The time taken for forested tropical ecosystems to re-establish post-disturbance is of widespread interest. Yet to date there has been no comparative study across tropical biomes to determine rates of forest re-growth, and how they vary through space and time. Here we present results from a meta-analysis of palaeoecological records that use fossil pollen as a proxy for vegetation change over the past 20,000 years. A total of 283 forest disturbance and recovery events, reported in 71 studies, are identified across four tropical regions. Results indicate that forests in Central America and Africa generally recover faster from past disturbances than those in South America and Asia, as do forests exposed to natural large infrequent disturbances compared with post-climatic and human impacts. Results also demonstrate that increasing frequency of disturbance events at a site through time elevates recovery rates, indicating a degree of resilience in forests exposed to recurrent past disturbance.
Tropical forests are recognized globally for the important ecosystem services that they provide. Knowledge of recovery rates and responses of tropical forest to past forms of disturbance may facilitate our understanding of the capacity of these ecosystems to respond to present and future events. Although it is generally accepted that if left long enough, tropical rainforest will recover1, there is much debate about the nature of forest re-growth and the time taken for it. Re-establishment of forest to approximate pre-disturbance levels, as reported predominantly from single-site2,3 and chronosequence studies4, typically requires 20–200 years, depending on the variable measured5,6,7. In tierra firme forests of the Amazon basin, for example, levels of species richness comparable to those found in mature forest are re-established in a quarter of the time taken for equivalent forest biomass4. However, these studies make no explicit reference to the history of disturbance in the described location, which could account for significant variation in rates of recovery between sites, even among those from similar abiotic and biotic settings. Through examining recovery rates from 283 past episodes of disturbance reported in palaeoecological records, we identified the factors that affected responses of tropical forest ecosystems to perturbation through time. We addressed two fundamental questions: first, how quickly has forest re-established after deforestation events in the past?, and, second, what factors—disturbance type, geographical location, frequency of disturbance events—affect recovery rates?
To determine trends in reforestation rates of tropical forests, we conducted a meta-analysis of 71 published fossil pollen records, which focused on four tropical regions: Asia, Africa, and Central and South America. After identifying studies through a literature search using Scopus ( www.scopus.com), exploring both key words, such as ‘tropical forest’ and ‘fossil pollen’, and key authors performing research in these regions, various selection criteria were applied. Data sets were included based on their location (within 23°N and 23°S), evidence of disturbance events (and associated recovery) over the past 20,000 years and good chronological control (14C dating); a lack of any of these criteria resulted in the exclusion of the study. From the selected 71 records, each resulting from a sediment core extracted from a specific geographical location, a data set of 283 disturbance events was compiled and analysed, with a quarter of records demonstrating five or more of these episodes. Disturbance events are defined as perturbations that result in a sharp loss of forest pollen in the palynological record and subsequent gain, and include both catastrophic disturbances, where relative forest pollen may decline by > 90% (FD, see Table 1), to smaller perturbations where declines of <10% may occur during a period of relative forest stability or longer-term recovery. Forest recovery is described as the maximum increase in the percentage of forest pollen in the displayed pollen sum after a decline, before a stabilizing point or further decline (Fmax, see Table 1). The focus of this meta-analysis is on the recovery rate (RR) of forest, as defined uniquely in each individual study (see Supplementary Data 1), representing the speed and extent to which this ecological unit re-grows relative to its pre-disturbance abundance (not always equivalent to an undisturbed state), with the assumption that vegetation re-establishment, as inferred through the proxy of fossil pollen, is indicative of sustained ecosystem functionality. The type of disturbance at each event was classified according to information on the published pollen diagrams and/or in the article text (Table 2). The main variables extracted for forest RR calculations are presented in Table 1.
This novel approach to analysing long-term trends in tropical forest re-establishment provides fundamental insights into the functioning and resilience of tropical forest ecosystems. Results demonstrate that forests in the Central American tropics respond more rapidly to disturbance than those in Asia, and that recovery after large infrequent events is more dynamic compared with re-growth post-climatic or anthropogenic impacts. In addition, it is the frequency of past disturbance events that appear to play the most significant role in determining the rate of reforestation in these tropical regions: the greater the rate of disturbance through time, the faster the recovery. These findings suggest that tropical forests, in response to an ecologically-relevant history of exposure to natural disturbances, are adapting to perturbation through time, evolving mechanisms that increase their resilience in the face of environmental change.
