With annotations by: AccessIPCC - Version 1.02 - 2010 Dec 14 - Contains annotated versions of all 44 Chapters of Working Groups 1, 2 & 3
With the exception of Chapter and Section headings, all coloured text has been inserted by AccessIPCC. The non-coloured text is the IPCC original.
A number of emails from the Climate Research Unit (CRU) of the University of East Anglia were published on the Internet in November 2009. This has provided a window into the world of climate science.
We have identified a number of key individuals involved in the emails whom we have designated as Persons of Concern [PoC]; a Journal in which a PoC has published has been designated as a Journal of Concern [JoC].
This is not to suggest that we believe such papers are necessarily flawed, but rather that, as Joseph Alcamo noted at Bali in October 2009, "as policymakers and the public begin to grasp the multi-billion dollar price tag for mitigating and adapting to climate change, we should expect a sharper questioning of the science behind climate policy".
References occur in a list at the end of each chapter. Citations are within the normal text of sections and paragraphs.
Person of Concern Key individual involved in CRU emails as defined in this spreadsheet.
|References, Citations, IPCC Roles||-||-|
Journal of Concern A Journal which has published articles by one or more PoCs (Person of Concern)
Model or Simulation Reference appears to be a model or simulation, not observation or experiment
Non Peer Reviewed Reference has no Journal or no Volume or no Pages or it has Editors.
Self Reference Concern Author of a chapter containing references to own work.
|References, Citations, IPCC Roles||59||100|
Paper authored or co-authored by person who is also in list of Authors of another chapter.
Paper dated 2007, when IPCC policy stated cutoff was December 2005
The short inline citation matched with more than one reference; however, AccessIPCC will link to the first reference found.
The short inline citation was not matched with any reference. Believed to be caused by typing errors.
The reference was probably peer reviewed.
|Chapter 8: Agriculture||-||-||-||-|
|8.10 Long-term outlook||8||10||-||-|
|8.2 Status of sector, development trends including production and consumption, and implications||3||11||-||-|
|8.3 Emission trends (global and regional)||-||9||-||-|
|8.3.1 Trends since 1990||-||3||-||-|
|8.3.2 Future global trends||1||10||-||-|
|8.3.3 Regional trends||-||9||-||-|
|8.4 Description and assessment of mitigation technologies and practices, options and potentials, costs and sustainability||-||-||-||-|
|8.4.1 Mitigation technologies and practices||9||13||-||-|
|18.104.22.168 Cropland management||33||40||-||1|
|22.214.171.124 Grazing land management and pasture improvement||17||18||-||-|
|126.96.36.199 Management of organic/peaty soils||4||5||-||-|
|188.8.131.52 Restoration of degraded lands||-||-||-||-|
|184.108.40.206 Livestock management||22||19||1||-|
|220.127.116.11 Manure management||11||4||-||-|
|8.4.2 Mitigation technologies and practices: per-area estimates of potential||1||9||-||-|
|8.4.3 Global and regional estimates of agricultural GHG mitigation potential||-||-||-||-|
|18.104.22.168 Technical potential for GHG mitigation in agriculture||-||16||-||-|
|22.214.171.124 Economic potential for GHG mitigation in agriculture||-||24||1||-|
|8.4.4 Bioenergy feed stocks from agriculture||-||-||-||-|
|126.96.36.199 Residues from agriculture||-||1||-||-|
|188.8.131.52 Dedicated energy crops||-||9||-||-|
|8.4.5 Potential implications of mitigation options for sustainable development||1||8||-||-|
|8.5 Interactions of mitigation options with adaptation and vulnerability||-||5||-||-|
|8.6 Effectiveness of, and experience with, climate policies; potentials, barriers and opportunities/implementation issues||-||-||-||-|
|8.6.1 Impact of climate policies||1||10||-||-|
|8.6.2 Barriers and opportunities/implementation issues||3||10||-||-|
|8.7 Integrated and non-climate policies affecting emissions of GHGs||-||-||-||-|
|8.7.1 Other UN conventions||-||-||-||-|
|8.7.2 Macroeconomic and sectoral policy||-||4||-||-|
|8.7.3 Other environmental policies||-||-||-||-|
|8.8 Co-benefits and trade-offs of mitigation options||17||14||-||-|
|8.9 Technology research, development, deployment, diffusion and transfer||-||4||-||-|
|Number of citations of various credibilities||137||283||2||1|
|Percentages of citations of various credibilities||32.4%||66.9%||0.5%||0.2%|
Pete Smith (UK) [SRC:15], Daniel Martino (Uruguay) [SRC:2],
|SRC >= 5||1|
|Potentially Biased Authors||2|
Zucong Cai (PR China) [SRC:8], Daniel Gwary (Nigeria) [SRC:2], Henry Janzen (Canada) [SRC:8], Pushpam Kumar (India) [SRC:3], Bruce McCarl (USA) [SRC:13], Stephen Ogle (USA) [SRC:7], Frank O’Mara (Ireland) [SRC:8], Charles Rice (USA) [SRC:6], Bob Scholes (South Africa), Oleg Sirotenko (Russia) [SRC:3], Mark Howden (Australia) [SRC:2], Tim McAllister (Canada) [SRC:3], Genxing Pan (China) [SRC:5], Vladimir Romanenkov (Russia) [SRC:3], Steven Rose (USA) [SRC:1], Uwe Schneider (Germany) [SRC:5], Sirintornthep Towprayoon (Thailand) [SRC:2], Martin Wattenbach (UK) [SRC:2],
|SRC >= 5||8|
|Potentially Biased Authors||17|
Kristin Rypdal (Norway), Mukiri wa Githendu (Kenya),
Smith, P., D. Martino, Z. Cai, D. Gwary, H. Janzen, P. Kumar, B. McCarl, S. Ogle, F. O’Mara, C. Rice, B. Scholes, O. Sirotenko, 2007: Agriculture. In Climate Change 2007: Mitigation. Contribution of Working Group III to the Fourth Assessment Report of the Intergovernmental Panel on Climate Change [B. Metz, O.R. Davidson, P.R. Bosch, R. Dave, L.A. Meyer (eds)], Cambridge University Press, Cambridge, United Kingdom and New York, NY, USA.
Agricultural lands (lands used for agricultural production, consisting of cropland, managed grassland and permanent crops including agro-forestry and bio-energy crops) occupy about 40-50% of the Earth’s land surface.
Agriculture accounted for an estimated emission of 5.1 to 6.1 GtCO2-eq/yr in 2005 (10-12% of total global anthropogenic emissions of greenhouse gases (GHGs)). CH4 contributes 3.3 GtCO2-eq/yr and N2O 2.8 GtCO2-eq/yr. Of global anthropogenic emissions in 2005, agriculture accounts for about 60% of N2O and about 50% of CH4 (medium agreement, medium evidence). Despite large annual exchanges of CO2 between the atmosphere and agricultural lands, the net flux is estimated to be approximately balanced, with CO2 emissions around 0.04 GtCO2/yr only (emissions from electricity and fuel use are covered in the buildings and transport sector, respectively) (low agreement, limited evidence).
Globally, agricultural CH4 and N2O emissions have increased by nearly 17% from 1990 to 2005, an average annual emission increase of about 60 MtCO2-eq/yr. During that period, the five regions composed of Non-Annex I countries showed a 32% increase, and were, by 2005, responsible for about three-quarters of total agricultural emissions. The other five regions, mostly Annex I countries, collectively showed a decrease of 12% in the emissions of these gases (high agreement, much evidence).
A variety of options exists for mitigation of GHG emissions in agriculture. The most prominent options are improved crop and grazing land management (e.g., improved agronomic practices, nutrient use, tillage, and residue management), restoration of organic soils that are drained for crop production and restoration of degraded lands. Lower but still significant mitigation is possible with improved water and rice management; set-asides, land use change (e.g., conversion of cropland to grassland) and agro-forestry; as well as improved livestock and manure management. Many mitigation opportunities use current technologies and can be implemented immediately, but technological development will be a key driver ensuring the efficacy of additional mitigation measures in the future (high agreement, much evidence).
Agricultural GHG mitigation options are found to be cost competitive with non-agricultural options (e.g., energy, transportation, forestry) in achieving long-term (i.e., 2100 ) climate objectives. Global long-term modelling suggests that non-CO2 crop and livestock abatement options could cost-effectively contribute 270– 1520 MtCO2-eq/yr globally in 2030 with carbon prices up to 20 US$/tCO2-eq and 640– 1870 MtCO2-eq/yr with C prices up to 50 US$/tCO2-eq Soil carbon management options are not currently considered in long-term modelling (medium agreement, limited evidence).
Considering all gases, the global technical mitigation potential from agriculture (excluding fossil fuel offsets from biomass) by 2030 is estimated to be ~5500-6,000 MtCO2-eq/yr (medium agreement, medium evidence). Economic potentials are estimated to be 1500 - 1600, 2500 - 2700, and 4000-4300 MtCO2-eq/yr at carbon prices of up to 20, 50 and 100 US$/tCO2-eq, respectively About 70% of the potential lies in non-OECD/EIT countries, 20% in OECD countries and 10% for EIT countries (medium agreement, limited evidence).
Soil carbon sequestration (enhanced sinks) is the mechanism responsible for most of the mitigation potential (high agreement, much evidence), with an estimated 89% contribution to the technical potantial. Mitigation of CH4 emissions and N2O emissions from soils account for 9% and 2%, respectively, of the total mitigation potential (medium agreement, medium evidence). The upper and lower limits about the estimates are largely determined by uncertainty in the per-area estimate for each mitigation measure. Overall, principal sources of uncertainties inherent in these mitigation potentials include: a) future level of adoption of mitigation measures (as influenced by barriers to adoption); b) effectiveness of adopted measures in enhancing carbon sinks or reducing N2O and CH4 emissions (particularly in tropical areas; reflected in the upper and lower bounds given above); and c) persistence of mitigation, as influenced by future climatic trends, economic conditions, and social behaviour (medium agreement, limited evidence).
The role of alternative strategies changes across the range of prices for carbon. At low prices, dominant strategies are those consistent with existing production such as changes in tillage, fertilizer application, livestock diet formulation, and manure management. Higher prices elicit land-use changes that displace existing production, such as biofuels, and allow for use of costly animal feed-based mitigation options. A practice effective in reducing emissions at one site may be less effective or even counterproductive elsewhere. Consequently, there is no universally applicable list of mitigation practices; practices need to be evaluated for individual agricultural systems based on climate, edaphic, social setting, and historical patterns of land use and management (high agreement, much evidence).
GHG emissions could also be reduced by substituting fossil fuels with energy produced from agricultural feed stocks (e.g., crop residues, dung, energy crops), which would be counted in sectors using the energy. The contribution of agriculture to the mitigation potential by using bioenergy depends on relative prices of the fuels and the balance of supply and demand. Using top-down models that include assumptions on such a balance the economic mitigation potential for agriculture in 2030 is estimated to be 70- 1260 MtCO2-eq/yr at up to 20 US$/tCO2-eq, and 560- 2320 MtCO2-eq/yr at up to 50 US$/tCO2-eq There are no estimates for the additional potential from top down models at carbon prices up to 100 US$/tCO2-eq, but the estimate for prices above 100 US$/tCO2-eq is 2720 MtCO2-eq/yr. These potentials represent mitigation of 5-80%, and 20-90% of all other agricultural mitigation measures combined, at carbon prices of up to 20, and up to50 US$/tCO2-eq, respectively. An additional mitigation of 770 MtCO2-eq/yr could be achieved by 2030 by improved energy efficiency in agriculture, though the mitigation potential is counted mainly in the buildings and transport sectors (medium agreement, medium evidence).
Agricultural mitigation measures often have synergy with sustainable development policies, and many explicitly influence social, economic, and environmental aspects of sustainability. Many options also have co-benefits (improved efficiency, reduced cost, environmental co-benefits) as well as trade-offs (e.g., increasing other forms of pollution), and balancing these effects will be necessary for successful implementation (high agreement, much evidence).
There are interactions between mitigation and adaptation in the agricultural sector, which may occur simultaneously, but differ in their spatial and geographic characteristics. The main climate change benefits of mitigation actions will emerge over decades, but there may also be short-term benefits if the drivers achieve other policy objectives. Conversely, actions to enhance adaptation to climate change impacts will have consequences in the short and long term. Most mitigation measures are likely robust to future climate change (e.g., nutrient management), but a subset will likely be vulnerable (e.g., irrigation in regions becoming more arid). It may be possible for a vulnerable practice to be modified as the climate changes and to maintain the efficacy of a mitigation measure (low agreement, limited evidence).
In many regions, non-climate policies related to macro-economics, agriculture and the environment, have a larger impact on agricultural mitigation than climate policies (high agreement, much evidence). Despite significant technical potential for mitigation in agriculture, there is evidence that little progress has been made in the implementation of mitigation measures at the global scale. Barriers to implementation are not likely to be overcome without policy/economic incentives and other programmes, such as those promoting global sharing of innovative technologies.
Current GHG emission rates may escalate in the future due to population growth and changing diets (high agreement, medium evidence). Greater demand for food could result in higher emissions of CH4 and N2O if there are more livestock and greater use of nitrogen fertilizers (high agreement, much evidence). Deployment of new mitigation practices for livestock systems and fertilizer applications will be essential to prevent an increase in emissions from agriculture after 2030 . In addition, soil carbon may be more vulnerable to loss with climate change and other pressures, though increases in production will offset some or all of this carbon loss (low agreement, limited evidence).
Overall, the outlook for GHG mitigation in agriculture suggests that there is significant potential (high agreement, medium evidence). Current initiatives suggest that synergy between climate change policies, sustainable development and improvement of environmental quality will likely lead the way forward to realize the mitigation potential in this sector.
Agriculture releases to the atmosphere significant amounts of CO2, CH4, and N2O ( Cole et al., 1997 [MoS] ; IPCC, 2001a [NPR] ; Paustian et al., 2004 [SRC] ). CO2 is released largely from microbial decay or burning of plant litter and soil organic matter ( Smith, 2004b [NPR, SRC] ; Janzen, 2004 [SRC] ). CH4 is produced when organic materials decompose in oxygen-deprived conditions, notably from fermentative digestion by ruminant livestock, from stored manures, and from rice grown under flooded conditions ( Mosier et al. 1998 [JoC] ). N2O is generated by the microbial transformation of nitrogen in soils and manures, and is often enhanced where available nitrogen (N) exceeds plant requirements, especially under wet conditions ( (Oenema et al., 2005; ) ( Smith and Conen, 2004 ) ). Agricultural greenhouse gas (GHG) fluxes are complex and heterogeneous, but the active management of agricultural systems offers possibilities for mitigation. Many of these mitigation opportunities use current technologies and can be implemented immediately.
