Ghg Balance of Agricultural Intensification & Bioenergy Production in the Orinoquia Region, Colombia

: Energy crop expansion can increase land demand and generate displacement of food crops, which impacts greenhouse gas (GHG) emissions mainly through land-use change (LUC). Increased agricultural productivity could compensate for this. Our study aims to evaluate the regional combined GHG emissions of increasing agricultural yields for food crop and beef production and using the generated surplus land for biomass production to replace fossil fuels in the Orinoquia region of Colombia until 2030. The results show that surplus land for biomass production is obtained only when strong measures are applied to increase agricultural productivity. In the medium and high scenario, a land surplus of 0.6 and 2.4 Mha, respectively, could be generated. Such intensification results in up to 83% emission reduction in Orinoquia’s agricultural sector, largely coming from increasing productivity of cattle production and improving degraded pastures. Biofuel potential from the surplus land is projected at 36 to 368 PJ per year, with a low risk of causing indirect LUC, and results in GHG emission reductions of more than 100% compared to its fossil fuel equivalent. An integrated perspective of the agricultural land use enables sustainable production of both food and bioenergy. as N (0.46% N), was assumed to report a lower production emission factor compared to Urea. Therefore, the emission factor of the lowest nitrogen fertilizers (SAM) is applied. d Emission factors for N 2 O emissions calculation (direct/indirect) resulting from N-fertilization were taken from [43]. e Fossil fuel emission factor were taken from [43].


Introduction
Based on the need to reduce fossil fuel consumption and GHG emissions, bioenergy production has increased in the past decades and it is projected to continue to grow [1]. However, expansion of energy crop production could incur increased land demand, and thereby increase greenhouse gas (GHG) emissions due to direct and indirect land-use change ((I)LUC) [2]. To minimize these effects, the sustainability criteria of the Renewable Energy Directive (RED II) require low-ILUC risk-biofuels and minimum GHG emission savings compared to the fossil fuel equivalent [2]. Biofuels are considered to have a low-ILUC-risk, when energy crops are cultivated on surplus land that can be made available due to the implementation of measures to further increase yields of agricultural production compared to a business-as-usual scenario [3]. Producing energy crops at surplus land

General Approach
The net GHG balance of the Orinoquia region for 2030 is calculated considering (i) agricultural intensification of food crop and beef production and (ii) bioenergy from energy crops produced on the generated surplus land. We first determine agricultural production for 2030 (Section 2.3). Since most of the crops produced in the region are destined for human consumption, they are referred to as food crops in this study. Moreover, since most of the region's cattle production is dedicated to beef production, only beef production is included in this study. Next, we assess how agricultural productivity may develop until 2030 and calculate the resulting surplus (or shortage) of land (Section 2.4). Our analysis is conducted for four scenarios; besides a reference scenario, which assumes a business-as-usual development in agricultural intensification, three agricultural intensification scenarios are included (low, medium, high). We then determine GHG emissions for agricultural production and intensification (Section 2.5), for bioenergy supply chains and their reference fossil fuel chains (Section 2.6) and land use change (Section 2.7). Three biomass production routes (i.e., sugarcane bioethanol, palm oil biodiesel, and acacia wood for bioelectricity) are considered, assuming production only takes place on surplus land.
Note that each energy crop is analyzed individually, which means, each energy crop is planted on 100% of the land released in each scenario (i.e., only oil palm, or only sugarcane, or only acacia is planted on surplus land by scenario). We do not consider planting the three energy crops at the same time in an area. By combining the GHG emissions of agricultural intensification, bioenergy production, and LUC, the overall GHG balance for the region is estimated for each scenario and each energy crop. Figure 2 presents an overview of the main steps of our approach.

Figure 2.
Methodological approach to assess the GHG balance of agricultural intensification and using the generated surplus land for bioenergy production to replace fossil fuels.

Agricultural Production in 2030
Food production in the Orinoquia region in 2030 is calculated according to Equation (1). Food production is estimated at national level, multiplying the estimated national population in 2030 with the per capita consumption, the self-sufficiently ratio (SSR) and food losses of each food product. National food production is then multiplied by the contribution of the Orinoquia region to the national production of each food product. The per capita consumption of food products in Colombia is expected to increase towards 2030 [1,30]. In line with the studies of MADR, (2016) and Younis et al., (2020), the SSR, food losses, and the relative contribution of Orinoquia region to national food production are assumed to remain stable to 2030. The land demand projection for agriculture in 2030 is based on the amount of land in use in 2018 (crops and cattle). For input data, see Table A1 in the Appendix A.
where: FoodProi = Orinoquia food production (t yr −1 ); i = Food product (rice, corn, soybean, cassava, plantain, palm oil, and beef); Pop = National population; Coni = Per capita consumption for food product i (kg person −1 yr −1 ); SSRi = Self-sufficiently ratio of food product i (%); Pi.orq = Orinoquia contribution to national production per each food product i (%); Lossi = Food losses in the supply chain for food product i (%). After calculating the production per food product for 2030, we calculate the land required for food production in 2030 for each scenario by dividing the production by the yields related to each scenario Equation (2).

Agricultural Intensification (Food Crops and Cattle)
Increasing agricultural productivity in the region could generate surplus land if the increase in productivity surpasses the increase in demand for agricultural products. Figure 3 illustrates how surplus land is determined, i.e., the difference between current land demand and future land demand that is projected according to different levels of agricultural intensification (see Table 1). The intensification scenarios assume improved agricultural practices such as the efficient use of fertilizers and the reduction of fossil fuel consumption. Before describing the key characteristics of improved agricultural practices and resulting yields below, we first summarize the scenarios here; additional information on the scenarios can be found in Appendix B. The reference scenario follows the conventional agricultural conditions (i.e., inefficient practices in fertilizer application and soil management). For the low intensification scenario, conventional agricultural practices are assumed, with an increase in crop yield based on some improvement in fertilizer application. In the medium intensification scenario, improvement of some agricultural practices is assumed such as crop fertilization and improved cattle management (cattle are fed with improved grasses and forage sorghum). For the high intensification scenario, sustainable intensification is assumed, with fertilizer application in accordance with soil requirements, soil improvements, and improved cattle feed quality (see Appendix B).