Rates of recovery
Results demonstrate that the majority of past disturbances were caused by forest clearing, followed by climatic changes and large infrequent events (n=166, n=87 and n=13, respectively). For the majority of disturbances, forest re-growth stopped before 100% recovery either due to the onset of another disturbance event or the establishment of a lower forest proportion in the landscape (approximated through fossil forest pollen percentages); nevertheless, median forest abundance after disturbance reached 95.5% of pre-disturbance levels (n=283). Across disturbance types, recovery rates varied greatly, with projected times to 95.5% forest recovery from the pre-disturbance baseline ranging from <10 to 6,846 years (n=283), while the estimated median time was 210 years (n=283) (Fig. 1) and average time 503 years (s.d.=768.16, n=283).
Recovery rate versus disturbance category
The response rates of tropical forest to natural versus anthropogenic disturbances were not significantly different, though the greatest range in RR across categories was between climatic and large infrequent disturbances (linear mixed-effects model, P value=0.072, n=283; Table 3) (Fig. 2a). RRs were fastest after large infrequent disturbances (LI) (median=2.84% relative reforestation per year, n=13) (see Table 2 for details of RR calculation), and notably slower after climatic changes (C) and human-induced disturbances (FC) (for both, medians=0.41% relative reforestation per year, n=87 and n=166, respectively).
Recovery rate versus geographical location
The broad geographical region in which the forests reside did significantly affect the RR (Figs 2b and 3). In general, forest ecosystems in the Central American tropics recovered significantly faster than those in Asia (linear mixed-effects model, P-value=0.027, n=283; Table 3), the latter of which recovered the slowest, with median times for 95.5% recovery of 141 years (n=111) and 415 years (n=58), respectively. In general, RRs were also significantly faster in African forests compared with those in South America and Asia (linear mixed-effects model, P-value=0.041 and 0.009, n=283, respectively; Table 3). However, latitude did not appear to have a significant effect on RR (linear mixed-effects model, P-value=0.111, n=283; Table 3), along with the longitudinal and altitudinal setting of the forest (both excluded from Model I (Eq. 1) when P-values>0.100 were demonstrated in initial regression analyses, n=283).
Frequency of past disturbance
The standardized rate of disturbance events, SRD, which was calculated by dividing the number of disturbances in a site by the approximate time over which they occurred, giving a rate per 1,000 years (Table 1) allows investigation of whether frequency of past disturbance contributes to the pattern of RR observed across these tropical forests. Of all covariates tested, the SRD displayed the most significant relationship with RR (linear mixed-effects model, P value<0.001, n=283; Table 3) (Fig. 2c), indicating that forests that had experienced a higher frequency of disturbance events in the past tended to recover more rapidly after each subsequent perturbation. Further analysis demonstrated that of the four different categories of disturbance recorded, large infrequent events occurred at the greatest rate (median=10.444 events per 1,000 years, n=13) and forest clearance at the lowest (median=1.072 events per 1,000 years, n=87) (Fig. 4a; Table 4). In terms of geographical location, forested sites in the African tropics experienced the least frequent disturbance in the past (median=0.578 events per 1,000 years, n=29) and Central American forests the most (median=1.278 events per 1,000 years, n=111) (Fig. 4b; Table 4). Although these patterns have emerged, none of the locations or disturbance categories proved significantly different to each other in their SRD (except for climatic disturbance and forest clearance; Table 4), suggesting, for example, that forests in Central America have not experienced considerably more disturbance events per millennium than the other tropical regions in the past. Greater and more consistent sample sizes across groups would help to clarify these differences.
Results from this meta-analysis show that tropical forests have been disturbed by a variety of factors over the Late Glacial and Holocene periods, and recovery has proceeded at varying rates. Our analyses indicate that for most tropical forest ecosystems, the length of time taken to re-establish forest to values c. 95% of former arboreal abundance takes >200 years. This finding is supported by palaeoecological studies independent of this analysis (lacking inclusion requirements), for example (ref. 8). Only after approximately 20% of disturbance events did forest recover within the 42 years reported as the average for complete recovery in tropical and boreal forests across the world9. Length of time is an important distinction to make because while there are a number of studies that suggest that any form of disturbed (often referred to as secondary) forest has less ecological value than primary forests10,11, few of these have examined forests that have been recovering for >200 years and therefore are unlikely to be comparing like-with-like but rather a forest ecosystem in the early stages of succession. This relatively extended period required for recovery is relevant to contemporary forestry management where periods allocated for forest re-growth post-logging are rarely ecologically suitable12 and practices are underpinned by inadequate and biased knowledge13. Incorporating a longer rotation period into forest management plans, to allow for enhanced regeneration, may improve forest productivity.
