Ocean–atmosphere climatic interactions, such as those resulting from El Niño Southern Oscillation (ENSO) are known to influence sea level, sea surface temperature, air temperature, and rainfall in the western Pacific region, through to the north-west Australian Ningaloo coast. Mangroves are ecologically important refuges for biodiversity and a rich store of blue carbon. Locations such as the study site (Mangrove Bay, a World Heritage Site within Ningaloo Marine Park and Cape Range National Park) are at the aridity range-limit which means trees are small in stature, forests small in area, and are potentially susceptible to climate variability such as ENSO that brings lower sea level and higher temperature. Here we explore the relationship between mangrove dieback, and canopy condition with climatic variables and the Southern Oscillation Index (SOI)—a measure of ENSO intensity, through remote sensing classification of Landsat satellite missions across a 29 year period at a north-west Australian site. We find that the SOI, and seasonal mean minimum temperature are strongly correlated to mangrove green canopy (as indicator of live canopy) area. This understanding of climate variations and mangrove temporal heterogeneity (patterns of abundance and condition) highlights the sensitivity and dynamics of this mangrove forest and recommends further research in other arid and semi-arid tropical regions at mangrove range-limits to ascertain the extent of this relationship.
The global climate system controls ocean and atmosphere interactions, influencing sea surface temperature (SST), air temperature, rainfall, and wind1. Such climatic variables have been reported as drivers of mangrove variability at local and regional scales2. Most notably, temperature, salinity and precipitation have been consistently reported as constraining abiotic variables in mangrove forest condition, and distribution3, and when altered have resulted in tree mortality4, change in species composition, and loss or reduction in function (e.g., ability to store carbon)5.
Mangroves in arid ecoregions are often characterised by trees that are small in stature and limited in areal cover, yet they are ecologically important refuges for biodiversity in the region3, important blue carbon sinks5, and act as a buffer for coastal protection6. Avicennia spp. covers the largest range, exhibiting a broad tolerance to such abiotic conditions. Whilst salt-tolerant, mangroves are susceptible to high salinity and as such are vulnerable to the effects of climatic changes, including the frequency and intensity of drought events7,8. However, extreme conditions can result in physiological thresholds being reached or exceeded, thereby impacting metabolic processes9 and causing physiological stress or mortality, as has been observed during extreme drought events, or post hydrological enforcements (e.g., tide barriers)10.
Coupled ocean–atmosphere phenomena, such as the El Niño Southern Oscillation (ENSO) influence sea level, SST, air temperature, and rainfall in the western Pacific region, with effects noted at various regions across the globe11. In north-west Australia, the Ningaloo coast experiences known fluctuations in sea level, and SST. The weakening of the equatorial trade winds during El Niño events results in the shoaling of the thermocline in the western Pacific, and in turn lower sea levels caused by cooler waters on the west Australian coastline12,13. The reverse occurs during La Niña events. Therefore, during an El Niño event the mangroves of north-western Australia are subjected to lower sea levels14. The minimal freshwater input in these semi-arid environments means they are potentially subjected to higher saline conditions in the upper tidal and edge locations, which can lead to loss of mangrove canopy and mortality. For example, Drexler and Ewel15 reported that during the 1997/98 El Niño, salinity in a Micronesian mangrove forest increased, while rainfall decreased and the water table lowered, limiting freshwater in the forest and resulting in a decline in mangrove growth rate15. Furthermore, the largest mangrove mortality observed occurred in remote northern Australia and coincided with the 2015/16 El Niño4,7,16. This large-scale dieback event has been linked to lower water levels and high salinity4,7,16, resulting in changes to the geochemical composition of the trees and sediment pre and post the mortality7.
Mangroves provide critical habitat, coastal protection, and store vast amounts of atmospheric carbon. The frequency, and duration of El Niño events is expected to intensify with increased global temperatures17. Variations in climatic events, and in turn the variables they influence, such as sea level, and temperature, have repercussions for the marine environment. ENSO events have shown to influence juvenile fish recruitment, and whale shark aggregation on the Ningaloo coast (north-west Australian coastline)18. At Mangrove Bay, within Ningaloo Marine Park and Cape Range National Park, two known mangrove dieback events coincided with El Niño events, and associated lower sea levels, that resulted in higher soil salinity5,19. Understanding how variation in climate and environment influences the temporal heterogeneity (patterns of abundance and condition) of mangrove forests remains an ongoing priority, especially in a semi-arid climatic zone that is at the upper mangrove abiotic thresholds (e.g., temperature and salinity).