This chapter describes the development of GHG emissions from the agricultural sector ( Section 8.2 ), and details agricultural practices that may mitigate GHGs ( Section 8.4.1 ), with many practices affecting more than one GHG by more than one mechanism. These practices include: cropland management; grazing land management/pasture improvement; management of agricultural organic soils; restoration of degraded lands; livestock management; manure/bio-solid management; and bio-energy production.
It is theoretically possible to increase carbon storage in long-lived agricultural products (e.g., strawboards, wool, leather, bio-plastics) but the carbon held in these products has only increased from 37 to 83 MtC per year over the past 40 years. Assuming a first order decay rate of 10 to 20 % per year, this is estimated to be a global net annual removal of 3 to 7 MtCO2 from the atmosphere, which is negligible compared to other mitigation measures. The option is not considered further here.
Smith et al. 2007a [NPR, SRC, 2007] ) recently estimated a global potential mitigation of 770 MtCO2-eq/yr by 2030 from improved energy efficiency in agriculture (e.g., through reduced fossil fuel use), However, this is usually counted in the relevant user sector rather than in agriculture and so is not considered further here. Any savings from improved energy efficiency are discussed in the relevant sections elsewhere in this volume, according to where fossil fuel savings are made, for example, from transport fuels ( Chapter 5 ), or through improved building design ( Chapter 6 ).
Population pressure, technological change, public policies, and economic growth and the cost/price squeeze have been the main drivers of change in the agricultural sector during the last four decades. Production of food and fibre has more than kept pace with the sharp increase in demand in a more populated world. The global average daily availability of calories per capita has increased ( (Gilland, 2002 ) ), with some notable regional exceptions. This growth, however, has been at the expense of increased pressure on the environment, and depletion of natural resources ( Tilman et al., 2001 [JoC, MoS] ; Rees, 2003 [JoC] ), while it has not resolved the problems of food security and child malnutrition suffered in poor countries ( Conway and Toenniessen, 1999 [JoC] ).
Agricultural land occupied 5023 Mha in 2002 ( FAOSTAT, 2006 [NPR] ). Most of this area was under pasture (3488 Mha, or 69%) and cropland occupied 1405 Mha (28%). During the last four decades, agricultural land gained almost 500 Mha from other land uses, a change driven largely by increasing demands for food from a growing population. Every year during this period, an average 6 Mha of forestland and 7 Mha of other land were converted to agriculture, a change occurring largely in the developing world ( Table 8.1 ). This trend is projected to continue into the future ( Huang et al., 2002 [JoC] ; Trewavas, 2002 [JoC] ;( Fedoroff and Cohen, 1999; ) Green et al., 2005 [JoC] and Rosegrant et al., 2001 [NPR] ) project that an additional 500 Mha will be converted to agriculture during 1997 - 2020, mostly in Latin America and Sub-Saharan Africa.
|Area (Mha)||Change 2000s/1960s|
|2. Developed countries|
|3. Developing countries|
Technological progress has made it possible to achieve remarkable improvements in land productivity, increasing per-capita food availability ( Table 8.2 ), despite a consistent decline in per-capita agricultural land ( Figure 8.1 ). The share of animal products in the diet has increased consistently in the developing countries, while remaining constant in developed countries ( Table 8.2 ). Economic growth and changing lifestyles in some developing countries are causing a growing demand for meat and dairy products, notably in China where current demands are low. Meat demand in developing countries rose from 11 to 24 kg/capita/yr during the period 1967 - 1997, achieving an annual growth rate of more than 5% by the end of that period. Rosegrant et al. 2001 [NPR] ) forecast a further increase of 57% in global meat demand by 2020, mostly in South and Southeast Asia, and Sub-Saharan Africa. The greatest increases in demand are expected for poultry (83 % by 2020; ( Roy et al., 2002 ) ).
|1961-70||1971-80||1981-90||1991-00||2001-02||%||cal/d or g/d|
|1. Developed countries|
|Energy, all sources (cal/day)||3049||3181||3269||3223||3309||+9||261|
|% from animal sources||27||28||28||27||26||-2||--|
|Protein, all sources (g/day)||92||97||101||99||100||+9||8|
|% from animal sources||50||55||57||56||56||+12||--|
|2. Developing countries|
|Energy, all sources (cal/day)||2032||2183||2443||2600||2657||+31||625|
|% from animal sources||8||8||9||12||13||+77||--|
|Protein, all sources (g/day)||9||11||13||18||21||+123||48|
|% from animal sources||18||20||22||28||30||+67||--|
|Source: FAOSTAT, 2006.|
Annual GHG emissions from agriculture are expected to increase in coming decades (included in the baseline) due to escalating demands for food and shifts in diet. However, improved management practices and emerging technologies may permit a reduction in emissions per unit of food (or of protein) produced. The main trends in the agricultural sector with the implications for GHG emissions or removals are summarized as follows:
With an estimated global emission of non-CO2 GHGs from agriculture of between 5120 MtCO2-eq/yr ( Denman et al., 2007 [NPR, ARC, 2007] ) and 6116 MtCO2-eq/yr ( US-EPA, 2006a [NPR] ) in 2005, agriculture accounts for 10-12 % of total global anthropogenic emissions of GHGs. Agriculture contributes about 47% and 58% of total anthropogenic emissions of CH4 and N2O, respectively, with a wide range of uncertainty in the estimates of both the agricultural contribution and the anthropogenic total. N2O emissions from soils and CH4 from enteric fermentation constitute the largest sources, 38% and 32% of total non-CO2 emissions from agriculture in 2005, respectively ( US-EPA, 2006a [NPR] ). Biomass burning (12%), rice production (11%), and manure management (7%) account for the rest. CO2 emissions from agricultural soils are not normally estimated separately, but are included in the land use, land use change and forestry sector (e.g., in national GHG inventories). So there are few comparable estimates of emissions of this gas in agriculture. Agricultural lands generate very large CO2 fluxes both to and from the atmosphere ( IPCC, 2001a [NPR] ), but the net flux is small. US-EPA, 2006b [NPR] ) estimated a net CO2 emission of 40 MtCO2-eq from agricultural soils in 2000, less than 1% of global anthropogenic CO2 emissions.
Both the magnitude of the emissions and the relative importance of the different sources vary widely among world regions ( Figure 8.2 ). In 2005, the group of five regions mostly consisting of non-Annex I countries was responsible for 74% of total agricultural emissions.
In seven of the ten regions, N2O from soils was the main source of GHGs in the agricultural sector in 2005, mainly associated with N fertilizers and manure applied to soils. In the other three regions - Latin America and The Caribbean, the countries of Eastern Europe, the Caucasus and Central Asia, and OECD Pacific - CH4 from enteric fermentation was the dominant source ( US-EPA, 2006a [NPR] ). This is due to the large livestock population in these three regions which, in 2004, had a combined stock of cattle and sheep equivalent to 36% and 24% of world totals, respectively ( FAO, 2003 [NPR] ).
Emissions from rice production and burning of biomass were heavily concentrated in the group of developing countries, with 97% and 92% of world totals, respectively. While CH4 emissions from rice occurred mostly in South and East Asia, where it is a dominant food source (82% of total emissions), those from biomass burning originated in Sub-Saharan Africa and Latin America and the Caribbean (74% of total). Manure management was the only source for which emissions where higher in the group of developed regions (52%) than in developing regions (48%; US-EPA, 2006a [NPR] ).
The balance between the large fluxes of CO2 emissions and removals in agricultural land is uncertain. A study by US-EPA 2006b [NPR] ) showed that some countries and regions have net emissions, while others have net removals of CO2. Except for the countries of Eastern Europe, the Caucasus and Central Asia, which had an annual emission of 26 MtCO2/yr in 2000, all other countries showed very low emissions or removals.
Globally, agricultural CH4 and N2O emissions increased by 17% from 1990 to 2005, an average annual emission increase of 58 MtCO2-eq/yr ( US-EPA, 2006a [NPR] ). Both gases had about the same share of this increase. Three sources together explained 88% of the increase: biomass burning (N2O and CH4), enteric fermentation (CH4) and soil N2O emissions ( US-EPA, 2006a [NPR] ).
During that period, according to US-EPA 2006a [NPR] ; Figure 8.2 ), the five regions composed of Non-Annex I countries showed a 32% increase in non-CO2 emissions (equivalent to 73 MtCO2-eq/yr).The other five regions, with mostly Annex I countries, collectively showed a decrease of 12% (equivalent to 15 MtCO2-eq/yr). This was mostly due to non-climate macroeconomic policies in the Central and Eastern European and the countries of Eastern Europe, the Caucasus and Central Asia (see Section 8.7.1 and 8.7.2 ).
Agricultural N2O emissions are projected to increase by 35-60% up to 2030 due to increased nitrogen fertilizer use and increased animal manure production ( FAO, 2003 [NPR] ). Similarly, Mosier and Kroeze 2000 [MoS] and US-EPA 2006a [NPR] ; Figure 8.2 ) estimated that N2O emissions will increase by about 50% by 2020 (relative to 1990 ). If demands for food increase, and diets shift as projected, then annual emissions of GHGs from agriculture may escalate further. But improved management practices and emerging technologies may permit a reduction in emissions per unit of food (or protein) produced, and perhaps also a reduction in emissions per capita food consumption.
If CH4 emissions grow in direct proportion to increases in livestock numbers, then global livestock-related methane production is expected to increase by 60% up to 2030 ( FAO, 2003 [NPR] ). However, changes in feeding practices and manure management could ameliorate this increase. US-EPA 2006a [NPR] ) forecast that combined methane emissions from enteric fermentation and manure management will increase by 21% between 2005 and 2020 .
The area of rice grown globally is forecast to increase by 4.5% to 2030 ( FAO, 2003 [NPR] ), so methane emissions from rice production would not be expected to increase substantially. There may even be reductions if less rice is grown under continuous flooding (causing anaerobic soil conditions) as a result of scarcity of water, or if new rice cultivars that emit less methane are developed and adopted ( (Wang et al., 1997 ) ). However, US-EPA 2006a [NPR] ) projects a 16% increase in CH4 emissions from rice crops between 2005 and 2020, mostly due to a sustained increase in the area of irrigated rice.
No baseline agricultural non-CO2 GHG emission estimates for the year 2030 have been published, but according to US-EPA 2006a [NPR] ), aggregate emissions are projected to increase by ~13% during the decades 2000 - 2010 and 2010 - 2020 . Assuming similar rates of increase (10-15%) for 2020 - 2030, agricultural emissions might be expected to rise to 8000–8400, with a mean of 8300 MtCO2-eq by 2030 . The future evolution of CO2 emissions from agriculture is uncertain. Due to stable or declining deforestation rates ( FAO, 2003 [NPR] ), and increased adoption of conservation tillage practices ( FAO, 2001 [NPR] ), these emissions are likely to decrease or remain at low levels.
The Middle East and North Africa, and Sub-Saharan Africa have the highest projected growth in emissions, with a combined 95% increase in the period 1990 to 2020 ( US-EPA, 2006a [NPR] ). Sub-Saharan Africa is the one world region where per-capita food production is either in decline, or roughly constant at a level that is less than adequate ( Scholes and Biggs, 2004 [NPR] ). This trend is linked to low and declining soil fertility ( Sanchez, 2002 [JoC] ), and inadequate fertilizer inputs. Although slow, the rising wealth of urban populations is likely to increase demand for livestock products. This would result in intensification of agriculture and expansion to still largely unexploited areas, particularly in South and Central Africa (including Angola, Zambia, DRC, Mozambique and Tanzania), with a consequent increase in GHG emissions.
East Asia is projected to show large increases in GHG emissions from animal sources. According to FAO ( FAOSTAT, 2006 [NPR] ), total production of meat and milk in Asian developing countries increased more than 12 times and 4 times, respectively, from 2004 to 1961 . Since the per-capita consumption of meat and milk is still much lower in these countries than in developed countries, increasing trends are expected to continue for a relatively long time. Accordingly, US-EPA 2006a [NPR] ) forecast increases of 153% and 86% in emissions from enteric fermentation and manure management, respectively, from 1990 to 2020 . In South Asia, emissions are increasing mostly because of expanding use of N fertilizers and manure to meet demands for food, resulting from rapid population growth.
In Latin America and the Caribbean, agricultural products are the main source of exports. Significant changes in land use and management have occurred, with forest conversion to cropland and grassland being the most significant, resulting in increased GHG emissions from soils (CO2 and N2O). The cattle population has increased linearly from 176 to 379 Mhead between 1961 and 2004, partly offset by a decrease in the sheep population from 125 to 80 Mhead. All other livestock categories have increased in the order of 30 to 600% since 1961 . Cropland areas, including rice and soybean, and the use of N fertilizers have also shown dramatic increases ( FAOSTAT, 2006 [NPR] ). Another major trend in the region is the increased adoption of no-till agriculture, particularly in the Mercosur area (Brazil, Argentina, Paraguay, and Uruguay). This technology is used on ~30 Mha every year in the region, although it is unknown how much of this area is under permanent no-till.
In the countries of Central and Eastern Europe, the Caucasus and Central Asia, agricultural production is, at present, about 60-80% of that in 1990, but is expected to grow by 15-40% above 2001 levels by 2010, driven by the increasing wealth of these countries. A 10-14% increase in arable land area is forecast for the whole of Russia due to agricultural expansion. The widespread application of intensive management technologies could result in a 2 to 2.5-fold rise in grain and fodder yields, with a consequent reduction of arable land, but may increase N fertilizer use. Decreases in fertilizer N use since 1990 have led to a significant reduction in N2O emissions. But, under favourable economic conditions, the amount of N fertilizer applied will again increase, although unlikely to reach pre- 1990 levels in the near future. US-EPA 2006a [NPR] ) projected a 32% increase in N2O emissions from soils in these two regions between 2005 and 2020, equivalent to an average rate of increase of 3.5 MtCO2-eq/yr.
OECD North America and OECD Pacific are the only developed regions showing a consistent increase in GHG emissions in the agricultural sector (18% and 21%, respectively between 1990 and 2020; Figure 8.2 ). In both cases, the trend is largely driven by non-CO2 emissions from manure management and N2O emissions from soils. In Oceania, nitrogen fertilizer use has increased exponentially over the past 45 years with a 5 and 2.5 fold increase since 1990 in New Zealand and Australia, respectively. In North America, in contrast, nitrogen fertilizer use has remained stable; the main driver for increasing emissions is management of manure from cattle, poultry and swine production, and manure application to soils. In both regions, conservation policies have resulted in reduced CO2 emissions from land conversion. Land clearing in Australia has declined by 60% since 1990 with vegetation management policies restricting further clearing, while in North America, some marginal croplands have been returned to woodland or grassland.