Significant differences in recovery rates suggest that certain factors will influence the speed of tropical forest restoration. The result that recovery is fastest following natural disturbances, such as hurricanes, is somewhat intuitive; these are processes that have been occurring throughout the earth’s history and considered to play an important role in ecosystem dynamics14. Despite being labelled as large infrequent disturbances, an ecological term that illustrates the greater intensity, duration and spatial extent of these perturbations compared with those that ‘typically’ affect an ecosystem15, it is also the type of perturbation that has occurred with the greatest frequency (SRD) in the past (Fig. 4a). This further supports one of the main conclusions of this study that these ecosystems recover most rapidly after exposure to natural disturbances, occurring at frequencies through time of ecological relevance, that is, events per thousands of years (see for example, the tens of years and novel forms of disturbance pervading many of these ecosystems today), which results in their greater ability to respond dynamically, manifest here in an increasing rate of recovery, and inferred resilience. Similar findings arose from a study investigating recovery rates in overexploited marine populations16; moderate levels of stock depletion over an extended period, that is, >50 years, led to the adaptation of populations to the historical fishing regime, enhancing recovery rates and thus promoting resilience. This result lends further support, from a disparate biome to the fundamental concept of ecological adaptation, whether through life-history changes16 or ecological sorting/habitat filtering17, over long-term time scales. For these tropical forest ecosystems, this result implies that designing anthropogenic forest disturbances that more closely mimic natural disturbance regimes will result in a lesser decline in the abundance of trees in the landscape and may markedly reduce the time required and resources needed for forest regeneration. The slow recovery rates recorded following human-induced burning are of particular concern, given that this is the favoured mode of conversion to agriculture in tropical forests; it is also sometimes adopted by conservation managers to enhance diversity through invoking a particular disturbance regime18.
The slower recovery rate apparent in Asia and South America compared with Central America and Africa may be attributable to current abiotic drivers, such as soil fertility4 and climate19, and biotic influences such as vegetation life histories determining functional group composition5, tree species diversity20 and age structure7; variables inherently linked to the regime of past disturbance events4,21. The species and functional diversity of these tropical forest communities, the initial state of the forest pre-disturbance and the relative severity of the disturbance events3, for example the resultant impact on seed availability and seedling vulnerability22, were not explicitly considered in this study (in the most part due to data limitations), though all may play a significant role in shaping the rates and patterns of recovery observed here23,24. Future work, investigating in more detail the impact of these abiotic and biotic components (via the development of a universal independent proxy in the case of disturbance magnitude), would extend understanding of the causal reasons underlying this study’s findings and provide further knowledge on the ecology of tropical forests, as well as information for application in ecosystem management and restoration. Nonetheless, despite the relatively coarse temporal and spatial scale of the analyses performed here, findings provide many valuable insights for the sustainable use of tropical forest resources, not least estimates of the time required for the reforestation of these pivotal ecosystems. For the development of successful ecosystem service markets, trading in, for example, carbon credits resulting from effective forest restoration, this information is sorely lacking and urgently required25.
In addition, this study has been able to test for the first time the hypothesis that increased past exposure to perturbation (in particular frequency of events per 1,000 years, Fig. 2c) leads to the evolution of adaptations that enable forested ecosystems across the tropics to respond more dynamically to future disturbance. As well as the abiotic and biotic factors mentioned previously, the faster rates of forest re-growth in Africa and Central America may result from more extensive histories of disturbance in those regions. Past perturbations relevant to the ecological context of this meta-analysis may include human disturbance resulting from large-scale forest-based ancient civilizations26,27,28 and extreme weather events, for example, droughts in Central Africa29 and hurricanes in Central America30.