Remotely sensed spatiotemporal datasets enable large amounts of data to be interrogated at local (site) to global scales20. In particular, Landsat imagery provides a regular, consistent and recent history of mangrove change that can be used to compare with environmental data over time. The distinct spectral signature of mangroves means remotely sensed data can enable their extent and some of their structural and physiological properties to be mapped17,18,22. Previous studies have tended to focus on specific locations within the mangrove canopy and not across the entire mangrove area, or on a singular event, and not across a significant time-period covering both impact and recovery of mangrove canopy alongside multiple ENSO phases, we aim to do this here. The objective of this study is to investigate the relationship between mangrove canopy extent, with climatic variables (air temperature, precipitation) and the Southern Oscillation Index (SOI). We also explore the Normalised Difference Vegetation Index (NDVI) as a proxy to determine the spatial variation in the canopy condition through the study period. The SOI provides an indication of the intensity of ENSO conditions23 by measuring the strength of the Walker Circulation23, which refers to the wind circulation in same tropical region (Julian and Chervin 1978).
To examine the relationship between mangroves in north-west Australia, climatic variables and the SOI we first determine mangrove canopy area for each time-point across the observed period (1987 to 2016) through classifying green mangrove canopy from the spectral properties in the Landsat image series for Mangrove Bay (Fig. 1) using a supervised classification method. Mangrove Bay was specifically chosen as it represents a marginal environment where environmental gradients limiting mangrove growth are expressed in a small accessible geographic area. We use Generalised Additive Mixed Models (GAMMs) to ascertain the relationship between climatic variables and the SOI, with mangrove canopy area. We then explore the spatial heterogeneity of the canopy using the NDVI as a proxy to determine the spatial variation in canopy condition as observed across the time-period, as a means to illustrate where change in condition has occurred within the canopy. NDVI is related to condition in mangroves, with higher values indicating healthy, dense forests24.
Mangrove Bay is located in a semi-arid environment in the Pilbara region of NW Australia within Ningaloo Marine Park and Cape Range National Park (Fig. 1). It is dominated by Avicennia marina, though a range of other species make minor contributions to the canopy. The region can experience rapid heavy rainfall due to tropical cyclones occurring December–April, though a higher incidence of rainy days generally occurs in the winter months. Mean annual temperature ranges from 18 to 32 °C, with higher temperatures averaging 37 °C December-February. Despite its small size, Mangrove Bay is of high ecological importance due to its role in supporting biodiversity in the region as one of the southernmost mangrove stands in Western Australia (Cassata and Collins 2008; Reef et al. 2014), and an important ecotone near the tropical and temperate marine transition zone.
The mangrove canopy area derived from supervised classification of the Landsat image series (5TM, 7 ETM, 8OLI) from 213 time-points (months) varied temporally (Fig. 2). The classification was based on green canopy and represents the live (as represented by green leaves) mangrove canopy area from spectral properties. Mean annual canopy area identified illustrated an oscillating pattern (Fig. 2) across the years, which correlated with the SOI (Fig. 2). Temperature and precipitation varied across the years and were also correlated with canopy area (SI1).
Mangroves, climatic variables and the SOI
The GAMMs analysis showed that the SOI intensity, and mean minimum temperature were strongly correlated to variation in green mangrove canopy area across the 29 years when analysed seasonally (AICc = 326.69, r2(adj) = 0.508, t = 37.09, n = 58; SOI: F = 27.09, P = 0.0001; Mean Minimum Temperature: F = 36.95, P = 0.0001) (Table 1 and SI6). SOI displayed a positive linear association with the canopy area, indicating that increases in green canopy cover occurred when conditions were not likely to be representative of El Niño events (Fig. 3). Whilst seasonal mean minimum temperature displayed a negative linear association with canopy, indicating the increases in green canopy occurred when seasonal mean minimum temperature was lower (Fig. 3).
