http://orcid.org/0000-0002-6524-1775
Figures
Abstract
Shifting cultivation has resulted in large-scale deforestation and forest degradation in the tropics; however the abandoned fallows are known to have high potential for carbon capture. The paper is an attempt to determine the forest recovery patterns following shifting cultivation by evaluating the tree species composition, diversity and abundance with respect to topographical factors in Manipur, India. We also used ordination analysis to understand the change in species composition with regard to environmental variables. The living woody biomass carbon of each fallow was quantified, and the factors affecting the recovery of carbon stock along an increasing fallow gradient was assessed. Our results showed that the species richness and basal area recovered relatively with time since abandonment, and the north-facing lower elevation fallow sites displayed higher species richness and stem density than those in higher elevations. Environmental variables had no impact on the regeneration of Elaeocarpus floribundus Blume and Castanopsis hystrix Hook. f. & Thomson ex A. DC. which suggests that they may be capable of effective restoration of degraded forest areas. As these species appear naturally in the forests, it would facilitate quicker rehabilitation and reinstate the soil nutrients making the soil reusable in a short term. We also found that fallow age plays a vital role in recovering above-ground biomass carbon from living woody species followed by the aspect of the site. The total living woody biomass carbon ranged from 0.98 Mg ha-1 in 5 years fallow to 142.58 Mg ha-1 in 20 years fallow. The above-ground biomass carbon recovery of the oldest fallow was 39% to 40% of the reference undisturbed forest and the estimated time for the shifting cultivation fallows to reach that of the undisturbed forest level was approximately 39 years to 41 years.
Citation: Thong P, Sahoo UK, Thangjam U, Pebam R (2020) Pattern of forest recovery and carbon stock following shifting cultivation in Manipur, North-East India. PLoS ONE 15(10): e0239906. https://doi.org/10.1371/journal.pone.0239906
Editor: Gerhard Hartwig Buck-Sorlin, Institut Agro - AGROCAMPUS OUEST, FRANCE
Received: November 1, 2019; Accepted: September 15, 2020; Published: October 8, 2020
Copyright: © 2020 Thong et al. This is an open access article distributed under the terms of the Creative Commons Attribution License, which permits unrestricted use, distribution, and reproduction in any medium, provided the original author and source are credited.
Data Availability: All relevant data are within the paper and Supporting Information files.
Funding: The author(s) received no specific funding for this work
Competing interests: The authors have declared that no competing interests exist.
Introduction
Shifting cultivation is a major land use in tropics despite the fact that it is blamed to be a major cause of forest loss. Serious concerns are raised that this practice though the oldest form of agriculture may negatively affect biodiversity, carbon stocks and greenhouse gas emissions [1–3]. However, this practice provides subsistence livelihoods to millions of people worldwide [1] and, therefore, it is likely to continue as it is intricately linked to cultural, ecological and economic aspects of communities [4]. This practice is characterized by the alternation of the cropping and fallow phase, while the abandoned land regenerates naturally. After a certain fallow period, the trees are slashed and burnt for the ashes to enrich the soil, thus allowing a new cropping phase. This intervening period between two successive slashed and burnt practices is termed as Jhum cycle. The fallow duration and cropping period are specifically influenced by ecological and socio-economic factors [5]. In North-East India, this practice is locally known as Jhum where the cropping period has been reported to be 1–2 years with a fallow duration varying from 6–12 years [6, 7]. The regional estimation of abandoned land after Jhum differs significantly depending on the means of estimation. However, this region encompasses 3697.14 km2 of the National area of abandoned land [8]. Manipur, in particular, has 0.45% (100.10 km2) of its total geographical area under abandoned Jhum land. Under the natural process of ecological recovery, the abandoned lands are eventually restored to secondary forests.
In the tropical region, secondary forests constitute over 50% of the forested area and have the ability to assimilate and store carbon [9]. In India, secondary forests cover about 32 million ha which is approximately 45.8% of the forest area of the country [10]. The dynamic nature of shifting cultivation results in a landscape mosaic of Jhum field, secondary forests and old-growth forests. As such, many forests in North-East India are secondary forests at different stages of succession following shifting cultivation. These forests are an essential source of rural livelihood and also for multiple environmental functions such as soil and watershed conservation, flood control and carbon storage [11]. However, secondary forests get constantly subjected to increasing exploitation by the growing population as well as by budding industrial and urban demand for forest products. Succession following Jhum is comprised of fast growing species with high regeneration and species accumulation than other human-modified and abandoned agroforestry systems [12]. In the tropics, the diversity of woody species steadily increases with the age of fallow [13]. The quantity of biomass in a forest ascertains the potential amount of carbon added to the atmosphere or sequestered on the land [14]. An understanding of species recovery especially woody species and carbon stock is vital not only for developing rehabilitation strategy for shifting cultivation areas but also for carbon-based payments for ecosystem services such as reducing emissions from deforestation and forest degradation.