This meta-analysis has demonstrated disturbance-recovery dynamics over long-term time scales, revealing increasing recovery rates with higher frequency of disturbance (Fig. 2c). Such a result runs counter to recent studies modelling ecosystem resilience to contemporary forms and intensities of disturbance, namely human induced over short time scales, which, to a great extent, are far from mimicking natural disturbance regimes13,31. For example, refs 32, 33 identify slowing recovery rates with increasing disturbance as a robust indicator of a loss of resilience in different systems. It is important that a distinction is drawn between the types of disturbance experienced in the past versus today, with the impacts of contemporary regimes, and forest responses, yet to be fully observed. Accounting for both hypotheses on resilience may require careful consideration of both the type of perturbation and the temporal and spatial context of the ecosystem, which determines its ecological memory and consequently the disturbance and recovery dynamics. For understanding resilience, this study has demonstrated how crucial it is to adopt a long-term view in analysis.
Various procedures were used to date the published diagrams. Where age-depth models were not present in the published study, the dating programme, clam34, in R35 (ref. 35), was used to construct the best-fitting age-depth model for the reported ages. Similarly, clam was used to calibrate dates reported in 14C radiocarbon years. Where data were not available in the reference for surface dates, a default of −55 Cal. yr BP, with error 1, was used, in line with conventional dating of modern samples36. In the absence of age uncertainties for a radiocarbon date, an average of the value for dates on either side was used, or in the case of basal samples, the youngest date reported. If no age uncertainties were reported, a default of 50 years was used, for example in ref. 37. IntCal09 and SHCal04 curves were used for Northern and Southern Hemisphere age-depth model construction and calibrations, respectively, except where the latter had dates older than 10,522 14C radiocarbon years, in which case the IntCal09 curve was employed. Calibrated ages are reported as the average of the 95.4% two sigma (2σ) calibrated age range that obtains the greatest relative area under the probability distribution curve.
Measurements and notation
Table 1 documents the focal features and variables extracted from pollen diagrams, used in calculations of recovery rates. Details of the disturbance types, and associated indicators, recorded from published palaeoecological studies are displayed in Table 2.
Data acquisition and analysis
The response metric, RR, calculated as percentage forest pollen increase per unit time from the fossil pollen diagrams selected for this meta-analysis, provides a basic measure of forest recovery. RR is measured as an average across the entire period of forest pollen increase (representing forest re-establishment), until the maximum increase in percentage of forest pollen post-decline is achieved, before a stabilizing point or further decline. It therefore incorporates any non-linear components of the trajectory, which may result, for example, from low-level perturbations during the period of recovery; it is, however, the overall rate at which the forest is responding to each disturbance event that is the variable of interest here. Datathief III38 was used to extract RR components from the published fossil pollen diagrams, to reduce potential bias resulting from visual interpretation and assist in the calculation of an average rate over the entire period of forest re-establishment.
The species or functional diversity of the individuals contributing to this summed forest value was not recorded, in part due to lack of reporting of such information across selected studies. Thus, the computed RR does not take into account the biotic character, for example, primary versus secondary taxa, and turnover in the recovering vegetation, both of which form important components of ecological resilience and may influence the speed at which the ecosystem recovers from perturbation24. The focus of this meta-analysis is rather on the RR of forest, as defined uniquely in each individual study (see Supplementary Data 1 for details of studies), representing the speed and extent to which this ecological unit re-grows relative to its pre-disturbance abundance, with the assumption that vegetation re-establishment, as inferred through the proxy of fossil pollen, is indicative of sustained ecosystem functionality. Under this criteria, a variety of forest types, ranging from full canopy cover to some fraction of that (indicated by Fpre values of individual events; see Supplementary Data 1), are included in this meta-analysis.
Where emergent variables measured from pollen diagrams demonstrated a skewed pattern, such as Fmax, and sample sizes were quite different between groups within variables, for example, disturbance type, non-parametric descriptive statistics were used to illustrate trends in the data.