Western Europe is the only region where, according to US-EPA 2006a [NPR] ), GHG emissions from agriculture are projected to decrease to 2020 ( Figure 8.2 ). This is associated with the adoption of a number of climate-specific and other environmental policies in the European Union, as well as economic constraints on agriculture, as discussed in Sections 8.7.1 and 8.7.2 .
Opportunities for mitigating GHGs in agriculture fall into three broad categories  , based on the underlying mechanism:
a. Reducing emissions: Agriculture releases to the atmosphere significant amounts of CO2, CH4, or N2O ( Cole et al., 1997 [MoS] ; IPCC, 2001a [NPR] ; Paustian et al., 2004 [SRC] ). The fluxes of these gases can be reduced by more efficient management of carbon and nitrogen flows in agricultural ecosystems. For example, practices that deliver added N more efficiently to crops often reduce N2O emissions ( Bouwman, 2001 [NPR, MoS] ), and managing livestock to make most efficient use of feeds often reduces amounts of CH4 produced ( (Clemens and Ahlgrimm, 2001 ) ). The approaches that best reduce emissions depend on local conditions, and therefore, vary from region to region.
b. Enhancing removals: Agricultural ecosystems hold large carbon reserves ( IPCC, 2001a [NPR] ), mostly in soil organic matter. Historically, these systems have lost more than 50 Pg C ( Paustian et al., 1998 [JoC] ;( Lal, 1999, ) 2004a ), but some of this carbon lost can be recovered through improved management, thereby withdrawing atmospheric CO2. Any practice that increases the photosynthetic input of carbon and/or slows the return of stored carbon to CO2 via respiration, fire or erosion will increase carbon reserves, thereby ‘sequestering’ carbon or building carbon ‘sinks’. Many studies, worldwide, have now shown that significant amounts of soil carbon can be stored in this way, through a range of practices, suited to local conditions ( Lal, 2004a [JoC] ). Significant amounts of vegetative carbon can also be stored in agro-forestry systems or other perennial plantings on agricultural lands ( (Albrecht and Kandji, 2003 ) ). Agricultural lands also remove CH4 from the atmosphere by oxidation (but less than forests; ( Tate et al., 2006 ) ), but this effect is small compared to other GHG fluxes ( (Smith and Conen, 2004 ) ).
c. Avoiding (or displacing) emissions: Crops and residues from agricultural lands can be used as a source of fuel, either directly or after conversion to fuels such as ethanol or diesel ( Schneider and McCarl, 2003 [SRC] ;( Cannell, 2003 ) ). These bio-energy feedstocks still release CO2 upon combustion, but now the carbon is of recent atmospheric origin (via photosynthesis), rather than from fossil carbon. The net benefit of these bio-energy sources to the atmosphere is equal to the fossil-derived emissions displaced, less any emissions from producing, transporting, and processing. GHG emissions, notably CO2, can also be avoided by agricultural management practices that forestall the cultivation of new lands now under forest, grassland, or other non-agricultural vegetation ( Foley et al., 2005 [JoC] ).
Many practices have been advocated to mitigate emissions through the mechanisms cited above. Often, a practice will affect more than one gas, by more than one mechanism, sometimes in opposite ways, so the net benefit depends on the combined effects on all gases ( (Robertson and Grace, 2004; ) ( Schils et al., 2005; ) ( Koga et al., 2006 ) ). In addition, the temporal pattern of influence may vary among practices or among gases for a given practice; some emissions are reduced indefinitely, other reductions are temporary ( Six et al., 2004 [SRC] ; Marland et al., 2003a [JoC, ARC] ). Where a practice affects radiative forcing through other mechanisms such as aerosols or albedo, those impacts also need to be considered ( Marland et al., 2003b [ARC] ; Andreae et al., 2005 [JoC, MoS] ).
The impacts of the mitigation options considered are summarized qualitatively in Table 8.3 . Although comprehensive life-cycle analyses are not always possible, given the complexity of many farming systems, the table also includes estimates of the confidence based on expert opinion that the practice can reduce overall net emissions at the site of adoption. Some of these practices also have indirect effects on ecosystems elsewhere. For example, increased productivity in existing croplands could avoid deforestation and its attendant emissions (see also Section 8.8 ). The most important options are discussed in Section 8.4.1 .
|Mitigative effectsa||Net mitigationb (confidence)|
|Water management (irrigation, drainage)||+/-||+||*||*|
|Set-aside, land-use change||+||+||+||***||***|
|Grazing land management/ pasture improvement||Grazing intensity||+/-||+/-||+/-||*||*|
|Increased productivity (e.g., fertilization)||+||+/-||**||*|
|Species introduction (including legumes)||+||+/-||*||**|
|Management of organic soils||Avoid drainage of wetlands||+||-||+/-||**||**|
|Restoration of degraded lands||Erosion control, organic amendments, nutrient amendments||+||+/-||***||**|
|Livestock management||Improved feeding practices||+||+||***||***|
|Specific agents and dietary additives||+||**||***|
|Longer term structural and management changes and animal breeding||+||+||**||*|
|Manure/biosolid management||Improved storage and handling||+||+/-||***||**|
|More efficient use as nutrient source||+||+||***||**|
|Bio-energy||Energy crops, solid, liquid, biogas, residues||+||+/-||+/-||***||**|
Because often intensively managed, croplands offer many opportunities to impose practices that reduce net GHG emissions ( Table 8.3 ). Mitigation practices in cropland management include the following partly-overlapping categories:
a. Agronomy: Improved agronomic practices that increase yields and generate higher inputs of carbon residue can lead to increased soil carbon storage ( Follett, 2001 [NPR] ). Examples of such practices include: using improved crop varieties; extending crop rotations, notably those with perennial crops that allocate more carbon below ground; and avoiding or reducing use of bare (unplanted) fallow ( (West and Post, 2002; ) Smith, 2004a [SRC] , b; ( Lal, 2003, ) 2004a; Freibauer et al., 2004 [SRC] ). Adding more nutrients, when deficient, can also promote soil carbon gains ( (Alvarez, 2005 ) ), but the benefits from N fertilizer can be offset by higher N2O emissions from soils and CO2 from fertilizer manufacture ( Schlesinger, 1999 [JoC] ; Pérez-Ramírez et al., 2003 [NPR] ; Robertson, 2004 [NPR] ;( Gregorich et al., 2005 ) ). Emissions per hectare can also be reduced by adopting cropping systems with reduced reliance on fertilizers, pesticides and other inputs (and therefore, the GHG cost of their production: Paustian et al., 2004 [SRC] ). An important example is the use of rotations with legume crops ( (West and Post, 2002; ) ( Izaurralde et al., 2001 ) ), which reduce reliance on external N inputs although legume-derived N can also be a source of N2O ( Rochette and Janzen, 2005 [MoS, SRC] ). Another group of agronomic practices are those that provide temporary vegetative cover between successive agricultural crops, or between rows of tree or vine crops. These ‘catch’ or ‘cover’ crops add carbon to soils ( (Barthès et al., 2004; ) Freibauer et al., 2004 [SRC] ) and may also extract plant-available N unused by the preceding crop, thereby reducing N2O emissions.
b. Nutrient management: Nitrogen applied in fertilizers, manures, biosolids, and other N sources is not always used efficiently by crops ( (Galloway et al., 2003; ) Cassman et al., 2003 [ARC] ). The surplus N is particularly susceptible to emission of N2O ( (McSwiney and Robertson, 2005 ) ). Consequently, improving N use efficiency can reduce N2O emissions and indirectly reduce GHG emissions from N fertilizer manufacture ( Schlesinger, 1999 [JoC] ). By reducing leaching and volatile losses, improved efficiency of N use can also reduce off-site N2O emissions. Practices that improve N use efficiency include: adjusting application rates based on precise estimation of crop needs (e.g., precision farming); using slow- or controlled-release fertilizer forms or nitrification inhibitors (which slow the microbial processes leading to N2O formation); applying N when least susceptible to loss, often just prior to plant uptake (improved timing); placing the N more precisely into the soil to make it more accessible to crops roots; or avoiding N applications in excess of immediate plant requirements ( Robertson, 2004 [NPR] ;( Dalal et al., 2003; ) Paustian et al., 2004 [SRC] ; Cole et al., 1997 [MoS] ;( Monteny et al., 2006 ) ).
c. Tillage/residue management: Advances in weed control methods and farm machinery now allow many crops to be grown with minimal tillage (reduced tillage) or without tillage (no-till). These practices are now increasingly used throughout the world (e.g., ( Cerri et al., 2004 ) ). Since soil disturbance tends to stimulate soil carbon losses through enhanced decomposition and erosion ( (Madari et al., 2005 ) ), reduced- or no-till agriculture often results in soil carbon gain, but not always ( (West and Post, 2002; ) Ogle et al., 2005 [Ambiguous] ;( Gregorich et al., 2005; ) ( Alvarez 2005 ) ). Adopting reduced- or no-till may also affect N2O, emissions but the net effects are inconsistent and not well-quantified globally ( (Smith and Conen, 2004; ) Helgason et al., 2005 [MoS, SRC] ; Li et al., 2005 [JoC, MoS] ; Cassman et al., 2003 [ARC] ). The effect of reduced tillage on N2O emissions may depend on soil and climatic conditions. In some areas, reduced tillage promotes N2O emissions, while elsewhere it may reduce emissions or have no measurable influence ( Marland et al., 2001 [JoC, SRC] ). Further, no-tillage systems can reduce CO2 emissions from energy use ( Marland et al., 2003b [ARC] ;( Koga et al., 2006 ) ). Systems that retain crop residues also tend to increase soil carbon because these residues are the precursors for soil organic matter, the main carbon store in soil. Avoiding the burning of residues (e.g., mechanising sugarcane harvesting, eliminating the need for pre-harvest burning ( (Cerri et al., 2004 ) )) also avoids emissions of aerosols and GHGs generated from fire, although CO2 emissions from fuel use may increase.
d. Water management: About 18% of the world’s croplands now receive supplementary water through irrigation (Millennium Ecosystem Assessment, 2005 ). Expanding this area (where water reserves allow) or using more effective irrigation measures can enhance carbon storage in soils through enhanced yields and residue returns ( Follett, 2001 [NPR] ; Lal, 2004a [JoC] ). But some of these gains may be offset by CO2 from energy used to deliver the water ( Schlesinger 1999 [JoC] ;( Mosier et al., 2005 ) ) or from N2O emissions from higher moisture and fertilizer N inputs ( (Liebig et al. 2005 ) ), The latter effect has not been widely measured. Drainage of croplands lands in humid regions can promote productivity (and hence soil carbon) and perhaps also suppress N2O emissions by improving aeration ( (Monteny et al., 2006 ) ). Any nitrogen lost through drainage, however, may be susceptible to loss as N2O.(Reay et al. 2003 ).
e. Rice management: Cultivated wetland rice soils emit significant quantities of methane ( Yan et al., 2003 [MoS] ). Emissions during the growing season can be reduced by various practices ( (Yagi et al., 1997; ) Wassmann et al., 2000 [MoS] ;( Aulakh et al., 2001 ) ). For example, draining wetland rice once or several times during the growing season reduces CH4 emissions ( (Smith and Conen, 2004; ) Yan et al., 2003 [MoS] ; Khalil and Shearer, 2006 [NPR] ). This benefit, however, may be partly offset by increased N2O emissions ( Akiyama et al. 2005 [JoC] ), and the practice may be constrained by water supply. Rice cultivars with low exudation rates could offer an important methane mitigation option ( (Aulakh et al., 2001 ) ). In the off-rice season, methane emissions can be reduced by improved water management, especially by keeping the soil as dry as possible and avoiding water logging ( Cai et al., 2000 [JoC, SRC] 2003; Kang et al., 2002 [SRC] ; Xu et al., 2003 [SRC] ). Increasing rice production can also enhance soil organic carbon stocks ( Pan et al., 2006 [SRC] ). Methane emissions can be reduced by adjusting the timing of organic residue additions (e.g., incorporating organic materials in the dry period rather than in flooded periods; Xu et al., 2000 [SRC] ; Cai and Xu, 2004 [NPR, SRC] ), by composting the residues before incorporation, or by producing biogas for use as fuel for energy production ( (Wang and Shangguan, 1996; ) Wassmann et al., 2000 [MoS] ).
f. Agro-forestry: Agro-forestry is the production of livestock or food crops on land that also grows trees for timber, firewood, or other tree products. It includes shelter belts and riparian zones/buffer strips with woody species. The standing stock of carbon above ground is usually higher than the equivalent land use without trees, and planting trees may also increase soil carbon sequestration ( (Oelbermann et al., 2004; ) ( Guo and Gifford, 2002; ) ( Mutuo et al., 2005; ) ( Paul et al., 2003 ) ). But the effects on N2O and CH4 emissions are not well known ( (Albrecht and Kandji, 2003 ) ).
g. Land cover (use) change: One of the most effective methods of reducing emissions is often to allow or encourage the reversion of cropland to another land cover, typically one similar to the native vegetation. The conversion can occur over the entire land area (‘set-asides’), or in localized spots, such as grassed waterways, field margins, or shelterbelts ( Follett, 2001 [NPR] ; Freibauer et al., 2004 [SRC] ;( Lal, 2004b; ) Falloon et al., 2004 [SRC] ; Ogle et al., 2003 [MoS, SRC] ). Such land cover change often increases carbon storage. For example, converting arable cropland to grassland typically results in the accrual of soil carbon because of lower soil disturbance and reduced carbon removal in harvested products. Compared to cultivated lands, grasslands may also have reduced N2O emissions from lower N inputs, and higher rates of CH4 oxidation, but recovery of oxidation may be slow ( Paustian et al., 2004 [SRC] ). Similarly, converting drained croplands back to wetlands can result in rapid accumulation of soil carbon (removal of atmospheric CO2). This conversion may stimulate CH4 emissions because water logging creates anaerobic conditions ( Paustian et al., 2004 [SRC] ). Planting trees can also reduce emissions. These practices are considered under agro-forestry ( Section 184.108.40.206 f); afforestation ( Chapter 9 ), and reafforestation ( Chapter 9 ). Because land cover (or use) conversion comes at the expense of lost agricultural productivity, it is usually an option only on surplus agricultural land or on croplands of marginal productivity.
