Environmental stress and eutrophication in freshwater wetlands: evidence from carbon and nitrogen stable isotopes in cattail (Typha domingensis Pers.)
Ecological Processes volume 8, Article number: 31 (2019)
Florida’s Everglades is a vast freshwater peatland that has been impacted by the alterations of hydrological pattern and water quality which led to changes in plant species composition and biodiversity. In this study, carbon and nitrogen stable isotopes (δ13C and δ15N) in cattail (Typha domingensis) are evaluated as indicators of environmental changes in the Everglades wetlands along nutrient and hydrological gradients represented by reference sites with total phosphorus (TP) < 10 μg L−1, transition sites with TP ≥ 10 μg L−1 < 20 μg L−1 and impacted sites with TP ≥ 20 μg L−1 which differed in hydrology or habitats (marsh and canal).
Cattail δ13C values decreased significantly from reference (–24.1‰), transition (–26.8‰) to the impacted sites (–28.2‰). In contrast, δ15N values increased significantly from reference (–5.2‰), transition (2.4‰) to the impacted site (5.9‰). In response to a poor hydrological condition, cattail in marsh area displayed 13C enrichment (–26.0‰) and 15N depletion (0.2‰). By contrast, cattail grown in the canal sites with favorable hydropattern displayed 13C depletion (–27.6‰) and 15N enrichment (5.9‰) from the canal sites with more favorable hydrological condition.
The different patterns for the changes in δ13C and δ15N in cattail suggested that increased nutrients led to increased stomatal conductance and 13C fractionation during carbon uptake and decreased 15N fractionation with increasing nitrogen demand while poor hydrological condition coupled with low nutrients led to reduced plant growth indicated by higher δ13C and lower δ15N values. Findings from this study suggested that δ13C in emerged macrophytes such as cattail can be used as an indicator for environmental stress while δ15N is a robust indicator for wetland eutrophication.
Florida’s Everglades is the largest subtropical peatland in the USA with its historic geochemistry and biological community characterizing an oligotrophic ecosystem (Richardson 2010). Since human settlement, a large portion of the Everglades peatland immediately south of Lake Okeechobee was converted into farmlands, i.e., Everglades Agricultural Area (EAA). The remaining Everglades has been divided into three Water Conservation Areas (WCA-1, WCA-2, and WCA-3) and Everglades National Park (ENP). Increased P loads have shifted portions of the ecosystem from oligotrophic to eutrophic states. The sawgrass in northern WCA-2A, an area that has received EAA discharge, has been replaced by cattail which was not present in large quantity in the historic Everglades (Sklar et al. 2005). To protect the biodiversity from further deterioration, several Stormwater Treatment Areas (STAs) have been constructed at the northern end of the EPA to treat EAA runoff for P removal (Chimney and Goforth 2006).
Current indicators of environmental changes for the Everglades as well as for other aquatic systems focus on the impacts of nutrient loading such as soil and water total P (TP) and total N (TN) concentrations, species composition, biomass, and primary production (Newman et al. 1996; Sklar et al. 2002, 2005; Wright et al. 2008). These indicators often reveal the changes in the impacted systems that have taken place. Ecological research and restoration efforts indicate that it is extremely difficult to restore ecosystems that have been severely disturbed. Therefore, the identification of early symptoms of environmental change, prior to major damage, is critical for the restoration of disturbed systems to conserve natural resources (Mwaura et al. 2017).
Carbon and nitrogen stable isotope compositions (δ13C and δ15N) of biota may be an alternative means to detect early environmental changes in aquatic ecosystems (Oczkowski et al. 2014; Wang et al. 2015; Gooddy et al. 2016; Nigro et al. 2017) and can provide insight into the sources, sinks, and cycling of carbon and nitrogen in biota that interact with their physical and chemical environments. Several studies have indicated that δ13C and δ15N values can be used as early indicators for environmental changes (McKee et al. 2002; Wang et al. 2015; Zhang et al. 2016; Nigro et al. 2017). The 13C depletion in the mangrove trees has been attributed to reduced stomatal conductance under environmental stressors such as nutrients and salinity (Lin and Sternberg 1992; McKee et al. 2002). Inglett and Reddy (2006) found different responses of δ13C in sawgrass and cattail along a nutrient gradient of the WCA-2A of the Florida Everglades.