Food Crop Production
According to UPRA (2019), current fertilizer use is inadequate in Colombia since the application is not carried out based on soil analysis or plant nutrient requirements. This can result in deficits or excess of fertilizers and affects crop yields [31]. In this study, the fertilizer inputs per scenario, to achieve the crop nutrition requirements, consider the three main nutrients Nitrogen (N), Phosphorus (P), and Potassium (K). The amount of nutrients (kg ha −1 ) applied to each crop is based on literature and is related to the yield (see Table A2 in the Appendix B). Another important factor in agricultural yield intensification is crop mechanization [5]. Agricultural mechanization in Colombia is used mostly for soil preparation and harvesting, while the other tasks can also be carried out manually [31]. Rice is the crop that uses the most machines/equipment in Colombia [31]. In the Orinoquia region, rice is grown in rainfed conditions (dry rice), which means this crop receives water mainly from rainwater. Therefore, it does not require mechanization linked to irrigation [31]. Although currently mechanization is used in agriculture, there is not enough available historical data about fossil fuel consumption related to each crop in Colombia. Therefore, diesel usage in the reference scenario is based on literature as shown in Table A2 in the Appendix B. For the intensification scenarios, diesel consumption was assumed to reduce by 10% in the high scenario compared to the reference scenario, based on the study by Brinkman et al. (2018) [32] (see Table A2 in the Appendix B).
To establish the crop yield levels for each scenario, data analysis of agricultural yields for the period 2012-2018 for the Orinoquia region was conducted. The yield levels in the reference scenario are set at the 50th percentile of the reported yield levels in Orinoquia region in the period 2012-2018. The low scenario is set at 65th percentile, the medium scenario is set at 80th percentile, and the high scenario is set at the 95th percentile of the yield levels of the Orinoquia region in the period 2012-2018. Thus, for example, the rice crop yield is 4.97 t ha −1 yr −1 for the reference scenario and for the intensification scenarios, crop yields are 5.06; 5.26; and 5.96 t ha −1 yr −1 for the low, medium, and high scenarios, respectively. Projected yields for all food crops are shown in Table 1.

Beef Production
To increase cattle productivity, the production system can be intensified by several improvements such as fertilizing pastures, improved grasses, a better quality of animal feed, and pasture rotation [21,[33][34][35][36]. The current cattle production in the region is carried out in an extensive system. Considering that in this system (i) the pastures do not receive fertilization at any time of their lifetime, and (ii) the soil of the region is low in nutrients [37], we assume that the land from current cattle production is degraded. Since all future scenarios include cattle production on the current degraded land, we assume that in all future scenarios the land used for cattle is degraded. However, as better practices are applied to increase productivity, the increase in beef yield includes the improvement of cattle production systems with the use of improved (fertilized) pastures and silvopastoral systems as described as follow.
For the reference and low scenario, the current extensive production system of the foothill-high plain area is assumed, in which animal feed is based on pastures with low nutrient levels (e.g., Trachypogon vestitus) [10,37,38]. For the medium and high scenarios, it is assumed the cattle feed quality is improved (see Appendix B), using improved grassland (e.g., Brachiaria decumbens) and forage sorghum for the medium scenario [29]. While a mix of improved grassland (e.g., Brachiaria decumbens), fodder plants (e.g., leguminous herbs, and shrubs/trees), and forage sorghum improve the quality of the animal feed in the high scenario (it has been considered that for sustainable development of cattle production, the use of a silvopastoral grazing system is proper [33]). It was considered that the sorghum forage needs to be cultivated within the land used for cattle production. This land use is included in the total GHG emissions for cattle production as feed emissions. The characteristics of the production systems for the reference and intensification scenarios are described in the Appendix B. The projected increases in cattle productivity for the intensification scenarios follow the three levels of projected productivity increases of the Colombian livestock strategic plan of the National Federation of Breeders [15,39]. We consider these projected increases in cattle productivity realistic given the large range in current productivity, wherein some traditional farms an animal density of 1.5-1.8 heads per hectare is achieved. while in farms with improved systems animal densities of 3-4 heads per hectare are realized [40]. The resulting yields are reported in Table 1.

GHG Emission Associated with Agricultural Production
The GHG emissions of agricultural production were calculated for each scenario, taking a system boundary of cradle-to-farm gate. The emissions for all crop systems are expressed as kg CO2eq t −1 of product, which corresponds to tons of rice, tons of corn, tons of soybean, tons of plantain, tons of cassava, and tons of oil palm-fresh fruit bunches. For beef production, the emissions are expressed as kg CO2eq t −1 beef. The emissions include LUC-related emissions (see Section 2.7) and the emissions related to (annual and perennial) crop cultivation and beef production. The GHG emissions related to crop production include emissions of fertilizer production, fertilizer application, and diesel usage. In addition, since one of the annual crops is rice, methane (CH4) emissions from rice production are included following the Equations (A3) and (A4) in the Appendix B. The fertilizer application rate is related to the yield and the nutrition requirements of each crop, see Table  A2 in the Appendix B. For example, it was assumed that in a sustainable scenario like our high scenario, the fertilizer is applied according to the soil requirements. Furthermore, to improve the fertilization of crops, we assumed an increase in the efficiency of the use of nitrogen fertilizers that includes both the use of good agricultural practices and the use of slow-release nitrogen fertilizers (Appendix B). Emissions from fertilization include fertilizer production and direct/indirect N2O emissions of fertilizer application. For the diesel usage, we assumed the fossil fuel use by machinery goes down with higher agricultural yields, due to higher efficiency of the agricultural operations per ton of output. Diesel usage per crop per scenario, emission factors of fertilizers, and fertilizer application are included in Tables A2 and A3 in the Appendix B.
The GHG emissions from beef production includes emissions from feed production (CO2 and direct/indirect N2O; these emissions are calculated as for food crops), enteric fermentation (CH4), and manure management (CH4 and direct/indirect N2O). Emissions were calculated following IPCC 2019 Refinement guidelines (i.e., equations: 10.21; 10.22; 10.30; 11.1; and 11.5) [43]. Note that for all scenarios in this study, it is estimated that all cattle production is run on a grazing system. Therefore, following the IPCC 2019 method, it corresponds to the manure management system PRP i.e., "Pasture/Range/Paddock" where manure is not managed [43]. We assumed the increase in beef productivity is related to better quality/quantity feed supply (dry matter intake). This is because the change from pastures with low nutrient levels to pastures which deliver a higher nutrient content via the integrated systems of trees and fodder. This better fodder improves the digestibility of dry matter and increase the nutritional value of the feed, in terms of total protein and minerals [33,44].
Moreover, sustainable cattle production also includes better animal welfare (disease management), better management of pastures, fodders, and soil quality. One of the sustainable cattle production systems suggested for Colombia is called the silvopastoral system which could contribute to improving soil conditions and increasing C-stock [13,33]. The input data for calculating the GHG emissions of beef production for all scenarios are included in Table A4 in the Appendix. Considering that the IPCC 2019 methodology refined some of the default data according to high and low cattle productivity systems [43], we assume the use of these default data (when available) to apply it to the scenarios according to the related best practices (see Table A4 in the Appendix B).