Grazing lands occupy much larger areas than croplands ( FAOSTAT, 2006 [NPR] ) and are usually managed less intensively. The following are examples of practices to reduce GHG emissions and to enhance removals:
a. Grazing intensity: The intensity and timing of grazing can influence the removal, growth, carbon allocation, and flora of grasslands, thereby affecting the amount of carbon accrual in soils ( (Conant et al., 2001; ) 2005; Freibauer et al., 2004 [SRC] ; Conant and Paustian, 2002 [JoC] ;( Reeder et al., 2004 ) ). Carbon accrual on optimally grazed lands is often greater than on ungrazed or overgrazed lands ( (Liebig et al., 2005; ) Rice and Owensby, 2001 [NPR, SRC] ). The effects are inconsistent, however, owing to the many types of grazing practices employed and the diversity of plant species, soils, and climates involved ( Schuman et al., 2001 [NPR, SRC] ;( Derner et al., 2006 ) ). The influence of grazing intensity on emission of non-CO2 gases is not well-established, apart from the direct effects on emissions from adjustments in livestock numbers.
b. Increased productivity: (including fertilization): As for croplands, carbon storage in grazing lands can be improved by a variety of measures that promote productivity. For instance, alleviating nutrient deficiencies by fertilizer or organic amendments increases plant litter returns and, hence, soil carbon storage ( Schnabel et al., 2001 [NPR] ;( Conant et al., 2001 ) ). Adding nitrogen, however, often stimulates N2O emissions ( (Conant et al., 2005 ) ) thereby offsetting some of the benefits. Irrigating grasslands, similarly, can promote soil carbon gains ( (Conant et al., 2001 ) ). The net effect of this practice, however, depends also on emissions from energy use and other activities on the irrigated land ( Schlesinger, 1999 [JoC] ).
c. Nutrient management: Practices that tailor nutrient additions to plant uptake, such as those described for croplands, can reduce N2O emissions ( (Dalal et al., 2003; ) Follett et al., 2001 [NPR] ). Management of nutrients on grazing lands, however, may be complicated by deposition of faeces and urine from livestock, which are not as easily controlled nor as uniformly applied as nutritive amendments in croplands ( (Oenema et al., 2005 ) ).
d. Fire management: On-site biomass burning (not to be confused with bio-energy, where biomass is combusted off-site for energy) contributes to climate change in several ways. Firstly, it releases GHGs, notably CH4 and, and to a lesser extent, N2O (the CO2 released is of recent origin, is absorbed by vegetative regrowth, and is usually not included in GHG inventories). Secondly, it generates hydrocarbon and reactive nitrogen emissions, which react to form tropospheric ozone, a powerful GHG. Thirdly, fires produce a range of smoke aerosols which can have either warming or cooling effects on the atmosphere; the net effect is thought to be positive radiative forcing ( Andreae et al., 2005 [JoC, MoS] ; Jones et al., 2003 [MoS] ; Venkataraman et al., 2005 [JoC] ; Andreae, 2001 [JoC] ; Andreae and Merlet, 2001 [JoC] ; Anderson et al., 2003 [JoC, MoS] ; Menon et al., 2002 [JoC] ). Fourth, fire reduces the albedo of the land surface for several weeks, causing warming ( (Beringer et al., 2003 ) ). Finally, burning can affect the proportion of woody versus grass cover, notably in savannahs, which occupy about an eighth of the global land surface. Reducing the frequency or intensity of fires typically leads to increased tree and shrub cover, resulting in a CO2 sink in soil and biomass ( (Scholes and van der Merwe, 1996 ) ). This woody-plant encroachment mechanism saturates over 20-50 years, whereas avoided CH4 and N2O emissions continue as long as fires are suppressed. Mitigation actions involve reducing the frequency or extent of fires through more effective fire suppression; reducing the fuel load by vegetation management; and burning at a time of year when less CH4 and N2O are emitted ( (Korontzi et al., 2003 ) ). Although most agricultural-zone fires are ignited by humans, there is evidence that the area burned is ultimately under climatic control ( (Van Wilgen et al., 2004 ) ). In the absence of human ignition, the fire-prone ecosystems would still burn as a result of climatic factors.
e. Species introduction: Introducing grass species with higher productivity, or carbon allocation to deeper roots, has been shown to increase soil carbon. For example, establishing deep-rooted grasses in savannahs has been reported to yield very high rates of carbon accrual ( Fisher et al., 1994 [JoC] ), although the applicability of these results has not been widely confirmed ( (Conant et al., 2001; ) Davidson et al., 1995 [JoC] ). In the Brazilian Savannah (Cerrado Biome), integrated crop-livestock systems using Brachiaria grasses and zero tillage are being adopted ( Machado and Freitas, 2004 [NPR] ). Introducing legumes into grazing lands can promote soil carbon storage ( (Soussana et al., 2004 ) ), through enhanced productivity from the associated N inputs, and perhaps also reduced emissions from fertilizer manufacture if biological N2 fixation displaces applied N fertilizer N( (Sisti et al., 2004; ) ( Diekow et al., 2005 ) ). Ecological impacts of species introduction need to be considered.
Grazing lands also emit GHGs from livestock, notably CH4 from ruminants and their manures. Practices for reducing these emissions are considered under Section 220.127.116.11 : Livestock management.
Organic or peaty soils contain high densities of carbon accumulated over many centuries because decomposition is suppressed by absence of oxygen under flooded conditions. To be used for agriculture, these soils are drained, which aerates the soil, favouring decomposition and therefore, high CO2 and N2O fluxes. Methane emissions are usually suppressed after draining, but this effect is far outweighed by pronounced increases in N2O and CO2( (Kasimir-Klemedtsson et al., 1997 ) ). Emissions from drained organic soils can be reduced to some extent by practices such as avoiding row crops and tubers, avoiding deep ploughing, and maintaining a shallower water table. But the most important mitigation practice is avoiding the drainage of these soils in the first place or re-establishing a high water table ( Freibauer et al., 2004 [SRC] ).
A large proportion of agricultural lands has been degraded by excessive disturbance, erosion, organic matter loss, salinization, acidification, or other processes that curtail productivity ( Batjes, 1999 [NPR] ; Foley et al., 2005 [JoC] ;( Lal, 2001a, ) 2003, 2004b ). Often, carbon storage in these soils can be partly restored by practices that reclaim productivity including: re-vegetation (e.g., planting grasses); improving fertility by nutrient amendments; applying organic substrates such as manures, biosolids, and composts; reducing tillage and retaining crop residues; and conserving water ( (Lal, 2001b; ) 2004b; Bruce et al., 1999 [SRC] ;( Olsson and Ardö, 2002; ) Paustian et al., 2004 [SRC] ). Where these practices involve higher nitrogen amendments, the benefits of carbon sequestration may be partly offset by higher N2O emissions.
Livestock, predominantly ruminants such as cattle and sheep, are important sources of CH4, accounting for about one-third of global anthropogenic emissions of this gas ( US-EPA, 2006a [NPR] ). The methane is produced primarily by enteric fermentation and voided by eructation ( Crutzen, 1995 [NPR] ;( Murray et al., 1976; ) ( Kennedy and Milligan, 1978 ) ). All livestock generate N2O emissions from manure as a result of excretion of N in urine and faeces. Practices for reducing CH4 and N2O emissions from this source fall into three general categories: improved feeding practices, use of specific agents or dietary additives; and longer-term management changes and animal breeding ( Soliva et al., 2006 [NPR] ;( Monteny et al., 2006 ) ).
a. Improved feeding practices: Methane emissions can be reduced by feeding more concentrates, normally replacing forages ( Blaxter and Claperton, 1965 [MoS] ;( Johnson and Johnson, 1995; ) Lovett et al., 2003 [SRC] ;( Beauchemin and McGinn, 2005 ) ). Although concentrates may increase daily methane emissions per animal, emissions per kg-feed intake and per kg-product are almost invariably reduced. The magnitude of this reduction per kg-product decreases as production increases. The net benefit of concentrates, however, depends on reduced animal numbers or younger age at slaughter for beef animals, and on how the practice affects land use, the N content of manure and emissions from producing and transporting the concentrates ( Phetteplace et al., 2001 [MoS] ; Lovett et al., 2006 [SRC] ). Other practices that can reduce CH4 emissions include: adding certain oils or oilseeds to the diet (e.g., Machmüller et al., 2000 [NotFound] ; Jordan et al., 2006c [SRC] ); improving pasture quality, especially in less developed regions, because this improves animal productivity, and reduces the proportion of energy lost as CH4 ( Leng, 1991 [NPR] ;( McCrabb et al., 1998; ) Alcock and Hegarty, 2006 [NPR] ); and optimizing protein intake to reduce N excretion and N2O emissions ( Clark et al., 2005 [NPR] ).
b. Specific agents and dietary additives: A wide range of specific agents, mostly aimed at suppressing methanogenesis, has been proposed as dietary additives to reduce CH4 emissions:
Ionophores are antibiotics that can reduce methane emissions ( (Benz and Johnson, 1982; ) ( van Nevel and Demeyer, 1996; ) ( McGinn et al., 2004 ) ), but their effect may be transitory ( (Rumpler et al., 1986 ) ); and they have been banned in the EU.
Halogenated compounds inhibit methanogenic bacteria ( (Wolin et al., 1964; ) ( van Nevel and Demeyer, 1995 ) ) but their effects, too, are often transitory and they can have side-effects such as reduced intake.
Novel plant compounds such as condensed tannins ( (Pinares-Patiño et al., 2003; ) Hess et al., 2006 [NPR] ), saponins ( (Lila et al., 2003 ) ) or essential oils ( Patra et al., 2006 [NPR] ; Kamra et al., 2006 [NPR] ) may have merit in reducing methane emissions, but these responses may often be obtained through reduced digestibility of the diet.
Probiotics, such as yeast culture, have shown only small, insignificant effects ( (McGinn et al., 2004 ) ), but selecting strains specifically for methane-reducing ability could improve results ( Newbold and Rode, 2006 [NPR] ).
Propionate precursors such as fumarate or malate reduce methane formation by acting as alternative hydrogen acceptors ( Newbold et al., 2002 [NPR] ). But as response is elicited only at high doses, propionate precursors are, therefore, expensive ( (Newbold et al., 2005 ) ).
Vaccines against methanogenic bacteria are being developed but are not yet available commercially ( (Wright et al., 2004 ) ).
Bovine somatotropin (bST) and hormonal growth implants do not specifically suppress CH4 formation, but by improving animal performance ( (Bauman, 1992; ) ( Schmidely, 1993 ) ), they can reduce emissions per-kg of animal product ( (Johnson et al., 1991; ) McCrabb, 2001 [NPR] ).
c. Longer-term management changes and animal breeding: Increasing productivity through breeding and better management practices, such as a reduction in the number of replacement heifers, often reduces methane output per unit of animal product ( (Boadi et al., 2004 ) ). Although selecting cattle directly for reduced methane production has been proposed ( (Kebreab et al., 2006 ) ), it is still impractical due to difficulties in accurately measuring methane emissions at a magnitude suitable for breeding programmes. With improved efficiency, meat-producing animals reach slaughter weight at a younger age, with reduced lifetime emissions ( Lovett and O’Mara, 2002 [MoS, SRC] ). However, the whole-system effects of such practices may not always lead to reduced emissions. For example in dairy cattle, intensive selection for higher yield may reduce fertility, requiring more replacement heifers in the herd ( Lovett et al., 2006 [SRC] ).
Animal manures can release significant amounts of N2O and CH4 during storage, but the magnitude of these emissions varies. Methane emissions from manure stored in lagoons or tanks can be reduced by cooling, use of solid covers, mechanically separating solids from slurry, or by capturing the CH4 emitted ( (Amon et al. 2006; ) ( Clemens and Ahlgrimm, 2001; ) ( Monteny et al. 2001, ) 2006; Paustian et al., 2004 [SRC] ). The manures can also be digested anaerobically to maximize CH4 retrieval as a renewable energy source ( (Clemens and Ahlgrimm, 2001; ) ( Clemens et al., 2006 ) ). Handling manures in solid form (e.g., composting) rather than liquid form can suppress CH4 emissions, but may increase N2O formation ( Paustian et al., 2004 [SRC] ). Preliminary evidence suggests that covering manure heaps can reduce N2O emissions, but the effect of this practice on CH4 emissions is variable ( (Chadwick, 2005 ) ). For most animals, worldwide there is limited opportunity for manure management, treatment, or storage; excretion happens in the field and handling for fuel or fertility amendment occurs when it is dry and methane emissions are negligible ( (Gonzalez-Avalos and Ruiz-Suarez, 2001 ) ). To some extent, emissions from manure might be curtailed by altering feeding practices ( (Külling et al., 2003; ) ( Hindrichsen et al., 2006; ) Kreuzer and Hindrichsen, 2006 [NPR] ), or by composting the manure ( (Pattey et al., 2005; ) ( Amon et al., 2001 ) ), but if aeration is inadequate CH4 emissions during composting can still be substantial ( Xu et al., 2007 [SRC, 2007] ). All of these practices require further study from the perspective of their impact on whole life-cycle GHG emissions.
Manures also release GHGs, notably N2O, after application to cropland or deposition on grazing lands. Practices for reducing these emissions are considered in Subsection 18.104.22.168 : Cropland management and Subsection 22.214.171.124 : Grazing land management.
Increasingly, agricultural crops and residues are seen as sources of feedstocks for energy to displace fossil fuels. A wide range of materials have been proposed for use, including grain, crop residue, cellulosic crops (e.g., switchgrass, sugarcane), and various tree species ( Edmonds, 2004 [ARC] ;( Cerri et al., 2004; ) Paustian et al., 2004 [SRC] ;( Sheehan et al., 2004; ) ( Dias de Oliveira et al., 2005; ) Eidman, 2005 [NPR] ). These products can be burned directly, but can also be processed further to generate liquid fuels such as ethanol or diesel fuel ( Richter, 2004 [JoC] ). Such fuels release CO2 when burned, but this CO2 is of recent atmospheric origin (via photosynthetic carbon uptake) and displaces CO2 which otherwise would have come from fossil carbon. The net benefit to atmospheric CO2, however, depends on energy used in growing and processing the bioenergy feedstock ( (Spatari et al., 2005 ) ).
The competition for other land uses and the environmental impacts need to be considered when planning to use energy crops (e.g., European Environment Agency, 2006 ). The interactions of an expanding bioenergy sector with other land uses, and impacts on agro-ecosystem services such as food production, biodiversity, soil and nature conservation, and carbon sequestration have not yet been adequately studied, but bottom-up approaches ( Smeets et al., 2007 [ARC, 2007] ) and integrated assessment modelling ( Hoogwijk et al., 2005 [ARC] ; Hoogwijk, 2004 [NPR, ARC] ) offer opportunities to improve understanding. Latin America, Sub-Saharan Africa, and Eastern Europe are promising regions for bio-energy, with additional long-term contributions from Oceania and East and Northeast Asia. The technical potential for biomass production may be developed at low production costs in the range of 2 US$/GJ ( Hoogwijk, 2004 [NPR, ARC] ; Rogner et al., 2000 [NPR, ARC] ).
