Elani B. Elizondo
Joanna C. Carey
Alia N. Al-Haj
Ariel E. Lugo
Robinson W. Fulweiler- 1Department of Earth and Environment, Boston University, Boston, MA, United States
- 2Maths and Science Division, Babson College, Wellesley, MA, United States
- 3International Institute of Tropical Forestry, USDA Forest Service, Río Piedras, PR, United States
- 4Department of Biology, Boston University, Boston, MA, United States
Over the last two decades, recognition of the important role terrestrial plants play in regulating silicon (Si) cycling has emerged. Si improves plant fitness by protecting them from abiotic (e.g., desiccation) and biotic (e.g., fungal attack) stressors. Once incorporated into plant biomass this biogenic Si is more bio-available than the lithogenic material from which it was ultimately derived. Thus plants play a key function in regulating the amount and timing of Si availability in downstream ecosystems. Recent work has highlighted the importance of salt marshes in the temperate Si cycle. However, the role of their tropical counterparts, mangroves, has largely gone unexplored. Here we report foliar concentrations of plant Si (as %Si by dry weight) for four Caribbean mangrove species: Conocarpus erectus (buttonwood), Laguncularia racemosa (white mangrove), Avicennia germinans (black mangrove), and Rhizophora mangle (red mangrove). Overall, the median Si concentration was low (0.07%) and did not vary among plant part (e.g., foliage, twig, and propagule). There was also little variation in Si among species. Using literature values of aboveground net primary production, and the concentrations reported here, we estimate an aboveground mangrove Si uptake rate of 2–10 kg Si ha–1 year–1. These rates are on par with rates reported for temperate and boreal forests as well as low nutrient salt marshes, but lower than estimates for high nutrient salt marshes. Thus, despite the low Si concentrations observed in mangroves, their high productivity appears to make them a hot spot of Si cycling in tropical coastal systems.
Introduction
Silicon (Si) is the second most abundant element in the Earth’s crust, and is released as silicic acid [dissolved silica (DSi); Si(OH)4] via weathering. A variety of marine organisms are silicifiers including diatoms, radiolarians, silicoflagellates, select sponges, and even picocyanobacteria (Tréguer and De La Rocha, 2013). Photosynthesizing silicifiers (e.g., diatoms) take up significant amounts of Si along with nitrogen, phosphorus, and inorganic carbon, tightly coupling these biogeochemical cycles (Tréguer et al., 2021). Diatoms are responsible for ∼50% of oceanic primary productivity (Rousseaux and Gregg, 2013) and are an important source of carbon (C) export to the deep ocean (Tréguer et al., 2018). Diatoms also play a key role in coastal productivity and food web structure (Hackney et al., 2002).
Over 80% of the annual inputs of DSi to the global ocean comes from land (Tréguer and De La Rocha, 2013). While rivers are the primary transport mechanism, the path of DSi from land to sea is not direct (Struyf and Conley, 2012). Over the last two decades a new paradigm has emerged that highlights the importance of Si uptake by terrestrial vegetation, with land plants intercepting Si as it makes its way along the land-ocean continuum (Conley, 2002; Carey and Fulweiler, 2012). In fact, Si is rapidly recycled through the terrestrial plant reservoir, and this terrestrial cycle helps regulate the flux of Si from continents (Conley, 2002; Carey and Fulweiler, 2012; Struyf and Conley, 2012). Plants take up DSi from the soil solution and groundwater via their roots and transport it throughout the plant where it is deposited as biogenic silica (BSi; Epstein, 1994; Raven, 2003). BSi mostly accumulates as siliceous bodies known as phytoliths at transpiration termini (Epstein, 1994; Raven, 2003). Plants return this BSi to soils, chiefly as litter fall, where it dissolves seven to 20 times faster than mineral silicates (Fraysse et al., 2009; Cornelis et al., 2011). Thus on biological time scales, terrestrial vegetation plays an important yet not fully understood role in altering Si cycling within and across ecosystems.
