Keywords
Forest Farm Interface, Biomass Carbon, Soil Organic Carbon, Litter
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Forest Farm Interface, Biomass Carbon, Soil Organic Carbon, Litter
Forests and forest management have changed greatly over the past two decades. In 1990, the world had 4.13 billion hectares (ha) of forests (31.6% of total land area of Earth). However, according to the Food and Agriculture Organization of the United Nations, by 2015 this area has decreased to 3.99 billion ha (30.6% of total land area of Earth) (FAO, 2015). This caused a net loss of 129 million ha of forests (natural and planted) from 1990 to 2015. However, the net annual rate of loss has reduced from 0.18% in the 1990 to 0.08% in 2015. The net annual natural forest loss between 1990 to 2000 was 8.5 million ha per year; however, from 2010 to 2015, natural forest decreased by a net of 6.6 million ha per year (8.8 million ha of loss and 2.2 million ha of gain). This resulted in a reduction of 697 million mega tons per year or about 2.5 gigaton (GT) of carbon dioxide (CO2) for the past 25 years (FAO, 2015). The world forest assessment in 2015 also indicated that world’s forests store an estimated 296 GT of carbon in both aboveground and belowground biomass (FAO, 2015).
Ethiopia has a wide range of ecological conditions ranging from the arid lowland in the East to high altitudes in the central high lands (Hurni, 1998). This wide range of ecological conditions coupled with the corresponding heterogeneous flora and fauna has made the country one of the internationally recognized major centers for biodiversity (Scholte, 2012). However, through time to time, there has been a dramatic decline in forested area in the country. Accordingly, from 1990 to 2000 and from 2000 to 2010, forest losses were estimated at 8.3 million ha and 5.2 million ha respectively (Eshetu, 2014). These days major parts of the remaining natural forests which harbor high biodiversity are located on steep slopes at high altitude and in the remote southern and southwestern parts of the country. These few remaining high forests are also threatened by anthropogenic activities and converted to agricultural and other land use systems (Abere, 2011). Similarly, other remaining natural forests have also been threatened by pressure from investors and changed to industrial plantation like coffee and tea (Abere, 2011; Moges et al., 2010). This reduction and conversion of natural forest to other land use systems in many parts of Ethiopia has led to the decline in number and distribution of many plant species, shortage of raw materials for wood processing industries and disturbance of ecosystem services (Lemenih & Kassa, 2014). Subsequently, it has resulted the expansion of forest farm interface in and around the forest ecosystem.
“For this study forest farm interface is defined as a complex geographic and temporal mosaic landscape of integrated management and production practices that combine agriculture, forest and livestock land uses and formed from shifting of forest land uses by smallholder farmers and /or investors. The interface is not a discrete line separating farms and forests.” (CIFOR, 2017)
For the past five decades, the government of Ethiopia has attempted to reforest degraded forests. Hundreds of aid projects have been implemented in different parts of the country to reverse deforestation and forest degradation in the country. However, the success stories were below expectations and the problems are still immense. This resulted from the lack of effective management practices and quantification of the available forest resources. This insufficiency of scientific quantitative data brought lack of responsiveness for sound management of natural resources in the country.
Gura-Ferda forest is one of the Afromontane rainforests in the southwestern region of Ethiopia and grows at altitudes from 700 to 2,300 meter above sea level. This forest area is one of the areas in Ethiopia where traditional beliefs and ecological knowledge have assisted the conservation of forests up to now. During the past decades, especially since 1984, large parts of this forest have progressively been disturbed and fragmented due to forest conversion to settlements, agriculture, and industrial plantation (Schmitt et al., 2010). Nowadays, pressure produced by immigration and investors is increasing forest disturbance. However, there is no quantitative information on the change of species diversity and carbon stocks resulting from the conversion of natural forests to forest farm interface and farmlands. The overall objective of this study was, therefore, to analyze the woody species diversity and carbon stock change in association with the change of natural forests to forest farm interface and farmlands. The study hypothesized that, the conversion of natural forests to forest farm interface and farmlands affect the woody species diversity, biomass and soil organic carbon (SOC) stocks.