Major transitions are required to exploit the large potential for bioenergy. Improving agricultural efficiency in developing countries is a key factor. It is still uncertain to what extent, and how fast, such transitions could be realized in different regions. Under less favourable conditions, the regional bio-energy potential(s) could be quite low. Also, technological developments in converting biomass to energy, as well as long distance biomass supply chains (e.g., those involving intercontinental transport of biomass derived energy carriers) can dramatically improve competitiveness and efficiency of bio-energy ( Faaij, 2006 [ARC] ; Hamelinck et al., 2004 [ARC] ).
As mitigation practices can affect more than one GHG  , it is important to consider the impact of mitigation options on all GHGs ( Robertson et al,. 2000 [JoC, MoS] ; Smith et al., 2001 [MoS, SRC] ;( Gregorich et al., 2005 ) ). For non-livestock mitigation options, ranges for per-area mitigation potentials of each GHG are provided in Table 8.4 (tCO2-eq/ha/yr).
Mitigation potentials for CO2 represent the net change in soil carbon pools, reflecting the accumulated difference between carbon inputs to the soil after CO2 uptake by plants, and release of CO2 by decomposition in soil. Mitigation potentials for N2O and CH4 depend solely on emission reductions. Soil carbon stock changes were derived from about 200 studies, and the emission ranges for CH4 and N2O were derived using the DAYCENT and DNDC simulation models ( IPCC, 2006 [NPR] ; US-EPA, 2006b [NPR] ; Smith et al., 2007b [SRC, 2007] ; Ogle et al., 2004 [SRC] , 2005 ).
Table 8.5 presents the mitigation potentials in livestock (dairy cows, beef cattle, sheep, dairy buffalo and other buffalo) for reducing enteric methane emissions via improved feeding practices, specific agents and dietary additives, and longer term structural and management changes/animal breeding. These estimates were derived by Smith et al. 2007a [NPR, SRC, 2007] ) using a model similar to that described in US-EPA 2006b [NPR] ).
Some mitigation measures operate predominantly on one GHG (e.g., dietary management of ruminants to reduce CH4 emissions) while others have impacts on more than one GHG (e.g., rice management). Moreover, practices may benefit more than one gas (e.g., set-aside/headland management) while others involve a trade-off between gases (e.g., restoration of organic soils). The effectiveness of non-livestock mitigation options are variable across and within climate regions (see Table 8.4 ). Consequently, a practice that is highly effective in reducing emissions at one site may be less effective or even counter-productive elsewhere. Similarly, effectiveness of livestock options also varies regionally ( Table 8.5 ). This means that there is no universally applicable list of mitigation practices, but that proposed practices will need to be evaluated for individual agricultural systems according to the specific climatic, edaphic, social settings, and historical land use and management. Assessments can be conducted to evaluate the effectiveness of practices in specific areas, building on findings from the global scale assessment reported here. In addition, such assessments could address GHG emissions associated with energy use and other inputs (e.g., fuel, fertilizers, and pesticides) in a full life cycle analysis for the production system.
|Climate zone||Activity||Practice||CO2 (tCO2/ha/yr)||CH4 (tCO2-eq/ha/yr)||N2O (tCO2-eq/ha/yr)||All GHG (tCO2-eq/ha/yr)|
|Mean estimate||Low||High||Mean estimate||Low||High||Mean estimate||Low||High||Mean estimate||Low||High|
|Croplands||Tillage and residue management||0.15||-0.48||0.77||0.00||0.00||0.00||0.02||-0.04||0.09||0.17||-0.52||0.86|
|Croplands||Set-aside and LUC||1.61||-0.07||3.30||0.02||0.00||0.00||2.30||0.00||4.60||3.93||-0.07||7.90|
|Grasslands||Grazing, fertilization, fire||0.11||-0.55||0.77||0.02||0.01||0.02||0.00||0.00||0.00||0.13||-0.54||0.79|
|Croplands||tillage and residue management||0.51||0.00||1.03||0.00||0.00||0.00||0.02||-0.04||0.09||0.53||-0.04||1.12|
|Croplands||Set-aside and LUC||3.04||1.17||4.91||0.02||0.00||0.00||2.30||0.00||4.60||5.36||1.17||9.51|
|Grasslands||Grazing, fertilization, fire||0.81||0.11||1.50||0.00||0.00||0.00||0.00||0.00||0.00||0.80||0.11||1.50|
|Croplands||Tillage and residue management||0.33||-0.73||1.39||0.00||0.00||0.00||0.02||-0.04||0.09||0.35||-0.77||1.48|
|Croplands||Set-aside and LUC||1.61||-0.07||3.30||0.02||0.00||0.00||2.30||0.00||4.60||3.93||-0.07||7.90|
|Grasslands||Grazing, fertilization, fire||0.11||-0.55||0.77||0.00||0.00||0.00||0.00||0.00||0.00||0.11||-0.55||0.77|
|Croplands||Tillage and residue management||0.70||-0.40||1.80||0.00||0.00||0.00||0.02||-0.04||0.09||0.72||-0.44||1.89|
|Croplands||Set-aside and LUC||3.04||1.17||4.91||0.02||0.00||0.00||2.30||0.00||4.60||5.36||1.17||9.51|
|Grasslands||Grazing, fertilization, fire||0.81||0.11||1.50||0.00||0.00||0.00||0.00||0.00||0.00||0.81||0.11||1.50|
|Improved feeding practicesb||Specific agents and dietary additivesc||Longer term structural/management change and animal breedingd|
|AEZ regions||Dairy cows||Beef cattle||Sheep||Dairy buffalo||Non-dairy buffalo||Dairy cows||Beef cattle||Sheep||Dairy buffalo||Non-dairy buffalo||Dairy cows||Beef cattle||Sheep||Dairy buffalo||Non-dairy buffalo|
The effectiveness of mitigation strategies also changes with time. Some practices, like those which elicit soil carbon gain, have diminishing effectiveness after several decades; others such as methods that reduce energy use may reduce emissions indefinitely. For example, Six et al. 2004 [SRC] ) found a strong time dependency of emissions from no-till agriculture, in part because of changing influence of tillage on N2O emissions.
There have been numerous attempts to assess the technical potenttial for GHG mitigation in agriculture. Most of these have focused on soil carbon sequestration. Estimates in the IPCC Second Assessment Report (SAR; IPCC, 1996 [NPR] ) suggested that 400-800 MtC/yr (equivalent to about 1400 - 2900 MtCO2-eq/yr) could be sequestered in global agricultural soils with a finite capacity saturating after 50 to100 years. In addition, SAR concluded that 300- 1300 MtC (equivalent to about 1100 -4800 MtCO2-eq/yr) from fossil fuels could be offset by using 10 to15% of agricultural land to grow energy crops; with crop residues potentially contributing 100-200 MtC (equivalent to about 400-700 MtCO2-eq/yr) to fossil fuel offsets if recovered and burned. Burning residues for bio-energy might increase N2O emissions but this effect was not quantified.
SAR ( IPCC, 1996 [NPR] ) estimated that CH4 emissions from agriculture could be reduced by 15 to 56%, mainly through improved nutrition of ruminants and better management of paddy rice, and that improved management could reduce N2O emissions by 9-26%. The document also stated that GHG mitigation techniques will not be adopted by land managers unless they improve profitability but some measures are adopted for reasons other than climate mitigation. Options that both reduce GHG emissions and increase productivity are more likely to be adopted than those which only reduce emissions.
Of published estimates of technical potential, only Caldeira et al. 2004 [NPR, ARC] and Smith et al. 2007a [NPR, SRC, 2007] ) provide global estimates considering all GHGs together, and Boehm et al. 2004 [JoC] ) consider all GHGs for Canada only for 2008 Smith et al. 2007a [NPR, SRC, 2007] ) used per-area or per-animal estimates of mitigation potential for each GHG and multiplied this by the area available for that practice in each region. It was not necessary to use baseline emissions in calculating mitigation potential. US-EPA 2006b [NPR] ) estimated baseline emissions for 2020 for non-CO2 GHGs as 7250 MtCO2-eq in 2020 (see Chapter 11 ; Table 11.4 ). Non-CO2 GHG emissions in agriculture are projected to increase by about 13% from 2000 to 2010 and by 13% from 2010 to 2020 ( US-EPA, 2006b [NPR] ). Assuming a similar rate of increase as in the period from 2000 to 2020, global agricultural non-CO2 GHG emissions would be around 8200 MtCO2-eq in 2030 .
The global technical potential for mitigation options in agriculture by 2030, considering all gases, was estimated to be ~4500 by Caldeira et al. 2004 [NPR, ARC] ) and ~5500-6000 MtCO2-eq/yr by Smith et al. 2007a [NPR, SRC, 2007] ) if considering no economic or other barriers. Economic potentials are considerably lower (see Section 126.96.36.199 ). Figure 8.3 presents global and regional estimates of agricultural mitigation potential. Of the technical potentials estimated by Smith et al. 2007a [NPR, SRC, 2007] ), about 89% is from soil carbon sequestration, about 9% from mitigation of methane and about 2% from mitigation of soil N2O emissions ( Figure 8.4 ). The total mitigation potential per region is presented in Figure 8.5 .
The uncertainty in the estimates of the technical potential is given in Figure 8.6 , which shows one standard deviation either side of the mean estimate (box), and the 95% confidence interval about the mean (line). The range of the standard deviation, and the 95% confidence interval about the mean of 5800 MtCO2-eq/yr, are 3000-8700, and 300- 1140 0 MtCO2-eq/yr, respectively, and are largely determined by uncertainty in the per-area estimate for the mitigation measure. For soil carbon sequestration (89% of the total potential), this arises from the mixed linear effects model used to derive the mitigation potentials. The most appropriate mitigation response will vary among regions, and different portfolios of strategies will be developed in different regions, and in countries within a region.
US-EPA 2006b [NPR] ) provided estimates of the agricultural mitigation potential (global and regional) at various assumed
carbon prices, for N2O and CH4, but not for soil carbon sequestration. Manne & Richels 2004 [NotFound] ) estimated the economic mitigation potential (at 27 US$/tCO2-eq) for soil carbon sequestration only.
In the IPCC Third Assessment Report (TAR; IPCC, 2001b [NPR] ), estimates of agricultural mitigation potential by 2020 were 350-750 MtC/yr (~ 1300 - 2750 MtCO2/yr). The range was mainly caused by large uncertainties about CH4, N2O, and soil-related CO2 emissions. Most reductions will cost between 0 and 100 US$/tC-eq (~0-27 US$/tCO2-eq) with limited opportunities for negative net direct cost options. The analysis of agriculture included only conservation tillage, soil carbon sequestration, nitrogen fertilizer management, enteric methane reduction and rice paddy irrigation and fertilizers. The estimate for global mitigation potential was not broken down by region or practice.
Smith et al. 2007a [NPR, SRC, 2007] ) estimated the GHG mitigation potential in agriculture for all GHGs, for four IPCC SRES scenarios, at a range of carbon prices, globally and for all world regions. Using methods similar to McCarl and Schneider 2001 [JoC, SRC] Smith et al. 2007a [NPR, SRC, 2007] ) used marginal abatement cost (MAC) curves given in US-EPA 2006b [NPR] ) for either region-specific MACs where available for a given practice and region, or global MACs where these were unavailable from US-EPA 2006b [NPR] ).
Recent bottom-up estimates of agricultural mitigation potential of CH4 and N2O from US-EPA 2006b [NPR] ) and DeAngelo et al. ( 2006 ) have allowed inclusion of agricultural abatement into top-down global modelling of long-term climate stabilization scenario pathways. In the top-down framework, a dynamic cost-effective portfolio of abatement strategies is identified. The portfolio includes the least-cost combination of mitigation strategies from across all sectors of the economy, including agriculture. Initial implementations of agricultural abatement into top-down models have employed a variety of alternative approaches resulting in different decision modelling of agricultural abatement ( Rose et al., 2007 [NPR, MoS, SRC, 2007] ). Currently, only non-CO2 GHG crop (soil and paddy rice) and livestock (enteric and manure) abatement options are considered by top-down models. In addition, some models also consider emissions from burning of agricultural residues and waste, and fossil fuel combustion CO2 emissions. Top-down estimates of global CH4 and N2O mitigation potential, expressed in CO2 equivalents, are given in Table 8.6 and Figure 8.7 .
|Carbon price||Mitigation (MtCO2-eq/yr)||Number of scenarios|
Comparing mitigation estimates from top-down and bottom-up modelling is not straightforward. Bottom-up mitigation responses are typically constrained to input management (e.g., fertilizer quantity, livestock feed type) and cost estimates are partial equilibrium in that input and output market prices are fixed as can be key input quantities such as acreage or production. Top-down mitigation responses include more generic input management responses and changes in output (e.g., shifts from cropland to forest) as well as changes in market prices (e.g., decreases in land prices with increasing production costs due to a carbon tax). Global estimates of economic mitigation potential from different studies at different assumed carbon prices are presented in Figure 8.8 .
The top-down 2030 carbon prices, as well as the agricultural mitigation response, reflect the confluence of multiple forces, including differences in implementation of agricultural emissions and mitigation, as well as the stabilization target used, the magnitude of baseline emissions, baseline energy technology options, the eligible set of mitigation options, and the solution algorithm. As a result, the opportunity cost of agricultural mitigation in 2030 is very different across scenarios (i.e., model/baseline/mitigation option combinations). As illustrated by the connecting lines in Figure 8.7 , agricultural abatement is projected to increase with the tightness of the stabilization target. On-going model development in top-down land-use modelling is expected to yield more refined characterizations of agricultural alternatives and mitigation potential in the future.