GHG Emission Associated with Energy Crops
It is assumed that energy crops are cultivated, one at a time, on the surplus land obtained from the agricultural intensification described in Section 2.4. The amount of energy crops that can be produced depends on the amount of surplus land generated in each scenario and the energy crop yield (see Table A7 in the Appendix C). Since only in the medium and high scenarios large amounts of surplus land are obtained, energy crop cultivation is only evaluated for these two scenarios. The GHG emissions of energy crops include the emissions related to cultivation (fertilization and fossil fuel consumption) and to LUC. Emissions from fertilization include fertilizer production and direct/indirect N2O emissions of fertilizer application (Table A7). The calculation of the GHG emissions of energy crop cultivation follow the same logic as for food crops, see Section 2.5. In Tables A3 and A7 of the Appendix B and C, all input data and factor emissions for the calculations of the GHG emissions of energy crops cultivation are included.

GHG emission Related to Land Use Change
The expansion and contraction of agricultural land and the use of surplus land for energy crops results in changes in C-stock. Changes in C-stock were calculated for five different possibilities of LUC in the Orinoquia region as follows: considering that for the reference and low scenarios, the increase in agricultural land demand requires the use of natural vegetation (shrubland) and that forest is excluded for agricultural land use, the land-use conversions for these two scenarios are (a) from shrubland to cropland for food crops production. (b) From shrubland to pastureland in degraded pastures for cattle production (i.e., pastures with low nutrient levels). Note that in line with Rincon Castillo et al., (2012) and Rodríguez Borray et al., (2019), we assume that the land currently used for extensive cattle production is degraded. Therefore, the considered land-use conversions in the medium and high intensification scenarios are (c) cropland to cropland for food crops and (d) from degraded pastures to managed pastures for cattle production (beef). In the intensification scenarios, all the surplus land comes from cattle production areas (i.e., pastures with low nutrient levels). Therefore, for energy crops production the considered land use conversion is (e) from degraded pasture to energy crops (sugarcane, oil palm, and acacia). GHG emissions caused by changes in C-stocks due to the LUC food crops were calculated using Equation (3).
where, ELULUC = GHG emissions from C-stock change due to LUC (t CO2eq t −1 crop product). ΔCS = CSR − CSA (CSR = C-stock associated with the prior land-use (t C ha −1 ); CSA = Cstock associated with the new land-use (t C ha −1 ). P = crop productivity (t ha −1 year −1 ). An amortization period of 20 years is assumed. The factor 44/12 is used to convert carbon into CO2.
Each land use has a different carbon stock. The total C-stocks, including above and below ground biomass and SOC, of each land use type are included in Table 2. The time to be considered for changes in C-stocks was 20 years, in line with [43]. Note that in this study, energy crops are only planted in surplus land of the medium and high scenario. The C-stock for energy crops in the medium scenario corresponds to the average between the C-stock of the low and the high scenario. a Data for low scenario from [45]. Note that in this study, oil palm is used both as a food crop and as an energy crop. b High C-stock value from [46]. The low C-stock value (59.3) taken from [47]. c Data from [48]. The low C-stock value corresponds to 80 t C ha −1 .

Total GHG of Bioenergy Supply Chains
The total GHG emissions of sugarcane-bioethanol, palm oil-biodiesel, and acacia-bioelectricity include GHG emissions of energy crop cultivation, LUC, conversion plant (industrial production stage), and combustion (i.e., it refers to the conversion of biofuel to heat, electrical, or mechanical energy). For this study, it is assumed that the conversion plant for each bioenergy chain includes the following stages:


For bioethanol, conversion plant includes cane transport, milling process, and ethanol plant [49].  For biodiesel, conversion plant includes palm oil mill, physical refining (refined, blanched, and deodorized); transesterification; esterification of the free fatty acid (FFA); BD purification; glycerin purification (USP), and methanol recovery [22].  For bioelectricity, conversion plant includes sawmill and pellet mill [50]. It was assumed a CHP (combined heat and power) system for bioelectricity production. For the calculation, the stationary combustion emissions factor of the IPCC, 2019 (volume 2, chapter 2) was used.
Data and emission factors in the three-supply chain are presented in Table A8 of the Appendix. Note that for all three bioenergy supply chains, it was assumed that both the emissions in the conversion plant and the emissions from bioenergy use (combustion) do not vary in the scenarios, since the focus of this study is on the cultivation stage. Emissions from biomass combustion include emissions of methane (CH4), and nitrous oxide (N2O), but the biogenic CO2 emissions of the crop biomass are considered carbon neutral.
The GHG emissions caused by changes in C-stocks due to the LUC energy crops were calculated using Equation (3). The net GHG emissions of the supply chain per bioenergy are calculated using Equation (4).
where, FC: Fossil fuel consumption emissions. LUC: Land use change emissions. CCS: Crops C-stock sequestration. F: Fertilizer emissions (production and application). BPE: Bioenergy emissions by industrial production stage, BU: Bioenergy emissions by use (combustion/burning).
Comparing the GHG emissions of the bioenergy production routes with the emissions from the fossil reference systems (gasoline, diesel, and coal; see Table A8 of the in Appendix D), we evaluate the potential emission savings from bioenergy. Consequently, it is analyzed if the bioenergy GHG reduction levels meet the RED II GHG saving requirements.

