Soil erodibility indices under different land uses in Ri-Bhoi district of Meghalaya (India)

Land use and land cover of the district

Ri-bhoi district of Meghalaya has multiple land uses including many sub-categories of agriculture and forest land covers. In the present study only four major land uses were considered (Fig. 2). Out of 2,359.67 km2 of total geographical area, forest constituted with 77.15%, agricultural land constituted with 8.11%, jhum area had 2.28% and wasteland was of 9.35%. Ri-bhoi, being a hilly district, most of the area fell under forest. Rice is the main crop both in agricultural and jhum areas. Majority of the agricultural area belonged to the practice of mono-crop, the valleys near the major stream is covered under vegetables. Baring forest covered area, the soil is expected to be manipulated with anthropogenic activities and falls under the major concern of soil erosion. Settlement constituted with 2.39% and water bodies made 0.70% of area. These two land uses were not considered for the study.

Particle size distribution

The erodibility is low for clay-rich soils with a low shrink-swell capacity because clay particles mass together as soil aggregate by the cohesiveness and they are difficult to detach32 but once the clay particles are detached they are easily transported in suspension until they reach the stagnant water. The present study revealed that the clay had negative correlation with soil erodibility in the all land use types i.e. agriculture, jhum, forest, and wasteland. The higher avg. clay content value was observed in wasteland 37.36% followed by jhum (34.14%) and agriculture (32.95%), with minimum in the forest land 30.76% (Table 1). The clay content varies in LUS because of the parent material, mineral characteristics and weathering processes. It was reported that there’s a negative significant correlation between the amounts of clay and soil erodibility factor33. Clay content is used for determining soil erodibility18 and defined that soil with 9–30% of clay is taken as the most erodible. The least resistant particles in size separates are silts and fine sands11. Soils with 40–60% silt are highly susceptible to erosion18. Silt was significantly correlated with the erodibility in all LUS of study area. Silt was higher in the wasteland with an avg. value of 32.66% (17–53%), it was 32.17% (15.5–46.65%), 28.86% (14.5–38.5%) and 26.64% (10.5–45.5%) in agriculture, forest and jhum land uses, respectively. It was observed that six locations within wasteland, two locations within agriculture and three locations within jhum land uses had silt content more than 40% indicating susceptibility of erosion. No location in forest LU was considered to be susceptible to erosion with respect to silt content. Fine sand was also showing the positively significant correlation with soil erodibility. Fine sand content in agriculture, jhum, forest and wasteland land uses were 13.93%, 13.43%, 13.01% and 11.58%, respectively. Large particles such as sand are erosion resistant because of the force required to displace them is more compare to silt and fine sand. It was observed from the results that the sand was negatively correlated with the erodibility in agriculture, jhum (Table 2). The sand content were found to be 32.17%, 18.39%, 27.37% and 37.96% in agriculture, jhum, forest and wasteland, respectively.

Table 1 Soil properties of different land uses.
Table 2 Correlation of K-index with determinant factors in the district.

Organic carbon

Soil organic carbon was observed to be higher in jhum LUS with average of 3.20% followed by forest LUS with 3.19%, agriculture 3.11% and lowest observed in wasteland 2.67%. Higher organic carbon was reported in forest LUS34 followed by agriculture and minimum in wasteland. Similarly organic carbon35 was reported higher in jhum and forest land. Silt, clay, residue turnover from biomass and its decomposition rate are the critical factors in SOC build up in soil36. It might be attributed to the deposition of plant litter falls and death decay of above ground biomass of natural vegetation. The slash and burring procedure of the jhumming might help in the exposure of OC in the terrestrial ecosystem. Variation in organic carbon in soils under various land uses might be due to varying leaf litter and their rate of decomposition30. Similar result saying that SOC of Natural Forest soils are found to be higher than in the other land use types. Maintaining SOC levels in tropical soils was found to be more difficult because of its rapid oxidation under prevailing high temperatures.

