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Effect of forest fire on tree diversity and regeneration potential in a tropical dry deciduous forest of Mudumalai Tiger Reserve, Western Ghats, India
Ecological Processes volume 6, Article number: 32 (2017)
The study was conducted in Mudumalai Tiger Reserve, in the Western Ghats to understand the effect of a single fire event on tree diversity and regeneration status. Four forest patches were selected which were unburned, 2-year-old burn, 5-year-old burn, and 15-year-old burn. Three 0.1 ha square plots were laid randomly in all four patches and analyzed for tree diversity, stand structure, and regeneration of tree species.
A total of 4129 individuals of tree species were recorded in field surveys, comprising 3474 seedlings, 121 saplings, and 534 trees. Totally, 40 tree species were recorded in study plots, from which 28 species were seedlings, 16 species were saplings, and 37 species were at tree stages.
Tree diversity decreased in 2-year-old and 5-year-old burnt plots and was reached to the level of unburnt plots in 15 years of interval. Stems of small size classes started increasing after the fire. Seedling density increased linearly in subsequent years after fire but sapling and tree density recorded less than control in B2 but was higher in B5 and B15. The overall fire affected diversity, but regeneration showed a positive trend.
Fire is a significant ecological event that can produce variable effects (Keane et al. 2002, Whelan 1995). Forest fires strongly affect the species composition of plant communities (Danthu et al. 2003) by influencing different aspects of growth and development, like flowering, seed dispersal, germination, seedling establishment, and plant mortality (De Luis et al. 2005, Walters et al. 2004). Forest fires affect vegetation by suppressing certain species and encouraging other species causing changes in vegetation structure and successional pattern (Syaufina and Nuruddin 2011). Forest regeneration has been affected by fire through killing stem tissues of seedlings and saplings and heating the soil sufficiently to kill roots and seeds near the soil surface (Balch et al. 2013, Kennard et al. 2002).
In tropical dry deciduous forests, where fires are very frequent, plants display some adaptive traits like thick bark, the capability of healing fire scars, seed adaptations, and re-sprouting capability (Khan and Tripathi 1986, 1989). The ecological significance of these recurrent fires on forest establishment is important. Fires firmly promote few fire-tolerant species that can replace the naturally growing species in an undisturbed environment.
Several studies have been conducted across the globe in the last few decades to understand the effect of fires on vegetation, soil properties, and biomass (Verma and Jayakumar 2012, Whelan 1995). But most of these studies were conducted in the temperate regions. Forest fires are widespread phenomena in Indian forests. Studies suggest that 90% of vegetation fires in India may be man-made, and annually about 3.73 million ha of forest areas are affected by forest fires (Srivastava and Garg 2013). Tropical dry deciduous forests are more vulnerable to forest fire than any other forest across the world (Janzen 1988, Murphy and Lugo 1986). Maximum forest fires in India have been reported in tropical dry deciduous followed by tropical moist deciduous forest and tropical semi-evergreen forest (FSI 2012). In India, studies on forest fire are majorly focused on monitoring and management of forest fire. Only a few studies have addressed the ecological perspective of a forest fire.
There are very limited studies in India on ecological dynamics of tropical deciduous forests after fire (Kodandapani et al. 2008, 2009, Saha and Howe 2003, Verma and Jayakumar 2015). Few researchers have tried to study forest fire in the Western Ghats, for example, Srivastava et al. (2014) mapped fire-risk areas in Mudumalai Tiger Reserve (MTR) and Mondal and Sukumar (2014) studied characteristic weather pattern associated with fire. Verma et al. (2015) studied the spatial and temporal pattern of forest fire in MTR. Kodandapani et al. (2004, 2008, and 2009) studied fire history, fire return interval, ecological impact of fire, and conservation threats of forest fire in the Western Ghats from 1989 to 2005 with changing fire regime, and they found that species diversity and regeneration initially increases in low fire frequencies and then start decreasing. Similar results were also reported by Verma and Jayakumar (2015) who studied the effect of fire frequencies on tropical dry deciduous forest in MTR. None of these studies have attempted to study the effect of single fire on diversity and regeneration of tree species and how much time these ecosystems take to recover from a single fire event.
The ubiquitous occurrence of fires suggests that fires potentially play a significant role in the management of landscapes. Without a proper understanding of the causes and effects of fire, it is not possible to meet the challenge of shrinking forest resources in the present and the challenge of climate change in the future. The mean fire return interval for the MTR had been increased significantly to 9.28 years (1999–2013) (Verma and Jayakumar 2015) which was 3.3 years in 1989–2002 as reported by Kodandapani et al. (2004). It has been assumed that these forests need more time for recovery with changing fire regime, and it will have an effect on the regeneration and species composition. Hence, the present study is aimed to understand the role of single fire event in the dynamics of tree species diversity, stand structure, and regeneration in a tropical dry deciduous forest of Western Ghats. The main questions are as follows: (1) How is tree diversity affected by a single fire event? (2) How does regeneration vary after different numbers of years since burning? (3) Which species are benefitted by single fire? and (4) How does a single fire affect tree density and stand structure?
