p > 0.05) but there were significant differences δ13C between species (ANOVA, df = 2, F = 7.57, p = 0.01). Sargassum’s associated turf δ13C values fluctuated from −18.65‰ to −15.37‰. The most negative δ13C mean value was displayed at Mahahual (−18.3 ± 0.5‰) for Sargassum’s associated turf.

Table 1:
Algal biomass values.
Mean ± standard deviation values of algal biomass (grams dry weight m−2) at Mahahual, Xahuayxol and Xcalak. Genus considered for the mixing models analysis. Data below the grey line belongs to pelagic taxa.
Mahahual Xahuayxol Xcalak
Genus WSE USE Genus WSE USE Genus WSE USE
Caulerpa 39.49 ± 20.79 19.82 ± 6.48 Caulerpa 5.38 ± 0.93 Caulerpa 7.97 ± 3.51 7.75 ± 5.4
Dictyota 19.92 ± 11.69 20.40 ± 5.41 Dictyota 6.61 ± 2.49 20.36 ± 5.96 Codium 3.01 ± 0.95
Halimeda 133.50 ± 30.29 145.99 ± 36.21 Halimeda 118.07 ± 29.43 89.18 ± 9.998 Dictyota 21.99 ± 5.99 17.76 ± 2.34
Laurencia 14.73 ± 22.15 Laurencia 8.49 ± 4.10 Lobophora 26.96 ± 4.30
Stypopodium 95.41 ± 66.10 Lobophora 19.933 ±11.50 Padina 12.62 ± 4.30
Turf 24.69 ± 9.17 19.042 ± 6.045 Penicillus 12.88 ± 3.94 Penicillus 27.49 ± 3.51 26.23 ± 2.45
Udotea 59.79 ± 45.74 Sargassum 14.26 ± 4.42 Sargassum 15.01 ± 4.30
Stypopodium 10.06 ± 12.13 Turf 12.00 ± 3.51 11.40 ± 4.21
Turf 5.886 ± 2.83 14.26 ± 7.84
Udotea 39.13 ± 14.76 34.02 ± 16.54
S. fluitans 12.39 ± 8.33 S. fluitans 11.86 ± 2.75 S. fluitans 13.00 ± 6.99
S. natans 4.92 ± 3.14 S. natans 7.07 ± 3.26 S. natans 10.03 ± 7.94
Sargassum’s associated turf 3.10 ± 1.21 Sargassum’s associated turf 3.23 ± 1.28 Sargassum’s associated turf 1.98 ± 1.29
DOI: 10.7717/peerj.7589/table-1
Table 2:
Mean ± standard deviation values of δ13C and δ15N of algal genus considered in the mixing model analysis taken from Mahahual, Xahuayxol and Xcalak, the asterisks represent the sources under Sargassum effect.
Mahahual Xahuayxol Xcalak
Genus δ13C δ15N Genus δ13C δ15N Genus δ13C δ15N
Caulerpa −9.89± 0.15 2.22± 0.01 Caulerpa −8.86± 0.19 5.68± 0.01 Caulerpa −12.60± 0.04 1.00± 0.10
Caulerpa* −16.22± 0.55 0.93±0.08 Dictyota −15.71± 0.90 2.29± 0.41 Caulerpa* −9.63± 0.02 2.02± 0.08
Dictyota −16.38± 1.23 1.56±1.37 Dictyota* −16.31± 0.95 0.71± 0.02 Codium −12.17 ± 0.07 1.25 ± 0.07
Dictyota* −15.95 ± 0.04 0.82 ± 0.04 Halimeda* −12.61 ± 1.70 0.88 ± 0.01 Dictyota −15.47 ± 0.68 0.67 ± 0.03
Halimeda −7.01 ± 1.25 0.29 ± 0.43 Laurencia −14.81 ± 0.23 1.36 ± 0.71 Dictyota* −15.69 ± 0.20 0.04 ± 0.06
Halimeda* −8.39 ± 0.69 0.68 ± 0.12 Lobophora* −10.49 ± 1.35 0.33 ± 0.64 Lobophora −14.15 ± 0.53 0.77 ± 0.33
Laurencia −16.16 ± 0.90 2.61 ± 1.41 Penicillus −11.51 ± 8.28 1.84 ± 0.30 Padina −10.18 ± 0.18 0.25 ± 0.19
Stypopodium −11.33 ± 0.52 0.67 ± 0.05 Sargassum −14.65 ± 1.82 3.21 ± 0.23 Penicillus −14.50 ± 0.08 0.06 ± 0.08
Turf −13.44 ± 0.00 3.03 ± 0.02 Stypopodium −16.80 ± 1.40 1.47 ± 0.56 Penicillus* −9.75 ± 0.14 1.98 ± 0.04
Turf* −16.54 ± 0.22 −0.51 ± 0.02 Turf −16.43 ± 1.32 1.84 ± 0.30 Sargassum* −14.76 ± 0.87 0.37 ± 0.08
Udotea −12.86 ± 0.42 2.19 ± 0.03 Turf* −18.56 ± 0.04 −0.89 ± 0.11 Turf −17.44 ± 0.48 4.59 ± 0.64
Udotea −11.62 ± 1.34 2.42 ± 1.12 Turf* −21.98 ± 0.10 0.41 ± 0.01
Udotea * −12.65 ± 0.20 2.65 ± 0.77
S. fluitans −16.03 ± 0.99 −0.53 ± 0.26 S. fluitans −16.36 ± 0.15 −1.74 ± 0.38 S. fluitans −16.26 ± 0.17 −2.51 ± 0.52
S. natans −17.44 ± 0.71 −1.59 ± 0.70 S. natans −16.82 ± 0.73 −1.49 ± 0.42 S. natans −17.28 ± 0.81 −1.62 ± 0.55
Sargassum’s associated turf −18.29 ± 0.51 −1.13 ± 0.05 Sargassum’s associated turf −15.93 ± 0.79 −0.47 ± 0.07 Sargassum’s associated turf −16.27 ± 0.63 −0.96 ± 0.01
DOI: 10.7717/peerj.7589/table-2