Smith et al. 2007a [NPR, SRC, 2007] ) estimated global economic mitigation potentials for 2030 of 1500 - 1600, 2500 - 2700, and 4000-4300 MtCO2-eq/yr at carbon prices of up to 20, 50 and 100 US$/tCO2-eq., respectively shown for OECD versus EIT versus non-OECD/EIT ( Table 8.7 ). The change in global mitigation potential with increasing carbon price for each practice is shown in Figure 8.9 .
|Price of CO2-eq (US$/tCO2-eq)|
|SRES Scenario||Up to 20||Up to 50||Up to 100|
|B1||OECD||310 (60-450)||510 (290-740)||810 (440-1180)|
|EIT||150 (30-220)||250 (140-370)||410 (220-590)|
|Non-OECD/EIT||1080 (210-1560)||1780 (1000-2580)||2830 (1540-4120)|
|A1b||OECD||320 (60-460)||520 (290-760)||840 (450-1230)|
|EIT||160 (30-230)||260 (150-380)||410 (220-610)|
|Non-OECD/EIT||1110 (210-1610)||1820 (1020-2660)||2930 (1570-4290)|
|B2||OECD||330 (60-470)||540 (300-780)||870 (460-1280)|
|EIT||160 (30-240)||270 (150-390)||440 (230-640)|
|Non-OECD/EIT||1140 (210-1660)||1880 (1040-2740)||3050 (1610-4480)|
|A2||OECD||330 (60-480)||540 (300-790)||870 (460-1280)|
|EIT||165 (30-240)||270 (150-400)||440 (230-640)|
|Non-OECD/EIT||1150 (210-1670)||1890 (1050-2760)||3050 (1620-4480)|
Bioenergy to replace fossil fuels can be generated from agricultural feedstocks, including by-products of agricultural production, and dedicated energy crops.
The energy production and GHG mitigation potentials depend on yield/product ratios, and the total agricultural land area as well as type of production system. Less intensive management systems require re-use of residues for maintaining soil fertility. Intensively managed systems allow for higher utilization rates of residues, but also usually deploy crops with higher crop-to-residue ratios.
Estimates of energy production potential from agricultural residues vary between 15 and 70 EJ/yr. The latter figure is based on the regional production of food (in 2003 ) multiplied by harvesting or processing factors, and assumed recoverability factors. These figures do not subtract the potential competing uses of agricultural residues which, as indicated by ( Junginger et al., 2001 [ARC] ), can reduce significantly the net availability of agricultural residues for energy or materials. In addition, the expected future availability of residues from agriculture varies widely among studies. Dried dung can also be used as an energy feedstock. The total estimated contribution could be 5 to 55 EJ/yr worldwide, with the range defined by current global use at the low end, and technical potential at the high end. Utilization in the longer term is uncertain because dung is considered to be a “poor man’s fuel”.
Organic wastes and residues together could supply 20-125 EJ/yr by 2050, with organic wastes making a significant contribution.
The energy production and GHG mitigation potentials of dedicated energy crops depends on availability of land, which must also meet demands for food as well as for nature protection, sustainable management of soils and water reserves, and other sustainability criteria. Because future biomass resource availability for energy and materials depends on these and other factors, an accurate estimate is difficult to obtain. Berndes et al. 2003 [MoS, ARC] ) in reviewing 17 studies of future biomass availability found no complete integrated assessment and scenario studies. Various studies have arrived at differing figures for the potential contribution of biomass to future global energy supplies, ranging from below 100 EJ/yr to above 400 EJ/yr in 2050 Smeets et al. 2007 [ARC, 2007] ) indicate that ultimate technical potential for energy cropping on current agricultural land, with projected technological progress in agriculture and livestock, could deliver over 800 EJ/yr without jeopardizing the world’s food supply. In Hoogwijk et al. 2005 [ARC] and Hoogwijk 2004 [NPR, ARC] ), the IMAGE 2.2 model was used to analyse biomass production potentials for different SRES scenarios. Biomass production on abandoned agricultural land is calculated at 129 EJ (A2) up to 411 EJ (A1) for 2050 and possibly increasing after that timeframe. 273 EJ (for A1) – 156 EJ (for A2) may be available below US$ 2/GJ production costs. A recent study ( Sims et al., 2006 [MoS, SRC] ) which used lower per-area yield assumptions and bio-energy crop areas projected by the IMAGE 2.2 model suggested more modest potentials (22 EJ/yr) by 2025 .
Based on assessment of other studies, Hoogwijk et al. 2003 [ARC] ), indicated that marginal and degraded lands (including a land surface of 1.7 Gha worldwide) could, be it with lower productivities and higher production costs, contribute another 60-150 EJ. Differences among studies are largely attributable to uncertainty in land availability, energy crop yields, and assumptions on changes in agricultural efficiency. Those with the largest projected potential assume that not only degraded/surplus land are used, but also land currently used for food production (including pasture land, as did Smeets et al., 2007 [ARC, 2007] ).
Converting the potential biomass production into a mitigation potential is not straightforward. First, the mitigation potential is determined by the lowest supply and demand potentials, so without the full picture (see Chapter 11 ) no estimate can be made. Second, any potential from bioenergy use will be counted towards the potential of the sectors where bioenergy is used (mainly energy supply and transport). Third, the proportion of the agricultural biomass supply compared to that from the waste or forestry sector cannot be specified due to lack of information on cost curves.
Top-down integrated assessment models can give an estimate of the cost competitiveness of bioenergy mitigation options relative to one another and to other mitigation options in achieving specific climate goals. By taking into account the various bioenergy supplies and demands, these models can give estimates of the combined contribution of the agriculture, waste, and forestry sectors to bioenergy mitigation potential. For achieving long-term climate stabilization targets, the competitive cost-effective mitigation potential of biomass energy (primarily from agriculture) in 2030 is estimated to be 70 to 1260 MtCO2-eq/yr (0-13 EJ/yr) at up to 20 US$/t CO2-eq, and 560- 2320 MtCO2-eq/yr (0-21 EJ/yr) at up to 50 US$/tCO2-eq ( Rose et al., 2007 [NPR, MoS, SRC, 2007] , USCCSP, 2006 [NPR] ). There are no estimates for the additional potential from top down models at carbon prices up to 100 US$/tCO2-eq, but the estimate for prices above 100 US$/tCO2-eq is 2720 MtCO2-eq/yr (20-45 EJ/yr). This is of the same order of magnitude as the estimate from a synthesis of supply and demand presented in Chapter 11 , Section 188.8.131.52 . The mitigation potentials estimated by top-down models represent mitigation of 5-80%, and 20-90% of all other agricultural mitigation measures combined, at carbon prices of up to 20, and up to 50 US$/tCO2-eq, respectively.
There are various potential impacts of agricultural GHG mitigation on sustainable development. The impacts of mitigation activities in agriculture, on the constituents and determinants of sustainable development are set out in Table 8.8 . Broadly, three constituents of sustainable development have been envisioned as the critical minimum: social, economic, and environmental factors. Table 8.8 presents the degree and direction of the likely impact of the mitigation options. The exact magnitude of the effect, however, depends on the scale and intensity of the mitigation measures, and the sectors and policy arena in which they are undertaken.
Agriculture contributes 4% of global GDP (World Bank, 2003 [NPR] ) and provides employment to 1.3 billion people ( Dean, 2000 [NPR] ). It is a critical sector of the world economy, but uses more water than any other sector. In low-income countries, agriculture uses 87% of total extracted water, while this figure is 74% in middle-income countries and 30% in high-income countries (World Bank, 2003 [NPR] ). There are currently 276 Mha of irrigated croplands ( FAOSTAT, 2006 [NPR] ), a five-fold increase since the beginning of the 20th century. With irrigation increasing, water management is a serious issue. Through proper institutions and effective functioning of markets, water management can be implemented with favourable outcomes for both environmental and economic goals. There is a greater need for policy coherence and innovative responses creating a situation where users are asked to pay the full economic costs of the water. This has special relevance for developing countries. Removal of subsidies in the electricity and water sectors might lead to effective water use in agriculture, through adaptation of appropriate irrigation technology, such as drip irrigation in place of tube well irrigation.
Agriculture contributes nearly half of the CH4 and N2O emissions ( (Bhatia et al., 2004 ) ) and rice, nutrient, water and tillage management can help to mitigate these GHGs. By careful drainage and effective institutional support, irrigation costs for farmers can also be reduced, thereby improving economic aspects of sustainable development ( Rao, 1994 [NPR] ). An appropriate mix of rice cultivation with livestock, known as integrated annual crop-animal systems and traditionally found in West Africa, India and Indonesia and Vietnam, can enhance net income, improve cultivated agro-ecosystems, and enhance human well-being (Millennium Ecosystem Assessment, 2005 ). Such combinations of livestock and cropping, especially for rice, can improve income generation, even in semi-arid and arid areas of the world.
Groundwater quality may be enhanced and the loss of biodiversity can be influenced by the choice of fertilizer used and use of more targeted pesticides. Further, greater demand for farmyard manure would create income for the animal husbandry sector where usually the poor are engaged. Various country strategy papers on The Millennium Development Goal (MDG) clearly recommend encouragement to animal husbandry (e.g., World Bank, 2005 [NPR] ). This is intended to enhance livelihoods and create greater employment. Better nutrient management can also improve environmental sustainability.
Controlling overgrazing through pasture improvement has a favourable impact on livestock productivity (greater income from the same number of livestock) and slows or halts desertification (environmental aspect). It also provides social security to the poorest people during extreme events such as drought (especially in Sub-Saharan Africa). One effective strategy to control overgrazing is the prohibition of free grazing, as was done in China ( Rao, 1994 [NPR] ) but approaches in other regions need to take into account cultural and institutional contexts. Dryland and desert areas have the highest number of poor people (Millennium Ecosystem Assessment, 2005 ) and measures to halt overgrazing, coupled with improved livelihood options (e.g., fisheries in Syria , Israel and other central Asian countries), can help reduce poverty and achieve sustainability goals.
Land cover and tillage management could encourage favourable impacts on environmental goals. A mix of horticulture with optimal crop rotations would promote carbon sequestration and could also improve agro-ecosystem function. Societal well-being would also be enhanced by providing water and enhanced productivity. While the environmental benefits of tillage/residue management are clear, other impacts are less certain. Land restoration will have positive environmental impacts, but conversion of floodplains and wetlands to agriculture could hamper ecological function (reduced water recharge, bioremediation, nutrient cycling, etc.) and therefore, could have an adverse impact on sustainable development goals ( Kumar, 2001 [NPR, SRC] ).
The other mitigation measures listed in Table 8.8 are context- and location-specific in their influence on sustainable development constituents. Appropriate adoption of mitigation measures is likely in many cases to help achieve environmental goals, but farmers may incur additional costs, reducing their returns and income. This trade-off would be most visible in the short term, but in the long term, synergy amongst the constituents of sustainable development would emerge through improved natural capital. Trade-offs between economic and environmental aspects of sustainable development might become less important if the environmental gains were better acknowledged, quantified, and incorporated in the decision-making framework.
|Activity category||Sustainable development||Notes|
|Croplands – agronomy||?||+||+||1|
|Croplands – nutrient management||?||+||+||2|
|Croplands – tillage/residues||?||?||+||3|
|Croplands – water management||+||+||+||4|
|Croplands – rice management||+||+||+||5|
|Croplands – set-aside & LUC||?||-||+||6|
|Croplands – agro-forestry||+||?||+||7|
|Grasslands – grazing, nutrients, fire||+||+||+||8|
|Organic soils – restoration||?||?||+||9|
|Degraded soils – restoration||+||+||+||10|
|Livestock – feeding||-/?||+||?||13|
|Livestock – additives||-/?||n/d||n/d||14|
|Livestock – breeding||-/?||n/d||n/d||14|
Large-scale production of modern bioenergy crops, partly for export, could generate income and employment for rural regions of world. Nevertheless, these benefits will not necessarily flow to the rural populations that need them most. The net impacts for a region as a whole, including possible changes and improvements in agricultural production methods should be considered when developing biomass and bioenergy production capacity. Although experience around the globe (e.g., Brazil, India biofuels) shows that major socioeconomic benefits can be achieved, new bioenergy production schemes could benefit from the involvement of the regional stakeholders, particularly the farmers. Experience with such schemes needs to be built around the globe.
As discussed in Chapters 3 , 11 and 12 , mitigation, climate change impacts, and adaptation will occur simultaneously and interactively. Mitigation-driven actions in agriculture could have (a) positive adaptation consequences (e.g., carbon sequestration projects with positive drought preparedness aspects) or (b) negative adaptation consequences (e.g., if heavy dependence on biomass energy increases the sensitivity of energy supply to climatic extremes; see Chapter 12 , Subsection 12.1.4). Adaptation-driven actions also may have both (a) positive consequences for mitigation (e.g., residue return to fields to improve water holding capacity will also sequester carbon); and (b) negative consequences for mitigation (e.g., increasing use of nitrogen fertilizer to overcome falling yield leading to increased nitrous oxide emissions). In many cases, actions taken for reasons unrelated to either mitigation or adaptation (see Sections 8.6 and 8.7 ) may have considerable consequences for either or both(e.g., deforestation for agriculture or other purposes results in carbon loss as well as loss of ecosystems and resilience of local populations). Adaptation to climate change in the agricultural sector is detailed in ( IPCC, 2007 [NPR, 2007] ; Chapter 5).