The δ15N values of various plant species have been used as indicators for the sources and magnitude of wastewater discharge into estuaries and coast ecosystems (Cole et al. 2004; Savage 2005; Lapointe et al. 2015; Mancinelli and Vizzini 2015) and inland waters (Hall et al. 1999; Lake et al. 2001). Biota δ15N has also been used as an indicator of eutrophication, especially under increased P loading. Studies show that primary producers respond to P enrichment with rapid N uptake, thereby resulting in decreases in 15N fractionation. Inglett and Reddy (2006) found higher δ15N in cattail than in sawgrass along a P gradient in WCA-2A and attributed the difference to the faster growth of cattail compared to sawgrass. Chang et al. (2009) found that sawgrass δ15N is correlated with cattail δ15N in WCA-1, suggesting similar responses to environmental variations in the two macrophytes.
The present study compared δ13C and δ15N in cattail (Typha domingensis Pers.) collected from the reference, transition, and impacted sites in south Florida wetlands. Cattail was chosen to test if stable isotope variations along the hydrological and nutrient gradients can be used to infer environmental stress and nutrient enrichment. It also provides insightful information on factors controlling isotope composition in cattail community.
Materials and methods
A total of 14 sites, with 2 sites in STA-1W and 12 sites in STAs and WCAs (Fig. 1) were used in this analysis. These sites were located at canals or marshes where water depth, retention time, nutrients, and other environmental conditions differed among sites (Table 4 in Appendix). Study sites at cell 3 and cell 4 of the STA-1W, and E0 and F1 of WCA-2A (impacted sites) that received direct EAA discharges are highly enriched with TP (> 20 μg L−1). Study sites located immediately downstream of STA-1W, WCAs, or close to interior canals (transition sites) are moderately enriched with TP (> 10 and ≤ 20 μg L−1). Interior marshes (reference sites) in WCAs typically maintain the oligotrophic state indicated by a low TP concentration (≤ 10 μg L−1). Total N and dissolved inorganic N (DIN) concentrations were also higher at the near inflow sites than the marsh interior sites, except for U3, the interior site of WCA-2A, which is enriched with ammonium and TN. All study sites are generally characterized by above-neutral pH (Table 4 in Appendix).
Sources of data
There are several sources of data used in this study. Stable isotope data on cattail were downloaded from the US Geological Survey South Florida Information Access (https://sofia.usgs.gov/metadata/sflwww/ever_isotope_data.html) and Wang et al. (2015). Typically, duplicate to triplicate samples were collected from each site for stable isotope determination. Select environmental data (Table 4 in Appendix) from the same time period (1995 to 2009) of the stable isotope data collection were downloaded from DBHYDRO, a hydrometeorologic, water quality, and hydrogeologic data retrieval system managed by the South Florida Water Management District (West Palm Beach Florida, USA), Miao and Sklar (1997) and Wang et al. (2015). When environmental data were not available from the same site of cattail collection, data from closely located sites were used.
Statistical analysis was conducted using the SigmaPlot 13.0 software (Systat Software, Inc). Data were tested for normality using the Shapiro-Wilk normality test and equal variance test (Brown-Forsythe) before an analysis was performed. Cattail isotope data from different sites or habitats were analyzed by analysis of variance (ANOVA). For data that did not pass normality and equal variance test, the Kruskal-Wallis ANOVA on ranks was used, followed by Dunn’s method or Tukey test. Spearman’s rank correlation was used to test significant trends. Statistics were considered significant at p < 0.05.
Environmental characteristics along nutrient gradient
A summary of select environmental variables grouped by reference, transition, and impacted sites are presented in Table 1 (N = 14 sites). Significant differences in TP concentration were found among reference, transition, and impacted sites. TP concentration at the transition sites was twice as high as the reference sites while TP concentration at the impacted sites was over three folds greater than the transition sites. Similarly, there were significant differences in soluble reactive phosphorus (SRP) concentration along the nutrient gradient. Despite there were tendencies with a progressive increase in TN, DIN, and pH from reference, transition to impacted sites, differences among these sites were not significant (p > 0.05).
Table 2 presented several biological and nutrient variables along the nutrient gradient from inflow to interior marsh in WCA-2A (the F transect, Fig. 1) obtained from the literature (Miao and Sklar 1997; Wang et al. 2015). Data were grouped into reference, transition, and impacted sites as described above. Average cattail plant height was lowest at the reference, intermediate at transition, and highest at the impacted sites. Similarly, the photosynthetic rate measured for cattail increased along the nutrient gradient. Surface water and soil TP also displayed a trend of increases along the transect. Surface water TN decreased slightly while soil TN increased slightly along the transect (Table 2).