Overall pelagic Sargassum δ15N values ranged from −2.87‰ to −0.30‰. The less negative mean value was exhibited at Mahahual (−0.53 ± 0.26‰) for S. fluitans. There was no significant difference for δ15N among sites (ANOVA, df = 2, F = 3.90, p = 0.05), but there was a remarkable trend to depleted δ15N at Xcalak where S. fluitans displayed the lowest mean values of δ15N (−2.51 ± 0.52‰). Turf associated to floating Sargassum δ15N values fluctuated from −0.42‰ to −1.17‰. The most depleted δ15N was exhibited at Mahahual (−1.13 ± 0.05‰) and the less negative mean value was displayed in Xahuayxol (−0.47 ± 0.07‰).

Sea urchins

There were significant differences δ15N among sites (ANOVA df = 2, F = 6.473, p = 0.005) and the interaction between site*effect (USE and WSE) showed significant differences (ANOVA, df = 2, F = 7.321, p = 0.003).

D. antillarum exhibited no differences among sites for δ13C values p > 0.05. However, we found significant differences analysing the USE and WSE effect (ANOVA df = 1, F = 5.301, p =0.03). The isotopic ratios of D. antillarum (USE) varied from 3.83‰ to 6.13‰ for δ15N, while δ13C ranged from −9.41‰ to −13.62‰. Mahahual was the site with the highest average values for δ15N 5.80 ± 0.30‰, while Xcalak displayed the lowest average value 4.38 ± 0.29‰. The isotopic ratios of D. antillarum (WSE) ranged from 4.69‰ to 6.16 for δ15N, while δ13C fluctuated from −8.83‰ to −13.42‰. We found significant differences for δ15N for sea urchins between sites (USE, ANOVA, df = 2, F = 6.47, p < 0.005).-Xcalak showed particularly low values under Sargassum effect (average value 4.38 ± 0.29‰ versus WSE average value 5.44 ± 0.36‰). Nevertheless, δ13C exhibited no significant differences although we noticed a negative trend in the values of δ13C under Sargassum effect (USE).