For mitigation, variables such as growth rates for bioenergy feedstocks, the size of livestock herds, and rates of carbon sequestration in agricultural lands are affected by climate change ( Paustian et al., 2004 [SRC] ). The extent depends on the sign and magnitude of changes in temperature, soil moisture, and atmospheric CO2 concentration, which vary regionally ( Christensen et al., 2007 [NPR, MoS, 2007] ). All of these factors will alter the mitigation potential; some positively and some negatively. For example: (a) lower growth rates in bioenergy feedstocks will lead to larger emissions from hauling and increased cost; (b) lower livestock growth rates would possibly increase herd size and consequent emissions from manure and enteric fermentation; and (c) increased microbial decomposition under higher temperatures will lower soil carbon sequestration potential. Interactions also occur with adaptation. Butt et al. 2006 [JoC, SRC] and Reilly et al. 2001 [NPR, SRC] ) found that modified crop mix, land use, and irrigation are all potential adaptations to warmer climates. All would alter the mitigation potential. Some of the key vulnerabilities of agricultural mitigation strategies to climate change, and the implications of adaptation on GHG emissions from agriculture are summarized in Table 8.9 .
|Agricultural mitigation strategies||Vulnerability of the mitigation option to climate change||Implication for GHG emissions of adaptation actions|
|Cropland management – agronomy||Vulnerable to decreased rainfall, and in cases near the limit of their climate niche, to higher temperatures.||NO2 emissions would increase if fertilizer use increased, or if more legumes were planted in response to climate-induced production declines.|
|Cropland management – nutrient management||Only weakly sensitive to climate change, except in cases where the entire cropping enterprise becomes unviable.||No significant adaptation to effects of climate change possible beyond tailoring of practices to ambient conditions. Therefore, additional GHGs not expected.|
|Cropland management – tillage/residue management||Sensitive to climate change. Higher temperatures could lower soil carbon sequestration potential. Warmer, wetter climates can increase risk of crop pests and diseases associated with reduced till practices.||Adaptation not anticipated to have a significant GHG effect.|
|Cropland management – water management||Irrigation is susceptible to climate changes that reduce the availability of water for irrigation or increases crop water demand.||Possible increase in energy-related GHG emissions if greater pumping distances or volumes are required. Adoption of more water-use efficient practices will generally lower GHG emissions.|
|Cropland management – rice management||Vulnerable to climate-change-induced changes in water availability. Low CH4 emitting cultivars may be susceptible to changes in temperature beyond their tolerance limits.||Adaptation strategies are limited and not expected to have large GHG consequences.|
|Cropland management – set-aside and land-use change||Set-asides may be needed to offset loss of productivity on other lands.||Adaptation is either to try to keep production high on non-set-aside land, which could increase GHG emissions, or return some set-asides to production. Increases in GHGs are in both cases fairly small, and less than the case of not having set-asides in the first place. They could be further mitigated by applying low GHG emitting practices in all cases.|
|Cropland management – agro-forestry||Large changes in climate could make certain forms of agro-forestry unviable in particular situations.||Adaptation of practices and species used to less favourable climates could lead to some loss of CO2 uptake potential.|
|Grazing land management/pasture improvement||Fire management can be impacted negatively or positively by climate change depending on ecosystem and sign of climate change. Extreme drying or warming could make marginal grazing lands unviable. Wetter conditions will promote conversion of grazing lands to crops.||Increased fire protection activities can increase GHGs emissions by a small amount, thus reducing the net benefit obtained from reducing fire extent and frequency.|
|Management of agricultural organic soils||The mitigation measure is sensitive to increases in temperature or decreases in moisture, both of which would decrease the carbon sequestration potential.||Some trade-offs between CO2 uptake and CH4 emissions can be expected if the soils become wetter as a result of the adaptation management.|
|Restoration of degraded lands||The sustainability of restored lands could be vulnerable to increased temperature and/or decreased soil moisture.||Energy used to replant, or fertilizer used to increase establishment, success could lead to small additional GHG emissions|
|Livestock - improved feeding practices, specific agents and dietary additives, longer term structural and management changes and animal breeding||Weakly vulnerable to climate change except if it leads to the loss of viability of livestock enterprises in marginal areas or increased cost (or decreased availability) of feed inputs.||No general adaptation strategies. Specific strategies may have minor impacts on GHG emissions, for example, transport of feed supplements from distant locations could lead to increased net GHG emissions.|
|Manure/biosolid management||Controlled waste digestion generally positively affected by moderately rising temperatures. Where GHGs are not trapped, higher temperatures could hamper management.||If used as a nutrient source on pasture can increase CO2 uptake and carbon storage.|
|Bioenergy – energy crops, solid, liquid, biogas, residues||Particular bioenergy crops potentially sensitive to climate change, either positively or negatively. Areas devoted to bioenergy could be under increasing competition with the needs for food agriculture or biodiversity conservation under changing climate.||Generally, results in net CO2 uptake on land (apart from the fossil-fuel substitution). N2O emissions would increase if N turnover rates were greater than under previous land uses. Possible positive and negative impacts on net GHG emissions at various stages of the energy chain (cultivation, harvesting, transport, conversion) must be managed.|
Many recent studies have shown that actual levels of GHG mitigation are far below the technical potential for these measures. The gap between technical potential and realized GHG mitigation occurs due to costs and other barriers to implementation ( Smith, 2004b [NPR, SRC] ).
Globally and for Europe, ( Cannell 2003 ) ) suggested that, for carbon sequestration and bioenergy-derived fossil fuel offsets, the realistically achievable potential (potential estimated to take account of all barriers) was ~20% of the technical potential. Similar figures were derived by Freibauer et al. 2004 [SRC] ) and the European Climate Change Programme ( 2001 ) for agricultural carbon sequestration in Europe. Smith et al. 2005a [MoS, SRC] ) showed recently that carbon sequestration in Europe is likely to be negligible by the first Commitment Period of the Kyoto Protocol ( 2008 - 2012 ), despite the significant technical potential (e.g., Smith et al., 2000 [MoS, SRC] ; Freibauer et al., 2004 [SRC] ; Smith, 2004a [SRC] ). The estimates of global economic mitigation potential in 2030 at different costs reported in Smith et al. 2007a [NPR, SRC, 2007] ) were 28, 45 and 73% of technical potential at up to 20, 50 and 100 US$/tCO2-eq, respectively.
In Europe, there is little evidence that climate policy is affecting GHG emissions from agriculture (see Smith et al., 2005a [MoS, SRC] ), with most emission reduction occurring through non-climate policy (see Section 8.7 Freibauer et al., 2004 [SRC] ). Some countries have agricultural policies designed to reduce GHG emissions (e.g., Belgium), but most do not ( Smith et al., 2005a [MoS, SRC] ). The European Climate Change Programme ( 2001 ) recommended improvement of fertilizer application, set-aside, and reduction of livestock methane emissions (mainly through biogas production) as being the most cost-effective GHG mitigation options for European agriculture.
In North America, the US Global Climate Change Initiative aims to reduce GHG intensity by 18% by 2012 . Agricultural sector activities include manure management, reduced tillage, grass plantings, and afforestation of agricultural land. In Canada, agriculture contributes about 10% to national emissions, so mitigation (removals and emission reductions) is considered to be an important contribution to reducing emissions (and at the same time to reduce risk to air, water and soil quality). Various programmes (e.g., AAFC GHG Mitigation programme) encourage voluntary adoption of mitigation practices on farms.
In Oceania, vegetation management policies in Australia have assisted in progressively restricting emissions from land-use change (mainly land clearing for agriculture) to about 60% of 1990 levels. Complementary policies that aim to foster establishment of both commercial and non-commercial forestry and agro-forestry are resulting in significant afforestation of agricultural land in both Australia and New Zealand. Research is being supported to develop cost-effective GHG abatement technologies for livestock (including dietary manipulation and other methods of reducing enteric methane emissions, as well as manure management), agricultural soils (including nutrient and soil management strategies), savannas, and planted forests. The Greenhouse Challenge Plus programme and other partnership initiatives between the Government and industry are facilitating the integration of GHG abatement measures into agricultural management systems.
In Latin America and the Caribbean, climate change mitigation is still not considered in mainstream policy. Most countries have devoted efforts to capacity building for complying with obligations under the UNFCCC, and a few have prepared National Strategy Studies for Kyoto Protocol’s Clean Development Mechanism (CDM). Carbon sequestration in agricultural soils has the highest mitigation potential in the region, and its exclusion from the CDM has hindered wider adoption of pertinent practices (e.g., zero tillage).
In Asia, China has policies that reduce GHG emissions, but these were implemented for reasons other than climate policy. These are discussed further in Section 8.7 . Currently, there are no policies specifically aimed at reducing GHG emissions. Japan has a number of policies such as Biomass Nippon Strategy, which promotes the utilization of biomass as an alternative energy source, and Environment-Conserving Agriculture, which promotes energy-efficient agricultural machinery, reduction in use of fertilizer, and appropriate management of livestock waste, etc.
In Africa, the impacts of climate policy on agricultural emissions are small. There are no approved CDM projects in Africa related to the reduction of agricultural GHG emissions per se. Several projects are under investigation in relation to the restoration of agriculturally-degraded lands, carbon sequestration potential of agro-forestry, and reduction in sugarcane burning. Many countries in Africa have prepared National Strategy Studies for the CDM in complying with obligations under UNFCCC. The main obstacles to implementation of CDM projects in Africa, however, are lack of financial resources, qualified personnel, and the complexity of the CDM.
Agricultural GHG offsets can be encouraged by market-based trading schemes. Offset trading, or trading of credits, allows farmers to obtain credits for reducing their GHG emission reductions. The primary agricultural project types include CH4 capture and destruction, and soil carbon sequestration. Although not included in current projects, measures to reduce N2O emissions could be included in the future. The vast majority of agricultural projects have focused on CH4 reduction from livestock wastes in North America (Canada, Mexico and the United States), South America (Brazil), China, and Eastern Europe. Most of these projects have resulted in the production of Certified Emission Reductions (CERs) from the CDM. Credits are bought and sold through the use of offset aggregators, brokers, and traders. Although the CDM does not currently support soil carbon sequestration projects, emerging markets in Canada and the United States are supporting offset trading from soil carbon sequestration. In Canada, farm groups such as the Saskatchewan Soil Conservation Association (SSCA) encourage farmers to adopt no-till practices in return for carbon offset credits. In the USA, the Pacific Northwest Direct Seed Association offers soil carbon credits generated from no-till management to an energy company The Chicago Climate Exchange (CCX) (www.chicagoclimatex.com/) allows GHG offsets from no-tillage and conversion of cropland to grasslands to be traded by voluntary action through a market trading mechanism. These approaches to agriculturally derived GHG offset will likely expand geographically and in scope. Policy instruments are detailed in Chapter 13 ( Section 13.2 ).
The commonly mentioned barriers to adoption of carbon sequestration activities on agricultural lands include the following:
Maximum Storage: Carbon sequestration in soils or terrestrial biomass has a maximum capacity for the ecosystem, which may be reached after 15 to 60 years, depending on management practice, management history, and the system ( (West and Post, 2002 ) ). However, sequestration is a rapidly and cheaply deployable mitigation option, until more capital-intensive developments, and longer-lasting actions become available ( Caldeira et al., 2004 [NPR, ARC] ; Sands and McCarl, 2005 [NPR, SRC] ).
Reversibility: A subsequent change in management can reverse the gains in carbon sequestration over a similar period of time. Not all agricultural mitigation options are reversible; reduction in N2O and CH4 emissions, avoided emissions as a result of agricultural energy efficiency gains or substitution of fossil fuels by bio-energy are non-reversible.
Baseline: The GHG net emission reductions need to be assessed relative to a baseline. Selection of an appropriate baseline to measure management-induced soil carbon changes is still an obstacle in some mitigation projects. The extent of practices already in place in project regions will need to be determined for the baseline.
Uncertainty: This has two components: mechanism uncertainty and measurement uncertainty. Uncertainty about the complex biological and ecological processes involved in GHG emissions and carbon storage in agricultural systems makes investors more wary of these options than of more clear-cut industrial mitigation activities. This barrier can be reduced by investment in research. Secondly, agricultural systems exhibit substantial variability between seasons and locations, creating high variability in offset quantities at the farm level. This variability can be reduced by increasing the geographical extent and duration of the accounting unit (e.g., multi-region, multi-year contracts; Kim and McCarl, 2005 [NPR, SRC] ).
Displacement of Emissions: Adopting certain agricultural mitigation practices may reduce production within implementing regions, which, in turn, may be offset by increased production outside the project region unconstrained by GHG mitigation objectives, reducing the net emission reductions. ‘Wall-to-wall’ accounting can detect this, and crediting correction factors may need to be employed ( Murray et al., 2004 [MoS, SRC] ; US-EPA, 2005 [NPR] ).
Transaction costs: Under an incentive-based system such as a carbon market, the amount of money farmers receive is not the market price, but the market price less brokerage cost. This may be substantial, and is an increasing fraction as the amount of carbon involved diminishes, creating a serious entry barrier for smallholders. For example, a 50 kt contract needs 25 kha under soil carbon management (uptake ~ 2 tCO2 ha/yr). In developing countries, this could involve many thousands of farmers.
Measurement and monitoring costs: ( Mooney et al. 2004 ) ) argue that such costs are likely to be small (under 2% of the contract), but other studies disagree ( Smith, 2004c [SRC] ). In general, measurement costs per carbon-credit sold decrease as the quantity of carbon sequestered and area sampled increase. Methodological advances in measuring soil carbon may reduce costs and increase the sensitivity of change detection. However, improved methods to account for changes in soil bulk density remain a hindrance to quantification of changes in soil carbon stocks ( Izaurralde and Rice, 2006 [NPR, SRC] ). Development of remote sensing, new spectral techniques to measure soil carbon, and modelling offer opportunities to reduce costs but will require evaluation ( Izaurralde and Rice, 2006 [NPR, SRC] ,( Brown et al., 2006; ) Ogle and Paustian, 2005 [SRC] ; Gehl and Rice, 2007 [JoC, SRC, 2007] ).
Property rights: Property rights, landholdings, and the lack of a clear single-party land ownership in certain areas may inhibit implementation of management changes.
Other barriers: Other possible barriers to implementation include the availability of capital, the rate of capital stock turnover, the rate of technological development, risk attitudes, need for research and outreach, consistency with traditional practices, pressure for competing uses of agricultural land and water, demand for agricultural products, high costs for certain enabling technologies (e.g., soil tests before fertilization), and ease of compliance (e.g., straw burning is quicker than residue removal and can also control some weeds and diseases, so farmers favour straw burning).
Many policies other than climate policies affect GHG emissions from agriculture. These include other UN conventions such as Biodiversity, Desertification and actions on Sustainable Development (see Section 8.4.5 ), macroeconomic policy such as EU Common Agricultural Policy (CAP)/CAP reform, international free trade agreements, trading blocks, trade barriers, region-specific programmes, energy policy and price adjustment, and other environmental policies including various environmental/agro-environmental schemes. These are described further below.
In Asia, China has introduced laws to convert croplands to forest and grassland in Vulnerable Ecological Zones under the UN Convention on Desertification. This will increase carbon storage and reduce N2O emissions. Under the UN Convention on Biodiversity, China has initiated a programme that restores croplands close to lakes, the sea, or other natural lands as conservation zones for wildlife. This may increase soil carbon sequestration but, if restored to wetland, could increase CH4 emissions. In support of UN Sustainable Development guidelines, China has introduced a Land Reclamation Regulation ( 1988 ) in which land degraded by, for example, construction or mining is restored for use in agriculture, thereby increasing soil carbon storage. In Europe (including Eastern Europe, the Caucasus and Central Asia) and North America, the UN conventions have had few significant impacts on agricultural GHG emissions. In Europe, the UN Convention on Long Range Trans-boundary Air Pollutants also leads to regulations to control air pollutants (e.g., by regulating N emissions) that could have substantial impacts on emission reductions in the agricultural sector.