Clay ratio (CR)

Clay ratio (CR) in agriculture, jhum, forest and waste land ranged from 0.63–6.40, 1.0–4.26, 1.02–8.52 and 0.72–5.25, respectively. The average values of CR in the land uses were 2.74, 2.39, 2.10 and 1.97, respectively for forest, agriculture, jhum and wasteland. The higher value of CR for forest soil was due to higher content of sand (40.38%). The lower CR value in wasteland was due to the lower sand content in the soils of wasteland compared to other land use systems. CR for overall Ri-Bhoi district ranged from 0.63 to 8.52 with an average value of 2.30. The Fig. 4 represents the Clay Ratio map of Ri-bhoi district. Though higher CR values indicate susceptibility to erosion, since this is a ratio between the erosion susceptible primary particles to clay, the CR values of different land uses could not give any conclusive understanding of its relationship to the erosion proneness. It was stated that for any meaningful interpretation the clay content should be more than 10%22. All the samples in the study had clay content more than 10%, but due to absence of any scale for erosion proneness, conclusive interpretation could not be drawn.

Figure 4

Clay Ratio (CR) of Ri-bhoi district. (

Modified clay ratio

Modified clay ratio for agriculture, jhum, forest and wasteland were observed in the range of 0.61–5.17, 0.94–3.57, 0.96–6.84 and 0.68–4.53, respectively. The average value of modified clay ratio was observed higher in forest land use (2.41). This is slightly less than the clay ratio because organic matter was added in the denominator. The trend of MCR was observed in the similar manner of CR and in the decreasing order for the land uses of agriculture, jhum and wasteland as 2.13, 1.89, 1.81, respectively. The MCR for Ri-Bhoi district of Meghalaya was observed in the range of 0.61–6.84 with the average value of 2.06. The MCR values of Ri-bhoi district is presented in Fig. 5. Similar to the CR, MCR also failed to give conclusive interpretation about the erosion proneness of the soil according to the land uses. However, as the average values of MCR were not so high, it could be inferred that soils in the district was not highly susceptible to erosion.

Figure 5

Modified Clay Ratio (MCR) of Ri-bhoi district. (

Critical level of soil organic matter (CLOM)

The results indicated that the values of CLOM for the district ranged from 4.72 to 16.56. Out of 100 samples, only one sample had CLOM value less than 5 and rest 99 samples had values more than 5 indicating that the soils of the district were moderate to stable soil structure and offer resistance to erosion. Average CLOM values were 8.84, 9.46, 9.41and 6.71 for agriculture, forest, jhum and wasteland, respectively. Land use wise CLOM values ranged from 5.70 to 16.56 for agriculture, 574 to 15.01 for forest, 6.31 to 12.52 for jhum and 4.72 to 9.69 for wasteland. Soils were moderately susceptible to erosion in 60%, 40%, 48% and 88% for agriculture, forest, jhum and wasteland land uses. Further, 40%, 60%, 52% and 8% locations in agriculture, forest, jhum and wasteland, respectively had very stable soil aggregates indicating the wasteland was relatively susceptible to erosion.

Soil aggregate stability is related to Soil Organic Matter. In the district, soil organic carbon ranged from 2.67 in wasteland to 3.20 in the forest land use which corroborate with the CLOM values indicating that soil stability positively correlated with the soil organic matter.

Soil structure

The Eq. (5) requires soil structure classes. It considers 4 classes of soil structure and assigned codes 1–4 for the equation. Codes are viz, 1: very fine granular (1–2 mm mean aggregate diameter), 2: fine granular (2–3 mm), 3: medium or coarse granular (3–5 mm) and 4: blocky, plat or massive (> 5 mm)8 . Soils in agricultural land found to have 1 and 2 structural codes, Jhum had 1, 2 and 3, forest had 2, 3 and 4 and the wasteland had the same structural codes of jhum land. Agricultural land with repeated tillage for cultivation had finer soil aggregates and prone to easier detachment and displacement. Similarly, forest soils with very less disturbance had better soil aggregation and resistance to erosion. As wasteland had higher clay content (37.36%), had finer to coarser soil aggregates even though the soils were exposed to various degradation forces. The Eq. (5) does not use absolute values of Mean Weight Diameter and hence it was difficult to enumerate the exact influence on soil erodibility in relation to land uses.