Algal source contributions (SIAR)

Mixing models provided evidence for the contribution of different algal resources for three sites USE and WSE (Table 3). SIAR analysis showed that D. antillarum behaved as an opportunistic grazer under the Sargassum effect, it is important to note that pelagic Sargassum, despite being one of the most abundant available resources, was not the most assimilated resource (Fig. 4). Relatedely, there was a reduction in benthic food sources USE (Fig. 4). Without Sargassum effect D. antillarum consumed, Laurencia, Stypopodium and Udotea (12–15% in average) at Mahahual; Caulerpa, Laurencia, Penicillus, Sargassum and Stypopodium (8–14% in average) at Xahuayxol; and Codium, Lobophora and Padina (13–15% in average) at Xcalak. Nevertheless, those resources were absent in the diet of D. antillarum under Sargassum effect (Table 3). Hence, the species displayed differential resource assimilation and Caulerpa was the most important resource for D. antillarum in Mahahual WSE (up to 37%), followed by Turf (up to 34%) and Halimeda and Udotea (up to 29% for both). USE the most important resource was Halimeda (up to 44%) followed by Caulerpa and Dictyota (both up to 31% of contribution). S. fluitans and S. natan s were no important sources (0–28% and 0–23% respectively), and turf associated to Sargassum blooms was the lesser assimilated resources by D. antillarum from 0 up to 22% (Table 3).

Table 3:
Average percentage (%) contribution of algal genus to the diet of the sea urchins D. antillarum considering the effect of Sargassum: without Sargassum effect (WSE) and under Sargassum effect (USE) at Mahahual, Xahyayxol and Xcalak produced by the SIAR model using isotope values from algae.
Minimum and maximum values for each algae are shown in parentheses.
Mahahual Xahuayxol Xcalak
Genus WSE USE Genus WSE USE Genus WSE USE
Caulerpa 19 (1–37) 14 (0–31) Caulerpa 14 (2–25 ) Caulerpa 14 (0–29) 22 (0–40)
Dictyota 9 (0–22) 14 (0–31) Dictyota 11 (0–22) 9 (0–23) Codium 15 (0–30)
Halimeda 16 (1–29) 31 (17–44) Halimeda 10 (0–19) 17 (0–35) Dictyota 12 (0–26) 11 (0–26)
Laurencia 12 (0–25) Laurencia 11 (0–21) Lobophora 13 (0–27)
Stypopodium 12 (0–25) Lobophora 20 (0–38) Padina 15 (0–29)
Turf 17 (0–34) 11(0–26) Penicillus 8 (0–18) Penicillus 12 (0–26) 22 (4–39)
Udotea 15 (0–29) Sargassum 12 (0–23) Turf 19 (0–45) 8 (0–19)
S. fluitans 12(0–28) Stypopodium 11 (0–21) Sargassum 13 (0–29)
S. natans 9(0–23) Turf 11 (0–22) 6 (0–16) S. fluitans 7 (0–18)
Sargassum’s associated turf 9 (0–22) Udotea 12 (0–23) 28 (2–61) S. natans 8 (0–19)
S. fluitans 6 (0–17) Sargassum’s associated turf 9 (0–23)
S. natans 6 (0–17)
Sargassum’s associated turf 8 (0–21)
DOI: 10.7717/peerj.7589/table-3
Algal resources proportions consumed by Diadema antillarum.

Figure 4: Algal resources proportions consumed by Diadema antillarum.

Contribution rates of algae to the diet of Diadema antillarum in the two scenarios (WSE and USE). Results are shown as 25% (light error bars), 75% (grey error bars) and 95% (dark error bars) of credibility intervals. (A) Represents the contribution for D. antillarum at Mahahual without Sargassum effect (WSE), (B) represents D. antillarum at Mahahual under Sargassum effect (USE); (C) represents D. antillarum in Xahuayxol WSE, (D) represents D. antillarum in Xahuayxol USE; (E) represents D. antillarum in Xcalak WSE and (F) represents D. antillarum in Xcalak USE. Bloom turf is the Sargassum’s associated turf. The blue bar represents the pelagic sources USE.