The mean temporal NDVI and its standard deviation was calculated for all pixels that were classified as mangrove from the above mangrove spectral classification. Spatial trends were apparent across the site (Fig. 4), with the edges of the core mangrove canopy area, particularly at the northern end of the region, exhibiting high variation in standard deviation of mean NDVI (Fig. 4), and lower mean NDVI. This area coincides with dead mangrove trees and subsequent new mangrove growth apparent in Fig. 4 and representative of the changes in green canopy area depicted in the spectral supervised classification (Fig. 2).
Climate change has heightened the need for increasing our understanding of how ocean-climate interactions influence the environmental variables and associated ecosystems. In addressing this issue our study focussed on the SOI, and variation in air temperature and precipitation. The SOI is known to influence factors that impose environmental constraints on mangroves in the NW region of Australia including sea level, and temperature, indicators we found to strongly correlate with mangrove canopy area across the study period. We were able to demonstrate the effect of SOI and high temperature on mangrove canopy at Mangrove Bay through analysis of twenty-nine years of near continuous Landsat data and provide a mechanism to further explore mangrove change relationships to climatic patterns. We found that during this study period mangrove canopy area at this NW Australian site exhibited a decreasing trend during periods of negative SOI, which are indicative of El Niño conditions.
The periods of negative SOI (El Niño conditions) coincide with low sea level, and low precipitation along the west Australian coast14. Previous studies have reported that high salinity, and low freshwater inputs from rainfall25, groundwater or river flows can lead to mangrove dieback, particularly in areas of restricted tidal flows26, or droughts7,10. With decreased inundation in arid conditions mangrove trees have been documented to progressively lose leaves with eventual death due to a diminished capacity for water uptake and salt exclusion10. El Niño conditions on the northern and west Australian coast appear to amplify this, with high levels of salinity associated with low sea level at this World Heritage Area site during two El Niño events19, and large-scale dieback also occurring at the Gulf of Carpentaria in northern Australia during the 2015–2016 El Niño event with low sea level, low rainfall, and high temperatures also recorded7,16,27. Both the Mangrove Bay and Gulf of Carpentaria sites occur within the northern Australia tropical region and have climate and other habitats influenced by ENSO (e.g., sea-surface temperature, coral bleaching). Whilst previous research is limited5,16,19 these dieback events suggest these areas have similar susceptibility to ENSO changes and in turn similar ecological responses were observed. Further research of stressors is required to ascertain if this response is apparent in other mangrove patches in this region.
Spatial differences in mangrove condition were illustrated by areas of high variance in canopy condition determined from NDVI. These areas were dynamic and illustrated tree death, and subsequent new growth as an oscillating pattern throughout the long-term study period (Fig. 2) and reflected earlier findings by Lovelock et al.19 at this site during two El Niño events that occurred during the time span of this study. Mangrove forest fragmentation has been associated with mangrove deforestation and loss of function, including changes in species composition28, the temporal NDVI spatial clustering metrics indicate that there are changes to the canopy that should be monitored further. The relationship with ENSO and the oscillating pattern in canopy area and condition displayed through our dataset shows that mangroves are sensitive to climate extremes though are able to recover during benign climatic periods, and in SOI phases indicative of La Niña conditions when sea level is higher in this region. The most spatially dynamic area of mangrove decline was found at the landward edge of the mangrove region, away from the creek entrance and lagoon. This area of the mangrove canopy has been shown to contain shorter trees compared to those close to the seaward side (Hickey et al. 2018), suggesting that this northern edge may be at the upper thresholds for optimal growth conditions in the area and therefore may be most sensitive to changes in environmental variables, such as a decline in sea level (associated with El Nino)14 and increase in air temperature as we report here.