Soil permeability

There are six permeability classes used in Eq. (5). They are viz. 1: rapid (> 150 mm/h), 2: moderate to rapid (50–150 mm/h), 3: moderate (12–50 mm/h), 4: slow to moderate (5–15 mm/h), 5: slow (1–5 mm/h) and 6: very slow (< 1 mm/h).

Permeability and stability of the soil structure are two very important soil properties, which affect its erodibility factor15. Agriculture lands have the permeability classes from 2,3,4,5 and 6. In jhum the permeability classes vary from 3, 4, 5 and 6. The permeability class for forest land was observed in the same trend as agriculture areas and similar trend for wasteland was observed as in case of jhum areas. Soil permeability class-1 was absent in all major LUS. Permeability class-1 has higher rate of infiltration with very low runoff potential and lowest rate of infiltration was derived for the class-68, 37. Lower permeability class values allows the water to enter in the soil rapidly which reduces the runoff and higher values of permeability classes shows the slow rate of infiltration which may increase the rate of runoff in the soil which allows the light texture particles viz., silt and fine sand to get affected with the erosive forces. Agriculture and forest areas had permeability class ranging from 2 to 6 and hence expected to have spatially variable infiltration. In the areas with 5 and 6 permeability classes are expected to have very high runoff potential and hence soil erosion. As compared to agriculture and forest, Jhun and wasteland are more susceptible to soil erosion due to higher overland flow with higher permeability classes.

Soil properties of different land uses and their impact on erodibility

The soil physical properties, that influence the soil erodibility index, were compared according to the land uses with the premise that land uses are many a times decided by the soil physico-chemical properties and the soil texture was expected to be varying according to the land uses. The average organic matter in the soils was varying from 2.67% in wasteland to 3.20% in jhum land. The organic matter content in agriculture and forest land was not significantly different from that in jhum land but statistically different from wasteland (Table 1). The silt content was found to be similar in forest and jhum land and the silt content in forestland was at par with agriculture and wasteland. The content of fine sand was statistically similar for all the land uses which was ranging from 11.58% to 13.93%. Clay content was found to be different according to the land use types. Wasteland was having highest clay content with average value of 37.36%, which was statistically different from forest land but at par with agriculture and jhum land.

The information of soil physical properties and the indices such as CR, MCR, CLOM, etc. gave only inference about the soils proneness to erosion. This is a qualitative information and not suitable for any application for soil erosion assessment models. However, this qualitative information may be useful in case of prioritization of soil conservation measures24 and hence their importance cannot be undermined. However, K-index as given in USLE8, gives quantitative values of soil erodibility and can be used directly for assessment of soil loss.


Soil erodibility values in agriculture LU were ranging from 0.08 to 0.42 with an average value of 0.25 ± 0.02 which was the highest in the district. In jhum LUS these values ranged from 0.08 to 0.42 with an average of 0.20 ± 0.01 which was lowest among all major land uses. For forest LUS, values were ranging from 0.09 to 0.40 with an avg. of 0.22 ± 0.02. The erodibility index values in wasteland were observed in the range of 0.10–0.34 with an avg. value of 0.23 ± 0.02.

