Coastal wetlands mainly include ecosystems of mangroves, coral reefs, salt marsh, and sea grass beds. As the buffer zone between land and sea, they are frequently threatened from both sides. The world coastal wetland lost more than 50% of its area in the 20th century, largely before their great value, such as wave attenuation, erosion control, biodiversity support, and carbon sequestration, was fully recognized. World wetland loss and degradation was accelerated in the last three decades, caused by both anthropogenic and natural factors, such as land reclamation, aquaculture, urbanization, harbor and navigation channel construction, decreased sediment input from the catchments, sea level rise, and erosion. Aquaculture is one of the key destinations of coastal wetland transformation. Profound consequences have been caused by coastal wetland loss, such as habitat loss for wild species, CO 2 and N 2 O emission from land reclamation and aquaculture, and flooding. Great efforts have been made to restore coastal wetlands, but challenges remain due to lack of knowledge about interactions between vegetation and morphological dynamics. Compromise among the different functionalities remains a challenge during restoration of coastal wetlands, especially when faced with highly profitable coastal land use. To solve the problem, multi-disciplinary efforts are needed from physio-chemical-biological monitoring to modelling, designing, and restoring practices with site-specific knowledge.
Selection for plant traits important for agriculture can come at a high cost to plant defenses. While selecting for increased growth rate and yield, domestication and subsequent breeding may lead to weakened defenses and greater susceptibility of plants to herbivores. We tested whether expression of defense genes differed among maize, Zea mays ssp. mays L. (Poaceae), and its wild relatives Zea mays ssp. parviglumis Iltis & Doebley and Zea diploperennis Iltis et al. We used two populations of Z. mays ssp. parviglumis: one expected to express high levels of an herbivore resistance gene, wound‐inducible protein (wip1), and another expected to have low expression of wip1. To test whether maize and wild Zea differed in induction of defenses against Spodoptera frugiperda (Smith) (Lepidoptera: Noctuidae), we quantified expression of several genes involved in plant defense: wip1, maize protease inhibitor (mpi), pathogenesis‐related protein (PR‐1), and chitinase. Moreover, we compared growth, development, and survival of caterpillars on maize and wild Zea plants. We found that maize expressed low levels of all but one of the genes when attacked by caterpillars, whereas the wild relatives of maize expressed induced defense genes at high levels. Expression of wip1, in particular, was much greater in the Z. mays ssp. parviglumis population that we expected to naturally express high levels of wip1, with expression levels 29‐fold higher than in herbivore‐free plants. Elevated expression of defenses in wild plants was correlated with higher resistance to caterpillars. Larvae were 15–20% smaller on wild Zea compared with maize, developed 20% slower, and only 22% of them survived to pupation on Z. mays ssp. parviglumis with high levels of wip1. Our results suggest that domestication has inadvertently reduced the resistance of maize, and it is likely that expression of wip1 and other genes associated with defenses play an important role in this reduction in resistance.
We experimentally increased salinities in a tidal freshwater marsh on the Altamaha River (Georgia, USA) by exposing the organic rich soils to 3.5 yr of continuous (press) and episodic (pulse) treatments with dilute seawater to simulate the effects of climate change such as sea level rise (press) and drought (pulse). We quantified changes in root production and decomposition, soil elevation, and soil C stocks in replicated (n = 6) 2.5 × 2.5 m field plots. Elevated salinity had no effect on root decomposition, but it caused a significant reduction in root production and belowground biomass that is needed to build and maintain soil elevation capital. The lack of carbon inputs from root production resulted in reduced belowground biomass of 1631 AE 308 vs. 2964 AE 204 g/m 2 in control plots and an overall 2.8 AE 0.9 cm decline in soil surface elevation in the press plots in the first 3.5 yr, whereas the control (no brackish water additions) and the fresh (river water only) treatments gained 1.2 AE 0.4 and 1.7 AE 0.3 cm, respectively, in a 3.5-yr period. There was no change in elevation of pulse plots after 3.5 yr. Based on measurements of bulk density and soil C, the decline of 2.8 cm of surface elevation resulted in a loss of 0.77 AE 0.5 kg C/m 2 in press plots. In contrast, the control and the fresh treatment plots gained 0.25 AE 0.04 and 0.36 AE 0.03 kg C/m 2 , respectively, which represents a net change in C storage of more than 1 kg C/m 2. We conclude that, when continuously exposed to saltwater intrusion, the tidal freshwater marsh's net primary productivity, especially root production, and not decomposition, are the main drivers of soil organic matter (SOM) accumulation. Reduced productivity leads to loss of soil elevation and soil C, which has important implications for tidal freshwater marsh persistence in the face of rising sea level.
Trees provide numerous benefits for urban residents, including reduced energy usage, improved air quality, stormwater management, carbon sequestration, and increased property values. Quantifying these benefits can help justify the costs of planting trees. In this paper, we use i-Tree Streets to quantify the benefits of street trees planted by nonprofits in three U.S. cities (Detroit, Michigan; Indianapolis, Indiana, and Philadelphia, Pennsylvania) from 2009 to 2011. We also use both measured and modeled survival and growth rates to "grow" the tree populations 5 and 10 years into the future to project the future benefits of the trees under different survival and growth scenarios. The 4059 re-inventoried trees (2864 of which are living) currently provide almost $40,000 (USD) in estimated annual benefits ($9-$20/tree depending on the city), the majority (75%) of which are increased property values. The trees can be expected to provide increasing annual benefits during the 10 years after planting if the annual survival rate is higher than the 93% annual survival measured during the establishment period. However, our projections show that with continued 93% or lower annual survival, the increase in annual benefits from tree growth will not be able to make up for the loss of benefits as trees die. This means that estimated total annual benefits from a cohort of planted trees will decrease between the 5-year projection and the 10-year projection. The results of this study indicate that without early intervention to ensure survival of planted street trees, tree mortality may be significantly undercutting the ability of tree-planting programs to provide benefits to neighborhood residents.
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