Changes in environmental conditions due to SOI are common to many regions of the world, with conditions in marine and terrestrial systems affected, including rainfall and drought conditions (Harris et al. 2018), sea surface temperature and coral bleaching29. However, this relationship in mangrove environments has only recently begun to be explored. Limited studies tend to focus on small locations within the mangrove canopy and not across the entire mangrove area, or on a singular event and not across a significant time-period covering both impact and recovery of mangrove canopy alongside multiple ENSO phases, as we do here. This study shows that the benign climatic phases are essential for recovery to occur. However, anthropogenic climate change has been shown to affect environmental variables such as increased temperature and change in rainfall patterns30. Such variations in temperature, or rainfall may alter the conditions during the benign climatic phase, potentially limiting the recovery opportunity for mangroves. This may further increase the vulnerability of these arid and semi-arid mangroves already near physiological thresholds, during sustained negative SOI impact events (that is El Niño conditions), such as increasing the area of mortality and decline in canopy condition16, or species composition28. The importance of SOI associated reductions in sea level and increased temperature warrants a larger investigation of the fate of mangroves in Australia, especially with predicted changes in aridity31 within tropical and subtropical regions, and the intensification of the effects of ENSO in the tropical Pacific and eastern Indian Ocean regions12,13,32.
Ecosystem structure, function, and species distribution are greatly influenced by climate extremes33. Further analysis of ecosystem-scale threshold responses elsewhere would build on the findings of this study and may provide information on the duration and level of variation in sea level and temperature increase required before canopy loss or dieback occurs, whilst also providing insight into recovery time, and areas of the mangrove stand that are most vulnerable. Undertaking such studies enables for enhanced anticipation of the response of mangroves to changes in climate, including the frequency and intensity of climate extremes34.
This study has shown that the SOI is strongly correlated to mangrove changes at Mangrove Bay, a site located within the World Heritage Area of Ningaloo Marine Park. This site, while relatively small, is representative of mangrove sites in arid and semi-arid regions. The NW Australian coastline, like other arid locations has mangrove trees that are small in stature and forests with limited extent, though they function as important habitats for fish and prawns, as well as other marine fauna in these regions. The long temporal record at Mangrove Bay has illustrated that ENSO conditions affect mangrove canopy area and ‘greenness’, which has been detected using free Landsat imagery, alongside climate variables. This method could be applied to other arid and semi-arid mangroves, or those mangrove stands located within tropical regions affected by ENSO conditions to further establish the relationship between mangroves condition and ENSO. This information may be used in management, to establish monitoring sites, and to minimise hydrologic constraints from anthropogenic activities during periods when sea level is lower due to ENSO and when mangroves may be experiencing reduced tidal connectivity and freshwater inundation.
Cloud-free Landsat 5, 7 TM and 8 OLI imagery (path 115, row 75) were acquired for all available months from 1987 to 2016 (n = 213) where there was no cloud, striping, atmospheric interference (SI8). Corrections were performed to convert the pixels (30 × 30 m) to top of atmosphere reflectance with the bands utilised (corrected for sun angle)31,32,37. A combination of unsupervised and supervised classification within ERDAS Imagine was used to categorise the mangrove canopy within the site (SI2). This was done separately for Landsat 8 OLI to account for the difference in band wavelengths (SI3). The site was classified into 7 classes and accuracy assessment was undertaken for 11 reference dates where high resolution orthorectified aerial imagery was available (SI5). Orthorectified aerial imagery was subdivided into 30 m grid cells that corresponded with Landsat scene pixels. Each cell was assigned to a class (SI5). Identification of cell as mangrove canopy, required dense mangrove surface area, or at least 80% surface coverage (SI5). This study presents the mangrove canopy classification which yielded the strongest accuracy assessment of the classes (SI5). Assessment in the form of kappa coefficients was used to assess the level of agreement for all reference dates (SI5)38. For each scene, pixels identified as mangrove comprised the mangrove canopy area.