Agricultural Intensification
In the reference scenario, the total calculated land demand for food production in the Orinoquia region in 2030 is 13.8 Mha, of which about 90% is used for beef production in extensive cattle grazing system ( Figure 4). Although this is still within the agricultural frontier area of 15.5 Mha, it is a little more than double the area currently in use for agriculture (6.8 Mha), due to the projected increase in demand. Compared to the reference scenario, there is 38% decrease in agricultural land use in the low scenario, 58% decrease in the medium scenario, and 70% decrease in the high scenario. In the medium and high scenario, the land for cattle production includes the land used to produce forage sorghum for improved beef production (491 and 496 thousand hectares, respectively).
In none of the intensification scenarios was surplus land obtained from food crops. Obtaining surplus land from agricultural intensification is only possible due to improvements in cattle productivity. In the low intensification scenario, there is not surplus land. In the medium scenario, it is possible to obtain 0.6 Mha of surplus land. In the high scenario, about 2.4 Mha of surplus land becomes available, which corresponds to 39% of the area currently used for cattle grazing (i.e., 6.2 Mha). For the medium and high scenario, the amount of energy cops and bioenergy that can be produced on surplus land is presented in Table 3. The highest bioenergy potentials are obtained when the surplus land is used to produce bioethanol from sugarcane or biodiesel from oil palm. This is due to the relatively higher ratio in the assumed conversion efficiency (MJ biofuel per kg raw material) of sugarcane and oil palm compared to acacia (i.e., one ton of FFB of oil palm produces 0.22 t of biodiesel with a calorific value of 37,000 MJ t −1 biodiesel, while one ton of sugarcane produces 0.07 t of bioethanol with a calorific value of 27,000 MJ t −1 bioethanol). In the high scenario, bioenergy potential is 3.8 to 5.4 times higher than in the medium scenario due to higher land availability and higher yield levels of the energy crops.  Figure 5 shows the annual GHG emissions of agricultural intensification (food crops and cattle) for all scenarios in 2030. LUC emissions result from the changes in C-stock due to land use change. The "LUC emissions" value in the figure considers both LUC emissions and C-stocks from food crops and pasture production for cattle. In the reference scenario, the largest GHG emission source is LUC which represents about 90% of the total GHG emissions of agricultural production (food crops and beef). The expansion of beef production is the main cause of LUC-related emissions (318 Mt CO2eq yr −1 ) due to the conversion of shrubland to degraded pastures (i.e., pastures with low nutrient levels). Regarding food crops in the reference scenario, the highest contribution to LUC emissions is related to the expansion of rice and oil palm (8.9 and 5.8 Mt CO2eq yr −1 , respectively) due to the conversion of shrubland to cropland.

GHG Emissions Associated with Agricultural Intensification
In the agricultural intensification scenarios, the LUC-related emissions are lower than in the reference scenario, but the low intensification scenario required the conversion of shrubland to degraded pastures to meet the demand for beef. Therefore, the LUC-related emissions in the low scenario are much higher than for the medium and high scenarios (191; 48; and 33 Mt CO2eq yr −1 , respectively). For the medium and high scenario, no natural land is converted to agricultural land and degraded pastures are improved to managed pastures. Moreover, the carbon storage in the managed pastures (fertilized) will increase productivity and therefore also increase the C-stocks of those lands. The emissions of feed production, i.e., sorghum forage, is only reported for the medium and high scenarios (3.4 and 2.9 Mt CO2eq yr −1 , respectively), as in these scenarios it is assumed that the quality of the animal feed was improved. These feed emissions include all emissions related to growing sorghum forage.
Note that, in agricultural production scenarios, the only two crops that report net carbon storage are oil palm and pastures. The oil palm cultivation to produce oil for human consumption is the only food crop that reports a net carbon sequestration as a perennial crop (i.e., negative LUC emissions) since the C-stock value considers the biomass of fronds, trunk and roots, the cover vegetation, and the associated organic matter that remains in the plantation after the harvest of the fruit (FFB). In the case of pastures to produce beef, the yield of beef production is directly linked with higher consumption of grass by cattle. For example, in the high scenario, total grass consumption is higher than in the reference scenario, but the demand for land to produce pastures is less in the high scenario compared to the reference scenario.
In the low, medium, and high scenario, the total (positive) emissions associated with food crop production (fertilization, fossil fuel, and CH4 emissions at the field) and beef production (CH4 emissions of enteric fermentation and manure, N2O emissions) are lower compared to the reference scenario. For the medium and high scenario, the reduction of emission is a result of better management practices such as increasing the fertilizer efficiency, reducing the consumption of fossil fuels, and improving cattle feed quality. Regarding the efficiency of fertilizers, from the application of urea in the reference scenario, we move on to the application of more efficient sources of fertilizer to reduce NH3 and N2O emissions by application and volatilization of fertilizers as described in the Appendix B. Regarding fossil fuel, the emission reduction is given mainly by the diesel reduction used by machinery (i.e., higher efficiency).
Regarding cattle feed quality, it is observed that with no change in quality animal feeding, as the number of animals increases, the CH4 emissions from enteric fermentation could increase, as observed between the current situation (2018) and the reference scenario (10.7 and 17.7 Mt CO2eq yr −1 , respectively). However, with a better-quality feed, the number of animals and their CH4 emissions by enteric fermentation would be reduced while the animal-beef ratio would be increased, as observed in the medium and high scenario (15.3 and 13.7 Mt CO2eq yr-1, respectively). When agricultural production intensifies sustainably (i.e., high scenario), there is a reduction in positive emissions of 83% compared to the reference scenario.

GHG Emissions Associated with Bioenergy Production
The net GHG emissions of bioenergy production and abated emissions compared to their fossil fuel equivalent for the medium and high scenario in 2030 are shown in Figure  6. For all bioenergy supply chains, the net GHG emissions are slightly higher in the high scenario than in the medium scenario, due to the use of better agricultural practices in the cultivation stage. For all bioenergy supply chains, the GHG emissions related to LUC dominate the GHG balance. Negative LUC emissions (sequestration) vary among bioenergy supply chains because the tree energy crops store much more carbon than the original vegetation present today (i.e., pastures with low nutrients). The LUC emissions from the oil palm crop behave the same as those described in Section 3.2, agricultural intensification.
For both scenarios, the emissions in the conversion of biomass to energy carriers of the three bioenergy chains are lower than the cultivation emissions, as shown in Table 4. The emissions from the use of biofuels (i.e., N2O and CH4 emissions by combustion) are the same for both biodiesel and bioethanol (0.3 g CO2eq MJ −1 biofuel) and higher for bioelectricity (i.e., burning of acacia pellets) (1.9 g CO2eq MJ −1 bioelectricity). Logically, under the high scenario, more surplus land is available for bioenergy production than in the medium scenario (2.4 and 0.6 Mha, respectively) and subsequently, the emissions related to each energy crop production system are in line with the quantity of raw material produced (PJ bioenergy yr −1 ). For example, the high scenario with biodiesel production reports a higher net GHG balance (−82.5 g CO2eq MJ −1 biofuel) than the high scenario with bioethanol production (−6 g CO2eq MJ −1 biofuel) as shown in Figure 6a. Industrial stage g CO2eq MJ −1 bioelectricity 0.0007 0.0007 The total GHG emissions of biofuels and bioelectricity production, including the emissions related to LUC, cultivation (fertilization and diesel use), conversion and direct use, are compared to their fossil counterpart to calculate the abated emissions ( Figure 6). Bioethanol, biodiesel, and bioelectricity production achieve more than 100% emission reduction compared to their fossil fuel equivalent. They thereby meet the RED II GHG saving requirements, which is 65% for biofuels (i.e., bioethanol and biodiesel) and 70% for bioelectricity.
In this study, the emissions resulting from the combustion biofuels in vehicle engines are not calculated, since CH4 and N2O emissions are highly dependent on the efficiency of the source technology, emission control, and combustion system that is not the core of this study. However, to identify whether the abated emission could be affected by the combustion of the biodiesel in an engine, we applied the brake thermal efficiency (BTE) of the computerized diesel engine reported by Soly et al. (2021), to the emissions from the biodiesel chain reported in our study (BTE is defined as the ratio of brake power of an engine and the energy of the fuel released during the combustion process [51]. Soly et al. (2021) found a BTE of 25.3% for diesel and 25.6% for biodiesel). As a result, the calculated abated emissions by the use of biodiesel, reported in our study, are affected by up to 1.3%.