The study was conducted at Gura-Ferda district of southwestern Ethiopia which is located at 603 km southwest of the capital city Addis Ababa (Figure 1). Geographically, it is positioned between 6°29’12” N and 7°13’22” N latitude and 34°52’23” E and 35°23’59” E longitude. The area coverage of this district is estimated to be 2565.42 km2. The annual average rainfall over the period of 1983–2012 was 1639.8 mm, with a maximum of 1946.3 mm and a minimum of 1289.8mm. The area receives a maximum rainfall in October and minimum rainfall in February. The average annual temperature is 23.4°C with a range from 16.1°C-30.6°C. The dominant soil type of the study area is nitisols with soil textural class loam to clay (Dewitte et al., 2013).
As the past data of the Gura-Ferda district specified, since 1984, there was a degradation of natural forest in the area (Table 1). The notable drivers of this forest area decrement were resettlement, crop investment and fuel wood. According to the office of Gura-Ferda district, in 1984, the populations of the district were 149. However, in 2016 they were increased to 45,028 (GFDAO, 2016). Moreover, during 2003/4 legal resettlement, massive deforestation of natural forest were accompanied for house construction of immigrates (Abere, 2011; Gessese, 2018). Next to resettlement, the taken up of forest by investors is other key drivers for the degradation and deforestation of natural forests in the area. According to (GFDAO, 2016), there were more than 30 investors who were involved in different agricultural investment especially coffee and rubber tree plantation. These investors had been used shrub land, natural forest, and grass lands for investment.
For the purpose of this research both primary and secondary data were employed. Primary data were obtained through field survey of the study area. Secondary data used were satellite images and publications such as articles, data from district land administration offices and censuses results. Multi-sensor and multi-temporal Landsat images were downloaded from United States Geological Survey (USGS) (https://earthexplorer.usgs.gov) (Table 2). Accordingly, satellite images of 1984 and 2016 were used for this study. Images of the year 1984 were taken because it was the time when the government organized a resettlement program at the study area. Similarly, images from the year 2016 was selected because it was the time when recent agricultural systems were expanded and government was focused on commercial investments in the area. Since it is a time of free atmospheric cloud, satellite images in the months of December to January were used.
Acquisition date | Path/Row | Cloud cover (%) | Sensor type | Spatial resolution (m) | LU/LCC related events |
---|---|---|---|---|---|
28/12/1984 | 170/055 | 0.0 | TM | 30x30 | Government Organized Resettlement Program |
26/12/2016 | 171/055 | 0.0 | OLI/TIRS | 30x30** | Recent Agricultural Expansion and focusing of government on commercial investments |
Before the resettlement program of 1984, all areas used for the sampling unit in this study time were covered by forest. However, nowadays, it is observed that the area has three discrete categories. These are: natural forest, forest farm interface and farmland (Figure 2; Figure 3).
Natural forest (NF): a landform consisting of trees, shrubs and other vegetation that originally emerged on its own without the influence or direct intervention of man and found adjacent to FFI.
Forest-farm interface (FFI): a neither agriculture nor forest mosaic landscape of integrated management and production practices which is typically used by smallholder farmers/investors and found between natural forest and farmlands (find full definition in the introduction).
Farmland (FL): an area which has been converted to intensive mono cropping with few/no scattered trees due to high disturbance and adjacent to FFI.
Field level data was collected from NF, FFI and FL which are adjacent to each other and historically forest land before 1984. With the help of a compass and Geographic Positioning System (GPS), three transects with a total of 30 plots (10 plots on each transect) were established for each land use system. Transect lines and samples plots were laid by a gap of 200m from each other (Figure 4). The sample plot size was determined based on expected density of woody species in each land use system (Tadesse et al., 2014; Tolera et al., 2008). Accordingly, for both NF and FFI a nested plot design of 400m2 with 25m2 and 1m2 size was used to collect vegetation data (tree, sapling and seedling respectively). In each of the quadrat (1m*1m), a number of all seedlings that have eight ≤ 50 cm and diameter at breast height (DBH) ≤ 2.5cm were recorded. Individuals attaining height > 50cm and DBH ≤ 2.5 cm were considered as sapling and counted. In the 400m2 sample plots, the diameter and height of all woody species ≥ 5cm DBH were measured. As per density and distribution of woody species is lower, plot size of 50 m x 100 m was used for FL (UNFCCC, 2015).
