Soil organic carbon stock and retention rate among land uses along Didessa toposequence in humid Western Ethiopia
Environmental Systems Research volume 9, Article number: 34 (2020)
There is scarcity of scientific information on stocks and retention rate of soil organic carbon (SOC) among mixed farming systems in humid Western Ethiopia. The objectives of study were to determine the SOC stocks and retention rates along a 53-km long toposequence of Didessa watershed. The study was conducted in mixed farming systems (annual arable cropping, grazing, fallow, grassland, coffee agroforestry, eucalyptus agroforestry and mechanized irrigated sugarcane production) within an elevation range of 1273 to 2543 m above sea level.
The results revealed that land use types greatly affected SOC stocks and retention rates in the upper 20 cm soil depth. The SOC stocks ranged from 9.27 to 13.5 Mg C ha−1 (0–20 cm) while the retention rates were 0.11, 0.20, 0.28, 0.31 and 1.14 Mg C ha−1 year−1 for coffee agroforestry, fallow, grazing, eucalyptus agroforestry and irrigated sugarcane production systems, respectively.
The retention rates demonstrated that the different farming systems are potential source of C sinks. The study indicated that the farming systems are efficient in sequestering SOC and their benefits can be further adopted for their economic values, social significance, restoration of degraded land, and sequestration of carbon (C) in humid tropical Western Ethiopia.
Emission of CO2 since the industrial revolution of 1750 and land use change have increased the amount of atmospheric carbon (C) by 31% (ESA 2000; Lal 2004a). The soil system is the largest reservoir of C pool which is 3.3 times the size of atmospheric C and 4.5 times the size of biotic C pool (Lal 2005, 2006). African soils have an estimated soil organic carbon (SOC) stock of 166,397 × 106 tons (0–100 cm). This corresponds to 9% of the global SOC stocks and 68% of the terrestrial C pool of Africa (Henry et al. 2009). Ethiopia has an estimated SOC stock of 6459 × 106 tons (0–100 cm) and it is the third largest SOC stocks in East Africa next to Tanzania and Zambia (Henry et al. 2009). However, conversion of natural ecosystem to agriculture in the tropics could cause loss of 75% or more of SOC (Lal 2005). Increased global C storage through sequestration into aboveground terrestrial biome and belowground stocks are feasible methods for reducing CO2 concentration in the atmosphere (ESA 2000; Lal 2004a, 2005). Global agricultural and degraded soils have high C sink capacity which could be in the order of 50 to 66% of 42 to 78 gigatons (Gt) of the historic C lost to atmosphere (Lal 2005). Soils of African continent have an estimated 30% of total global C sequestration potentials (Henry et al. 2009). The SOC sequestration has the potential to increase agricultural production and reduce CO2 concentration in the atmosphere (ESA 2000; Lal 2004b).
Topography and climate vary along landscape positions and affect SOC sequestration capacity of terrestrial ecosystems. Several studies in Ethiopia have been carried out to quantify effect of vegetation, land uses and climate on SOC concentrations (Wakene 2001; Dawit et al. 2002; Lemeniha and Itanna 2004; Abraha et al. 2012; Kilic et al. 2012; Achalu et al. 2013; Nega and Heluf 2013; Getahun and Bobe, 2015). They compared the effect of conversion of native vegetation to agricultural land uses and reported higher SOC concentration from forests and grasslands compared to arable cropping and grazing land uses. However, they could not make any account of the effect of different land uses under mixed farming systems along topographic elevation over broader landscape positions on SOC stocks and retention rates.