At Xahuayxol WSE D. antillarum showed Caulerpa was the most important resource for D. antillarum (from 2 up to 25%) and for the rest of algae there were very similar algal contribution (from 0 up to 23%). The main macroalgal contributor of USE was Udotea with up to 61%, followed by Halimeda and Lobophora (with up to 35% and 38% respectively) as secondary resources. Sargassum’s associated turf showed evidence of low contribution (from 0 up to 21%) and S. fluitans, S. natan s had negligible contribution to D. antillarum diet with a maximum of 17% of the proportional contribution (Table 3).

Turf was the main algal resources for D. antillarum in Xcalak WSE (up to 45%) followed by Caulerpa, Codium and Padina as secondary resources (close to 30% maximum of contribution); contrasting USE the main macroalgal contributors in Xcalak were Penicillus and Caulerpa with up to 39% and 40% respectively. Likewise Dictyota and Sargassum polyceratium ( benthic Sargassum) were secondary resources up to 26% and 29%, respectively. The pelagic components in the other reef lagoons were negligible contributors for D. antillarum diet with just 18–23% of maximum contribution (Table 3, Fig. 4).

Trophic Levels

The overall trophic level data for D. antillarum (TL) ranged from 1.97 to 3.22. The species exhibited significant differences among sites (ANOVA df = 2, F = 10.63, p = 0.0004), and exhibited significant differences between WSE and USE (ANOVA, df = 1, F = 17.7, p = 0.0003). Likewise, calculating the interaction between site*effect (USE and WSE) revealed significant differences (ANOVA, df = 2, F = 12.65, p = 0.0001). The highest TL values were reported for Mahahual USE, while the lowest one was recorded in Xahauayxol WSE. At Mahahual, the TL mean value of D. antillarum was 2.35 ± 0.18 WSE and 3.08 ± 0.13 USE; at Xahuayxol, the TL mean value was 2.13 ± 0.30 WSE and 2.49 ± 0.27 USE, and at Xcalak TL mean value was 2.62 ± 0.15 WSE and 2.45 ± 0.12 USE (Table 4).

Table 4:
Trophic level of D. antillarum.
Mean Trophic level (TL), and δ15N and δ13C ± standard deviation of D. antillarum without Sargassum effect (WSE) and under Sargassum effect (USE) at Mahahual, Xahuayxol and Xcalak.
Site TL WSE TL USE δ15N WSE δ15N USE δ13C WSE δ13C USE
Mahahual 2.35 ± 0.18 3.08 ± 0.13 5.22 ± 0.43 5.8 ± 0.3 −10.46 ± 0.6 −12.32 ± 0.95
Xahuayxol 2.13 ± 0.3 2.49 ± 0.27 5.09 ± 0.71 4.9 ± 0.24 −11.5 ± 0.81 −11.21 ± 1.48
Xcalak 2.62 ± 0.15 2.45 ± 0.12 5.44 ± 0.18 4.38 ± 0.29 −10.58 ± 2.01 −12.02 ± 0.89
DOI: 10.7717/peerj.7589/table-4

Isotopic Niches

Table 5 shows data on isotopic niche breadth as measured by the corrected standard ellipse area (SEAc). The Stable Isotope Bayesian Ellipses in R (SIBER) analysis suggested a reduction in trophic niche particularly in Xcalak. This site showed the main difference in the trophic niche breadth with SEAc of 3.48 and 0.14 (WSE and USE respectively). An overlap of isotopic niches between WSE and USE was only found in Xahuayxol (Fig. 5). SEAc was higher USE in this site with 3.57 versus 2.68 SEAc WSE (Fig. 5).

Table 5:
Trophic niche breadth of sea urchins without Sargassum effect (WSE) and under Sargassum effect (USE) at Mahahual, Xahuayxol and Xcalak calculated by SIBER analysis of muscle values.
SEAc, corrected standard ellipse area.
Niche breadth Mahahual Xahuayxol Xcalak
WSE USE WSE USE WSE USE
SEA 0.62 0.71 1.79 2.97 2.32 2.32
SEAc 0.83 0.89 2.68 3.57 3.48 0.14
DOI: 10.7717/peerj.7589/table-5
Isotope niche breadth of the sea urchin Diadema antillarum.

