The sediment capture is one of these critical ecological processes that contribute to a supporting ecosystem service, as the sedimentation in coastal ecosystems is associated with the regulation of tidal flow speed ( Kobashi and Mazda, 2005) and the concentrations of suspended sediment and organic matter in the water flowing through mangroves ( Kobashi and Mazda, 2005 Adame et al., 2015 Friess and McKee, 2021). These processes are essential for other mangrove ecosystem services, such as wood and food provision ( Mitsch et al., 2015). Some of them are related to reducing mangroves and adjacent habitats' vulnerability to climate change impacts, including supporting ecosystem services originating from key ecological processes such as soil formation, nutrient cycling, and primary productivity. The interactions between these characteristics generate many ecosystem services ( Getzner and Islam, 2020). The sediment accumulation in mangroves shows patterns ( Adame et al., 2010) at spatial and temporal scales related to hydrodynamics (e.g., floods, water flows, precipitation, tides, surges, and storms), which, in turn, control organic and inorganic sediment supplies ( Woodroffe et al., 2016), modulated by terrain slopes, topography, and geomorphological features ( Twilley and Rivera-Monroy, 2009 Cannon et al., 2020 MacKenzie et al., 2021). Different forest types can be observed according to their vegetation structure, growing in diverse areas with hydrological, physicochemical, and sediment characteristics ( Middelburg et al., 1996). This ecosystem shows variability in its vegetation characteristics and adaptations like prop roots and succulent leaves ( Naskar and Palit, 2015). Mangroves grow in the sea–land confluence zone of tropical and subtropical regions. According to their hydrogeomorphological drivers, conserving, managing, and restoring the mosaic of mangrove ecotypes improves ecosystem services, including mitigation and adaptation to climate change. These results indicate that mangroves in karstic environments can have critical roles in confronting climate change, considering water and sediment flows are the basis of sediment accumulation. The differences are given by tree density, but salinity, as a proxy variable of the freshwater influence, significantly influences the sedimentation rate. However, the sedimentation is high in fringe mangroves at the front of the lagoon and diminishes inland where peten mangroves exist. The structural, physicochemical, and sediment variables of the sites by mangrove ecotype show that dwarf mangroves represent a distinct group from those formed by fringe, basin, and peten mangroves. If the extension of each mangrove ecotype is considered, dwarf mangroves have the highest annual sediment accumulation (1,465 t year −1 in 14,706 ha). The highest sedimentation rate was recorded in the rainy season (0.24 ± 0.08 kg m −2 month −1), while spatially, the highest value was registered in the outer zone (0.44 ± 0.09 kg m −2 month −1).
Fringe mangroves are exposed to low hydrodynamism and show the highest sedimentation rate (3.37 ± 0.49 kg m −2 year −1) compared to basin (1.68 ± 0.22 kg m −2 year −1), dwarf (1.27 ± 0.27 kg m −2 year −1), and “peten” (0.52 ± 0.12 kg m −2 year −1) mangroves. We registered the structural variables of the forest, interstitial water physicochemical characteristics, and sediment variables that could influence the net sediment deposition. The measurements considering mangrove ecotypes and their spatial variability concerning the lagoon's salinity gradient (inner, middle, and outer lagoon zones) in three climate seasons (dry, rain, and “nortes”) were realized.
#Type fu similar drivers#
These drivers regulate the distribution of different mangrove ecotypes and their ecosystem services, so the net sediment accumulation rates in different mangrove ecotypes in Celestun Lagoon, a karstic zone in the NW Yucatan Peninsula, SE Mexico, were estimated. Mangrove vegetation is strongly dependent on the climate, the physicochemical variables of the sediment, and the hydrological dynamics. 3Department of Biodiversity Conservation and Ecological Restoration, Instituto Pirenaico de Ecología-CSIC, Zaragoza, Spain.2National Coastal Resilience Laboratory (LANRESC), National Laboratories CONACYT, Sisal, Mexico.
1Department of Marine Resources, Centre for Research and Advanced Studies of the National Polytechnic Institute (CINVESTAV-Merida Unit), Yucatan, Mexico.Siuling Cinco-Castro 1 *, Jorge Herrera-Silveira 1,2 and Francisco Comín 3
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