The distributions of the response variable (RR) and predictor covariates, for example SRD, were observed and transformations performed, resulting in logarithms of RR and SRD being used in the final analyses. Multiple regression analyses were run in R35, using the nlme package39, to investigate the relationship between RR and the range of recorded variables. Model I (equation 1) represents the linear mixed-effects model used in the analysis of RR:
(See Table 3 for model output.) Site ID was included as a random effect, providing a unique identifier for each fossil pollen record, to obviate potential bias resulting from pseudoreplication and to enable exploration of overall patterns in the data set without weighting each effect size by their associated group size (that is, number of events per pollen record); this was considered an inappropriate transformation in this meta-analysis given that effect sizes within each group varied greatly. Several covariates were excluded from the final multiple regression model (Model 1, Eq. 1), after they demonstrated an insignificant relationship with the response variable, log(RR) (linear mixed-effects model, P value>0.1, n=283), when considering their partial slopes: altitude (linear mixed-effects model, P-value=0.625, n=283) and sequential number of the disturbance event (linear mixed-effects model, P-value=0.728, n=283), both square-root transformed. Through manipulation of Model I (Eq. 1), comparisons were made of RR across location and disturbance category groups. To investigate the emergent significant relationship between RR and SRD (linear mixed-effects model, P-value<0.0001, n=283; Table 3), the degree of correlation between SRD and the location and disturbance category groups was tested using the following model (Eq. 2):
(See Table 4 for model output.) Site ID was included as a random effect (proving a more important component of this model due to the nature of SRD measurements). A third model, including log(Trec) as a covariate (Model III), demonstrated a significant relationship with log(SRD) (linear mixed-effects model, P-value<0.01, n=283); however, since Trec is used in the calculation of RR, this finding is not independent of the findings from Model I. In addition, disturbance events are assumed to occur randomly through time in each location, not as a function of the time spent in or level of recovery of the forest ecosystem.
How to cite this article: Cole, L. E. S. et al. Recovery and resilience of tropical forests after disturbance. Nat. Commun. 5:3906 doi: 10.1038/ncomms4906 (2014).
McNamara, S., Erskine, P. D., Lamb, D., Chantalangsy, L. & Boyle, S. Primary tree species diversity in secondary fallow forests of Laos. Forest Ecol. Manag. 281, 93–99 (2012).
Cole, R. J., Litton, C. M., Koontz, M. J. & Loh, R. K. Vegetation recovery 16 Years after Feral Pig removal from a wet Hawaiian forest. Biotropica 44, 463–471 (2012).
Uhl, C., Jordan, C., Clark, K., Clark, H. & Herrera, R. Ecosystem recovery in Amazon caatinga forest after cutting, cutting and burning, and bulldozer clearing treatments. OIKOS 38, 313–320 (1982).
Saldarriaga, J. G., West, D. C., Tharp, M. L. & Uhl, C. Long-term chronosequence of forest succession in the Upper Rio Negro of Colombia and Venezuela. J. Ecol. 76, 938–958 (1988).
Chazdon, R. L. et al. Rates of change in tree communities of secondary Neotropical forests following major disturbances. Philos. Trans. R Soc. B Biol. Sci. 362, 273–289 (2007).
D’Oliveira, M. V. N., Alvarado, E. C., Santos, J. C. & Carvalho, J. A. Forest natural regeneration and biomass production after slash and burn in a seasonally dry forest in the Southern Brazilian Amazon. Forest Ecol. Manag. 261, 1490–1498 (2011).
Peña-Claros, M. Changes in forest structure and species composition during secondary forest succession in the Bolivian Amazon. Biotropica 35, 450–461 (2003).
Bush, M. & Colinvaux, P. A. Tropical forest disturbance: palaeoecological records from Darien, Panama. Ecology 75, 1761–1768 (1994).
Jones, H. P. & Schmitz, O. J. Rapid recovery of damaged ecosystems. PLoS ONE 4, e5653 (2009).
Barlow, J. et al. Quantifying the biodiversity value of tropical primary, secondary, and plantation forests. PNAS 104, 18555–18560 (2007).
Gibson, L. et al. Primary forests are irreplaceable for sustaining tropical biodiversity. Nature 478, 378–381 (2011).
Asner, G. P. et al. Condition and fate of logged forests in the Brazilian Amazon. Proc. Natl Acad. Sci. USA 103, 12947–12950 (2006).
Lindenmayer, D. B. & Laurance, W. F. A history of hubris—cautionary lessons in ecologically sustainable forest management. Biol. Conserv. 151, 11–16 (2012).
Connell, J. H. Diversity in tropical rain forests and coral reefs. Science 199, 1302–1310 (1978).
Turner, M. G. & Dale, V. H. Comparing large, infrequent disturbances: what have we learned? Ecosystems 1, 493–496 (1998).
Neubauer, P., Jensen, O. P., Hutchings, J. A. & Baum, J. K. Resilience and recovery of overexploited marine populations. Science 340, 347–349 (2013).
Weiher, E. & Keddy, P. Ecological Assembly Rules: Perspectives, Advances, Retreats Cambridge University Press (2001).