Soil erodibility maps

The values of soil erodibility of the geo-coded sampling points were interpolated in GIS environment through kriging31 and soil erodibility maps according to land use systems were prepared and presented in Fig. 6. The higher K value in agriculture was due to the higher amount of silt and fine sand content. Silt and fine sand lacks adhesion properties and if moisturized, becomes easily broken and transported, having an increased impact on soil erodibility38. Lowest erodibility observed in the jhum LUS due to the higher organic matter that allowed soil fractions to make greater aggregate stability in jhum LUS and sand fraction had also played role for reducing the erodibility in jhum LUS because of greater force requirement to displacement the particles. In case of forest LUS, clay content and sand content had played dominant role to reduce the erodibility. Soil erodibility was negatively correlated with sand in agriculture, jhum and forest LUS but no trend was observed in wasteland because of clay fraction was dominant than other soil fractions. Sand had also shown the negative correlation with the erodibility, increase of sand content reduced the erodibility. In case of wasteland higher correlation was observed with clay. Similar trend was observed in earlier works4. Permeability had also shown negative correlation with erodibility which means in all LUSs which reduced the rate of runoff.

Figure 6

Soil Erodibility (K) Factor map of Ri-bhoi district. (

The K-index map was prepared for the district with five ranges of index values viz. 0.20–0.23, 0.23–0.25, 0.25–0.28, 0.28–0.31 and 0.31–0.34. Out of total area of 2,428.89 km17 of the district most of the area 72.52% had soils with K-index less than 0.28. It is seen from the Fig. 6, that forest and Jhum area mainly fall under these three categories. K-index ranging from 0.28 to 0.34, are mainly spread over agriculture and wasteland areas spreading towards northern and southern parts of the district and constitute 27.48% area of the district. The K-index map with these five categories of K-index values has been prepared with very small interval of 0.03 and represented with distinct colour coded polygons. This will enable to pick up K-index values easily from the polygon areas with the average values of the range interval.

Erodibility indices (K-index) vis-a-vis soil physical properties and land uses

Soil texture is an inherent property and does not change with land uses. However, erodibility indices are dependent on not only soil textures but also on the presence of OM, soil permeability and soil structures. It was observed from the Table 1 that K-index varied from 0.20 ± 0.1 (Jhum) to 0.25 ± 0.2 (agriculture) though difference among the K-indices corresponding to the land uses were not statistically significant. Average compositions of the primary particles of the soil (sand, fine sand, silt and clay) did not have any correlation with the land uses. Agriculture LU had higher silt and fine sand in comparison to the soils of other land uses as a result the soils in agricultural areas had higher K-index values. The presence of higher clay could not offset the effect of silt and fine sand. The presence of lower organic matter in agricultural LU in comparison to forest and Jhum LU also attributed to higher K-index. Wasteland had lowest amount of OM (2.67 ± 0.08) and highest amount of silt per cent (32.66 ± 2.02). Even though the clay per cent (37.36 ± 2.31) was the highest in wasteland soil among the four land uses, the K-index values on wasteland were relatively higher with an average value of 0.23 ± 0.02. From Table 1, it was evident that the soils in jhum area were less erodible than the soils in agriculture and wasteland LU. This is however against the popular belief that jhum soils are susceptible to soil erosion. This may be attributed to the content of higher organic matter (3.20 ± 0.09) in jhum soils.

The pairwise correlation of K-index with the soil texture and organic matter revealed (Table 2) very strong positive correlation of K-index with silt (0.798) and fine sand (0.648) and significant negative correlation with clay (− 0.612) and organic matter (− 0.340). K-index was also negatively correlated with soil permeability (− 0.259). These correlations corroborated the general understanding of the soil erodibility vis-a-vis soil texture, organic matter and permeability. Soil structural codes were not analysed for correlations as it was a qualitative range used in the Eq. (5).

Spatial variability of K-index

The greater variability of soil erodibility (K-index) was in jhum land use (0.08 to 0.42) and forest land use (0.09 to 0.4) as compared to that (0.1 to 0.34) of agricultural land use and wasteland. These findings clearly indicated that spatial variability of soil texture, organic matter; soil permeability and soil structure were more in jhum and forest land use than in agricultural and wasteland. The content of silt was found to be the strongest determinant of K-factor for agricultural, jhum and forest land uses, whereas the content of clay was for wasteland. Soil structure seemed to play more significant effect on K-factor of forest LU than that of agricultural, jhum and waste land uses.

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