DBH of sampled dead wood was measured following the techniques used by Pearson et al. (2005) and UNFCCC (2015). A complete list of woody species was made for each plot throughout the whole area and documented by local name. Species identification for common species was done in the field via different plant identification keys. However, for the less common species plant sample specimens were pressed and identified at the National Herbarium of Ethiopia, Addis Ababa University. Litter samples were collected from 1 m x 1 m subplot within the main plot. The collected fresh litter was weighed right on the site. Then the evenly mixed samples were taken to the laboratory and oven dried at 65ºC for 24 hours to determine dry to fresh weight ratio. Soil samples were collected from the sub-plots used for litter sampling. Two sets of soil samples were taken, one set for the determination of organic carbon fraction (%C), and one set for the determination of soil bulk density. A total of 90 soil samples (layers of 0–30 and 30–60 cm) were collected for %C analysis using soil auger. In addition, similar size of undisturbed soil samples were collected separately for determination of soil bulk density.
Diversity analysis. Shannon-Wiener index (H`) was used to determine diversity of woody species of the study area. H` was determined through the analysis of two components of species diversity. These are the species richness (the number of species in the sample plots) and evenness of species (abundance distribution among species).
Where pi, is the proportion of individuals found in the ith species
Beta diversity (β) which measures the change in the diversity of species among a set of land uses is determined using the formula provided by Whittaker (1972).
Where a, is the number of shared species in two land uses, and b and c are the numbers of species unique to each land use.
Allometric equation developed by Chave et al. (2014) was used for estimating the aboveground biomass of woody species in NF (Table 3). Biomass of standing dead wood which has branches was also estimated using this allometric equation. This equation was selected since it was established for estimating the biomass of woody species in tropical natural forests. Moreover, this equation used diameter at breast height and wood density which was the most important biomass predictor variables. The biomass of woody species in FFI and FL was estimated using allometric equation developed by Kuyah et al. (2012a); Kuyah et al. (2012b) since it was developed for land use systems having more or less similar climatic properties as those in the current study area. Woody density was taken from the document of Ethiopia’s fForest reference level submission to the United Nation Framework Convention on Climate Change (UNFCCC) (EFRLS, 2016).
Land Use | Equation | R2 | D (cm) | % C | Source | |
---|---|---|---|---|---|---|
Natural Forest | Woody species | AGB = ρ × d2 × H × 0.0559 BGB = 0.20 × AGB | - - | ≥5 ≥5 | 50 50 | (Chave et al., 2014) (IPCC, 2006) |
Forest Farm Interface | Woody species | AGB = 0.225 × d2.341 × ρ0.73 BGB = 0.28 × AGB | 0.98 - | ≥5 ≥5 | 48 48 | (Kuyah et al., 2012a) (Kuyah et al., 2012b) |
Farmlands | Woody species | AGB = 0.225 × d2.341 × ρ0.73 BGB = 0.28 × AGB | 0.80 - | ≥5 ≥5 | 48 48 | (Kuyah et al., 2012a) (Kuyah et al., 2012b) |
Aboveground biomass of standing dead wood which has no leaves was estimated following the procedure used by Pearson et al. (2005). The biomass of felled dead wood was estimated using allometric equation developed by Grais & Casarim (2013). The total biomass of the dead wood was estimated by summing up of the standing, logged and felled dead wood. Finally, estimated biomass of woody tree species in NF, FFI and FL were converted to carbon (C) stock using carbon fraction value of 0.5, 0.48, and 0.48 respectively (IPCC, 2006; Kuyah et al., 2012a). The loss on ignition method was used to estimate percentage of organic matter in the litter. The amount of C in the litter was estimated through multiplying of litter organic matter by 0.50 (Pearson et al., 2007).