Burrows, N. D. Linking fire ecology and fire management in south-west Australian forest landscapes. Forest Ecol. Manag. 255, 2394–2406 (2008).
Quesada, C. A. et al. Basin-wide variations in Amazon forest structure and function are mediated by both soils and climate. Biogeosciences 9, 2203–2246 (2012).
Hector, A. et al. The Sabah Biodiversity Experiment: a long-term test of the role of tree diversity in restoring tropical forest structure and functioning. Philos. Trans. R Soc. B Biol. Sci. 366, 3303–3315 (2011).
Muller-Landau, H. C. Carbon cycle: sink in the African jungle. Nature 457, 969–970 (2009).
Nepstad, D. C., Uhl, C., Pereira, C. A. & da Silva, J. M. C. A comparative study of tree establishment in abandoned pasture and mature forest of eastern Amazonia. Oikos 76, 25–39 (1996).
Chazdon, R. L. Tropical forest recovery: legacies of human impact and natural disturbances. Perspect. Plant Ecol. Evol. Syst. 6, 51–71 (2003).
Chapin, F. S. III et al. Biotic control over the functioning of ecosystems. Science 277, 500–504 (1997).
Palmer, M. A. & Filoso, S. Restoration of ecosystem services for environmental markets. Science 325, 575–576 (2009).
Heckenberger, M. J., Russell, J. C., Toney, J. R. & Schmidt, M. J. The legacy of cultural landscapes in the Brazilian Amazon: Implications for biodiversity. Philos. Trans. R Soc. B Biol. Sci. 362, 197–208 (2007).
Mueller, A. D. et al. Recovery of the forest ecosystem in the tropical lowlands of northern Guatemala after disintegration of classic Maya polities. Geology 38, 523–526 (2010).
Turner, B. L. II & Sabloff, J. A. Classic period collapse of the Central Maya Lowlands: insights about human-environment relationships for sustainability. PNAS 109, 13908–13914 (2012).
Van Gemerden, B. S., Olff, H., Parren, M. P. E. & Bongers, F. The pristine rain forest? Remnants of historical human impacts on current tree species composition and diversity. J. Biogeography. 30, 1381–1390 (2003).
Vandermeer, J. & Granzow De La Cerda, I. Height dynamics of the thinning canopy of a tropical rain forest: 14 years of succession in a post-hurricane forest in Nicaragua. Forest Ecol. Manag. 199, 125–135 (2004).
Barlow, J., Gardner, T. A., Lees, A. C., Parry, L. & Peres, C. A. How pristine are tropical forests? An ecological perspective on the pre-Columbian human footprint in Amazonia and implications for contemporary conservation. Biol. Conserv. 151, 45–49 (2012).
Dakos, V., Kéfi, S., Rietkerk, M., van Nes, E. H. & Scheffer, M. Slowing down in spatially patterned ecosystems at the brink of collapse. Am. Nat. 177, E153–E166 (2011).
Veraart, A. J. et al. Recovery rates reflect distance to a tipping point in a living system. Nature 481, 357–359 (2012).
Blaauw, M. Methods and code for ‘classical’ age-modelling of radiocarbon sequences. Quat. Geochronol. 5, 512–518 (2010).
R Core Team. R: A Language and Environment for Statistical Computing R Foundation for Statistical Computing (2012) http://www.R-project.org.
Taylor, R. E. Radiocarbon Dating: An Archaeological Perspective Academic Press (1987).
Deevey, E. S. et al. Mayan urbanism: Impact on a tropical karst environment. Science 206, 298–306 (1979).
Tummers, B. DataThief III. http://datathief.org/ (2006).
Pinheiro, J., Bates, D., DebRoy, S. & Sarkar, D. the R Development Core Team. NLME: Linear and Nonlinear Mixed Effects Models. R package version 3.1-111 (2013).
Olson, D. M. et al. Terrestrial ecoregions of the world: a new map of life on earth. BioScience 51, 933–938 (2001).
We thank JL Snaddon, P Long, M Macias-Fauria and S Nogué for comments and assistance, and NERC, UK for funding.
The authors declare no competing financial interests.
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Cole, L., Bhagwat, S. & Willis, K. Recovery and resilience of tropical forests after disturbance. Nat Commun 5, 3906 (2014). https://doi.org/10.1038/ncomms4906
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