Given the importance of the secondary forests and the human pressure on these resources, the present study is conducted to (1) understand the tree recovery pattern following shifting cultivation, (2) estimate the living woody biomass and carbon stock under different fallow regimes, (3) identify naturally occurring potential tree species to accelerate the restorative phase of the fallows. Despite the undulated topography, the state of Manipur has 77.69% of its total geographical area under forest cover, based on which we put forward the hypothesis that topographical parameters namely slope, aspect and elevation have a bearing on the species composition with increasing fallow age. We believe that the result of this study will provide baseline data on the rate of vegetation recovery and biomass carbon as accumulated by the living woody species in order to achieve proper management of such successive areas.
Materials and methods
Ethics statement
The study was carried out in four different shifting cultivation fallow lands owned by villagers in Ukhrul and Chandel district of Manipur. Permission was obtained from each of the land owner towards collection of plant samples and vegetation data. No rare or endangered species was used in this study, and besides the study did neither involve the use of wild animals nor threatened environmental systems.
Study area
The study was conducted in Ukhrul (24°29’6”-24°41’35”-N and 94°7’24”-94°44’44”E) and Chandel (23°50’11”-24°38’52”N and 93°53’58”-94°18’10”E) districts of Manipur, Northeast India. The satellite imagery for the map showing the study area was downloaded from www.glovis.usgs.gov which is a public domain (Fig 1). These districts are situated in the north-eastern and south-eastern part of the State. Ukhrul is located at an elevation of 1662 m a.s.l and Chandel at 957 m a.s.l. The subtropical climate of this region is affected by the southwest and northeast monsoons with distinct rainy (June to September) and dry (November to February) seasons. Ukhrul and Chandel districts have contributed to the increase in the net forest cover of the state by 151 km2 and 17 km2 respectively [15].
Site selection
Keeping in view the topographical parameters, soil type, and mean annual rainfall and temperature, we selected four different fallow periods after the abandonment of the Jhum fields, namely, 5 (JF5), 10 (JF10), 15 (JF15) and 20 (JF20) years fallow (Table 1). The study sites were selected as per the findings of Thong et al. [7] and the plot was navigated using a GPS.
Vegetation sampling
The vegetation sampling was conducted during the dry months of January and February for fallow aged 5 (JF5), 10 (JF10), 15 (JF15) and 20 (JF20) years. We identified a total of 12 sites (four fallow aged plots x three replicates) in each district. At each site, five quadrates of 10 m x 10 m were randomly laid for identifying tree species at different stages of their growth, namely trees, pole, saplings and seedlings. The diameter at breast height (dbh) was measured at 1.37 m from the ground level for individuals with dbh >3 cm. Mature trees were defined as stems with dbh ≥10 cm and height ˃2 m, poles as individuals with dbh ≥3 to <10 cm and height ˃2m, saplings as individuals with collar diameter <3cm and height ˃30 cm to ≤2 m, and seedlings as individuals with collar diameter <3cm and height upto 30 cm. The herbaria at Mizoram University and other published literatures were consulted for correct tree species identification for those which could not be identified in the field. We referred to The Plant List (www.theplantlist.org) for species nomenclature classification.
Analysis of plant diversity and community structure
Community structure variables such as density, frequency, abundance, basal area and important value index (IVI) of each species in different fallow sites were calculated according to Mueller-Dombois and Ellenberg [16]. Spatial distribution of tree species was determined following Whitford Index [17]. Plant diversity measures such as Shannon-Wiener diversity index (H'), Simpson’s dominance index (C), and Margalef species richness index (Dmg) were also determined [18–20].
Rarefaction curves based on the number of individuals encountered during the vegetation analysis was plotted to assess the species accumulation pattern for all tree species. The rate of change in species composition with increasing fallow age (β diversity) was calculated following Whittaker [21]. To analyse the similarity in species composition among the replicates of different fallow age stands, Jaccard’s similarity index was represented in the form of a dendrogram [22].
Biomass estimation
A non-destructive sampling method was adopted to estimate tree above and below-ground biomass and carbon stock of each tree species. With dbh as an independent variable, tree volume (dbh ≥5 cm) was calculated using local and regional based species specific volume equations given by Forest Survey of India (FSI) [23]. Specific gravity of the species was obtained from Global wood density database [24]. The above-ground biomass (AGB) of each individual tree (in kg) was calculated as:
However, for those species for which volume equations were not available, AGB was estimated using generic allometric models for tropical forests [25–29]. With the AGB estimated from local volume equation as the base model, the best predictive model was selected on the basis of adjusted R2, RMSE, MAD and systematic errors (bias). The AGB for those individuals with dbh<5 cm was derived by using the equation developed by Ali et al. [30]:
The above ground carbon stock for woody trees with dbh <10 cm, and ≥10 cm were calculated as 46% and 49% of the ABG respectively [31]. The below ground biomass (BGB) was determined by the equation given by Mokany et al. [32] and its carbon stock was calculated as 50% of the BGB.