Population pressure has pushed agriculture in Ethiopia to expand into forest on hillsides and slopping lands (Sima et al. 2011). Native vegetation is being changed into arable cropping lands with slight or no conservation measures and there has been a decreasing trend of forest coverage and SOC stocks. From 1990 to 2010 alone, 1.16Gt of C stocks from forest biome and 1.83Gt of SOC stocks were lost at country level (FAO 2010). Over grazing, fuel woods and production of charcoal, poor governance and land tenure system are some of the underlying causes for depletion of aboveground and belowground C stocks in Ethiopia (Sima et al. 2011). The inherent fragile soil properties coupled with low input agriculture have caused decline in the soil fertility within short term after conversion of marginal lands to agricultural land. Smallholder farmers fallow their field plots for three to four years until the soil fertility has partially restored. During the fallowing, controlled grazing is usually practiced. Land use changes from native vegetation to agricultural lands and the vice versa have been the sources and the sinks for atmospheric CO2. Land misuses and mismanagements have been the sources for the atmospheric CO2 while adoptions of restorative land uses and recommended management practices reduce rate of CO2 emission to atmosphere that could improve food security, water quality and environmental quality (Lal 2004a). Alley cropping system (Oelbermann et al. 2007), coffee gardening and agroforestry system (Xavier and Mendo 2011; Hombegowda et al. 2015), farm forestry and agroforestry systems (Prasad et al. 2012; Murthy et al. 2013), conversion of pasture and grazing lands to sugarcane plantation and silvo-pasture (Junior et al. 2012; Ensinas et al. 2015), soybean and maize inter-cropping (Junior et al. 2012) and preservation of vegetal biomass of sugarcane have sequestered C and increased the SOC stocks in many parts of the globe.
Traditional land use systems across various ecological regions and elevation gradients are practiced in Ethiopia since immemorial (Bishaw et al. 2013). Traditional smallholder and oxen drawn arable cropping, eucalyptus and coffee agroforestry, woodlots, protected forest, fallowing, grassland systems and mechanized sugarcane plantation are some among many mixed land use systems practiced in the humid tropical Western Ethiopia. The indigenous and traditional land use systems could be restorative land use systems compared to continuous cropping with limited inputs and biomass return to the soil system. The indigenous but traditional land use systems have been practiced for centuries and could be stable systems that could reduce CO2 emission and positively impact food production, income generation, livelihoods and energy sources (Bishaw et al. 2013). Mechanized irrigated sugarcane plantation was recently introduced into Didessa watershed. However, there is scarcity of available research information on the effect of indigenous land uses and mechanized irrigated land use systems practiced along toposequence on SOC stocks and retentions on intermediate to highly weathered soils of humid tropical Western Ethiopia. Thus, the dynamics of SOC stocks and rates of retention in indigenous land use systems, and mechanized irrigated sugarcane plantation along elevation gradient forming land use catena are lacking in the horn of Africa in general and Ethiopia in particular.
Therefore, the objectives of this research were to quantify SOC stocks and retention rates of indigenous land uses systems, recently introduced modern mechanized irrigated sugarcane production system in sequestering SOC stocks and retention rates in humid tropical environment of Western Ethiopia. We hypothesized that indigenous land uses of mixed farming systems along elevation gradients were more efficient restorative systems of sequestering atmospheric CO2 compare with modern mechanized cropping system and their efficiencies vary along elevation gradients.
Materials and methods
Didessa watershed is located in humid tropical Western Ethiopia. The topographic map of the 52 km long study transect extends from 9° 06′ 12.7180″ N, 36° 28′ 22.1868″ E to 8° 40′ 1.9920″ N, 36° 25′ 13.0308″ E. Didessa watershed drains an area of about 9,486km2 and agro-ecology indicated in Fig. 1. Didessa River is the tributary of Blue Nile that flows into North Western Ethiopia. The watershed covers about 5.4% of the total area of Blue Nile and contributes 6.86km3 annual discharges which accounts to 10.7% of the total annual discharge of Blue Nile (Conway 2000). The location of study land use systems along the same toposequence is indicated in Fig. 2.