Figure 5: Isotope niche breadth of the sea urchin Diadema antillarum.

Isotope niche breadth of the sea urchin Diadema antillarum at Mahahual (A), Xahuayxol (B) and Xcalak (C). Dotted lines are without Sargassum effect (WSE) and solid lines under Sargassum effect (USE).

Discussion

Our results provide evidence of the detrimental effect of Sargassum blooms on the physicochemical water properties and ecological processes in near-shore coral reef communities as recently has been identified in our study area (Rodríguez-Martínez, van Tussenbroek & Jordán-Dahlgren, 2016; van Tussenbroek et al., 2017; Cuevas, Uribe-Martínez & Liceaga-Correa, 2018). Particularly, the results provide evidence for the input of external carbon and nitrogen resulting from Sargassum blooms on benthic communities that alter the nutrient inputs and trophic niche for D. antillarum. These findings contribute to the growing recognition of the role of exogenous nutrient enrichment in modifying natural sources in a food web. Hence the organic matter inputs from Sargassum coupled with hypoxia leads to modification of natural algal resources for D. antillarum. Considering the detrimental effects this likely represents a nutrient limitation to sea urchin herbivory.

Onshore Sargassum exhibits physical processes of fragmentation, decomposition and remineralization by bacteria, meiofauna and grazers (Colombini & Chelazzi, 2003). The algae-derived organic matter, product of that decomposition, has an effect on in situ oxygen availability (Haas et al., 2010). Sargassum blooms clearly showed a negative impact hypoxic conditions found at the three studied reef lagoons (Fig. 3). This could ultimately drive the success of the communities’ nitrogen fixation, evidenced by depleted values of δ15N as reported by Dorado et al. (2012) and France (1995).

The dissolved oxygen values in the back reefs of our study areas were lower than the standard values for coral reefs dominated by algae (7.9 ± 0.5 mg l−1) according to Haas et al. (2010) and values reported by Camacho-Cruz et al. (2019) for Xahuayxol and Mahahual. This supports ideas from Kendrick et al. (2000) and Haas et al. (2010), who argue that benthic communities linked to reef lagoons are very susceptible to environmental degradation. Some benthic algae play an important play in the transfer of energy and can be catalyzers of oxygen dynamics in reefs due to coral reef associated algae-derived organic matter (Wild et al., 2010).

Isotopic variations in the algal resources

We found that the composition of benthic macroalgae assemblages were different under Sargassum and without Sargassum effect. USE showed a reduction in the taxonomic diversity of macroalgal food sources available to D. antillarum and isotope values presented substantially lower δ15N values (Table 2). The fact that there were fewer available algal sources in the USE condition implies that the trophic chain becomes less complex as the interaction of primary consumers with their resources is reduced (Phillips & Gregg, 2003).

Overall δ13C values ranged from −21.98 to −5.65‰ are similar to ranges reported by Fry & Sherr (1984) and Morillo-Velarde, Briones-Fourzán & Álvarez Filip (2018). Those authors reviewed the δ13C data of benthic algae, noting that values ranged between −30 and 5‰. δ15N overall algae values fluctuated from 0.02 to 5.68‰. Despite these values agree with the variation reported in other studies like Owens (1987) and France (1995), we found USE very low, ergo according to Lapointe et al. (2005) and France et al. (1998). These low 15N:14N ratios can be indicative of macroalgae living in oligotrophic reefs which experience nitrogen fixation (Montoya, Carpenter & Capone, 2002). In the presence of the leachates of decomposing Sargassum, it is possible that anaerobic bacteria gained significance over other benthic groups (Table 2), (Carpenter & Cox, 1974; Rooker, Turner & Holt, 2006), and could be the cause of the low macroalgal isotopic signatures. On the other hand, high values of δ15N in macroalgae are linked to land-based N enrichment sources, being a good indicator of anthropogenic nitrogen inputs (Umezawa et al., 2002) such as sewage discharges (Risk et al., 2009; Lapointe et al., 2011).