Hence, the total living woody biomass carbon was calculated as:
The uncertainty of total living woody biomass in each fallow stand was estimated as per Higuchi et al. [33]. And the recovery of biomass carbon of the fallow age was computed following the formula given by Mukul et al. [34]:
Where, Xfallow is the fallow site’s biomass carbon and Xs is the mean of biomass carbon in the old growth forest. The findings of Waikhom et al. [35] on sacred grove of Manipur was used as reference data for carbon stock recovery estimation. They estimated the biomass using regression equation developed by Chambers et al. [36] which had 38% moisture content. Therefore, biomass estimated from the sacred grove was converted to dry biomass by removing the water content and then the carbon stock was determined. This was done to assess the recovery percent of our estimated dry biomass carbon.
Statistical analysis
All statistical analysis was conducted using SPSS version 20.0 and PAST version 3.25. One-way ANOVA (Analysis of Variance) was used to examine if there is a significant difference in stem density, basal area, diversity, evenness, dominance and species richness (dependent variables) among different fallow ages (fixed variable). Multiple regression was performed to investigate the relationship of slope, aspect and altitude with species composition along an increasing fallow gradient. The constrained ordination technique of Canonical Correspondence Analysis (CCA) was used to assess the environmental variables contributing to the variation in species composition among fallows. The environmental variables used in CCA were (i) elevation (ii) fallow age (iii) slope, and (iv) aspect. Each of these environmental variables and its association with the variation in the distribution of species were tested using 999 unrestricted permutations.
Prior to analysis of carbon stock, the normality and heteroscedasticity of carbon distribution with increasing fallow age was checked using the Shapiro-Wilk and Levene’s test respectively. To assess variation in carbon stock, we constructed a linear mixed-effect model (LMEM) with fallow age, slope, aspect and elevation as fixed effects, and incorporated sites nested within fallow ages as random intercepts in the model. We applied the information theoretical approach based on the Akaike Information Criterion corrected for small sample sizes (AICc) for model selection, and the model with the lowest AICc score was selected as the best-fit model.
Results
Stand characteristic and tree diversity
A total of 58 tree species belonging to 27 families in Ukhrul and 59 tree species belonging to 31 families in Chandel were recorded from the fallow stands. The most dominant family in the study areas was Fagaceae except for the 15 years old fallow site specific to Chandel where the dominant family was Pinaceae. Phytosociological analysis showed high tree diversity and species richness while the low values of dominance index revealed inequitable distribution of trees across increasing fallow age (Table 2). The rarefaction curves of species accumulation indicated that the tree species richness curves in all the fallow ages reached a plateau with increasing fallow age which validates that time duration limits the appearance of new species in fallow ages. The highest number of individuals was recorded from the 20 years fallow with 404 individuals in Ukhrul and 449 in Chandel (Fig 2). Whittaker’s β index showed high level of species similarity between 5 years and 10 years fallow in Ukhrul as well as between 15 years and 20 years fallow in Chandel (Table 3). The three replicates of 5 years fallow, 10 years fallow, 15 years fallow and 20 years fallow were dissimilar to each other with regard to species composition in Ukhrul, while it was contrary in Chandel (Fig 3). Replicates of 15 years fallow showed lowest similarity while the highest was observed in the replicates of 20 years fallow. In Ukhrul, the younger fallows had more similar species which lessened as the fallow age increased. However, Chandel had low species similarity in the younger fallows which increased with the increase in fallow age. Environmental factors namely slope and aspect were found to be similar between 5 and 10 years fallow in Ukhrul as well as between 15 and 20 years fallow in Chandel. This explains for the high species similarity between the fallows (see S1 Table).
The values ranges from 0 (no similarity) to 1 (complete similarity).
Population density and distribution pattern
The distribution analysis of all tree species encountered in each fallow stand is represented in S2 Table. The dominance-distribution curves for all the fallow stands showed normal distribution with high dominance and low equitability in younger fallows which proceed to high equitability as the fallow age increases (Fig 4). In Ukhrul, Lithocarpus dealbatus (Hook.f.& Thomson ex Miq.) Rehder (IV1 29.32), Rhus chinenesis Mill. (IVI 27.85), Pinus kesiya Royle ex Gordon (IVI 35.73) and Schima wallichii Choisy (IVI 23.59) were the most dominant species along an increasing fallow gradient, while Quercus serrata Murray (IVI 24.26, 26.82) dominated in 5 and 10 years fallow in Chandel and Schima wallichii Choisy (IVI 35.25) and Castanopsis hystrix Hook. F. & Thomson ex A. DC. (IVI 24.76) dominated the 15 and 20 years fallow respectively. Most of the fallows showed contagious distribution pattern (32–90%) followed by random distribution (10–68%). Regular distribution was observed only for 20 years fallow in Chandel (Fig 5).