Regional GHG Balance of Agricultural Intensification & Bioenergy Production
The GHG balance on the entire regional level, for both the agricultural intensification and bioenergy production, is shown in Figure 7. Increased agricultural yields, use of better agricultural practices, and use of surplus land for bioenergy production result in a decrease in net GHG emissions in the medium and high scenario compared to the reference and low scenario, and the current situation (2018). When comparing the net emissions of the reference and low scenario with the emissions of the current situation (2018), the emissions of the low scenario are slightly higher than in 2018 (153 and 141 Mt CO2eq yr −1 , respectively). However, the emissions of the reference scenario (231 Mt CO2eq yr −1 ) are 65% higher than the net emissions of 2018. In Figure 7, the results show that it is feasible to produce bioenergy on surplus land obtained from agricultural intensification (i.e., medium and high scenario), reducing the total emissions of the region and contributing to the increase in carbon sequestration with the use of any of the three energy crops raised in this study.
The abated emissions are logically higher in the high scenario compared to the medium scenario for all energy crops because of the larger amounts of raw material produced on surplus land in the high scenario. Also, it must be considered that the LUC emissions (sequestration) are calculated over 20-year lifetime period for all the crops, then the LUC benefit can only be gained during that period. However, if that crop lifetime is extended more benefits could be obtained from the LUC-related emissions.

Discussion
In this study, we calculated the GHG balance of increasing agricultural yields for food crop and beef production and using the generated surplus land for biomass production to replace fossil fuels for a key region in Colombia. The results highlight that sustainable intensification is a key measure to reduce GHG emissions associated with agriculture in the region and to produce low-ILUC-risk bioenergy. Furthermore, since the surplus land is projected to come largely from improving extensive cattle farming areas with low carbon stocks and bioenergy crops have higher carbon stocks, bioenergy production contributes to carbon stock increase. However, there are many uncertainties related to the assumptions and data used to calculate the overall GHG balance, which affects the results obtained, as discussed next.
Region-specific carbon stock measurements are needed. Depending on the soil type and its initial c-stock, variations in carbon stocks can impact the LUC-related emissions to a greater or lesser extent. It has been reported that the Orinoquia savanna lands have a carbon stock of around 126 t C ha −1 [18]. If this land is converted to cropland with a low carbon stock, it results in high GHG emissions. However, due to lack of field measurements, there is large uncertainty on the carbon stocks of the various land uses in the region [18][19][20]52,53]. For example, a study conducted in the Orinoquia's highplain showed that carbon stocks did not change with the conversion of managed grasslands to oil palm plantations [19]. The study also highlighted that the conversion of pastureland (i.e., degraded pastures) to perennial energy crops could benefit the ecosystem carbon storage (both soil and biomass carbon stock) [19]. Thus, the conversion of surplus land from degraded pastures (i.e., pastures with low nutrient levels) to energy crops could potentially generate greater soil and biomass carbon sequestration than converting it to improved pasture. A key requirement to achieve energy crop sustainability is to avoid the negative impacts that expansion of these crops could generate in the region [19,27,52]. First, reducing ILUC risks of energy crop requires sustainable intensification of the current agricultural production. Second, sustainable energy crop production is not only about carbon sequestration but also about biodiversity and water availability. Third, the conversion of native savanna results in considerably increased LUC-related emission; its use for bioenergy crop production is therefore to be avoided because of the high indirect GHG emissions issues, it could cause.
Increasing current cattle productivity is key to reduce future agricultural land demand and associated GHG emissions. Increasing cattle productivity requires a set of management improvements (i.e., quantity of feed supplied, forage type, and forage quality) [29,40,54]. The implementation of those improvements over time is still a key topic for further research and will depend on support measures for the sector. In the Orinoquia region, the increased land demand leads to increased LUC emissions as shrubland (natural savannas) became pastureland. Therefore, a sustainable increase in cattle productivity would decrease land demand, increase the amount of beef produced, and decrease LUCrelated emissions. Moreover, improvement in the nutrition of cattle feed also contributes to the GHG emissions reduction [29,54].
To warrant low LUC-related emissions, more refined knowledge about the future location of surplus land is required. In this study, the location of the agricultural areas of the region was not considered. Only the amount of land used to produce both food crops and cattle was considered. Therefore, it is not possible to spatially identify the areas where the surplus land for the cultivation of energy crops is located. Just as specific measurements of carbon stocks in the region are required, it is also necessary to establish the location of current agricultural areas, particularly areas with an extensive cattle production system. This way the uncertainty of the related-LUC emissions could be reduced and facilitate the application of agricultural intensification measures. Another key point to reduce the uncertainty of emissions in cattle production is related to the quality of emission data of the different management levels of cattle. In this study, we use the factors updated by the IPCC in the 2019 refinement, which included data for Latin America. However, identification of national or regional emission factors could contribute to establishing more accurate results of emissions from cattle production.

Conclusions
In this study, the total GHG balance of future agricultural land use in the Orinoquia region was analyzed for different agricultural intensification scenarios and using the generated surplus land for energy crops. The total land requirement in the Orinoquia region to meet the demand for food crops and beef in 2030 shows an increase of a little more than double the land in the reference scenario compared to the demand for land in 2018. The largest land demand in the reference scenario is for beef production in extensive grazing systems, occupying more than 90% of the agricultural area. Although the land demand in the reference scenario is within the available agricultural land (agricultural frontier) of the region, it requires the conversion of shrubland to pastureland and causing large amounts of LUC-related emissions.
In the medium and high intensification scenario, less area is required to produce the same amount of food compared to 2018 due to an increase in agricultural productivity. The increase in cattle productivity is key to release between 10% and 38% of the current cattle production area for bioenergy feedstock production. The medium and high agricultural intensification scenarios result in decreased LUC-related emissions compared to the reference scenario, since no natural vegetation (shrubland) is converted, and degraded pastures are improved to be used as managed pastureland. The application of better agricultural practices when intensifying agricultural production can reduce up to 83% of the positive GHG emissions of the reference scenario.
Bioenergy potential production on the surplus land obtained is projected at 36 to 368 PJ per year been considered as low-ILUC-risk because using surplus land minimizes concerns related to competition for land and displacement effects. As the cattle areas that generated surplus land are expected to consist largely of degraded pastures, the conversion of degraded pastures to energy crops can result in substantial carbon sequestration. Moreover, bioenergy production (biodiesel, bioethanol, or bioelectricity) as the bioenergy options assessed results in a reduction in GHG emissions of more than 100% compared to its fossil fuel equivalent (diesel, gasoline, and coal, respectively), meeting the RED II GHG saving requirements. Our study focused only on GHG emissions, but sustainable intensification of crops and cattle production as well as bioenergy feedstock production also requires assessment of other environmental and socio-economic impacts of agricultural intensification and bioenergy production. This will be tackled in follow-up work being carried out by Ramirez-Contreras et al. (2021) [55]. Funding: This research was funded by the bilateral program "Towards a long-term science and innovation collaboration between Colombia and the Netherlands in Biomass Valorization" (RVO-TF13COPP7B). Moreover, funding support from the Palm Oil Promotion Fund (FFP), administered by Fedepalma.