Topography and climate
Elevation of the watershed range from 845 to 2685 m and characterized by sequence of contrasted landforms. Three broad categories of topographic positions are found in study transect. These include lowland, midland and highland with elevation ranges between 845–1500, 1500–2000 and 2000–2685 m above sea level (masl), respectively. Analysis of twenty years of weather data of twelve metrological stations in and around Didessa watershed showed that the mean annual rainfall of the watershed ranged from 1400 to 1920 mm per annum. The rainfall in the watershed has a unimodal pattern of distribution. The watershed has three types of length of growing period (LGP) that ranges from 165 to 210 days, from 210 to 240 days, and from 240 to 300 days. The annual average temperature varies from 19 °C in the highlands to 23 °C in the lowland.
Agro-ecologies and vegetation
The agro-climatic zones (ACZ) of the watershed were derived from twenty years of twelve metrological stations and topographic elevation from digital elevation model. According to Hurni (1998) classification system, three agro-climatic zones were identified namely warm sub-humid lowland (180–240 LGP, 20–27.5 °C, 500–1300 masl), tepid sub-humid midland (180–240 LGP, 15–20 °C, 1500–2000 masl) and tepid humid highland (240–300 LGP, 15–20 °C, 2000–2685 m). Grassland vegetation dominated the lowland topographic position. Mixed woodland and grassland dominated the midland position while woodland dominated the highland topographic position. As one move from lowland to highland, there are shifts in vegetation types and land use systems along the study transect.
Farming system of Didessa toposequence
The farming systems are predominantly subsistent mixed crop-livestock (mostly cattle, sheep and goat) production system. In the mixed farming system, cattle provide inexpensive and easily accessible inputs required for cultivation such as draught and threshing power, while crop production supplies crop residue as feed supplement for the livestock. However, most of the grazing is carried out on communal grazing and fallow lands. Manures from calves, sheep and goats are mainly used for homestead gardens. Farm fields away from home gardens often receive manure of cattle and equines (donkeys, horses, and mules) through kraal (cattle pen during night) rotation. Tillage involves oxen plowing with simple plows that cultivate the soils to shallow depths of 15 cm on average (oral communication with the farmers and personal observation).
Major crops grown in the lowland (less than 2000 m) of the transect include maize, sorghum, finger millet and noug while above this elevation highland potato, teff, field pea, faba bean and noug are common crops. Combination of manure and inorganic fertilizers are used for crop production but the amount of fertilizer applications is low. Farmers use di-ammonium phosphate (DAP) in combination with urea. The recommended rate of application is 100 kg ha−1 year−1 for both DAP and urea. However, some farmers use sometimes half of recommended amount and often none mainly due to economic reasons. The farming systems have traditional agroforestry system with scattered trees in the farm and grazing lands, eucalyptus woodlots at edge of farmlands, homestead coffee under shade trees. Farms of similar management history were selected by interviewing farm owners and village elders.
Sampling sites and land uses selection
Soil samples were collected at five sampling sites along the toposequence. The sampling sites were Fayinera, Dune Kane, Balho, and Lugama and Sugar plantation. At Fayinera and Dune Kane sampling sites, soil samples were collected from annual cropping land, fallow land and eucalyptus agroforestry (woodlots) that were in close juxtaposition (at edge of farmland). At Balho sampling sites, soil samples were collected from grazing and annual cropping lands. At Lugama sampling site, soil samples were collected from arable land, grazing land and home homestead coffee agroforestry. While at sugar plantation, soil samples were collected from grazing and mature sugar plantation. The soil samples collected from the distinct sampling farms (land uses) at the four sampling sites were close to each other within a distance of 10 m to 50 m from the edge of the respective land uses. Each of the sampling sites were rigorously checked for uniformity of soil types by augering and field characterization of physical and chemical properties, slope angle, length and aspects before sampling of soils from respective land uses and sampling sites. Flow directions of materials from farm lands at each of sampling farms and sampling sites were also considered for uniformity to aid interpretation of the results. Auger point observations to the depth of 120 cm were made and described according to FAO (2006) soil description field guide and checked uniformity of soil types, physically observable pedogenic features and processes. The results of field observation and description were used to verify the similarity in soil types among farms. These selection criteria, however, did not allow us to find farmlands of very similar land use characteristics, land configuration, and land management history along all the sampling sites.