Soil organic carbon stock estimation. Soil analyses were undertaken at Wondo Genet College of Forestry and Natural Resources soil laboratory. The soil samples for bulk density were oven-dried at 105 °C for 48 hours. Bulk density was estimated by the core method (Blake & Hartge, 1986). The soil samples for %C were air –dried and analyzed using Walkley-Black method (Schnitzer, 1982). A SOC stock (Mg C ha-1) was calculated by multiplying of %C, bulk density (g/cm3) and soil depth (cm)).
Total carbon stocks. Total C stock (Mg C ha-1) was calculated by summing up of biomass C stocks (above-and-below) and SOC stocks.
C stock of the three land uses were compared using one-way ANOVA and two-way ANOVA. All data were checked for normality prior to doing the analysis of variance using Kolmogorov-Smirnov test. The data were analyzed using Statistical Package for Social Science (SPSS version 20). All tests were conducted at 95% confidence level.
A total of 59, 24 and 19 woody species belonging to 34 families were recorded and identified in the sample plots of Gura-Ferda NF, FFI, and FL respectively (Table 4). Among these woody species, Moraceae, Rubiaceae and Sapotaceae were the richest family all represented by six species (8.82%) of total floristic composition. The remaining families represented less than 3% of species each.
Land use | Species richness | Shannon ('H) | Evenness (J) |
---|---|---|---|
Natural forest | 59 | 3.33 | 0.82 |
Forest-Farm interface | 24 | 1.57 | 0.49 |
Farm land | 19 | 1.42 | 0.48 |
The overall mean H’, species richness and evenness of NF were 3.33, 59 and 0.82 respectively. FFI enriched with 24 woody species has an overall mean H’ of 1.57. The results of H’ and evenness indices indicated a difference in species diversity and evenness among the land uses. NF is relatively the most diversified one followed by FFI. Relatively, highest evenness was exhibited by NF followed by FFI (Table 4).
Sorensen’s similarity coefficient indicated the highest floristic similarity was found between NF and FFI (0.51) followed by FFI and FL (0.37). The magnitude of beta diversity indicates the change in woody species composition between adjacent land uses along the land use changes. The highest change in woody species diversity was observed between the changes from NF to FL (0.67) followed by FFI to FL (0.63) (Table 5). Cordia africana, Croton macrostachyus and Lepidotrichlea volkensi were some of common woody species in all land uses.
Land Uses | Natural Forest | Forest Farm Interface | Farmland |
---|---|---|---|
Natural Forest | 1 | 0.51 (0.49) | 0.33 (0.67) |
Forest Farm Interface | 0.51 (0.49) | 1 | 0.37 (0.63) |
Farmland | 0.33 (0.67) | 0.37 (0.63) | 1 |
The basal area of woody species in NF (54.31±2.95 m2ha-1) was 2.3 and 4.1 times higher than FFI (26.66±2.28 m2ha-1) and FL (6.12±0.37 m2ha-1) respectively. The density of woody species ≥ 5cm DBH in the study area was 746±15.25 individuals per hectare for NF, 876±120 individuals per hectare for FFI and 158±6.9 individuals per hectare for FL.
The mean aboveground biomass (tree/shrub, dead wood and litter) C stocks of FFI (99.63± 9.72 Mg C ha-1) are significantly lower than the adjacent NF (134.40± 10.09 Mg C ha-1), but higher than that of FL (16.80± 1.18 Mg C ha-1). The mean aboveground biomass C stocks of NF were approximately 2.24 and 8.47 times higher than FFI and FL. The mean overall dead wood C stock of the study area was 2.3 ± 1.51 Mg C ha-1 for NF and 9 ± 2.56 Mg C ha-1 for FFI (Table 6). The mean litter biomass for aboveground biomass was 1.29 ±0.14 Mg C ha-1 for natural forest and 0.88 ±0.06 Mg C ha-1 for forest farm interface.
A belowground biomass C stock in the NF was significantly higher (p< 0.001) than the belowground biomass C stocks of FFI and FL (Table 6). The mean belowground biomass C stocks in the NF, FFI and FL were 26.16±2.02 Mg C ha-1, 17.95±1.94 Mg C ha-1 and 3.36±0.23 Mg C ha-1 respectively. The total biomass C stocks in NF was by 7.73% and 38.84% higher than FFI and FL. Cash generating coffee ≥2.5 DBH shared 0.5% and 2.3% of the total biomass C stocks in NF and FFI respectively. The contribution of litter for total biomass C in both NF and FFI was 1%.