Informed Consent Statement: Not applicable.
Data Availability Statement: Not applicable.

Conflicts of Interest:
The authors declare no conflict of interest.

 Agricultural intensification levels
Agricultural production in the Orinoquia region requires sustainable intensification to reduce GHG emissions while increasing food production (food crops and beef). The efficient use of fertilizers, reduction of fossil fuel consumption, and reduce the impact of LUC are related as some of the better agricultural practices known for their potential to reduce GHG emissions. See input data for food crops in Table A2 and input data for cattle production in Table A4. The intensification levels are based on the study by 5nd listed below: (i) Conventional agricultural practices: -For crops: it refers to the traditional production in the foothill-highplain area, where the agricultural practices are not enough improved to increase crop yield (i.e., fertilizer is applied without including soil requirements; no soil correction is made). Soil improvements or soil correction means adapting the soil to establish or maintain a crop. In the Orinoquia region, the main limiting factor for soils is acidity, then lime or another product is added to improve chemical deficiencies [29,59,60]. Generally, corrective measures are applied before planting activities that is why prior soil analysis is essential to detect these problems and formulate appropriate corrective applications [31]. -For beef production: this is the extensive cattle production system currently used in the foothill-highplain area, where cattle are fed only with natural grassland with low nutrient content. This grassland has not received fertilization.
(ii) Intermediate intensification: -For crops: it allows increasing crop yields with the improvement of some agricultural practices (i.e., fertilizer is applied according to the soil requirements, but no soil correction is made; adequate soil conditioning is not done).
-For beef production: it is an improved extensive production system. Cattle are fed with improved grasses (e.g., Brachiaria decumbens) and forage sorghum (fertilizer is used for improved grasses and forage sorghum). The forage sorghum is mainly used during dry season to complete the cattle feed.
(iii) Sustainable intensification: -For crops: this pathway uses better agricultural practices to increase crop yield (i.e., fertilizer is applied according to the soil requirements; soil correction is made; grasses/legume are used; zero tillage is done). -For beef production: Animal increase in productivity is attained by the improvement of feed quality supplied since the animal feed is based on improved grasses (e.g., Brachiaria decumbens) and forage sorghum. The forage is used to supply the needs in during the dry season (fertilizer is used for improved grasses and forage sorghum). It is assumed that for this sustainable scenario the grazing system is silvopastoral or agrosilvopastoral.

 Fertilization
The use of nitrogen fertilizers causes GHG emissions [61]. Nitrogen fertilizer urea (N) releases nitrous oxide (N2O) and ammonia (NH3) during its application. About 25% of the urea applied to a crop volatilizes as NH3, of which about 1-2% is subsequently converted to N2O. The reduction of NH3 and N2O emissions depends on increasing the efficiency of nitrogen fertilizer use, which includes both the use of good agricultural practices and the use of slow-release nitrogen fertilizers [62]. Therefore, we assumed that to reduce emissions by application and volatilization of fertilizers, in the high scenario, more efficient sources of fertilizer are used. Below are the nutrient sources used by scenario:

 Emission factors (EF)
Tables A2 and A3 show the input data and emission factors associated to crops production. Only chemical fertilization was considered. Organic fertilization was not considered. The EF of fertilizer production were taken from Ecoinvent database, version 3.0.1.0. For all crops, emission calculations include LUC emissions over twenty years following IPCC 2019 guidelines (IPCC equation 2.1 to calculate annual C-stock changes; equation 2.5 for LUC emissions; equations 11.1; 11.9 and 11.10 for N2O emissions) [43]. The N2O emissions from managed soil were calculated based on the IPCC methodology (IPCC equations for N2O emissions are equations 11.1; 11.9 and 11.10) [43] and following the Equations (A1) and (A2). The emissions factor of diesel production and diesel-burning by use are assumed based on IPCC guidelines [43]. To calculate the CH4 emissions for rainfed rice cultivation, the IPCC 2019 Tier 1 approach was used, see Equation (A3) (eq. 5.1 of chapter 5 of [43]). The factor emission (i.e., daily emission factor, kg CH4 ha −1 day −1 ) is calculated using the Equation (A4) (eq. 5.2 of chapter 5 of [43]). CH = EF * t * A * 10 (A3) where, CH4 rice = annual methane emissions from rice cultivation, Gg CH4 yr −1 . EFi = a daily emission factor for i condition, kg CH4 ha −1 day −1 . ti = cultivation period of rice for i condition, day. Ai = annual harvested area of rice for i condition, ha yr −1 . i = type of rice. EFc = baseline emission factor (1.27). SFw = scaling factor to account for the differences in water regime during the cultivation period (0.45, value taken from Table 5.12 of chapter 5 corresponding to "drought periods occur during every cropping season"). SFp = scaling factor to account for the differences in water regime in the pre-season before the cultivation period (1.22, value taken from Table 5.13 of chapter 5). a For all scenarios. fertilization data to each crop were calculated based on data from [63]. b The annual amount of synthetic N-fertilizer applied to crops also correspond to FSN value in Equation (A1) and Equation (A2). c For oil palm crop, the amount of fertilizer is expressed per ton of fresh fruit bunches (FFB). d Diesel consumption for the reference scenario is based on literature as follow: data for rice taken from [64]; for corn [65]; for oil palm [22]; for plantain [66]; for soybean [67]; for cassava [68]. For the intensification scenarios, it was assumed that diesel consumption would decrease from the reference scenario until reaches a reduction up 10% in the high scenario. This reduction is being considered based on the study by [32].  [64]. c Controlled release nitrogen fertilizer as N (0.46% N), was assumed to report a lower production emission factor compared to Urea. Therefore, the emission factor of the lowest nitrogen fertilizers (SAM) is applied. d Emission factors for N2O emissions calculation (direct/indirect) resulting from N-fertilization were taken from [43]. e Fossil fuel emission factor were taken from [43].