Soil sampling from four sampling sites
Soil samples were collected from four representative subsistent mixed farming systems identified along the Didessa toposequence. Thirty samples were collected from each of a uniform field from cropping land, fallow land and agroforestry land at Fayinera and Dune Kane sampling sites, from cropping and grazing land at Balho sampling site, from cropping, homestead coffee agroforestry and grazing land at Lugama sampling sites, and mature sugar plantation and grassland at sugar plantation sites. All the samples were collected from 0–20 cm depth with an auger. The thirty samples collected from each land use were bulked to form homogenous composite samples. Generally, 360 samples were collected and then twelve composite soil samples were made out of them following standard soil sampling and bulking procedure. From each of the composite samples, representative subsamples were collected into plastic bags for analysis of soil physical and chemical properties. Foreign materials such as coarse fragments, plant roots, and leaves were removed. The samples were air dried, ground, and sieved to pass through a 2 mm sieve.
Analysis of soil physical and chemical properties
The air dried, sieved to pass through 2 mm, and oven dried equivalent soil samples were analyzed for distribution of particle size determination according to modified sedimentation hydrometer procedure of Bouyoucos (Kroetsch and Wang 2006). The samples were pretreated with hydrogen peroxide to destroy organic matter and treated with sodium hexametaphosphate solution (NaPO3)6 to disperse other soil cementing agents. The proportions of sand, silt and clay sized particle size fractions were determined. The textural classes of soils were determined from textural triangle. The pH of the soils was measured in supernatant suspension of soil to liquid mixture of 1:2.5 ratios. The liquids were distilled water (pHH2O) and 1 M KCl (pH KCl) (Reeuwijk 1992). The SOC was determined according to the Walkley–Black procedure (Reeuwijk 1992). Soil organic matter (SOM) was estimated from SOC by assuming that SOM contains 58% of SOC (Reeuwijk 1992).
The bulk density (ρb, g cm−3) of soils were calculated as the dry weight of the soil divided by volume of soil core sampler. The SOC stocks were calculated as Mg ha−1 by multiplying the concentration (%) of SOC by the respective bulk density (g cm−3) and multiplied by the depth from which samples was collected (20 cm). The total SOC stocks of soil profiles were determined by summing up of the SOC stocks from the respective horizons and expressed as Mg C ha−1. The retention rates of SOC stocks were calculated as SOC stocks of the land use systems minus the SOC of the reference land use divided by the duration of the land use systems. The SOC stocks of crop land and grassland were used as reference SOC stocks with their respective indigenous land uses systems wherever available.
The map of Didessa watershed was prepared by use of ArcGIS software version 10.1 and three dimensional topographic map of study transect of Didessa toposequence was constructed using Global Mapper version 13. Soil data from similar land uses at sampling sites were treated as replications. SPSS statistics version 20 was utilized to carryout statistical analysis to determine effect of sites on SOC stocks and retention rates by. P-values of 0.05 and 0.01 were used statistically significant and highly significant differences, respectively.
Results and discussion
Soil physical and chemical properties
Table 1 indicates soil textures, soil textural classes and soil reactions of the study soils. Clay contents of upper 0–20 cm soil layers ranged from 16 to 34% and soil texture ranged from sandy clay to loam. Soils on more inclined surface had lower clay and higher sand contents due to surficial erosion of finer materials. The soil pH-H2O in the highlands ranged from 4.48 to 5.62 and pH-KCl ranged from 3.56 to 4.73. The pH-H2O in lowland soils ranged from 5.07 to 7.37. The pH-KCl ranged from 3.69 to 6.31 that is an indication of difference in exchange acidity of soils. The large variations in soil pH in the highland and lowland soils were due leaching of basic cations from the highland and the formation of secondary calcium carbonate in the lowland soils (Abdenna et al. 2018).