Variations in cattail δ13C and δ15N
Average cattail δ13C values decreased significantly from reference (−24.1‰), transition (−26.8‰) to the impacted sites (−28.2‰) (ANOVA, F = 23.5, df = 2, p < 0.001). Pairwise multiple comparisons indicated significant differences for all sites (Fig. 2a). By contrast, average cattail δ15N values increased significantly from reference (−5.3‰), transition (2.4‰) to the impacted site (6.0‰) (ANOVA, F = 17.6, df = 2, p < 0.001). Pairwise multiple comparisons indicated significant differences for all sites (Fig. 2b). Similar to stable isotope responses to nutrient enrichment, cattail δ13C and δ15N increased and decreased, respectively, as soil molar TN:TP ratio increased (Fig. 3a, b). When data from all sites were pooled, several significant correlations between cattail stable isotope values and nutrients are found (Table 3). Cattail δ13C values were negatively correlated with δ15N and TP concentrations, but positively correlated with molar TN/TP ratios. Cattail δ15N values were positively correlated with TP concentrations and negatively correlated with TN/TP ratios. Correlation between TN, δ13C, and δ15N was not significant.
When data were grouped by habitats, δ13C and δ15N values differed significantly between the marsh and canal sites (Fig. 4a, b). Average cattail δ13C values are higher (−26.0‰) in marsh area than in canal (−27.6‰) (F = 6.65, p = 0.024). By contrast, average cattail δ15N value was depleted in the marsh (0.2‰) than from the canal sites (5.9‰) (F = 6.80, p = 0.023). There were no significant differences in TP or TN between the marsh and canal sites (Fig. 4c, d).
Responses of cattail δ13C to nutrient enrichment
Similar to terrestrial plants, emergent aquatic plants use atmospheric CO2 which is well mixed worldwide. Therefore, substrate effects (concentration and isotope baseline) during C uptake can be eliminated as causes for cattail isotope changes along nutrient gradient. The δ13C values of cattail collected from STAs and WCAs in south Florida decreased from reference to the impacted sites. Chang et al. (2009) and Wang et al. (2015) also found a negative relationship between soil TP and cattail δ13C in WCA-1 and WCA-2A. We attribute the δ13C enrichments of cattail at the impacted marshes of the Everglades to reduced isotopic fractionation due to low stomatal conductance under environmental stress. Similar observations have been reported for scrub or dwarf red mangrove (Rhizophora mangle) growing in P-limited areas (Lin and Sternberg 1992; McKee et al. 2002). Miao et al. (1997) reported that the photosynthetic rate of sawgrass seedlings from the Everglades was a function of stomatal conductance in a nutrient addition experiment. With the increases in P concentrations and photosynthetic rate, plant stomatal conductance increases, reducing restriction to CO2 transport into the carboxylation sites, which may lead to higher 13C fractionation. Conversely, under P stress, emergent plants reduce their stomatal conductance, making CO2 diffusion a rate-limited process, which in turn results in reduced 13C fractionation. Low photosynthetic rates in the nutrient-poor environment may result in larger 13C fractionation. Apparently, the cattail 13C enrichment in the reference sites is controlled more by stomatal conductance (CO2 availability) than carboxylation rate (CO2 demand). This is verified in a recent study reported by Wang et al. (2015) who found that cattail δ13C decreased as the photosynthetic rate increased along the nutrient gradient in WCA-2A. These results demonstrated that the δ13C of emergent macrophytes such as cattail is a sensitive indicator for environmental stress, such as P deficiency in freshwater wetlands, consistent with the studies conducted in the mangrove forest (Lin and Sternberg 1992; McKee et al. 2002).
Responses of cattail δ15N to nutrient enrichment
The cattail δ15N may be controlled by various factors including the sources of N with different δ15N values, the concentration of DIN, and the growth rate which is affected greatly by P availability, plant physiology, and the underwater light condition. Nitrogen from human and animal wastes is enriched in δ15N (McClelland et al. 1997). Enriched δ15N of various taxa has been used as an indicator for sewage influence in the freshwater and coastal marine environments (Cole et al. 2004; Nixon et al. 2007; Bannon and Roman 2008; Orlandi et al. 2014; Lapointe et al. 2015). There have been no reports of any significant wastewater contributions from human or animal sources to the Everglades. In fact, Inglett and Reddy (2006) reported a similar δ15N of porewater NH4+ (~7‰) in the impacted and unimpacted areas in WCA-2A. Therefore, the high δ15N at the impacted sites is not the result of uptake of wastewater enriched with 15N.