 Beef production
In this study, we differentiate three categories of cattle based on the IPCC, 2019 classification: growing cattle, other mature cattle, and mature double-purpose cattle. It is assumed that the composition of the herd remains constant over time and is the same for all scenarios. The description of each category is as follows,

-
Growing cattle: it includes calves pre-weaning, growing/fattening cattle. It is estimated 18% of animals in the herd correspond to this category [57]. -Other mature cattle: it includes male used to produce meat, breeding, and draft purposes. It is estimated 28% of animals in the herd correspond to this category [57]. -Mature double-purpose cattle: it includes the cows used to produce the cattle for beef, also produce milk for raising the growing cattle and other purposes. It is estimated 54% of animals in the herd correspond to this category [57]. The cattle production system (i.e., extensive grazing, improved extensive grazing, and silvopastoral grazing) varies according to the scenarios, as described in Section 3.3 on agricultural intensification. When IPCC, 2019 does not require split up the cattle categories or when there are no specific values for a specific cattle category, we consider the closest value that resembles those that can be reported (see footnotes in the tables). Input data in Table A4.  [15,39]. b Animal population data was calculated considering the beef requirement per year, animal unit per ha, beef extraction factor, and extraction rate per scenario. c The cattle population was classified into three main subcategories according to [43] and it was considered the share for each category according to the information taken from [57]. d It is the percentage of carcass beef with respect to the live animal's weight. Data from [39,57]. e It correspond to the percentage of the annual quantity of slaughtered beef cattle, Data from [39,57]. f Own calculations based on the animal liveweight per categories and its relationship with the daily dry matter intake. g Considering that in Table 10.8a in chapter 10 of IPCC, 2019, the diet quality can be selected, we assumed low quality diet in the reference and low scenario. Moderate quality diet for medium scenario and high-quality diet for the high scenario. Then, average default values from Table  10.8a are selected [43]. h GE was calculated by multiplying the DMI value by the default value of 18,45 MJ kg-1 of dry matter [43]. i The Ym value of 7.0 is apply in reference and low scenario assuming non-dairy animal category and the nonfeedlot diets (low quality pasture). The Ym value of 6.3 is apply in the medium and high scenario assuming high quality forage diets [43]. j Default values for volatile solid excretion rate from Table 10.13A of the chapter 10 for Latin America region from [43]. For the reference and low scenario, it was selected "low PS for other cattle." For the medium scenario, it was selected "means value for other cattle." For the high scenario, it was selected "High PS for other cattle." k Default values in chapter 10 from [43]. l Default values in chapter 10 from [43]. Methane emission factor for all animals in low and high productivity under a pasture, range, and paddock manure managed system. m Default values from Table 10.19 of the chapter 10 for Latin America region from [43]. For the reference and low scenario, it was selected "low PS for other cattle." For the medium scenario, it was selected "means value for other cattle". For the high scenario, it was selected "High PS for other cattle." n Calculated with Equation 10,30 [43]. o Default value for wet climates from (a) Emissions from feed production (CO2, N2O) It is assumed that during the dry season, sorghum forage is consumed as part of the animal feed for the medium and high scenarios. Sorghum emissions are calculated as for food crops. The grain sorghum yield is 4.8 and 5.16 t ha −1 year −1 for the medium and high scenario, respectively [24]. The yield of the entire plant i.e., grain, leaves, and stalks was estimated at 55.5 t ha −1 year −1 [69]. LUC emissions are from degraded pastureland to annual cropland. Input data in Table A5   Table A5. Input data for sorghum forage for the medium and high scenarios.

Scenario
where, Total CH4 Enteric = Total methane emissions from enteric fermentation in Gg CH4 yr −1 . Ei,P = Methane emissions per cattle category i per production system P. The methane emissions from enteric fermentation per cattle category per production system, are calculated according to Equation (A6) (eq. 10.21 of IPCC 2019).
The DMI per head per day varies across cattle categories and production system and relates to the live body weight and diet of the cattle, see Equation (A8) for "growing cattle" where, DMI = dry matter intake, kg day −1 ; BW = live body weight, kg.
(c) Methane emissions from manure management For all scenarios, it is estimated that cattle production is run on a grazing system where manure deposited on pasture. According to IPCC 2019 method, it corresponds to the manure management system "Pasture/Range/Paddock" (PRP) [43]. In this system, to estimate CH4 produced from manure deposited on pasture, the manure management includes both dung and urine. When manure is deposited on pastures, rangelands or paddock less CH4 is produced since it tends to decompose under aerobic conditions. The methane emissions from manure management vary across cattle types, production system, and manure management system. Considering that in this study, the scenarios are raised under four levels of productivity (see Section 3.3), we applied the Tier 1a approach of the IPCC 2019 to estimate CH4 emissions from manure, see Equation (A10) and Equation (A11) (eq. 10.22 and eq. 10.22A of chapter 10 of [43]). where, CH4 (mm) = CH4 emissions from Manure Management, kg CH4 yr −1 . NT,P = number of head of livestock species/category T, for productivity system P; VS(T,P) = annual average vs. excretion per head of species/category T, for productivity system P, in kg vs. animal −1 yr −1 . AWMST,S,P = fraction of total annual vs. for each livestock species/category T that is managed in manure management system S in the country, for productivity system P, dimensionless. EFT,S,P = emission factor for direct CH4 emissions from manure management by animal species/category T, in manure management system S, for productivity system P, in g CH4 kg VS −1 . The vs. excretion per head per cattle type and per production system is calculated according to Equation (A11) (eq. 10.22A of IPCC 2019).
where, VS(T,P) = annual average vs. excretion per head of species/category T, for productivity system P, in kg vs. animal −1 yr −1 . VSrate (T,P)= default vs. excretion rate, for productivity system P, kg vs. (1000 kg animal mass) −1 day −1 . TAMT,P = typical animal mass for livestock category T, for productivity system P, kg animal −1 .
(d) Direct N2O emissions from manure management The direct N2O emissions generated by manure in the system 'pasture, range, and paddock' are reported by IPCC, 2019 method in Section 11.2 of Chapter 11, under the category 'N2O Emissions from Managed Soils' [43]. For cattle production in all the scenarios, N2O emissions are estimated using Equations (A12) and (A13) (Eq. 11.5 of chapter 11 of IPCC, 2019) by Tier 1 approach.
where, N2O-NPRP = annual direct N2O-N emissions from urine and dung inputs to grazed soils, kg N2O-N yr −1 . FPRP = annual amount of urine and dung N deposited by cattle grazing on pasture, range and paddock, kg N yr −1 . EF3PRP = emission factor for N2O emissions from urine and dung N deposited by cattle grazing on pasture, range and paddock, kg N2O-N (kg N input) −1 . 44/28 = Conversion of N2O-N emissions to N2O emissions for reporting purposes.
where, FPRP = annual amount of urine and dung N deposited by cattle grazing on pasture, range and paddock, kg N yr −1 . NT = number of head of livestock species/category T. NexT = annual average N excretion per head of species/category T in kg N animal −1 yr −1 . MST, PRP = fraction of total annual N excretion for each cattle category T that is deposited on pasture, range, and paddock.