Species recovery in Jhum fallows
In Ukhrul, a distinct rise of 42.9% in the count of tree species was observed from 5 years fallow to 10 years fallow. It further increased by 3.3% in 15 years fallow and then remained stable up to 20 years fallow. Likewise in Chandel, the count of tree species increased by 4% from 5 years fallow to 10 years fallow and which was further enhanced by 11.5% in 15 years fallow and 6.9% in 20 years fallow. Hence, the percent recovery of tree species from 5 years fallow to 20 years fallow was 61.9% and 34.78% in Ukhrul and Chandel respectively.
Influence of topographical parameters on the species composition
ANOVA results showed that species richness increases significantly from the youngest to the oldest fallow in Ukhrul (F = 13.17, P<0.001) as well as in Chandel (F = 13.28, P<0.001). It was also observed that in Ukhrul, significant difference (F = 16.71, P<0.001 and F = 8.707, P<0.005) was observed in the 15 years fallow replicates of species richness and stem density as well as in the 10 years fallow replicates of stem density (F = 4.244, P<0.05). On the other hand, Chandel species richness was found to be significant among the replicates of 15 years fallow (F = 3.912, P<0.05) and none of the replicates were significant for stem density. Multiple regression results revealed that topographical factors such as slope, aspect and elevation, all had a significant impact on the species richness and stem density along an increasing fallow gradient (Table 4). This finding supports our proposed hypothesis that slope, aspect and elevation have a bearing on the species composition in successional areas.
Species affected by environmental variables
The contribution of environmental variables in the distribution and abundance of tree species along an increasing fallow gradient was determined by Canonical Correspondence Analysis (CCA). Fig 6A showed that the abundance of Toona ciliata M. Roem and Prunus ceraseidos D. Don were closely associated with the elevation of the sites in Ukhrul, while Pinus kesiya Royle ex Gordon and Toona ciliata M. Roem were associated with the slope. The fallow age as well as the aspect of the sites also influenced the abundance of Spondias pinnata (L. f.) Kurz and Terminalia citrine Roxb.ex Fleming. In Chandel, the species mostly associated with the slope and aspect of the sites were Dipterocarpus turbinatus C. F. Gaertn and Gmelina arborea Roxb. (Fig 6B). Species namely Cinnamomum zeylanicum Blume, Bauhinia purpurea L. and Spondias pinnata (L. f.)Kurz, Sapindus mukorossi Gaertn. were associated with the elevation and fallow age simultaneously.
(a) Ukhrul where Trace = 0.799 and p = 0.001. The axis 1 accounts for 68.6% and axis 2 accounts for 19.8% of the variability. (b) Chandel where Trace = 0.541 and p = 0.001. The axis 1 accounts for 77.3% and axis 2 accounts for 14.4% of the variability.
Potential species for restoration
ANOVA results showed that the species composition of tree seedling and sapling decreases significantly from the youngest to the oldest fallow in Ukhrul (F = 136.81, P<0.001) and Chandel (F = 134.84, P<0.001) while the pole and mature tree species composition increases from the youngest to the oldest fallow in Ukhrul (F = 28.63, P<0.001) and Chandel (F = 22.70, P<0.001) as well. Some species establishes rapidly after abandonment and continues to grow to mature trees in older fallows. One such species is Elaeocarpus floribundus Blume in Ukhrul (Fig 7) and Castanopsis hystrix Hook. f. & Thomson ex A. DC. in Chandel (Fig 8) (see S3 Table). The CCA triplots further showed that these species (ElaeFlor and CastHyst) were generalist species, that is, they appear opposite to the direction of increasing value of the environmental variables and its relation with the tree species. This testifies that the elevation, fallow age, slope and aspect of the sites have no influence on the abundance of Elaeocarpus floribundus Blume and Castanopsis hystrix Hook. f. & Thomson ex A. DC. in Ukhrul and Chandel respectively.
(i) seedling and sapling stage, and (ii) pole and mature stage in Ukhrul from 5 years, 10 years, 15 years and 20 years fallow following shifting cultivation and its relation with selected environmental variables. Full species names are shown in S4 Table.
(i) seedling and sapling stage, and (ii) pole and mature stage in Chandel from 5 years, 10 years, 15 years and 20 years fallow following shifting cultivation and its relation with selected environmental variables. Full species names are shown in S4 Table.
Tree above-ground biomass and total carbon stock
Seven common models for tropical forests were fitted to our data to test the performance of the models with respect to FSI equation [23] (Table 5). The adjusted R2 of all the regression models were identical while the lowest values of RMSE and MAD in model 7 verified it as the best model to predict AGB in our study. From the 79 tree species, the AGB of 37 species were evaluated using species specific allometric model given by FSI. For the remaining species, AGB was assessed by following the equation suggested by Nath et al. [29] (see S4 Table). Total living woody biomass carbon (AGBC+BGBC) ranged from 0.98 Mg ha-1 to 138.84 Mg ha-1 in Ukhrul and 2.5 Mg ha-1 to 142.58 Mg ha-1 in Chandel. The uncertainty percentage of TLWBC decreased from 78% to 9% in Ukhrul and 56% to 11% in Chandel with increasing fallow age (see S5 Table). The total carbon stock increased rapidly with increased time since abandonment (Fig 9). Pearson correlation analysis showed positive significant correlation for slope and aspect with TLWBC in Ukhrul (R = 0.78, P<0.001) while elevation was found to be significant for TLWBC in Chandel (R = 0.99, P<0.001).