Table 2 indicates the duration of land uses in terms of years, SOC, soil bulk densities and SOC stocks of the study soils. The soil bulk densities ranged from 0.83 g cm−3 in coffee agroforestry to 1.44 g cm−3 in mechanized irrigated sugarcane plantation. Within coffee agroforestry system, the soil bulk densities varied within a narrow range of 0.83 to 0.88 g cm−3. The bulk densities in smallholder eucalyptus agroforestry system ranged from 0.99 to 1.22 g cm−3, while in cultivated land use system, the bulk densities ranged from 1.08 to 1.3 g cm−3. The bulk densities in short fallow land use system also varied with very narrow range and comparable with the bulk densities in cultivated land use system. Soils from grassland and mature sugarcane plantation had comparable soil bulk densities that ranged from 1.15 to 1.32 g cm−3. The higher the soil bulk density in sugar plantation could be due to compaction of Vertisols by heavy machineries during land preparation and harvesting of canes.
Soil organic carbon stocks among land uses
Table 2 indicates the stocks of SOC among land use systems along toposequence of Didessa watershed in mixed farming systems. The stocks of SOC varied with land use systems. It ranged from 9.27 Mg C ha−1 in grassland soils at lowland to 13.5 Mg C ha−1 in eucalyptus agroforestry system in the highland. The observed differences in stocks of SOC among land uses were statistically significant (P < 0.05). In the highland topographic position, the stocks of SOC were lower in annual arable cropping compared to other land uses. At the lowland, the stocks of SOC were lower in pristine grassland compared to mechanized irrigated sugarcane production system. The lower the stocks of SOC in arable cropping is agreement with previous study reports (Lemeniha and Itanna 2004; Vagen et al. 2005).
Figure 3 indicates the trends of SOC stocks in cultivated lands and fallow lands along Didessa toposequence. The stocks of SOC in cultivated and fallow lands increased with topographic elevation. The increasing trends of SOC stocks with increasing topographic elevation presumably related to low mineralization and higher stabilization of SOC due to relatively lower temperature in the higher topographic elevation. A similar trend of SOC stocks in the same toposequence was also reported earlier by Abdenna et al. (2018). In the study toposequence, farmers fallow their land for three to four years to restore soil fertility. This practice of short fallowing consistently increased the SOC stocks compared with continuous cultivation. The increased SOC stocks under fallow system in this study are in agreement with many research reports from tropical Africa and Latin America (Vagen et al. 2005; Styger and Fernandes 2006).
Soil organic carbon stocks in irrigated sugarcane plantation in lower topographic position in Didessa toposequence ranged from 7.41 to 13.31 Mg C kg−1 (Table 2). Higher SOC stocks were sequestered during harvesting of sugarcanes as compared to just before harvest of the sugarcanes. The higher SOC stocks during harvesting of sugarcanes were due to incorporation of leafy biomass of the sugarcanes to the soil system during harvesting. The higher the stocks of SOC in mechanized irrigated sugarcane plantation were also in agreement with several study reports from Brazilian sugarcane production systems (Junior et al. 2012; Aline et al. 2013; Ensinas et al. 2015). They reported that cultivation of sugarcane plantations increased the stocks of SOC. Similar ranges of stocks of SOC in sugarcane plantations were also reported by Junior et al. (2012). As compared to our study results, higher stocks of SOC in smallholder irrigation based fruit production system in Northern Ethiopia were reported (Aweke et al. 2014). They reported 17.47 Mg C ha−1 in irrigated fruit production system and 9.8 Mg C ha−1 in rain fed annual arable cropping system in the upper 0–20 cm soil surface. The reasons for the lower SOC stocks in irrigated sugarcane plantations could be due to the humid regional climate which facilitated mineralization of soil organic matter, and the low inherent C storage capacity of Alfisols and Ultisols of the humid tropical region (Lal 2004a). According to Aweke et al. (2014) the climate in North Western Ethiopia was semiarid with mean annual precipitation of 558 mm with Arenosols and Cambisols developed on alluvial deposits and Adigrat sandstone parent materials. Moreover, the lower stocks of SOC in our study thus could be due to high mineralization as favored by longer period of wet season and the residue quality returned to the soil system.