Mudumalai Tiger Reserve (11° 32′ and 11° 43′ N and 76° 22′ and 76° 45′ E) is located in the state of Tamilnadu, India, and is a part of the Nilgiri Biosphere Reserve. It lies at the tri-junction of Kerala, Karnataka, and Tamilnadu (Fig. 1).
The park is contiguous with Bandipur National Park (874 km2), Wayanad Wildlife Sanctuary (344 km2), and Sigur and Singara reserve forests. Its topography is extremely varied and comprises of hills, valleys, ravines, water courses, and swamps. It is spread over an area of 321 km2. Three distinct seasons are recognized in MTR: dry season (January–April), first wet season (May–August), and second wet season (September–December) (Dattaraja et al. 2013). Average annual rainfall varies from 721 mm year−1 in the east to 1681 mm year−1 in the west (Dattaraja et al. 2013). The mean temperature ranges from 15.7–28.7 °C between November and April. Champion and Seth (1968) classified the vegetation type in Mudumalai as southern tropical dry thorn forest, southern tropical dry deciduous forest, southern tropical moist deciduous forest, southern tropical semi-evergreen, moist bamboo brakes, and riparian forest. While vegetation in the eastern part of MTR is open thorny scrub to dry deciduous characterized by a poor and stunted growth, the vegetation in western portion tends to be semi-evergreen. The dry deciduous forest lies in northern portion whereas the vegetation in southern portion is moist deciduous. MTR was dominated by Dalbergia latifolia, Pterocarpus marsupium, and Lagerstroemia microcarpa 150 years ago (Cleghorn, 1861) which is at present dominated by Anogeissus latifolia and Terminalia crenulata (Verma and Jayakumar 2015).
Fire frequency maps were prepared by using fire maps of each year from 1999 to 2013. For the period between 2001 and 2012, fire maps available in the Tamilnadu Forest Department were obtained. Fire maps for the year 1999, 2000, and 2013 were prepared using satellite images of Landsat 5 Thematic Mapper acquired on 2 February 1999 and 7 April 1999; Landsat 7 ETM+ acquired on 28 January 2000, 1 April 2000, 17 April 2000, 3 May 2000, and 31 January 2013; and Landsat 8 OLI-TIRS acquired on 13 April 2013. Spatial resolution of satellite imagery was 30 m. Satellite images for the study area were extracted, geo-corrected, and classified into burned and unburned areas using supervised classification. We used ERDAS Imagine 2011 to analyze the satellite images.
From the fire map, unburned pixels and burned once between 1999 and 2013 were selected. The unburned pixels were grouped into control (B0), pixels that burned in 2012 were designed as 2-year-old burn (B2), pixels burned in 2009 were labeled as 5-year-old burn (B5), and pixels burned in 1999 were marked as 15-year-old burn (B15).
Field data collection
This study was conducted in the one-time burned deciduous forest patches which were burned once in 2012 (B2), 2009 (B5), and 1999 (B15), respectively. Three 0.1 ha square plots were laid randomly, independent to each other in all burned and unburned patches, and there were no significant differences within these plots. All woody stems inside the plots were enumerated. For seedlings, four 5 × 5 m subplots were laid on the four corners of the 0.1 ha plot. Plot size was constant across all samples. Vegetation data were collected in the month of November and December 2013. All the trees were identified using checklists and flora of Mudumalai (Sharma et al. 1978). Measurements such as collar girth (CG) (for saplings), girth at breast height (GBH) (for trees), and height (H) were recorded for all the woody plants for both living and dead. For seedlings, only number was counted. The seedlings were defined as height less than 50 cm whereas saplings were defined as height 50–150 cm and collar girth 1 to ≤ 10 cm. Trees were defined as > 10 cm GBH.
The diversity of all living stems was estimated by using the Shannon–Wiener index (H′) and Simpson’s dominance index (1-D) (Magurran 2013). The total number of species and species in different growth forms (seedlings, saplings, and trees) were calculated. For each growth form, stem density and basal area data were calculated and subjected to one-way ANOVA to examine significant differences in these variables among fire frequency classes. Means that exhibited differences were compared using Tukey’s test with a 5% probability significance threshold. GBH was converted to dbh (Diameter at breast height). Stem size distribution was analyzed as the total count per size class within fire class to see stand structure. All statistical analyses were performed using IBM SPSS Statistics 20.
Six fire frequencies were recorded between 1999 and 2013. Only 80.25 ha (0.25%) area received six-time fire in 15 years of the study period between 1999 and 2013, whereas 770.40 ha (2.40%) burned five times, 2664.30 ha (8.30%) burned four times, 4494 ha (14%) burned thrice, 5977.02 ha (18.62%) burned twice, 8503.29 ha (26.49%) burned once, and 9601.11 ha (29.91%) remained unburned. Burned area decreased with increasing fire frequency.