France (1995) reported nitrogen ranges of marine macroalgae from −3 to 18‰. The inconsistencies in this pattern with values of δ15N close to atmospheric signature of 0% suggest a fixation of nitrogen. Dorado et al. (2012) associated the depleted values of δ15N with nitrogen fixation and its impact on the trophic position of consumers. So, temporal difference between values in this study WSE and USE might be explained by the influence of organic input derived from floating Sargassum dragged components. We considered that it is likely that the Sargassum effect modifies organic matter dynamics. These modifications stem from changes in the oxygen levels, which were consistently reflected in the low δ15N values we recorded of for the primary producers.

Status of Diadema antillarum in the Mexican Caribbean

It is important to note that we focused our study on the most abundant species at the three localities and the most important shallow-bottom herbivore on Caribbean reefs (Carpenter, 1981; Hughes, 1994; Aronson & Precht, 2006; Kissling et al., 2014). For the Mexican Caribbean, there has been considerable variation in D. antillarum population data. Jordán-Garza et al. (2008) showed a high presence of D. antillarum with densities of more than 7 ind m−2 in several areas, including our study area. Jorgensen, Espinoza-Ávalos & Bahena-Basave (2008) reported densities of 12.6 ind m−2 after hurricane Dean. According to Maldonado-Sánchez (2018) population density of D. antillarum displayed <1 ind m−2 for five different habitats of the Parque Nacional Arrecifes de Xcalak (PNAX) reef lagoon (back reef, seagrasses, sandy bottoms and reef patches) and the fore reef. The back reef exhibited the highest abundance with an average of 0.5 ind m−2. However for Mahahual, we registered an average density of 0.6 ind m−2 (N Cabanillas-Terán, pers. obs., 2017), because of the broad variability exhibited in D. antillarum populations from the back reef.

Trophic parameters of D. antillarum

Our results support the evidence that Sargassum blooms impacted δ15N differentially among sites, as the ratios of δ15N and δ13C are determined by their resources (Phillips & Gregg, 2003). It was conspicuous that D. antillarum showed higher δ15N values USE at Mahahual.

Although some available resources (e.g., Dictyota and turf) were present in both conditions (WSE and USE), measuring the contribution of algae to the sea urchin tissues can display key information about how consumers assimilate habitat resources and this could reveal information on the degree of disturbance (Layman et al., 2007b). Therefore, it is possible that the ecological role of D. antillarum was different in each site and could be explained by the variation in the number of available resources and a differential assimilation (Table 3). The higher δ15N values USE in the muscle of D. antillarum were a result of the synergistic effect determined by resource availability and disturbance condition.

Pelagic sources may provide new sources of food and the possible nitrogen fixation carried out by turf attached to pelagic Sargassum undoubtedly brought a new source of organic matter to basal trophic levels (Rooker, Turner & Holt, 2006). However, those sources were not major contributors for D. antillarum and appear to avoid the invasive pelagic macroalgae. This is consistent with the feeding ecology by marine generalist herbivores (Boudouresque & Verlaque, 2001) and such feeding response is in line with evidence from other sea urchin species in the face of other invasive resources. The experiments carried out by Tomas, Box & Terrados (2011) provide evidence that some seaweed invaders were strongly avoided by Paracentrotus lividus and therefore escape enemy control by reducing herbivore preference.

The trophic level metric is very useful because the classical discrete trophic level definitions ignore the value of food web connections, omnivory, and diet changes (Polis & Strong, 1996; Vanderklift, Kendrick & Smit, 2006). Generally the sea urchin D. antillarum has been considered as a generalist herbivore (Ogden & Lobel, 1978; Sammarco, 1980; Solandt & Campbell, 2001; Weil, Torres & Ashton, 2005). Morillo-Velarde, Briones-Fourzán & Álvarez Filip (2018) found that for the North of Quintana Roo Mexico D. antillarum occupied an herbivorous trophic position. However, invertebrate samples have been found in the stomach contents this species in the Caribbean, suggesting omnivorous behaviour (Rotjan & Lewis, 2008; Rodríguez-Barreras et al., 2015; Rodríguez-Barreras et al., 2016).