The stocks of SOC in eucalyptus agroforestry ranged from 8.42 to 14.29 Mg C kg−1 (Table 2). The mean stocks of SOC in eucalyptus agroforestry system were higher than the mean stocks of SOC in annual arable cropping system in the highland. The stocks of SOC in eucalyptus agroforestry system were consistently higher than the stocks of SOC in arable cropping. The stocks of SOC along toposequence didn’t show consistent trend due to many uncontrolled factors such as level of soil erosion, slope variation and slight variation in duration of eucalyptus agroforestry. The higher the stocks of SOC under eucalyptus agroforestry could be explained by higher biomass productions, higher C:N ratios, higher soil bulk density, and production and release of allelochemicals. Eucalyptus species produce and release allele-chemicals into rhizosphere, which inhibit the growth, development and functioning of microbes. Eucalyptus species also produce large quantities of litter materials with high C:N ratios, high lignin and phenolic content (Snowdon et al. 2005; Silva 2012). Mulugeta et al. (2004) also reported higher C:N ratios of surface soils under eucalyptus species as compared to natural forests in Southern Ethiopia. Poultouchidou (2012) also reported increased stocks of SOC in soils from eucalyptus species and Silva (2012) also reported increased soil compaction, bulk density, and stocks of SOC as the result of conversion of pasture land into eucalyptus agroforestry in Brazil which are in agreement with our finding.
The stocks of SOC from coffee agroforestry system ranged from 9.0 to 12.18 Mg C kg−1 and the stocks of SOC were higher compared with the nearby stocks of SOC from annual arable cropping system (Table 2). The variations in stocks of SOC were due to variation chronology (ages) of the coffee agroforestry (Fig. 4). The stocks increased with duration (ages) of coffee agroforestry stands. The stocks of SOC in the coffee agroforestry system from our study were lower than the stocks of SOC of 21 Mg C ha−1 from 32 years old coffee agroforestry established on Andosols of Central Rift Valley of Ethiopia (Girma and Wolde-Meskel 2012). The low stocks of SOC stocks in coffee agroforestry in Didessa toposequence compared with the Central Rift Valley of Ethiopia could be due to difference in the soil types (Luvisols and Alisols) which inherently have lower sequestration capacity of stocks of SOC, and the favorable humid tropical climate of Western Ethiopia for higher mineralization, hence low stocks. The Andosols from Central Rift valley of Ethiopia favor stocks of SOC through decreasing mineralization due to moisture deficiency. Moreover, Lal (2004a) also reported that Andosols sequester more SOC than Luvisols and Alisols. Xavier and Mendo (2011) also reported higher stocks of SOC that ranged from 28.5 to 31.4 Mg C ha−1 in 0-10 cm from Brazilian coffee agroforestry system compared with stocks of SOC from coffee agroforestry system in our report. The stocks of SOC in the 0–20 cm depth in this Brazilian coffee agroforestry system could be even much higher than the SOC stocks in the current study coffee agroforestry system. The higher the value of SOC stocks (32.24 Mg C ha−1) in small holder coffee agroforestry system in Western highlands of Gautama was also reported by Schmitt-Harsh et al. (2012).
The stocks of SOC in grazing land in Didessa toposequence ranged from 8.91 to 15.21 Mg C kg−1 (Table 2). The mean stocks of SOC from grazing land use systems were higher compared with the stocks of SOC from arable cropping system (reference land use). Rimhanen et al. (2016) also reported comparable stocks of SOC in restrained grazing from Kobo district of Northern Ethiopia. They also reported higher stocks of SOC from grazing land use from Sire district of Central Rift Valley of Ethiopia with stocks of SOC ranging from 18 to 59 Mg C ha−1 in the upper 30 cm surface soil layer. These corresponded to stocks of SOC of 12 to 39 Mg ha−1 that were compareable to our finding from graizing lands. The stocks of SOC from grazing land use system of our study results were lower than the stocks of SOC from Kobo district of North Eastern Ethiopia. The stocks of SOC in our results were in the lower margin of SOC stocks reported from Sire district of Central Rift Valley of Ethiopia (Rimhanen et al. 2016). The difference in precipitation, temperature and soil types could be attributed to the difference in stocks of SOC in both locations. As compared to our result, higher stocks of SOC of magnitude of 39.31 Mg C ha−1 from open grazing land use from the upper 0-20 cm in a semi-arid in Tigray in the Northern Ethiopia was also reported by Aweke et al. (2014).