Within each land use, SOC stock was significantly higher (p<0.001) in the top layer (0–30cm) than in the lower layer (30–60 cm) (Table 7). The top layer stocked 57.84%, 54.76% and 56.98 of the total SOC in the NF, FFI and FL respectively. The total SOC stocks (0–60 cm depth) were significantly different among all land uses. SOC stock significantly differs along depths for all land uses. With respect to conversion of NF to FFI, 5.78% of SOC stocks (0–60 cm) were lost. Similarly, 21.82% of SOC stocks (0–60 cm) were lost in conversion of the NF to the FL.
Depth, cm | Natural Forest | Forest Farm interface | Farm Land |
---|---|---|---|
0 – 30 cm | 128.65± 17.66 | 108.47± 22.87 | 74.45±15.90 |
30 – 60 cm | 93.77± 11.55 | 89.62±23.13 | 56.21±8.68 |
Total (0 – 60 cm) | 222.42±21.89c | 198.09±36.18b | 130.66±21.01a |
The total C stock of the study area was calculated by summing up all the C value of each pool. Accordingly, the total C stock (Mg C ha-1) is significantly different among the three-land uses. The total C stock in NF was 382.97 ± 50.8 Mg C ha-1. While the total C stocks for FFI and FL were 315.68 ± 30.5 Mg C ha-1 and 150.76 ± 7.6 Mg C ha-1 respectively (Table 8). Of which, the SOC accounted for 58.07%, 62.75 and 86.63% for NF, FFI and FL, respectively. The total C stock of NF was approximately 1.21 and 2.54 times higher than that of FFI and FL.
Land use | Mean (±SE) | ||
---|---|---|---|
Total Biomass Carbon | SOC (0–60 cm) | Total Carbon Stocks | |
NF | 160.57±12.01 | 222.4 ±5.6 | 382.97 ± 50.8c |
FFI | 117.58±11.88 | 198.1 ± 9.3 | 315.68 ± 30.5b |
FL | 20.16±1.36 | 130.6 ± 5.4 | 150.76 ± 7.6a |
Gura-Ferda forest is among the most degraded and deforested forest in southwestern region of Ethiopia. A change in NF to FFI and FL are the major threats to forest woody species diversity. In association with the conversion of natural forest to forest farm interface more than 17 species are lost. While, in connotation with the conversion of NF to FL, more than 33 species are lost. More specifically, Sapotaceae, Moraceae, and Rubiaceae which are the dominant families in NF of this study area are the most threatened families as a result of the conversion of NF to FFI and FL. Almost all woody species recorded in the FFI and FL were not planted rather they were the remnants of trees and shrubs during conversion of NF to FFI and FL.
The observed lowered H’ in FFI and FL in Gura-Ferda district is directly attributed by conversion of NF to coffee farms and indirectly by population growth, colonization of previously uncultivated land by subsistence crops and the expansion of settlements. As shown in Table (1), FFI which emerged after the resettlement program of 1984 accounts for 23.28% of the NF within 1984–2016-year interval. As reported by Gessese (2018), and GFDAO (2016) the main problem related to land use land cover change at Gura-Ferda district was agricultural investment, fuel wood collection, wood for house construction and farm implementation, wildfire, resettlement, land certification, poor governance within the district, and subsistence agricultural land expansion.
According to a Gura-Ferda district land administration report, large areas of extra land were recorded for each farmer. The farmers had expanded their farmland into nearby forest, shrub/bush land and grass land and used those land uses for commercial crop production. Therefore, this increment of unregistered or unplanned farms and FL resulted from above mentioned drivers are the main causes for the loss of woody species diversity in the study area.