Wetlands are borderland ecosystems–not quite terrestrial, not quite aquatic. Yet, they play an important role in regulating the availability of Si in downstream ecosystems. All plants contain some Si in their tissue, with concentrations ranging from <0.1 to 10% by dry weight (Epstein, 1999; Raven, 2003; Hodson et al., 2005). Some plants, like those that characterize wetlands (e.g., grasses and sedges), have particularly high BSi concentrations. Thus wetlands are described as “hot spots” for Si cycling (Struyf and Conley, 2009). Wetland sediments also typically contain elevated amorphous silica (ASi) concentrations (Norris and Hackney, 1999; Struyf et al., 2010), particularly in the top sediment layers (Carey and Fulweiler, 2013). ASi is comprised mostly of the BSi fraction in soils, sourced from both plant BSi and benthic algae growth (Carey and Fulweiler, 2013). ASi is also comprised of the non-mineral pedogenic fraction, such as the Si sorbed to iron and aluminum oxi/hydroxides (Saccone et al., 2007; Cornelis et al., 2011). Substantial research effort has focused on Si cycling in temperate wetland ecosystems, specifically tidal freshwater and saltwater marshes, where large Si reservoirs in sediments, plants, and porewater have been documented (Struyf et al., 2005; Carey and Fulweiler, 2013; Müller, 2013). Tidal exchange connects salt marsh Si reservoirs to adjacent estuarine systems, often supplying substantial quantities of DSi to marine waters (Vieillard et al., 2011; Müller et al., 2013; Carey and Fulweiler, 2014a).
While evidence points to the dynamic and critical role of salt marshes in coastal temperate Si cycling, the role of salt marshes’ lower latitude counterpart–mangroves–in tropical coastal Si cycling remains unknown. We hypothesized that mangroves are significant reservoirs of Si and that their high productivity could make them an important, yet overlooked, driver of tropical Si cycling. Here we report concentrations of Si in the foliar tissue of four common species of Caribbean mangrove (Conocarpus erectus (buttonwood), Laguncularia racemosa (white mangrove), Avicennia germinans (black mangrove), Rhizophora mangle (red mangrove) from four locations. We also report twig and propagule Si concentrations for a sub-set of these species, as well as sediment concentrations for one of the study sites. Finally, we estimate net aboveground Si accretion in mangroves to determine their potential role as Si reservoirs in coastal tropical systems. To our knowledge, these are the first estimates of Si accretion rates in mangrove forests.
Materials and Methods
We collected samples from San Salvador Island in the Bahamas, Wee Wee Caye in Belize, the western coast of Florida, and at several locations on the island of Puerto Rico (Figure 1). The mangrove species present at each site varied by location, and thus, we did not collect samples from all species at all locations (Table 1). We were able to obtain foliar samples from Rhizophora mangle from all four locations. Samples were collected between 2010 and 2018 across a total of four sampling events. These samples were collected during other field research, coursework, or vacation and this research was not funded, which constrained our sampling ability. At each site we haphazardly collected 2–4 replicates of mangrove foliage, twig, and/or propagule samples from at least two different trees (in most cases; Table 1). In the field, samples were stored in clean, labeled, plastic bags.
Figure 1. Mangrove samples were collected from Florida and Puerto Rica, USA; San Salvador, Bahamas, and Wee Wee Caye, Belize (a). We collected samples from three sites in Florida (b), three sites in Puerto Rico (c), and two sites in the Bahamas (d).
Table 1. Median, median absolute deviation (mad), sample type, status, and the number of trees sampled (n) for mangrove Si concentrations (as %Si by dry weight) organized by location and species.
In Puerto Rico, we also obtained sediment samples for ASi concentrations from the edge and interior of an Avicennia germinans basin forest. Specifically, we collected triplicate sediment samples at 0–1 and 1–2 cm depths.
Upon return to the laboratory, mangrove samples were rinsed with deionized water, and all samples were oven dried at 60°C until a constant dry weight was reached. Dried foliar samples and sediment samples were milled using a Wig-L-Bug and ∼30 mg samples were digested using a 1% Na2CO3 wet alkaline digestion method (DeMaster, 1981; Conley and Schelske, 2002). Sediment samples were digested for a total of 5 h, and we subsampled at hours 3, 4, and 5 so that we could correct for mineral silicate (DeMaster, 1981; Sauer et al., 2006). Briefly, DSi concentrations are plotted overtime and a linear line is fit to the data. If there is no significant DSi concentration change overtime you take an average of the measured concentrations as the sample ASi value. If, however, the linear fit is significant then you extrapolate the linear part to zero and use the Y-intercept as the sample ASi value (DeMaster, 1981; Conley and Schelske, 2002).
The DSi in the digested samples were then analyzed using the molybdenum blue colorimetric method on a Seal AA3 flow injection analyzer (Strickland and Parsons, 1968) and DSi was then converted to %Si. Internal and external standards were used to ensure that the Seal AA3’s results were within 4% of expected values. Throughout this manuscript, we report biogenic Si as %Si by dry weight and thus do not refer to it as biogenic silica, which is really %SiO2. Similarly note, that ASi is often reported as %SiO2 and here we report it as %Si.