Mangroves, climatic variables and the SOI
Temperature and SOI variables were accessed from the Bureau of Meteorology (BOM) (http://www.bom.gov.au/climate/averages/tables/cw_005007.shtml). Temperature observations were recorded at Learmonth station (Latitude: − 22.24 Longitude: 114.10; Height of station above mean sea level (metres: 5) and seasonal statistics were generated from monthly values (mean minimum, mean maximum, lowest maximum, highest minimum). Seasonal mean SOI was generated from BOM data (http://www.bom.gov.au/climate/enso/soi/). A GAMM analysis was utilised within the R statistical package v.3.4.1, accessing the mgcv and MuMIn libraries to ascertain the relationship between air temperature derivatives (SI1), precipitation and the SOI, with mangrove canopy area. A GAMM analysis was utilised as it can fit both linear and non-linear responses in mixed effect models. Variables were checked for collinearity and were not highly correlated (correlation coefficients < 0.7). Overdispersion of data was checked a priori and normality of residuals in posthoc and neither showed significant deviation. All possible combinations of predictors were considered. The Gaussian model was applied to the data analysis. GAMM provided a flexible robust method to analyse the independent effects of environmental variables whilst also accounting for the temporal aspect. They allow for complex responses due to utilising non-parametric smoothing functions39. Time was treated as a random variable to account for potential temporal autocorrelation. The time variables used was year & season. The model with the fewest variables and within 2 AICc (Akaike Information Criterion corrected for finite samples) of the lowest AICc for all possible models was determined to be the best model40. A backward stepwise model was utilised for GAMM analysis. Relative importance of each environmental variable was calculated for each variable by summing the model weighted AICc values for all model combinations (maximum 4 variables) for each model where the variable was included41 (Table 1; SI6). Analysis was conducted using the R language packages mgcv and MuMIn using the function ‘importance’.
The mangrove boundary was determined as any pixel that was classified as mangrove from the spectral classification. Clear misclassified pixels (e.g., in water) were removed (5 pixels). The NVDI was calculated for each Landsat scene (SI7) for this mangrove boundary. NDVI is strongly correlated to canopy closure in mangroves (r2 = 0.91)24 and is often used as a proxy for measuring mangrove canopy condition, or ‘greenness’5,19,35,36,37,45, including in arid mangrove stands5,19,46. This is as it measures the absorbance of chlorophyll in the red band and the reflection of the mesophyll in the near-infrared band47. Values range from − 1 to + 1, where green vegetation corresponds to values above zero, and dense closed canopies are closer to 144. The temporal mean NDVI for each pixel was used to provide a spatial indication of mangrove canopy condition and identify clusters of high and low variances (standard deviation) in temporal mean NDVI to investigate any spatial patterns of variance.
McPhaden, M. J. & Busalacchi, A. J. The tropical ocean-global atmosphere observing system: A Decade of progress research. Oceans. https://doi.org/10.1029/97JC02906 (1998).
Osland, M. J. et al. Climatic controls on the global distribution, abundance, and species richness of mangrove forests. Ecol. Monogr. 87(2), 341–359 (2017).
Adame, M. F. et al. Mangroves in arid regions: Ecology, threats, and opportunities. Estuar. Coast. Shelf Sci. 1, 106796 (2020).
Asbridge, E. F. et al. Assessing the distribution and drivers of mangrove dieback in Kakadu National Park, Northern Australia. Estuar. Coast. Shelf Sci. 228, 106353 (2019).
Lovelock, C. E. et al. Assessing the risk of carbon dioxide emissions from blue carbon ecosystems. Front. Ecol. Environ. 15(5), 257–265 (2017).
Spalding, M. D. et al. The role of ecosystems in coastal protection: adapting to climate change and coastal hazards. Ocean. Coast. Manag. 90, 50–57 (2014).
Sippo, J. Z., Lovelock, C. E., Santos, I. R., Sanders, C. J. & Maher, D. T. Mangrove mortality in a changing climate: An overview. Estuar. Coast. Shelf Sci. 215, 241–249 (2018).
Mafi-Gholami, D., Zenner, E. K., & Jaafari, A. Mangrove regional feedback to sea level rise and drought intensity at the end of the 21st century. Ecol. Indic. 110, 105972 (2020).
Jump, A. S., & Penuelas J. Running to stand still: adaptation and the response of plants to rapid climate change. Ecol. Lett. 8(9), 1010–1020 (2005).
Jimenez, J. A., Lugo, A. E. & Cintron, G. Tree mortality in mangrove forests. Biotropica 17, 177–185 (1985).
Xie, S.-P. et al. Indo-western pacific ocean capacitor and coherent climate anomalies in post-ENSO summer: A review. Adv. Atmos. Sci. 33(4), 411–432 (2016).
Hamlington, B. D. et al. An ongoing shift in Pacific Ocean sea level. J. Geophys/ Res. Oceans 121, 5084–5097 (2016).