The main reason for the lower woody species diversity in FFI in relation to NF in the study area is due to the application of intensive thinning of different woody species in the system in order to reduce shading effect. (Gole, 2003) also reported that, managing forest for coffee production has resulted in significant changes in species diversity, composition and vegetation structure in coffee forests of southwestern Ethiopia. The number of woody species recorded in Gura-Ferda NF is comparable to the Komba-Daga moist evergreen forest in southwestern Ethiopia (62 woody species) (Geneme et al., 2015). For instance, the number of woody species recorded in the Gura-Ferda NF of the current study area is substantially higher than those reported for Agama tropical Afromontane forest of Ethiopia (39 woody species) (Addi et al., 2016). However, the number of woody species in the current studied NF is lower than the woody species recorded for Wondo Genet Afromontane forest in the central highlands of Ethiopia (72 woody species) (Kebede et al., 2013).
Our results also indicated that, the woody species richness in FFI of the current study is comparatively lower than woody of species in agroforestry system of south-central and southern highlands of Ethiopia (Asfaw, 2003; Seta & Demissew, 2017). Since maximizing coffee production is the main goal, most of the native trees have been cleared by cultivators and few shade plant species are retained in highly populated coffee shrubs.
The study showed how C stocks in biomass and soils were varied across different land use systems. NF had higher biomass C stocks compared to FFI and that of the FL. Rajput et al. (2017) and Solomon et al. (2018) reported higher biomass C in forest land use system as compared to other land cover types in northwestern Himalaya and northern Ethiopia, respectively. From the studied land use systems of this area, most of the C was stocked in NF. FFI and FL biomass C stocks were 7.73% and 38.84% lower than the C stocks in the NF. The accumulation of high C stock in NF was attributed by the presence of diversified woody species in the NF in comparison with FFI and FL. Additionally, the NF has found to accumulate larger aboveground biomass in the litter compared with that of FFI. This result is in line with the result of Solomon et al. (2018) which stated that tree density, diversity and diameter have an effect on biomass C.
Case studies have showed as different land use systems stocked different amounts of C in their biomass component. Accordingly, the biomass C stocks recorded in the NF of the current study area is substantially lower than the biomass C stocks of Adaba-Dodola community forest, southeastern Ethiopia (Bazezew et al., 2015). The biomass C stocks of NF of the current study area was approximately three times lower than the biomass C stocks reported for woody plants of Mount Zequalla Monastery in Ethiopia (Girma et al., 2014). Similarly, the biomass C stocks of FFI in this study was higher than that of the coffee based agroforestry system in Gera, Jimma Zone, South-West Ethiopia (Mohammed & Bekele, 2014). The difference in biomass C stocks might be due to various factors such as difference in diversity of trees (woody and non woody) of larger sizes, the used allometric equation, soil condition and climate factors. For instance, in the coffee based agroforestry system studied by Mohammed & Bekele (2014), trees aboveground biomass was determined using Brown et al. (1989) allometric equations. But, for this study, the generic equation developed by Chave et al. (2014) and Kuyah et al. (2012a) were used for woody tree species. The biomass C stocks of the FFI of the current study area was relatively equivalent with the total biomass C stocks of fruit coffee system of indigenous agroforestry systems of the south-eastern Rift Valley escarpment, Ethiopia (Negash & Starr, 2015).
The average mean above ground biomass C stock of the FFI was higher than the mean biomass C stocks of organic polyculture coffee, non-organic polyculture coffee and organic Inga species in Chiapas, Mexico (Soto-Pinto & Aguirre-Dávila, 2014). The variability among these systems in this respect might be because of differences in species composition, site characteristics, management practices, land holding sizes, ancillary factors (e.g. soil condition, climate, system age, land-use history), and adopted allometric model for biomass estimation (Montagnini & Nair, 2004).
Concentrations of SOC decreased with an increment of depth in all NF, FFI and FL. The highest SOC stock in the NF might be attributed to the lower organic carbon turnover rate as a result of minimum soil disturbance in the system, and more litter fall inputs from different wood tree species. While in the FFI, common intensive management practices like cleaning, weeding, burning and relocation of biomass might influence accumulation of litter carbon. It was in agreement with results by Aticho (2013) who claimed the diminishing trend of SOC content with depth in his study in Kafa, Southwest Ethiopia. Yimer et al. (2015) also observed a declining trend in SOC concentration with depth in the Central Rift Valley area of Ethiopia.