Dissolved inorganic nitrogen concentration may also influence cattail δ15N through a substrate-mediated isotope effect (Peterson and Fry 1987). An increase in N concentration will normally lead to an increase in isotopic fractionation and therefore a decrease in plant tissue δ15N. However, across the nutrient gradient, changes in DIN concentrations were not significant (Table 1). The high molar ratios of TN:TP which is greater than 16 implies that N is not a limiting nutrient to plant growth in the Everglades. The negative correlation between the water column TN:TP ratio and cattail δ15N also indicates that P, not N, is the limiting nutrient in the Everglades.
The major external source of N in the Everglades is an agricultural runoff. Because manufactured fertilizers are depleted in 15N (Kohl et al. 1971), assimilation of this 15N-depleted N will not result in 15N enrichment in the impacted sites. We conclude that the 15N enrichment in cattail at the impacted sites of the Everglades is the result of increased plant growth stimulated by P availability. The cattail low δ15N at the reference sites was the result of slow growth and large 15N fractionation under P stress. The high N availability at the reference sites also allowed selective assimilation of 14N by cattail, further lowering the tissue δ15N. Similarly, low δ15N in the transition and dwarf trees of the red mangrove was attributed to low N demand (McKee et al. 2002). Mwaura et al. (2017) also reported an apparent onshore-offshore gradient in macrophyte δ15N stimulated by terrestrial loading of nutrients. In contrast, the high δ15N at the impacted sites was due to P enrichment which leads to high N demand and low 15N fractionation. Many studies have demonstrated that P is the limiting nutrient in the Everglades (Newman et al. 1996; Smith et al. 2009). Recent studies using stable isotopes found a positive relationship between TP and δ15N of periphyton, sawgrass, and cattail in WCA-1 and WCA-2A, which was attributed to P-driven plant growth and reduced isotope fractionation (Inglett and Reddy 2006; Chang et al. 2009).
Responses of cattail δ13C and δ15N to changes in hydropattern
Water depth and duration may affect the growth of aquatic plants which in turn affects tissue δ13C and δ15N. Newman et al. (1996) demonstrated that water depth and duration of flooding significantly impact cattail expansion in two south Florida wetlands. In the Everglades, marsh typically has shallower water depth and shorter hydroperiod than canals. Compared to cattail grown in the marsh, 13C depletion in the canal habitat may suggest that high growth rate led to plant stomatal conductance increases, reducing restriction to CO2 transport into the carboxylation sites, leading to higher 13C fractionation. By contrast, slow-growth cattail in the marsh habitat requires less CO2 to support photosynthesis, resulting in less isotope fractionation. The effects on cattail δ13C along the hydrological gradient are similar to those along the nutrient gradient: environmental stress may lead to less isotope fractionation due to reduced substrate demand (Lin and Sternberg 1992; McKee et al. 2002; Wang et al. 2015).
The δ15N in cattail grown in the canal habitat was significantly higher than that in the marsh habitat. Both TP and TN concentrations did not differ significantly between the marsh and canal habitat although the average TP concentration at the canal sites was twice high as that in the marsh. Cattail growth in the canal habitat was stimulated by more favorable hydropattern than those grown in the marsh sites. Apparently, high N uptake results in reduced isotope fractionation (Peterson and Fry 1987; Dawson et al. 2002). More research is needed to understand the interactive relationship between nutrients, hydrology, plant growth, and δ15N in cattail under different hydrological and nutrient scenarios.
Human influences have led to multiple ecosystem changes. This study demonstrates that stable isotopes are generally sensitive environmental indicators and can be used to assess the responses of aquatic plants to nutrient stress, enrichment, and water management. The 13C enrichment in cattail from the pristine marsh is an indicator for nutrient stress which is reduced at transition and especially the impacted sites as δ13C become depleted due to increases in gas conductance. This conclusion is consistent with the findings from the studies of red mangrove isotope composition along salinity and nutrient gradients. The eutrophication process resulting from excessive P loading from the agricultural runoff to the Everglades is best demonstrated using cattail δ15N which responded positively to the increases in TP concentration. Similar responses of cattail δ13C and δ15N to hydrological changes were also identified in this work. Further study needs to understand the role of each factor (nutrient and hydrology) in controlling δ15N in cattail along the nutrient and hydrological gradient.
Availability of data and materials
All data used in this manuscript will be available upon request.
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We appreciate the United States Geological Survey and the South Florida Water Management District for providing stable isotope and water quality data.
This study was supported from an Overseas Research collaboration grant (2018AHB020) funded by Hubei Province, China.
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Zheng, Z., Xu, Y., Wang, J. et al. Environmental stress and eutrophication in freshwater wetlands: evidence from carbon and nitrogen stable isotopes in cattail (Typha domingensis Pers.). Ecol Process 8, 31 (2019). https://doi.org/10.1186/s13717-019-0186-4