Soil organic carbon stocks along toposequence
Table 3 indicates the mean stocks of SOC in the upper 0–20 cm soil surface layers from different locations along toposequence in the mixed farming systems along Didessa toposequence. The stocks of SOC ranged from 10.54 Mg C ha−1 at mechanized irrigated sugarcane production system to 14.045 Mg C ha−1 at Balho site. The higher the stock of SOC at Balho site was significantly (P < 0.05) higher compared with other sites along Didessa toposequence. The trend of stcoks of SOC increased with increased topographic elevation (Fig. 5) along the increasing precipitation and decreasing temperature paterns. The higher SOC stock at Balho was due to cooler weather and longer growth periods (Abdenna et al. 2018). The observed pattern was due to the effect of precipitation and temperature. Similar observed pattern of increasing SOC stocks with increasing topographic elevation was also reported ealier in Southern Ethiopia (Lemeniha and Itanna 2004) and in South Eastern Ethiopia (Yimer et al. 2006).
Soil organic carbon retention among land uses
Table 4 indicates the mean annual SOC retention rates in different land uses of mixed farming systems along Didessa toposequence. In reference to annual arable cropping system for midland and highland, and grassland for lowland systems, the annual retention rates ranged from 0.114 to 1.14 Mg C ha−1 year−1 that there were statistically significantly (P < 0.05) different among SOC retention rates. These results were in the range of SOC retention rates (− 0.98 to 1.91 Mg C ha−1 year−1) reported in major agroforestry systems in tropical Africa (Feliciano et al. 2018). The magnitudes of SOC retention rates revealed that retention rate in irrigated sugarcane plantation system > eucalyptus agroforestry system > grazing land use system > fallow land use system. The mechanized irrigated sugarcane production located at the lowland topographic position resulted in more retention of SOC compared with the nearby reference pristine grassland system. The positive SOC retention rate in sugarcane production system was due higher sugarcane biomass production. The higher biomass production was due to fertilization of sugarcane plantation with supplemental irrigation water during dry season, and incorporation of sugarcane residues into the soil system at the time of harvesting of sugarcanes. Our results are comparable with SOC retention rates in conventional tillage (0.67 Mg C ha−1 year−1), and zero tillage (1.63 Mg C ha−1 year−1) from Brazilian sugarcane production system as reported by Aline et al. (2013). They attributed the positive retention rates of SOC to the maintenance of sugarcane straws and incorporation to soils at the time of harvesting of the sugarcanes. The annual retention rate of SOC in sugarcane plantation in our study was higher than the SOC retention rate of 0.56 Mg C ha−1 year−1 in smallholder irrigation fruit production system in semiarid Northern Ethiopia (Aweke et al. 2014).
The mean magnitude of SOC retention rate in eucalyptus agroforestry system along Didessa toposequence was 0.308 Mg C ha−1 year−1. It is comparable with the SOC retention rates reported earlier by Aweke et al. (2014) in Faidherbia albida silvopasture (0.46 Mg C ha−1 year−1), and Faidherbia albida agroforestry system (0.19 Mg C ha−1 year−1) from semiarid Northern Ethiopia. The retention rate of SOC in eucalyptus agroforestry system was higher than the SOC retention rates of agroforestry system (1.2 Mg C ha−1 year−1), and restrained grazing (0.7 Mg ha−1 year−1) in Kobo district of Northern Ethiopia and Sire district of Rift valley of Ethiopia (Rimhanen et al. 2016).