The mean trophic level for D. antillarum exhibited at Mahahual was 2.35 ± 0.18 WSE up to 3.08 ± 0.13 USE. Hence, WSE supported the idea that this species occupies an herbivorous position. However USE D. antillarum revealed that the species can occupy different trophic niches when faced with resource limitation. Under Sargassum blooms, D. antillarum displayed a position more in line with omnivorous conditions, suggesting trophic level indicative of herbivorous behaviour tending towards omnivory, according to Vander Zanden & Rasmussen (1999). These authors stated that primary consumers have a trophic position of 2.0 (strictly herbivorous); but if organisms assimilate primary consumers, they are considered to be a trophic level of 3.0. The results for Mahahual are consistent with Andrew (1989) who argued that sea urchins could take advantage of ecosystem changes through omnivory if variation exists in the availability of resources. Our results suggest that D. antillarum behave as a facultative omnivore depending on patterns of nutrient availability. δ15N signatures for D. antillarum in Mahahual suggest a different carbon source USE. These signatures are also likely the result of anthropogenic nitrogen inputs, as this site has a high eutrophication, being an area with elevated touristic demand (Martínez-Rendis et al., 2016; Arias-González et al., 2017). Furthermore, possible nitrogen fixation by anaerobic bacteria as an important factor in the variation of available sources of food.

Regarding the TL values exhibited for D. antillarum in Mahahual USE 3.08 ± 0.13 versus 2.35 ± 0.18 for WSE would place D. antillarum in an omnivorous position tending towards carnivory. Similar values were obtained from Mediterranean sea urchins as a strategy to avoid exclusion by sympatric species (Wangensteen et al., 2011). However, we cannot state that D. antillarum is carnivorous in Mahahual. This would require a more complete temporal study, and an adjustment of a new δ15N baseline for primary producers, considering that 15N/14N ratios can vary spatially and temporally (Jennings et al., 1997; Vanderklift, Kendrick & Smit, 2006).

The results for Xahuayxol showed also a trend towards higher δ15N. However by analyzing the condition of D. antillarum in Xahuayxol no significant differences were observed. We can assume that this locality was least changed in its foraging behavior position against the nutrients modification and the species occupied a lower trophic level WSE. Meanwhile, Xcalak displayed the opposite trend compared to Mahahual and Xahuayxol and USE D. antillarum trophic level was lower than WSE. Our results suggest that for Xcalak the effect of Sargassum blooms completely modified and reduced the possibility for finding available resources, displaying a trophic level around 2.5 between the two scenarios of Sargassum blooms. This corresponds to a predominantly herbivorous to omnivorous condition. Moreover this was confirmed with the isotopic niche breadth data where a reduced niche was observed for Xcalak (Fig. 3).

The rank found for D. antillarum in this study is consistent with the study conducted by Rodríguez-Barreras et al. (2015) in Puerto Rico where microinvertebrates were used as source of organic matter by the sea urchin. Finally, TL values support the premise that echinoids are able to modify their foraging behaviour depending on the availability of resources (Randall, Schroeder & Starck, 1964; Muthiga & McClanahan, 2007), and in this case under Sargassum blooms condition was not only determined by macroalgae availability, but for unusual conditions that caused a shift in the ecosystem (Cabanillas-Terán et al., 2016).

Isotopic niche breadth

The ellipses provide integrated information on the relationship between the availability of sources and the niche width. The results of Mahahual indicated that in USE. D. antillarum consumes different carbon and nitrogen sources (Fig. 4).

Several studies (Lawrence, 1975; Carpenter, 1981; Sammarco, 1982; Hay & Fenical, 1988) noted that echinoids have the ability to adapt their foraging behavior depending on algae availability as well as their population density and site characteristics (Bak, Carpay & De Ruyter Van Steveninck, 1984; Bak, 1994; Alvarado et al., 2016). We observed at Mahahual that USE D. antillarum exhibited a broader trophic niche than WSE. Despite the limited resources this could lead to trophic overlap and stronger habitat degradation. SIAR results showed a resource shift and this could be explained in terms of omnivory as stated by France et al. (1998) “omnivory is a prevalent attribute of aquatic food webs”.