Merrifield, M. A., Thompson, P. R. & Lander, M. Multidecadal sea level anomalies and trends in the western tropical Pacific. Geophys. Res. Lett. 39, 2–6 (2012).
Godfrey, J. S. & Ridgway, K. R. The large-scale environment of the poleward-flowing Leeuwin Current, Western Australia: Longshore steric height gradients, wind stresses and geostrophic flow. J. Phys. Oceanogr. 15, 481–495 (1985).
Drexler, J. Z. & Ewel, K. C. Wetland complex linked references are available on JSTOR for this article: Effect of the 1997–1998 ENSO-related drought on hydrology and salinity in a Micronesian wetland complex. Estuaries 24, 347–356 (2001).
Duke, N. C. et al. Large-scale dieback of mangroves in Australia’s Gulf of Carpentaria: A severe ecosystem response, coincidental with an unusually extreme weather event. Mar. Freshw. Res. 68(10), 1816–1829 (2017).
Cai, W. et al. More extreme swings of the South Pacific convergence zone due to greenhouse warming. Nature 488, 365–369 (2012).
Wilson, S. G., Taylor, J. G., & Pearce, A. F. The Seasonal Aggregation of Whale Sharks at Ningaloo Reef, Western Australia: Currents, Migrations and the El Niño/Southern Oscillation. Environmental Biology of Fishes. https://idp.springer.com/authorize/casa?redirect_uri=https://link.springer.com/article/10.1023/A:1011069914753&casa_token=55v4NHJmcDcAAAAA:owpASeBazqNzQzH7Z9xJI0BOtHzNZMvjTiJHRjLGIFCWzhyiWwMvYJUU8cloH46JDWCSZ7XOhu_CZuzZ0w. (2001).
Lovelock, C. E., Feller, I. C., Reef, R., Hickey, S. & Ball, M. C. Mangrove dieback during fluctuating sea levels. Sci. Rep. 1, 1–8 (2017).
Giri, C. Observation and monitoring of mangrove forests using remote sensing: Opportunities and challenges. Remot. Sens. 8, 783 (2016).
Fatoyinbo, T. E., Simard, M., Washington-Allen, R. A. & Shugart, H. H. Landscape-scale extent, height, biomass, and carbon estimation of Mozambique’s mangrove, forests with Landsat ETM+ and Shuttle Radar Topography Mission elevation data. J. Geophys. Res. Biogeosci. 113, 1–13 (2008).
Rodriguez, W., Feller, I. C. & Cavanaugh, K. C. Spatio-temporal changes of a mangrove saltmarsh ecotone in the northeastern coast of Florida, USA. Glob. Ecol. Conserv. 7, 245–261 (2016).
Bureau of Meteorology. Record-Breaking La Niña Events. Australian Government. http://www.bom.gov.au/climate/enso/history/La-Nina-2010-12.pdf (2012).
Jensen, J. R. et al. The measurement of mangrove characteristics in southwest Florida using spot multispectral data. Geocarto Int. 6, 13–21 (1991).
Eslami-Andargoli, L., Dale, P., Sipe, N. & Chaseling, J. Mangrove expansion and rainfall patterns in Moreton Bay, Southeast Queensland, Australia. Estuar. Coast. Shelf Sci. 85, 292–298 (2009).
Hicks, W., Fitzpatrick, R. W., & Bowman, G. (2003) Managing coastal acid sulfate soils: the East Trinity example. in Advances in regolith: Proceedings of the CRC LEME regional regolith symposia. CRC LEME, Bentley 174–177.
Harris, N. L. et al. Using spatial statistics to identify emerging hot spots of forest loss. Environ. Res. Lett. 12, 024012 (2017).
Bryan-Brown, D. N. et al. Global trends in mangrove forest fragmentation. Sci. Rep. 10(1), 7117 (2020).
Hughes, T. P. et al. Spatial and temporal patterns of mass bleaching of corals in the anthropocene. Science 359(6371), 80–83 (2018).
Wang, H. J., Zhang, R. H., Cole, J. & Chavez, F. El Niño and the related phenomenon southern oscillation (ENSO): The largest signal in interannual climate variation. Proc. Natl. Acad. Sci. USA. 96(20), 11071–11072 (1999).