Land-use changes (LUC)
LUC were considered based on the current regional conditions of the available area within the agricultural frontier and analyzing the results of the land demand for the proposed scenarios. Therefore, since the reference and low scenarios project an increase in the land demand for agricultural production, the conversion of shrubland to cropland is required for food crops production. On the other hand, beef production conditions for these two scenarios correspond to extensive cattle production. Considering that this cattle production system leads to soil degradation [10,13,20] and the use of more land to meet future needs, it was defined that beef production requires the conversion of shrubland to degraded pastures. For the medium and high scenarios, it is projected that the increase in land demand does not exceed the current land demand. Therefore, for food crop production, the conversion is from cropland to cropland. For beef production, it is estimated that the cattle production system improves then, the land conversion is from degraded pastures to managed savannas, where the improvement in pastures and the mixture with forages, legumes, and trees allows the improvement of carbon stock of the entire production system and it benefits animal welfare [33].
In Colombia, the areas suitable for agricultural, livestock, forestry, aquaculture, and fisheries production were delimited recently [12]. According to UPRA [12], the suitable land was identified based on a comprehensive analysis of physical, ecosystemic, and socio-economic criteria of the territory at the national level. (1) Physical criteria include temperature, precipitation, soil moisture, nutrient availability, degree of erosion, soil texture, soil slope, and landslide susceptibility. (2) Ecosystem criteria include land cover, ecological integrity, fire threat, strategic ecosystems. (3) Socio-economic criteria include infrastructure and logistics, cost of land, economic indicators, labor market [12]. Considering that delimitation, Table A6 shows the land distribution we assumed for this study. The largest area to focus the land intensification should be the foothill-high plain since this area has the mayor available agricultural area (ha) of the region. To date, the flooded plain area has been devoted mostly to cattle production rather than crop production. Moreover, considering the flooded plain has a sensitive ecosystem that could be affected by largescale production of crops [27,28]. Then, we consider that in the flooded plain area the focus should be mostly on livestock production and only in some small areas produce annual crops.  [23]. b Official data of the national government which corresponds to available land for agricultural production in the Orinoquia region, Also called Agricultural frontier [23]. c According to the zoning of production areas within the agricultural frontier made by [12,28], land suitability is classified as follow: highly suitable (+++) corresponds to land with the best physical, ecosystem and socioeconomic conditions for crop or cattle production. Moderately suitable (++) is related to areas with moderate physical, ecosystem or socioeconomic limitations that require investment around the area for optimal production management. Lowly suitable (+) is related to areas with significant limitations (physical, ecosystem or socioeconomic), which require large investments or the development of new technologies for optimal production [12,28].

Appendix C. Parameters for Calculation of GHG Emissions Associated to Energy Crops
For determining the GHG emissions for energy crops, the following key characteristics of the energy crop production are needed: for sugarcane, it is assumed that its production is exclusive for bioethanol production, a ratoon cycle of 7 years is assumed [49]. Currently, oil palm plantations in Colombia are used to produce crude palm oil (CPO) for both food use and biodiesel [71]. However, it is assumed all oil palm cultivated on surplus land is dedicated to biodiesel production. Input data (chemicals, water, fuel, and electricity) for biodiesel production is based on a previous study by [22]. For oil palm crop, a lifetime of 25 years is assumed (5 years of establishment, 20 years of full crop cover, 24 harvests of fresh fruit bunches-FFB per year). Note that byproducts of sugarcane and oil palm production are not accounted for this analysis. The lignocellulosic biomass assessed is acacia (A. mangium) which is assumed to be used to produce bioelectricity (combined heat and power -CHP). A rotation of 10 years and one harvest is assumed [72]. Data and assumptions see Table A7. A. mangium is one of the most prominent species given its rapid growth, its high adaptive capacity to different environments, the potential for recovery of degraded soils, and the possibility of generating rapid changes in the landscape [73][74][75]. This plant has a high tolerance to conditions of water stress (deficit or excess) and nutritional deficiency in soils. Thus, it can grow in tropical areas with low rainfall, high solar radiation and high temperatures [74]. The use of A.mangium from the Orinoquia region is estimated for traditional timber products (boards, wood pulp) and wood products for the chemical, cosmetic and food industry, energy, second generation biofuels, charcoal, charcoal briquettes and activated carbon [17,76]. However, the greatest use is expected to produce electricity [75]. a Yield data from [24,41]. Sugarcane is expressed in tons of cane per hectare. Note sugarcane crop yield does not report great variation between scenarios because the data were taken from the only current crop in the region with information from 2013-2018. Where medium scenario corresponds to percentile 80 of the period data; and high scenario corresponds to percentile 95. b Yield data from [77]. Oil palm yield is expressed in terms of Fresh fruit bunches (FFB) per hectare. The yield increase follows the regional data for the period 2012-2018. Where medium scenario corresponds to percentile 80 of the period data; and high scenario corresponds to percentile 95. c Yield data from [78] Acacia is expressed in tons of wood per hectare. d For all scenarios, fertilization data to each energy crop were calculated based on data from [63]. The use of nitrogen fertilizers has implications for GHG emissions as described in Appendix A. e Diesel consumption for oil palm is based on data from [22]. Diesel consumption in sugarcane from [79]. Diesel consumption in acacia plantation is taken from a forest harvesting system working the traditional forestry tasks using chainsaw, winch, and walking tractor [80].

Appendix D. Parameters for Calculation of GHG Emissions Associated to Bioenergy Products
The emissions associated with the three bioenergy products are calculated (i.e., sugarcane-bioethanol, oil palm-biodiesel, and acacia wood-bioelectricity) (see Table A8). For all cases, the cultivation stage, the conversion plant, and the bioenergy burning (combustion) stage (i.e., the process of converting biofuel to energy: heat, electricity, or mechanical energy) are included.