The total SOC stocks at soil depth for the three land use systems in this study were within the range of SOC stocks reported for other similar systems in Ethiopia (Gebeyehu et al., 2017). The upper layer (0–30 cm depth) SOC stock of FFI in this study area was higher than the mean SOC (65.2 Mg C ha-1) of Nitisol soil under agroforestry systems in Ethiopia (Gebeyehu et al., 2017). The result of SOC in 0–30 systems cm depth in FFI was also higher than the 0–30 cm depth SOC recorded in Gununo watershed agroforestry practices (Bajigo et al., 2015), and 0–30 cm depth SOC (60.8 Mg C ha-1) of Indonesia homegarden agroforestry system (Roshetko et al., 2002).
The results indicate that 5.78 % and 21.82% of SOC stocks (0–60 cm) were lost in conversion of the NF to the FFI and FL respectively within 33 years. Another meta-analysis of Wei et al. (2014) found that SOC decreased by 44.5% following conversion from a NF to a crop field. Yimer et al. (2007) also found that SOC decreased by 30.9% after 15 years of deforestation in the Bale Mountains of Ethiopia.
FFI in the southwestern part of Ethiopia plays an important role in maintaining more woody species and sinks of C. The higher contribution of NF to climate change mitigation is mainly due to the higher diversity and density of larger woody species in the system as compared to the adjacent FFI and FL. Trees in particular play substantial roles for enhancing biomass C stocks in forests and any other land use systems. However, the increment of FL found adjacent to the NF and FFI showed a lower role of biodiversity conservation and C stock. This shows that sustainability of the system is questionable. If the NF is not sustainably managed and certification of land is not carried out in the area, there will be expansion of FFI and FL which will cause further deforestation and forest degradation. Therefore, it needs to recognize FFI as part of climate change mitigation strategies, as it can also provide much benefit to the community and a potential to reduce pressure on adjacent NF.
Zenodo: Conversion of Natural Forests to Farmlands and Its Associated Woody Species Diversity and Carbon Stocks in a Span of 33 Years (1984 To 2016): In the Case of Southwestern Ethiopia, http://doi.org/10.5281/zenodo.4601418 (Betemariyam et al., 2021).
This project contains the following underlying data:
Average DBH and Height per Plot.xlsx
Processed data of SOC.xlsx
Processed data of TBC.xlsx
Processed Data of Woody Species Diversity.xlsx
Data are available under the terms of the Creative Commons Attribution 4.0 International license (CC-BY 4.0).
We acknowledge the logistic and technical support we got from Wondo Genet College of Forestry and Natural Resources Soil Laboratory, Hawassa University. We sincerely thank the farmers of the study area for their kindness and enthusiasm to talk to us and for allowing us to take measurements on their farms. Our gratitude goes to experts at National Herbarium of Ethiopia, Addis Ababa University, for their generous support on species identification that makes our research very fruitful.
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Is the work clearly and accurately presented and does it cite the current literature?
Partly
Is the study design appropriate and is the work technically sound?
Yes
Are sufficient details of methods and analysis provided to allow replication by others?
Yes
If applicable, is the statistical analysis and its interpretation appropriate?
Yes
Are all the source data underlying the results available to ensure full reproducibility?
Partly
Are the conclusions drawn adequately supported by the results?
Partly
References
1. Gifford R, Roderick M: Soil carbon stocks and bulk density: spatial or cumulative mass coordinates as a basis of expression?. Global Change Biology. 2003; 9 (11): 1507-1514 Publisher Full TextCompeting Interests: No competing interests were disclosed.
Reviewer Expertise: Wetlands ecology and greenhouse gas monitoring
Is the work clearly and accurately presented and does it cite the current literature?
Partly
Is the study design appropriate and is the work technically sound?
No
Are sufficient details of methods and analysis provided to allow replication by others?
No
If applicable, is the statistical analysis and its interpretation appropriate?
No
Are all the source data underlying the results available to ensure full reproducibility?
Partly
Are the conclusions drawn adequately supported by the results?
Partly
Competing Interests: No competing interests were disclosed.
Reviewer Expertise: My broad-scale research interests are in the area of forest or plant ecology, particularly related to multiple abiotic and biotic controls on ecosystem functions and processes.
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