Species contribution to carbon stock
The highest total living woody biomass carbon (TLWBC) in Ukhrul was contributed by Antidesma acidum Retz. in 5 years old fallow followed by Rhus chinensis Mill., Pinus kesiya Royle ex Gordon and Schima wallichii Choisy in 10, 15 and 20 years old fallow respectively. In Chandel, Toona ciliata M. Roem and Pinus kesiya Royle ex Gordon contributed the highest TLWBC in 5 and 15 years old fallow while Quercus serrata Murray contributed the highest TLWBC in 10 and 20 years old fallow (Table 6).
Factors affecting the recovery of carbon stock in fallow regime
The fallow age was found to have contributed the most to the recovery of carbon from living woody biomass in Ukhrul and Chandel as well (Table 7). It was also observed that the aspect of the sites in Ukhrul was important in explaining the increase in carbon stock. Although slope and elevation displayed a positive correlation with the carbon stock in Ukhrul and Chandel respectively, it did not influence the recovery of carbon stock in the Jhum fallows.
Recovery of carbon stock
The recovery percent of 20 years fallow in Ukhrul and Chandel was 39% and 40% of the control. Furthermore, based on the regional regression model between AGBC and fallow period, the estimated recovery period was found to be 41 years for Ukhrul and 39 years for Chandel (Table 8).
Discussion
Characteristics of secondary successive communities on Jhum fallows
The structure of secondary communities after the abandonment of Jhum fields generally becomes more complex as a result of species recovery. The findings of this study are in agreement with earlier studies which state that there is an increase in the number of trees with increase in fallow age [37]. The basal area is also considered as an essential predictor of ecological succession, and as reported from similar aged fallows in tropical moist forest, the present study also showed a positive association between basal area and fallow age [38, 39]. The values of the Shannon-Wiener diversity index (H') and the Margalef species richness index (Dmg) along an increasing fallow gradient indicates high diversity and species richness in the successive communities.
Species composition along an increasing fallow gradient
All species response individually to the process of succession, but the similarity of species among fallows is reported by many researchers. The species similarity between 5 year and 10 year fallow in Ukhrul, and 15 year and 20 year fallow in Chandel suggests that the species compositions of fallows having similar age are more identical than those with more differing ages [40, 41]. The fallows were predominantly composed of fast-growing pioneer and shade-tolerant tree species. Both pioneer and forest tree species got established in the young fallows and dominated at different stages of succession depending on their life span and growth rate [42].
Relationship between species composition and topographical parameters
In a hilly region, elevation, slope and aspect are considered as key topographical factors that strongly affect the species composition, structure and distribution patterns of vegetation [43]. Elevation affects the micro-climate in several ways and thus results in the variation of communities [44, 45]. In the present study, Chandel situated in lower elevation displays higher species richness and stem density than the Ukhrul site which concurs with the results of other workers [46, 47]. In the northern hemisphere, southern slopes are directly exposed to radiation while northern exposures are cold and humid which could sustain more tree species and stem density [48, 49]. With majority of the sampling sites facing north, our result showed significant relation between species richness and number of individuals along an increasing fallow gradient, identical to the findings of other studies [50, 51].
Recovery of Jhum fallows
The percent recovery of tree species from 5 years fallow to 20 years fallow was more in Ukhrul than in Chandel because the forest recovery increased with increasing elevation [52]. High altitude species have great potential to adapt to diverse micro-climatic situation as high elevation forests are generally open forests and therefore have more ability to recruit in the deforested areas [53]. In our study, five species in Ukhrul and eight species in Chandel were associated with the youngest fallow in the stage of seedlings and saplings, and survived as mature trees in the oldest fallow. Amongst all tree species, Elaeocarpus floribundus Blume and Castanopsis hystrix Hook. f. & Thomson ex A. DC. were independent of any environmental variables, and this suggests that they may be capable of effective restoration of degraded forest areas. These tree species can be considered as generalist species as they rapidly establish after abandonment and survive in dense forest. Since both the species occur naturally in wild, they can be utilized for active restoration to accelerate the recovery process of fallows.
Our result showed a positive relationship between the fallow period and the total living woody biomass carbon which is in accord with other works related to recovery following shifting cultivation in the tropical forests and neotropical secondary forests [54–56].