We estimated mangrove Si accretion rates following the methods used by Conley (2002) and Carey and Fulweiler (2012). First, we calculated the Si:C ratio by dividing the median mangrove aboveground Si concentration by 47%, the average C concentration typically found in mangrove leaves (Castañeda-Moya et al., 2013). We then multiplied this Si:C ratio by recently reported estimates of above ground net primary production (NPP) for a representative system: mangroves in Florida (Castañeda-Moya et al., 2013). We report uptake rates in kg of Si ha–1 year–1.
Data analysis was conducted in R studio version 1.3.1056. We present median ± median absolute deviation (mad) %Si concentrations and used non-parametric statistics (i.e., Kruskal–Wallis test) to compare the %Si content across the mangrove species and across sites because the data were not normally distributed (Shapiro–Wilk test: p < 0.0001). We considered p-value < 0.05 as significant in this study. The full data set is available at via fighare at: https://figshare.com/s/9d49c0f6fe4e63fec7ee
Results
Plant Si concentrations ranged from 0.02% in Rhizophora mangle foliage from Florida to 0.24% (± 0.09) in the twigs of Conocarpus erectus from Puerto Rico (Table 1). We observed few significant differences in mangrove Si concentrations across plant part, location, and species. Including data from all mangrove species, Si concentrations did not differ significantly between plant part sampled (e.g., foliar, twig, or propagule; p = 0.75) or between live or dead samples (p = 0.33). In addition to the lack of difference among plant parts or status, we found no significant differences in plant Si concentrations within a single species by location. For example, Si concentrations in Rhizophora mangle, which was present at all four locations, were the lowest in Belize and the highest in the Bahamas, but not significantly so (p = 0.0686; Figure 2A).
Figure 2. Foliar Si concentrations (as %Si) of Rhizophora mangle (red mangrove) are not significantly different across the four sampling sites (p = 0.0686). Median foliar %Si (dashed blue line) for Rhizophora mangle was 0.06 (±0.04 median absolute deviation). (A) Foliar Si concentrations (as %Si) for four mangrove species from Puerto Rico. (B) Laguncularia racemosa Si concentrations are significantly (p = 0.048) higher than Si concentrations observed in Rhizophora mangle. Median foliar %Si (dashed blue line) for mangroves in Puerto Rico was 0.07 (±0.02). Mangroves are listed in order of the generally observed zonation patterns from inland to coast.
Within individual species at a single site (i.e., Puerto Rico), we observed little variability in Si concentrations, with the exception of Avicennia germinans which demonstrated some (Figure 2B). Overall, Rhizophora mangle had the lowest Si concentrations, but only significantly (p = 0.048) so when compared Laguncularia racemosa.
In contrast to the low concentrations in the mangrove biomass, we found much higher concentrations of ASi in sediments from the Avicennia germinans basin forest in Puerto Rico, ranging from 0.42 to 1.94% Si. ASi concentrations were significantly higher (p = 0.001) at the forest edge compared to the interior (median: 0.53 and 1.46%, respectively).
Discussion
The aboveground mangrove Si concentrations we observed are similar to the those in Rodin and Bazilevich (1967), who report Si concentrations from Rhizophora mucronata leaves (0.08%) collected in China as well as Rhizophora mangle leaves (0.1%), fruit (0.11%), branches (0.11%), and sub-aerial roots (0.24%) collected in Brazil. Overall, the Si concentrations observed in mangroves are relatively low, especially compared to salt marsh grasses. For example, mature aboveground biomass of Spartina alterniflora, a common salt marsh grass, typically ranges from 0.21 to 0.53% along its native coast of North America (Norris and Hackney, 1999; Carey and Fulweiler, 2013, 2014b). Similarly, mature aboveground Spartina patens, another native grass commonly found in North American salt marshes, typically exhibit Si concentrations ranging from 0.14 to 0.42% (Carey and Fulweiler, 2013, 2014b). Moreover, mature aboveground Juncus Roemerianus, observed in the more southern Mid-Atlantic coast of North America, had higher Si concentrations (0.0.21%) compared to the mangroves we studied here (Norris and Hackney, 1999).