The trophic niche of Xahuayxol reflects that there was no difference in the use of carbon and nitrogen sources. It is noteworthy that for the case of Xcalak, the resulting isotopic niche of D. antillarum was significantly smaller under Sargassum effect. This is consistent with the metric that associates smaller niche amplitude with disturbed ecosystems (Layman et al., 2007b).

Limitations of the study

To assess the effect of differential management of Sargassum and to effectively evaluate the effect of disposal management, quantitative information on beach disposal would be necessary.

From our results, it is clear that algae communities were modified due to Sargassum. However, due to the structuring role of sea urchins, and, considering that algae respond to temporal variability naturally, it would be necessary to study changing gradients at different time scales. Such a temporal study would provide more conclusive information about the effect of Sargassum spp. on benthic communities.

It is necessary to strengthen the sampling effort to evaluate current population status. A more comprehensive discussion would need to include the interactions with other herbivorous/omnivorous species, that coexist at each site and whether, or how they carry out resource partitioning.

The metrics used in this study allowed us to evaluate the variation of the isotopic signatures that formed the trophic spectrum of D. antillarum under two different scenarios. Metric values based on an instantaneous characterization of a single food web provide a limited view of the food web. Therefore, to evaluate the trophic structure and consequently its functional structure, the most promising evaluations would have to include a comparison of multiple gradients, and, to examine the same food web on a longer temporal perspective.

The deposited biomass regarding to S. fluitans and S. natans did not include a measurement of the total arrived Sargassum blooms. However, our results established a baseline for the amounts that were more available for the echinoids that inhabit the back section of the Caribbean shallow reefs.

It would be challenging to evaluate the ecological role of other coexisting species (Echinometra viridis, E. lucunter and Eucidaris tribuloides), and to include samples of micro-invertebrates. However, this could offer new clues to the connectivity between sympatric species, including trophic loops and successional states of algal communities (Camus, Daroch & Opazo, 2008) within the benthic communities of coral reefs.

Conclusions

The present study provides an initial review of how trophic parameters of D. antillarum were modified by the impact of pelagic Sargassum blooms in the Mexican Caribbean. The results indicated that the effects of the leachates generated by the decomposition process, the input of organic material and deposition in its vegetal structures modify the organic matter in the environment and hence the isotopic signatures. This has negative consequences in the benthic trophic structure, limiting the natural herbivory of D. antillarum. The source of available carbon and nitrogen was modified, and the isotopic signatures of macroalgae associated with the reef sites exhibited significantly lower values of δ15N. Consequently, the trophic niches were changed and in the case of Xcalak, significantly reduced.

Supplemental Information

Photograph showing the effect of Sargassum blooms on D. antillarum

DOI: 10.7717/peerj.7589/supp-1

Dissolved oxygen values

DOI: 10.7717/peerj.7589/supp-2

Algae genus biomass considered for the mixing models

Values of algal biomass (grams dry weight m−2) at Mahahual, Xahuayxol and Xcalak.

DOI: 10.7717/peerj.7589/supp-3

Data of δ13C and δ15N of algal genus from sampling locations

Raw data of δ13C and δ15N of algal genus considered in the mixing model analysis taken from Mahahual, Xahayxol and Xcalak, the asterisks represent the sources under Sargassum effect.

DOI: 10.7717/peerj.7589/supp-4

Values of δ13C and δ15N of D. antillarum at Mahahual, Xahuayxol and Xcalak

DOI: 10.7717/peerj.7589/supp-5

Sampling collection of algae and sea urchins

DOI: 10.7717/peerj.7589/supp-6

Figure from van Tussenbroek et al., 2017

Confidential supplemental file. We based our Figure 2 on this Figure by van Tussenbroek et al., 2017.

DOI: 10.7717/peerj.7589/supp-7

Permission Letter

Permission Letter written by Alejandro A. Aragón-Moreno

DOI: 10.7717/peerj.7589/supp-8