Sources of uncertainty
Generally uncertainty in carbon stock estimation arises mainly due to inventory protocol and method utilized to convert tree measurement to biomass. The latter can be quantified based on allometric equations or on biomass expansion factor. Conversion from tree volume to carbon content results in larger uncertainties as compared to the use of allometric models [57]. This explains the high uncertainty percentage in the present study.
Implications for management of Jhum fallows
Over the years, it is accepted that regrowth forests in the tropics provide similar ecosystem goods and services as old-growth forests [58]. This region however has been a huge contributor of greenhouse gas emission due to deforestation and adapting proper land-use system will help recover biomass carbon stock in the forests [59]. Tree plantation may be adapted to accelerate the steady process of natural succession in the fallows thereby restoring the species richness and enhancing the carbon sinks. And as per our findings, Elaeocarpus floribundus Blume and Castanopsis hystrix Hook. f. & Thomson ex A. DC. which occurs naturally in wild can be utilized as potential species for active restoration to accelerate the recovery process of fallows.
Conclusion
With the decrease in the pristine forests, secondary forests are of greater importance and value in the conservation and restoration of tropical biodiversity. Species richness and basal area recovered relatively with time since abandonment in our study, while the species composition recovery showed resemblance between similar-aged fallows. Topographical factors namely elevation, slope and aspect influenced the high species richness and stem density of fallows in Chandel than in Ukhrul. Regeneration fallow stands are considered to mitigate forest degradation and contribute to global carbon sequestration. We found that the fallow age plays a vital role in recovering aboveground biomass from living woody species followed by the aspect of the site. In this study, we identified two species which can be used in the active restoration of Jhum fallows and which colonize early fallows and appear naturally in the forests. The seedlings of these tree species can be collected from the surrounding forests or germinated and planted in Jhum fallows to accelerate natural succession. Tropical Amazonia had observed 90% survival in the transplantation of seedlings into fallows with partially established vegetation [60]. This would facilitate quicker rehabilitation and reinstate the soil nutrients making the soil reusable in a short term, such that the expansion of slashing and burning of primary forests for cultivation would be reduced. A gradual increase in the diversity of woody species along the fallow age evinces the potential of longer fallow forests to enhance carbon stock. Further, the results would help in formulating appropriate policy interventions on conservation strategies and developing climate change mitigation policies for efficient preservation of forest carbon stocks.
Supporting information
S1 Table. Tukey HSD multiple comparison between Jhum fallows with respect to environmental factors of Ukhrul and Chandel.
https://doi.org/10.1371/journal.pone.0239906.s001
(DOCX)
S2 Table. Density, basal area (m2 ha-1) and IVI of tree species in Jhum fallows.
https://doi.org/10.1371/journal.pone.0239906.s002
(DOCX)
S3 Table. Abundance of species in seedling and sapling stage and pole and mature stage after abandonment.
https://doi.org/10.1371/journal.pone.0239906.s003
(DOCX)
S4 Table. Allometric models used in the present study with species name in short.
https://doi.org/10.1371/journal.pone.0239906.s004
(DOCX)
S5 Table. Uncertainty percentage for the parameters of TLWBC in all fallow age.
https://doi.org/10.1371/journal.pone.0239906.s005
(DOCX)
Acknowledgments
The authors thank the Head of Department, Department of Forestry, Mizoram University for providing the necessary equipment for carrying out this work.
References
- 1. Brady NC. Alternatives to slash-and-burn: A global imperative. Agric Ecosyst Environ. 1996; 58:3–11.
- 2. Fearnside PM. Global warming and traditional land-use change: greenhouse gas emissions from biomass burning, decomposition and soils in forest conversion, shifting cultivation and secondary vegetation. Clim Change. 2000; 46:115–158.
- 3. Kotto-Same J, Woomer PL, Appolinaire M, Louis Z. Carbon dynamics in slash-and-burn agriculture and land use alternatives of the humid forest zone in Cameroon. Agric Ecosyst Environ. 1997; 809: 245–256.
- 4.
Ramakrishnan PS. Shifting agriculture and sustainable development: An interdisciplinary study from North-eastern India. UNESCO-MAP Series, Paris (republished by Oxford University Press, New Delhi, India).
- 5. Mertz O. The relationship between length of fallow and crop yields in shifting cultivation: a rethinking. Agrofor Syst. 2002; 55: 149–159.
- 6. Thong P, Pebam R, Sahoo UK. A geospatial approach to understand the dynamics of shifting cultivation in Champhai district of Mizoram, North-East India. J Indian Soc Remote. 2018; 46: 1713–1723.
- 7. Thong P, Sahoo UK, Pebam R, Thangjam U. Spatial and temporal dynamics of shifting cultivation in Manipur, North-East India based on time-series satellite data. Remote Sens App: Soc Environ. 2019; 14: 126–137.
- 8.
NRSC (National Remote Sensing Centre). Wasteland atlas of India. Indian Space Research Organisation. Hyderabad: India; 2010.
- 9. Jepsen MR. Above ground carbon stocks in tropical fallows, Sarawak, Malaysia. Forest Ecol Manag. 2006; 225: 287–295.