The higher concentrations of Si observed in salt marsh grasses compared to mangrove trees is not surprising given that grasses are well known to accumulate high concentrations of Si relative to other plant groups (Epstein, 2001; Hodson et al., 2005). Si concentrations in trees vary substantially. For example, Si concentrations in Fagus sylvatica (European beech), Quercus sp. (oak), and Acer sp. (maple) are typically at least an order of magnitude greater (>0.47% Si by dry weight) than what we observe in mangrove forests (Cornelis et al., 2010b; Fulweiler et al., 2015; Clymans et al., 2016). Rodin and Bazilevich (1967) report foliar Si concentrations for twenty tropical tree species ranging from 0.03% for Caparis aphylla to 5.68% for Lagerstroemia flosreginae. Nevertheless, the low Si concentrations observed in mangrove species are still within the range of observations from other tree species. For example, mangrove foliage Si closely match that of Betula alleghaniensis (yellow birch; 0.16 ± 0.06%) and several temperate gymnosperm tree species, such as Pinus thunbergia (black pine; 0.02–0.05%) (Cornelis et al., 2010a,b). Moreover, mangrove foliage Si concentrations also nicely align with those of the most common tropical dryland tree species, which typically have Si concentrations <0.47% Si (de Tombeur et al., 2020).
The lower concentrations of Si in mangroves, compared to higher latitude wetlands and many temperate tree species could be due to several factors. First, DSi availability may be low in Caribbean mangrove systems due to typically low DSi concentrations in tropical marine waters, carbonate platforms, and highly weathered soils (Kaye, 1959; Marfia et al., 2004; Shipe et al., 2006; Gulley et al., 2014; Mattheus and Fowler, 2015). Lower DSi availability in sediments, and therefore sediment porewater, would result in lower Si accumulation as plants passively (i.e., take up Si as they take up water) incorporate Si into their transpiration stream. In addition, soil age may also be a factor dictating Si availability, as Si availability is lowest in young and very old soils and highest in middle-aged sites (de Tombeur et al., 2020). Finally, low Si accumulation in mangrove foliage could be due to relatively low transpiration rates in mangrove ecosystems (Passioura et al., 1992), resulting in less DSi uptake and reduced Si deposition within the plants.
The similar Si concentration we observe across mangrove plant parts (i.e., foliage vs. twig) appears unique among trees. For example, observations from six species of temperate angiosperms and gymnosperms from two separate regions document foliar Si concentrations consistently one or two orders of magnitude greater than woody tissue (Markewitz and Richter, 1998; Cornelis et al., 2010b; Maguire et al., 2017). The lack of difference between foliar and woody tissue in mangroves appears to be a function of their low foliar concentrations, as mangrove low woody Si concentrations are typical of many tree species.
Sediment ASi concentrations are on par with those reported for temperate forests (Gewirtzman et al., 2019) and several temperate salt marshes, both from North Carolina (United States) (Norris and Hackney, 1999) and an outlet of the Yangtze River (China) (Hou et al., 2010). However, the ASi concentrations (0.42–1.94% Si) measured in the top 2 cm of the mangrove sediments we studied here are drastically lower than those reported for the top 1 cm of sediment in two New England temperate salt marshes (∼4% ASi by dry weight) (Carey and Fulweiler, 2013). Clearly, sediment ASi concentrations range dramatically across higher latitude coastal wetlands (i.e., salt marshes) and thus, likely vary across mangrove ecosystems as well. While these data are preliminary, they suggest that mangrove forests may concentrate bio-available Si more in their sediments compared to their biomass. Compared to mineral silicates, ASi is often much more labile, with a large fraction consisting of highly soluble BSi (Saccone et al., 2007; Cornelis et al., 2011). ASi-rich sediment stores could become sources of bioavailable Si to their surrounding estuaries during periods of erosion and sediment export.
We calculated an aboveground Si accretion rate by mangroves and, for comparison, salt marshes. Our estimated median aboveground mangrove Si:C ratio is 0.0015. Given that foliage and woody tissue Si concentrations did not significantly vary in the mangroves we study here, we feel comfortable using one value to represent aboveground mangrove Si:C ratios. Moreover, these ratios are on par with those estimated previously for a range of biomes (Carey and Fulweiler, 2012). We estimate that mangroves take up between ∼2 and 10 kg Si ha–1 year–1, depending on aboveground productivity at the site. These accretion rates overlap with estimates of aboveground accretion from a low nutrient reference salt marsh dominated by Spartina patens (8 ± 0.8 kg Si ha–1 year–1) but are an order of magnitude lower than those observed from a Spartina alterniflora dominated marsh (29 ± 3.1 kg Si ha–1 year–1) (Carey and Fulweiler, 2013; Table 2). Moreover mangrove Si uptake is on par with or lower than uptake rates reported for aboveground biomass alone or full ecosystem uptake of Si in other ecosystems (2–67 kg Si ha–1 year–1; Table 2).