A total of 4129 individuals of tree species were recorded in field surveys, comprising 3474 seedlings, 121 saplings, and 534 trees. The mean density of tree species was 0.34 individual m−2. Totally, 28 species were present in seedlings, 16 species in saplings, and 37 species in tree stage in the study area. Shannon–Weiner index and Simpson dominance index showed that diversity was highest in the control (Fig. 2). Diversity decreases immediately after the fire and then start increasing thereafter but could not reach the level of control even after 15 years. Number of species was also highest in B0 in all stages. The highest basal area was recorded for B0, and the lowest was for 2-year-old burn (Table 1). Stand density was highest for B15 (570 ± 26.5 ha−1) and lowest for B2 (370 ± 52.9 ha−1). Stand density decreased immediately after the fire but increased 5 years after fire (Table 1).
Fire significantly affected the stand structure of tree species. The number of stems in smaller size class started increasing after the fire. In the control plot, maximum number of stems were present in 20–30 cm dbh size class, whereas the number of stems was highest in 0–10 cm dbh size class in B15. Significant changes were observed only in lower size classes (< 20 cm) (Fig. 3).
Significant differences in the mean stem density of seedlings (F3, 8 = 8.83; P = 0.006) and saplings (F3, 8 = 8.82; P = 0.006) were observed among fire classes. Tree population (F3, 8 = 0.259, P = 0.853) did not show substantial variation among the fire classes. Seedling density (Fig. 4a) increased in all classes after fire, whereas sapling (Fig. 4b) and tree (Fig. 4c) density initially decreased but increased 5 years after fire.
Abundance data showed that in seedlings A. latifolia dominated in all fire classes followed by Randia dumetorum and Tectona grandis (Table 2). For saplings, individuals of A. latifolia, T. grandis, and T. crenulata increased with increasing time after fire (Table 2). In tree stage, T. grandis was most abundant in B0, B2, and B5 whereas A. latifolia and Phyllanthus emblica were most abundant in B15 (Table 2).
Fire used to be extremely rare in tropical forests, leaving ample time for forests to regenerate to pre-fire conditions (Slik et al. 2008). In recent decades, however, tropical forest fires occur more frequently and at larger spatial scales than they used to be earlier (Dickson et al. 2006, Slik et al. 2008, Stephens et al. 2015). Annual fires are very common all over MTR. Most of these are low-intensity surface fires (Kodandapani et al. 2008), but their impact on the forest ecosystem is large. These fires are anthropogenic in nature, and the main causes of these fires are poaching, antler collection, grazing, tourism, estates, and settlements in and around the reserve (Srivastava et al. 2014, Verma et al. 2015). The poachers light fire for visibility. The inflammable material continuously cast down by the deciduous trees offers even an accidental spark, the chance of developing into an extensive and devastating fire (Verma et al. 2015).
Results showed that a single fire event can significantly affect diversity and regeneration of trees. Species diversity decreased and dominance increased immediately after fire due to stem mortality in lower size class. After 5 years of fire, diversity was slightly higher but it may take longer time than 15 years to reach the level of control. Post fire decrease in species richness is also reported by Saha and Howe (2003) in dry deciduous forest of Central India. They suggested that fire favors proliferation of root-sprouters, which leads to decrease in diversity.
Single fire event did not show a significant impact on the density of trees and basal area, which suggest that mortality caused by fire would be in lower size classes. Analysis of stand distribution in different girth classes showed variation in lower size classes alone.
The density of seedling and sapling was significantly higher in burned plots and increasing with time. It suggests that single fire event could be beneficial for the regeneration of trees. Increased available nutrient, decrease in pathogen population, breaking in seed dormancy, and opening of mineral soils could be the reason for enhanced number of seedlings and saplings. Our results also supported by the studies of Gould et al. (2002) and Mondal and Sukumar (2015). They have also found increased number of seedlings and sapling in burnt patches compared to unburnt patches.
It is concluded from this study that even a single fire event has a varying degree of impact on tree species of dry deciduous forest. The single fire has affected stem density significantly, which initially decreases but increases after 5 years. All fire classes (B2, B5, and B15) have recorded with less diversity than control. Maximum impacts of fire were on trees in smaller stem size. The number of seedlings increased after fire, whereas the number of saplings and trees decreased in B2 but increased after 5 years. Further studies are required to understand future responses to post-fire changes and to build a predictive model for different burned forest environments.
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We thank the Tamil Nadu Forest Department for granting us permission and providing data to conduct this study at the Mudumalai Tiger Reserve. We acknowledge the support of field assistants and forest staff of Mudumalai Tiger Reserve for their help and cooperation. The first author thank the University Grants Commission, New Delhi for providing the financial support for the Ph.D. research through Junior Research Fellowship (UGC letter No. F. 17-115/98 (SA-I) dated 11 June 2013).
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