- 10. Chaturvedi AN. Management of secondary forests. Wasteland News.1992; 7: 40–44.
- 11. Heinimann A, Mertz O, Frolking S, Christensen AE, Hurni K, Sedano F, et al. A global view of shifting cultivation: recent, current and future extent. PLoS One. 2017; 12: 1–21.
- 12. Ferguson BG, Vandeermeer J, Morales H, Griffith DM. Post-agricultural succession in El-Petèn, Guatemela. Conserv Biol. 2001; 17: 818–828.
- 13. Thong P, Pebam R, Sahoo UK. Recovery pattern of vegetation during succession following slash and burn agriculture in Mizoram, North-East India. Journal of Plant Biology and Soil Health. 2016; 3: 1–8.
- 14. Brown SL, Schrooder P, Kern JS. Spatial distribution of biomass in forests of the eastern USA. Forest EcolManag. 1999; 123: 81–90.
- 15.
India State of Forest Report. Forest Survey of India. Dehradun: India; 2017.
- 16.
Mueller-Dombois D, Ellenberg H. Aims and methods of vegetation ecology. New York: USA; 1974.
- 17. Whitford PB. Distribution of woodland plants in relation to succession and clonal growth. Ecology. 1948; 30: 199–208.
- 18.
Shannon CE, Weaver W. The mathematical theory of communication. Urbana: USA; 1949.
- 19. Simpson EH. Measurement of diversity. Nature. 1949; 163: 688.
- 20.
Margalef R. Perspectives in ecological theory. Chicago: USA; 1968.
- 21. Whittaker RH. Vegetation of the Siskiyou Mountains, Oregon and California. Ecol Monogr. 1960; 30: 279–338.
- 22. Jaccard P. Comparative study of floral distribution in a portion of Alps and Jura. Bulletin de la Soci'et'eVaudoise des Sciences Naturelles. 1901; 37: 547–579. French.
- 23.
FSI (Forest Survey of India). Volume equations for forests of India, Nepal and Bhutan, Dehradun: India; 1996.
- 24. Zanne AE, Lopez-Gonzalez G, Coomes DS, Ilic J, Jansen S, Lewis SL, et al. Global wood density database; 2009.
- 25. Brown S, Gillespie AJR, Lugo AE. Biomass estimation methods for tropical forests with application to forest inventory data. For Sci. 1989; 35: 881–902.
- 26. Brown S, Iverson LR. Biomass estimates for tropical forests. World Resource Review. 1992; 4: 366–384.
- 27.
Brown S. Estimating biomass and biomass change in tropical forest. A primer. Forestry paper, Food and Agricultural Organizations of the United Nations. 1997; 134: 55.
- 28.
IPCC (Intergovernmental Panel on Climate Change). Good practice guidance for Land Use, Land-Use Change and Forestry. IPCC National Greenhouse Gas Inventories Programme. Hayama: Japan; 2003.
- 29. Nath AJ, Tiwari BK, Sileshi GW, Sahoo UK, Brahma B, Deb S, et al. Allometric models for estimation of forest biomass in northeast India. Forests. 2019; 10: 103.
- 30. Ali A, Xu M-S, Zhao Y-T, Zhang Q-Q, Zhou L-L, Yang X-D, et al. Allometric biomass equations for shrub and small tree species in subtropical China. Silva Fenn. 2015; 49: Article id 1275.
- 31. Hughes RF, Kauffman JB, Jaramillo-Luque VJ. Ecosystem-scale impacts of deforestation and land use in a humid tropical region of Mexico. Ecol Appl. 2000; 10: 515–527.
- 32. Mokany K, Raison RJ, Prokushkin AS. Critical analysis of root: shoot ratios in terrestrial biomes. Glob Change Biol. 2006; 12: 84–96.
- 33.
Higuchi N, Suwa R, Higuchi FG, Lima AJN, Santos Jdos, Noguchi H, et al. Overview of forest carbon stock study in Amazonas state, Brazil. In: Nagy L, Forsberg BR, Artaxo P, editors. Interactions between biosphere, atmosphere and human land use in the Amazon basin. Berlin Heidelberg: Springer-Verlag; 2016. pp. 171–187.
- 34. Mukul SA, Herbohn J, Firn J. Tropical secondary forests regenerating after shifting cultivation in the Philippines uplands are important carbon sinks. Sci Rep. 2016; 6: 22483 pmid:26951761
- 35. Waikhom AC, Nath AJ, Yadava PS. Aboveground biomass and carbon stock in the largest sacred grove of Manipur, Northeast India. J For Res. 2017;
- 36. Chambers JQ, Santos JD, Ribeiro RJ, Higuci N. Tree damage, allometric relationships, and above-ground net primary production in Central Amazon forest. For EcolManag. 2001; 152: 73–84.