Table 2. Silicon uptake rates (kg Si ha–1 year–1) as reported for a range of ecosystems and the first estimate for mangroves.
We recognize that our aboveground mangrove Si accretion rate values are simplified first estimates that exclude belowground Si accretion, which could be large (Donato et al., 2011; Lamont et al., 2020). It is unclear whether belowground portions of mangroves would exhibit higher or lower Si concentrations compared to their above counterparts. While similar Si concentrations have been reported for aboveground and belowground biomass of two salt marshes species in an undisturbed system in New England during peak growing season (Carey and Fulweiler, 2013) studies show both similarities and differences between aboveground and belowground Si concentrations from temperate ecosystems. For example, Gérard et al., 2008 find similar concentrations in fine roots and bole biomass of spruce trees, whereas Maguire et al. (2017) find root Si concentrations are dramatically higher than aboveground woody tissue but lower than foliage in red maple. Rodin and Bazilevich (1967) reported sub-aerial root Si concentrations that were double that of the foliage and branches in mangroves in Brazil. If such a pattern holds true generally, then mangroves may be sequestering much more Si in their belowground biomass, making their contribution to tropical Si cycling potentially much larger. Clearly, future work should partition aboveground versus belowground mangrove accretion rates, examining how these rates vary spatially and by species.
Compared to higher latitude coastal temperate systems, tropical coastal systems generally exhibit more muted Si dynamics. For example, unlike coastal temperate waters where diatoms dominate (Rousseau et al., 2002; Barton et al., 2013), the Caribbean phytoplankton community is dominated by coccolithophores (Winter et al., 2002), phytoplankton that do not require Si to survive. While pulses of diatom blooms do occur in the Caribbean (Dandonneau et al., 2006), such blooms are often associated with La Niña events and are short-lived (Alvain et al., 2008). Correspondingly, surface waters of the Caribbean are often Si-depleted, ranging from 2 to 4.5 μM, depending on the season (Froelich et al., 1978), lower than those typically found in higher latitude coastal systems (Shipe et al., 2006). Together, differences in coastal autotrophic communities, surficial water DSi availability, and coastal wetland type indicates that Si cycling in tropical systems may be less dynamic compared to higher latitude systems. Mangroves appear to follow this pattern, exhibiting low Si concentrations in their foliage and little differences in Si concentration among aboveground plant parts. However, their elevated primary productivity and standing stock of biomass results in mangrove forests serving as relatively large reservoirs of Si in tropical coastal systems, reinforcing the idea that wetlands are “hot spots” of Si cycling, even in the tropics. Future research should more robustly account for the differential Si uptake and recycling rates of Si among various plant parts in mangrove systems, as well as the potential for these systems to export Si to tropical receiving waters via tidal exchange.
Data Availability Statement
The datasets presented in this study can be found in online repositories. The names of the repository/repositories can be found below: https://figshare.com/s/9d49c0f6fe4e63fec7ee.
Author Contributions
RWF and JCC conceived of this study. AA-H, JCC, AEL, and RWF collected samples. AA-H and JCC processed samples in the laboratory. EBE, JCC, and RWF conducted data analysis and wrote the manuscript. All authors contributed to editing of this manuscript.
Funding
This project was funded in part by a Sloan Foundation Fellowship to RWF. Travel to the Bahamas was funded by the University of Virginia.
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.
Acknowledgments
We thank Daniel Orchard, Alexandra Bijak, and Jennie Rheuban for sample collection help in Puerto Rico and in Bahamas. Work in Puerto Rico was done in collaboration with the University of Puerto Rico. We thank Dr. Tim Maguire for helpful discussion on statistics and the role of terrestrial plants in Si cycling.
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Keywords: foliage, terrestrial Si cycle, plants, biogeochemistry, silicon
Citation: Elizondo EB, Carey JC, Al-Haj AN, Lugo AE and Fulweiler RW (2021) High Productivity Makes Mangroves Potentially Important Players in the Tropical Silicon Cycle. Front. Mar. Sci. 8:652615. doi: 10.3389/fmars.2021.652615
Received: 12 January 2021; Accepted: 06 April 2021;
Published: 20 May 2021.
Edited by:
Christian Grenz, UMR 7294 Institut Méditerranéen d’Océanographie (MIO), FranceCopyright © 2021 Elizondo, Carey, Al-Haj, Lugo and Fulweiler. 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.
*Correspondence: Robinson W. Fulweiler, rwf@bu.edu