Berg, A. et al. Land-atmosphere feedbacks amplify aridity increase over land under global warming. Nat. Clim. Chang. 6, 869–874 (2016).
Perry, S. J., McGregor, S., Gupta, A. S. & England, M. H. Future changes to El Niño-southern oscillation temperature and precipitation teleconnections. Geophys. Res. Lett. 44(20), 10608–10616 (2017).
Osland, M. J. et al. Beyond just sea-level rise: Considering macroclimatic drivers within coastal wetland vulnerability assessments to climate change. Glob. Change Biol. 22, 1–11 (2016).
Jentsch, A. & Beierkuhnlein, C. Research frontiers in climate change: Effects of extreme meteorological events on ecosystems. C.R. Geosci. 340, 621–628 (2008).
Chander, G., Markham, B. L. & Helder, D. L. Summary of current radiometric calibration coefficients for Landsat MSS, TM, ETM+, and EO-1 ALI sensors. Remote Sens. Environ. 113, 893–903 (2009).
Landsat 7 (L7) Data Users Handbook. USGS. https://prd-wret.s3.us-west-2.amazonaws.com/assets/palladium/production/atoms/files/LSDS-1927_L7_Data_Users_Handbook-v2.pdf. (2009).
Landsat 8 (L8) Data Users Handbook. USGS. https://prd-wret.s3.us-west-2.amazonaws.com/assets/palladium/production/atoms/files/LSDS-1574_L8_Data_Users_Handbook-v5.0.pdf. (2009).
Story, M. & Congalton, R. G. Accuracy assessment: A user’s perspective. Photogramm. Eng. Remote. Sens. 52, 397–399 (1986).
Moore, C. et al. Improving essential fish habitat designation to support sustainable ecosystem-based fisheries management. Mar. Policy 69, 32–41 (2016).
Burnham, K. P., & Anderson, R. A practical information-theoretic approach. in Model Selection and Multimodel Inference 2. http://sutlib2.sut.ac.th/sut_contents/H79182.pdf.
Burnham, K. P., & Anderson, D. R. Practical use of the information-theoretic approach. in Model Selection and Inference: A Practical Information-Theoretic Approach (eds. Burnham K. P. & Anderson D. R.) 75–117 (New York, NY, Springer, 1998).
Cornforth, W. A., Fatoyinbo, T. E., Freemantle, T. P. & Pettorelli, N. Advanced land observing satellite phased array type L-Band SAR (ALOS PALSAR) to inform the conservation of mangroves: Sundarbans as a case study. Remot. Sens. 5, 224–237 (2013).
Giri, C., Pengra, B., Zhu, Z., Singh, A. & Tieszen, L. L. Monitoring mangrove forest dynamics of the Sundarbans in Bangladesh and India using multi-temporal satellite data from 1973 to 2000. Estuar. Coast. Shelf Sci. 73, 91–100 (2007).
Long, J., Giri, C., Primavera, J. & Trivedi, M. Damage and recovery assessment of the Philippines ’ mangroves following Super Typhoon Haiyan. MPB 109, 734–743 (2016).
Satyanarayana, B., Mohamad, K. A., Idris, I. F., Husain, M.-L. & Dahdouh-Guebas, F. Assessment of mangrove vegetation based on remote sensing and ground-truth measurements at Tumpat, Kelantan Delta, East Coast of Peninsular Malaysia. Int. J. Remot. Sens. 32, 1635–1650 (2011).
Almahasheer, H., Aljowair, A., Duarte, C. M. & Irigoien, X. Decadal stability of red sea mangroves. Estuar. Coast. Shelf Sci. 169, 164–172 (2016).
Pettorelli, N. et al. Using the satellite-derived NDVI to assess ecological responses to environmental change. Trends Ecol. Evol. 20, 503–510 (2005).
BR and SH undertook the research as part of the ICoAST collaborative project and acknowledge support from the Indian Ocean Marine Institute Research Centre collaborative research fund and partner organisations AIMS, CSIRO, DPIRD and UWA.
The authors declare no competing interests.
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Hickey, S.M., Radford, B., Callow, J.N. et al. ENSO feedback drives variations in dieback at a marginal mangrove site. Sci Rep 11, 8130 (2021). https://doi.org/10.1038/s41598-021-87341-5