The SOC retention rate in grazing land use system was 0.279 Mg C ha−1 year−1. The magnitude of the SOC retention in the grazing land in our result was lower than the SOC retention in open pasture (0.73 Mg C ha−1 year−1), and silvo-pasture (0.46 Mg C ha−1 year−1) in semiarid Northern Ethiopia (Aweke et al. 2014). Moreover, the SOC retention rate in grazing land in our finding was lower than SOC retention of restrained grazing (0.7 Mg C ha−1 year−1) in Kobo district of Northern Ethiopia and Sire district of Rift valley of Ethiopia (Rimhanen et al. 2016). The lowest SOC retention rate in our finding was obtained from fallow land use system. The relatively small SOC retention rate in fallow land use system was due to short fallow duration (< 2 years) from which the land could not get enough time for vegetation restoration that produces biomass the returns vegetal materials to the soil system.
Soil organic carbon retention rates along toposequence
Figure 6 indicates trends of SOC retention rates among three land uses along toposequence of Didessa watershed. The trends indicated decreasing retention rates of SOC with increasing topographic elevation. Eucalyptus agroforestry and fallow land use systems were more efficient in retention rates of SOC compared with coffee agroforestry system. The lower retention rates with increasing topographic elevation could be due to higher precipitation and moisture over longer growing period that led to more mineralization of SOC, and the vice versa. Moreover, with increasing topographic position, the landscape gets steeper and soil erosion becomes severe leading to removal of organic materials that could ultimately decrease the rate of SOC retention. Bajigo et al. (2015) also reported higher SOC retention rates in lower topographic elevation in agroforestry practices in Gununo watershed in Southern Ethiopia. They attributed to higher retention rates in lower topographic position due to dense vegetation. Feliciano et al. (2018) also reported the order of retention rates of SOC in the order of tropical > semiarid > temperate climate indicating the importance of climate on SOC retention rates.
Conclusion and recommendation
Traditional coffee agroforestry, eucalyptus agroforestry, grazing land and irrigated sugarcane production system practiced in Western Ethiopia sequester SOC and moderate the loss of SOC stocks in the form of CO2 into the atmosphere. Traditional coffee agroforestry, eucalyptus agroforestry, and traditional grazing systems practiced by local communities and the recent introduction of mechanized irrigated sugarcane system into pristine grassland sequester and restore considerable amount of SOC stocks in the upper soil layers. The annual efficiency of SOC stocks sequestration potential followed the order of sugarcane plantation > eucalyptus agroforestry > grazing land > short fallow land > coffee agroforestry systems. The annual SOC retention rates of these indigenous land use systems practiced along the toposequence and the recent introduced mechanized irrigated sugarcane plantation revealed that the systems are efficient in sequestering C and could be considered as SOC stock restorative land use systems. Thus, mixed land use systems restore SOC, besides sustainably provision of goods and services that have both economic and ecological significances. Adoption of these restorative land use systems could provide economic and social values, sequester SOC stocks, and restore degraded lands in humid tropical Western Ethiopia.
Availability of data and materials
- CO2 :
Length of growing period
Soil organic carbon
Soil organic matter
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The authors would like to thank the Ministry of Education and Wollega University of the Federal Democratic Republic of Ethiopia for funding the research project. Wollega University was also acknowledged for provision of logistics and support during field works. Moreover, we extend our gratitude to Arjo-Didessa Sugar Development Enterprise for allowing us to collect soil samples and provision of vehicle and field guidance during field work, and Nekemte Soil Research Center for provision of support during soil laboratory analysis.
Wollega University (Grant No. 016/06) and Ministry of Education of FDR Ethiopia funded the study.
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Deressa, A., Yli-Halla, M. & Mohamed, M. Soil organic carbon stock and retention rate among land uses along Didessa toposequence in humid Western Ethiopia. Environ Syst Res 9, 34 (2020). https://doi.org/10.1186/s40068-020-00199-w