- 37. Klanderud L, Mbolatiana HZH, Vololomboahangy MN, Radimbison MA, Roger E, Totland Ø, et al. Recovery of plant species richness and composition after slash-and-burn agriculture in tropical rainforest in Madagascar. Biodivers Conserv. 2010; 19: 187–204.
- 38. Lohbeck M, Poorter L, Paz H, Pla L, Breugel M.van, Martinez-Ramos M, et al. Functional diversity changes during tropical forest succession. Perspect Plant Ecol Evol Syst. 2012; 14: 89–96.
- 39. Kammesheidt K. The role of tree sprouts in the restoration of stand structure and species diversity in tropical moist forest after slash-and-burn agriculture in Eastern Paraguay. Plant Ecol. 1998; 139: 155–165.
- 40. Toledo M, Salick J. Secondary succession and indigenous management in semi deciduous forest fallows of the Amazon Basin. Biotropica. 2006; 38: 161–170.
- 41. Aweto AO. Secondary succession and soil fertility restoration in south-western Nigeria I, Succession. J Ecol. 1981; 69: 601–607.
- 42. Pena-Claros M. Change in forest structure and species composition during secondary forest succession in the Bolivian Amazon. Biotropica. 2003; 35: 450–461.
- 43. Titshall LW, O’Connor TG, Morris CD. Effect of long-term exclusion of fire and herbivory on the soils and vegetation of sour grassland. Afr J Range For Sci. 2000; 17: 70–80.
- 44. Kikvidze Z, Khetsuriani L, Kikodze D, Callaway RM. Seasonal shifts in competition and facilitation in subalpine plant communities of the central Caucasus. J Veg Sci.2006; 17: 77–82.
- 45. Vittoz P, Bayfield N, Brooker R, Elston DA, Duff EI, Theurillat JP, et al. Reproducibility of species lists, visual cover estimates and frequency methods for recording high-mountain vegetation. J Veg Sci. 2010; 21: 1035–1047.
- 46. Kӧrner C. Why are there global gradient in species richness? Mountains might hold the answer. Trends EcolEvol. 2000; 15: 513–514.
- 47. Odland A, Birks HJB. The altitudinal gradient of vascular plant richness in Aurland, Western Norway. Ecography. 1999; 22: 548–566.
- 48.
Geiger R, Aron RH, Todhunter P. The climate near the ground. 6th ed. Maryland: USA; 2003.
- 49. Maren IE, Karki S, Prajapati C, Yadav RK, Shretha BB. Facing north or south: Does slope aspect impact forest stand characteristics and soil properties in a semiarid trans-Himalayan Valley?.J Arid Environ. 2015; 121: 112–123.
- 50. Lovett JC, Marshall AR, Carr J. Changes in tropical forest vegetation along an altitudinal gradient in the Udzungwa Mountains National Park, Tanzania. Afr J Ecol. 2006; 44: 478–490.
- 51. Zhang JT, Zhang F. Diversity and composition of plant functional groups in mountain forests of the Lishan Nature Reserve, North China. Botanical Studies. 2007; 48: 339–348.
- 52. Lippok D, Beck SG, Renison D, Gallegos SC, Saavedra FV, Hensen I, et al. Forest recovery of areas deforested by fire increases with elevation in the tropical Andes. Forest Ecol Manag. 2013; 295: 69–76.
- 53. Homeier J, Breckle SW, Günter S, Rollenbeck RT, Leuschner C. Tree diversity, forest structure and productivity along altitudinal and topographical gradients in a species-rich Ecuadorian montane rain forest. Biotropica. 2010; 42: 140–148.
- 54. Pelletier J, Codjia C, Potvin C. Traditional shifting agriculture: Tracking forest carbon stock and biodiversity through time in Western Panama. Glob Change Biol. 2012; 18: 3581–3595.
- 55. Chan N, Takeda S, Suzuki R, Yamamoto S. Assessment of biomass recovery and soil carbon storage of fallow forests after swidden cultivation in the Bago Mountains, Myanmar. New For. 2016; 47: 565–585.
- 56. Poorter L, Bongers F, Aide TM, Zambrano AMA, Balvanera P, Becknell , et al. Biomass resilience of Neotropical secondary forests. Nature. 2016; 530: 211–214. pmid:26840632
- 57. Njana MA. Indirect methods of tree biomass estimation and their uncertainties. S For J For Sci. 2017; 79: 41–49.
- 58. Bonner MTL, Schmidt S, Shoo LP. A meta-analytical global comparison of aboveground biomass accumulation between tropical secondary forests and monoculture plantations. Forest Ecol Manag. 2013; 291: 73–86.
- 59. Budiharta S, Meijaard E, Erskine PD, Rondinini C, Pacifici M, Wilson KA. (2014). Restoring degraded tropical forests for carbon and biodiversity. Environ Res Lett. 2014; 9: 114020.
- 60. Uhl C. Factors controlling succession following slash-and-burn agriculture in Amazonia. J Ecol. 1987; 75: 337–407.