Some macro-economic changes, such as the burden of a high external debt in Latin America, triggered the adoption in the 1970 s of policies designed for improving the trade balance, mainly by promoting agricultural exports ( Tejo, 2004 [NPR] ). This resulted in the changes in land use and management (see Section 8.3.3 ), which are still causing increases in annual GHG emissions today. In other regions, such as the countries of Eastern Europe, the Caucasus and Central Asia and many Central and East European countries, political changes since 1990 have meant agricultural de-intensification with less inputs, and land abandonment, leading to a decrease in agricultural GHG emissions. In Africa, the cultivated area in Southern Africa has increased by 30% since 1960, while agricultural production has doubled ( Scholes and Biggs, 2004 [NPR] ). The macroeconomic development framework for Africa ( NEPAD, 2005 [NPR] ) emphasises agriculture-led development. It is, therefore, anticipated that the cropped area will continue to increase, especially in Central, East, and Southern Africa, perhaps at an accelerating rate. In Western Europe, North America, Asia (China) and Oceania, macroeconomic policy has tended to reduce GHG emissions. The declining emission trend in Western Europe is likely a consequence of successive reforms of the Common Agricultural Policy (CAP) since 1992 . The 2003 EU CAP reform is expected to lead to further reductions, mainly through reduction of animal numbers ( Binfield et al., 2006 [NPR] ). The reduced GHG emissions could be offset by activity elsewhere. Various macro-economic policies that potentially affect agricultural GHG emissions in each major world region are presented in Table 8.10 .
|Region||Macro-economic policies potentially affecting agricultural GHG emissions||Impact on CO2 emissions||Impact on N2O emissions||Impact on CH4 emissions|
|North America||• Energy conservation and energy security policies – promote bio-energy – increase fossil fuel offsets and possibly SOC (USA)||+|
|• Energy price adjustments - encourage agricultural mitigation - more reduced tillage – increase SOC (USA)||+||?|
|• Removal of the Grain Transportation Subsidy shifted production from annual to perennial crops and livestock (Canada)||+||+||+|
|Latin America||• Policies since 1970s to promote agricultural products exports (Tejo, 2004) resulting in land management change –increasing GHG emissions (Latin America)||-||-||-|
|• Promotion of biofuels (e.g., PROALCOOL (Brazil)||+|
|• Brazil and Argentina implemented policies to make compulsory 5% biodiesel in all diesel fuels consumed (Brazil & Argentina)||+|
|Europe, the Caucasus and Central Asia||• Common Agricultural Policy (CAP) 2003 - Single Farm Payment decoupled from production - replaces most of the previous area-based payments. Income support conditional to statutory environmental management requirements (e.g., legislation on nitrates) and the obligation to maintain land under permanent pasture (cross-compliance).||+||+|
|• Political changes in Eastern Europe - closure of many intensive pig units - reduced GHG emissions (EU and wider Europe)||+||+||+|
|• Macro-economic changes in the countries of Eastern Europe, the Caucasus and Central Asia:|
|a) Abandonment of croplands since 1990 (1.5 Mha); grasslands and regenerating forests sequestering carbon in soils and woody biomass (all countries of Eastern Europe, the Caucasus and Central Asia:)||+||+|
|b) Use of agricultural machinery declined and fossil fuel use per ha of cropland (Romanenkov et al., 2004) - decreased CO2 (fossil fuel) increased CO2 (straw burning – all countries of Eastern Europe, the Caucasus and Central Asia)||+|
|c) Fertilizer consumption has dropped; 1999 N2O emissions from agriculture 19.5% of 1990 level (Russia & Belarus).||+|
|d) CO2 emissions from liming have dropped to 8% of 1990 levels (Russia)||+|
|e) Livestock CH4 emissions in 1999 were less than 48% of the 1990 level (Russia)||+|
|f) The use of bare fallowing has declined (88% of the area in bare fallow in 1999 compared to 1990; Agriculture of Russia, 2004) (Russia)||+|
|g) Changes in rotational structure (more perennial grasses) (Russia)|
|Africa||• The cultivated area in Southern Africa has increased 30% since 1960, while agricultural production has doubled - agriculture-led development (Scholes and Biggs 2004; NEPAD 2005).Cropped area will continue to increase, especially in Central, East and Southern Africa, perhaps at an accelerating rate.||-||-||-|
|Asia||• In some areas, croplands are currently in set-aside for economic reasons (China)||+||+|
|Oceania||• Australia and New Zealand continue to provide little direct subsidy to agriculture - highly efficient industries that minimize unnecessary inputs and reduce waste - potential for high losses (such as N2O) is reduced. Continuing tightening of terms of trade for farm enterprises, as well as ongoing relaxation of requirements for agricultural imports, is likely to maintain this focus (Australia and New Zealand)||+|
|• The establishment of comprehensive water markets are expected, over time, to result in reductions in the size of industries such as rice and irrigated dairy with consequent reductions in the emissions from these sectors (Australia)||+||+|
WTO negotiations, to the extent they move toward free trade, would permit countries to better adjust to climate change and the dislocations in production caused by mitigation activities, by adjusting their import/export mix. International trade agreements such as WTO may also have impacts on the amount and geographical distribution of GHG emissions. If agricultural subsidies are reduced and markets become more open, a shift in production from developed to developing countries would be expected, with the consequent displacement of GHG emissions to the latter. Since agricultural practices and GHG emissions per unit product differ between countries, such displacement may also cause changes in total emissions from agriculture. In addition, the increase in international flow of agricultural products which may result from trade liberalization could cause higher GHG emissions from the use of transport fuels.
In most world regions, environmental policies have been put in place to improve fertility, to reduce erosion and soil loss, and to improve agricultural efficiency. The majority of these environmental policies also reduce GHG emissions. Various environmental policies not implemented specifically to address GHG emissions but potentially affect agricultural GHG emissions in each major world region are presented in Table 8.11 .
In all regions, policies to improve other aspects of the environment have been more effective in reducing GHG emissions from agriculture than policies aimed specifically at reducing agricultural GHG emissions (see Section 8.6.1 ). The importance of identifying these co-benefits when formulating climate and other environmental policy is addressed in Section 8.8 .
|Region||Other environmental policies potentially affecting agricultural GHG emissions||Impact on CO2 emissions||Impact on N2O emissions||Impact on CH4 emissions|
|North America||• Environmental Quality Incentives Program (EQIP) – cost-sharing and incentive payments for conservation practices on working farms (USA)||+||+|
|• Conservation Reserve Program (CRP) - environmentally sensitive land converted to native grasses, trees, etc. (USA)||+||+|
|• Conservation Security Program (CSP) – assistance promoting conservation on cropland, pasture and range land (and farm woodland) (USA)||+||+|
|• Green cover in Canada and provincial initiatives – encourages shift from annual to perennial crop production on poor quality soils (Canada)||+||+|
|• Agriculture Policy Framework (APF) programmes to reduce agriculture risks to the environment, including GHG emissions (Canada)||+||+||+|
|• Nutrient Management programmes – introduced to improve water quality, may indirectly reduce N2O emissions (Canada)||+||+||+|
|Latin America||• Increasing adoption of environmental policies driven by globalization, consolidation of democratic regimes (Latin America & Caribbean)||+/-||+/-||+/-|
|• 14 countries have introduced environmental regulations over the last 20 years – most have implemented measures to protect the environment||+||?|
|• Promotion of no-till agriculture in the Mercosur area (Brazil, Argentina, Uruguay and Paraguay)||+||?|
|• “Program Crop-Livestock Integration” promotes soil carbon, reduced erosion, reduced pathogens, fertility for pastures, no till cropping (Brazil)||+|
|Europe, the Caucasus and Central Asia||• EU set aside programme - encouraged carbon sequestering practices, but now replaced by the single farm payment under the new CAP (EU)||+|
|• EU/number of member states - soil action plans to promote soil quality/health/ sustainability, encourages soil carbon sequestration (EU)||+|
|• Encouragement of composting in some EU member states (e.g., Belgium; Sleutel 2005), but policies are limited (Smith et al., 2005a) (EU)||+|
|• EU Water Framework Directive (WFD) promotes careful use of N fertilizer. Impact of WFD on agricultural GHG emissions as yet unclear (EU)||?||+|
|• The ban of burning of field residues in the 1980s (for air quality purposes) enhance soil carbon, reduce N2O and CH4 (Smith et al., 1997; 2000) (EU)||+||+||+|
|• The dumping ban at sea of sewage sludge in Europe in 1998 - more sludge reached agricultural land (Smith et al., 2000; 2001) (EU)||+|
|• "Vandmiljøplaner" (water environmental plans) for the agricultural sector with clear effect (decrease) of GHGs (Denmark)||+|
|• Land Codes of the Russian Federation, Belarus and the Ukraine - land conservation for promoting soil quality restoration and protection||+|
|• “Land Reform Development in Russian Federation” & “Fertility 2006-2010” - plans to promote soil conservation/fertility/sustainability (Russia)||+|
|• Ukrainian law “Land protection” - action plans to promote soil conservation/increase commercial yields/fertility/sustainability (Ukraine)||+|
|• Laws in Belarus such as “State Control of Land Use and Land Protection” encourages carbon sequestration (Belarus)||+||+|
|• Laws in the Ukraine to promote conversion of degraded lands to set-aside (Ukraine)||+||+|
|• Water quality initiatives, for example, Water Codes encourage reforestation and grassland riparian zones (Russia, Ukraine and Belarus)||+||?|
|• The ban of fertilizer application in some areas - reduce N2O emissions (Russia, Belarus, Ukraine) & regional programmes for example, Revival of the Volga||+||+|
|Africa||• The reduction of the area of rangelands burned - objective of both colonial and post-colonial administrations; renewed efforts (South Africa, 1998)||+||+||+|
|Asia||• Soil sustainability programmes - N fertilizer added to soils only after soil N testing (China)||+|
|• Regional agricultural development programmes - enhance soil carbon storage (China)||+|
|• Water quality programmes that control non-point source pollution (China)||+|
|• Air quality legislation - bans straw burning, thus reducing CO2 (and CH4 and N2O) emissions (China)||+||+||+|
|• “Township Enterprises” & “Ecological Municipality” - reduce waste disposal, chemical fertilizer and pesticides, and bans straw burning (China)||+||+||+|
|Oceania||• Wide range of policies to maintain function/conservation of agricultural landscapes, river systems and other ecosystems (Australia and New Zealand)||+||-||-|
|• Industry changes leading to rapid increase in N fertilizer use over the past decade (250% and 500% increases in Australia and New Zealand, respectively)||+||+|
|• Increases in intensive livestock production; raised concerns about water quality and the health of riverine/offshore ecosystems (Australia and New Zealand)||+||+|
|• Policy responses are being developed that include monitoring, regulatory, research and extension components (Australia and New Zealand)||+||+||+|
Many of the measures aimed at reducing GHG emissions have other impacts on the productivity and environmental integrity of agricultural ecosystems, mostly positive ( Table 8.12 ). These measures are often adopted mainly for reasons other than GHG mitigation (see Section 8.7.3 ). Agro-ecosystems are inherently complex and very few practices yield purely win-win outcomes; most involve some trade-offs (DeFries et al., 2004; Viner et al., 2006 [NPR] ) above certain levels or intensities of implementation. Specific examples of co-benefits and trade-offs among agricultural GHG mitigation measures include:
The co-benefits and trade-offs of a practice may vary from place to place because of differences in climate, soil, or the way the practice is adopted. In producing bio-energy, for example, if the feedstock is crop residue, that may reduce soil quality by depleting soil organic matter. Conversely, if the feedstock is a densely rooted perennial crop that may replenish organic matter and thereby improve soil quality ( Paustian et al., 2004 [SRC] ).These few examples, and the general trends described in Table 8.12 , demonstrate that GHG mitigation practices on farm lands exert complex, interactive effects on the environment, sometimes far from the site at which they are imposed. The merits of a given practice, therefore, cannot be judged solely on effectiveness of GHG mitigation.
|Measure||Examples||Food security (productivity)||Water quality||Water conservation||Soil quality||Air quality||Bio-diversity, wildlife habitat||Energy conservation||Conservation of other biomes||Aesthetic/ amenity value|
|Water management (irrigation, drainage)||+||+/-||+/-||+/-||-||+|
|Set-aside, land-use change||-||+||+||+||+||+||+||-||+|
|Grazing land management/ pasture improvement||Grazing intensity||+/-||+||+||+|
|Increased productivity (e.g., fertilization)||+||+/-|
|Species introduction (including legumes)||+||+||+|
|Management of organic soils||Avoid drainage of/restore wetlands||-||+||+||+||-||+|
|Restoration of degraded lands||Erosion control, organic amendments, nutrient amendments||+||+||+||+||+||+|
|Livestock management||Improved feeding practices||+||+/-||+|
|Specific agents and dietary additives||+|
|Longer term structural and management changes and animal breeding||+|
|Manure/biosolid management||Improved storage and handling||+||+/-||+||+/-|
|More efficient use as nutrient source||+||+||+||+||+|
|Bioenergy||Energy crops, solid, liquid, biogas, residues||-||-||+||-|
|References (see footnotes)||a||b||c||d||e||f||g||h||i|
There is much scope for technological developments to reduce GHG emissions in the agricultural sector. For example, increases in crop yields and animal productivity will reduce emissions per unit of production. Such increases in crop and animal productivity will be implemented through improved management and husbandry techniques, such as better management, genetically modified crops, improved cultivars, fertilizer recommendation systems, precision agriculture, improved animal breeds, improved animal nutrition, dietary additives and growth promoters, improved animal fertility, bio-energy crops, anaerobic slurry digestion and methane capture systems. All of these depend to some extent on technological developments. Although technological improvement may have very significant effects, transfer of these technologies is a key requirement for these mitigations to be realized. For example, the efficiency of N use has improved over the last two decades in developed countries, but continues to decline in many developing countries due to barriers to technology transfer (International Fertilizer Industry Association, 2007 ). Based on technology change scenarios developed by Ewert et al. 2005 [MoS] ), and derived from extrapolation of current trends in FAO data, Smith et al. 2005b [SRC] ) showed that technological improvements could potentially counteract the negative impacts of climate change on cropland and grassland soil carbon stocks in Europe. This and other work ( Rounsevell et al., 2006 [MoS, SRC] ) suggest that technological improvement will be a key factor in GHG mitigation in the future.
In most instances, the cost of employing mitigation strategies will not alter radically in the medium term. There will be some shifts in costs due to changes in prices of agricultural products and inputs, but these are unlikely to be of significant magnitude. Likewise, the potential of most options for CO2 reduction is unlikely to change greatly. There are some exceptions which fall into two categories: (i) options where the practice or technology is not new, but where the emission reduction potential has not been adequately quantified, such as improved nutrient utilization; and (ii) options where technologies are still being refined such as probiotics in animal diets, or nitrification inhibitors.
Many of the mitigation strategies outlined for agriculture employ existing technology (e.g., crop management, livestock management). With such strategies, the main issue is technology transfer, diffusion, and deployment. Other strategies involve new use of existing technologies. For example, oils have been used in animal diets for many years to increase dietary energy content, but their role as a methane suppressant is relatively new, and the parameters of the technology in terms of scope for methane reduction are only now being defined. Other strategies still require further research to allow viable systems to operate (e.g., bio-energy crops). Finally, many novel mitigation strategies are presently being refined, such as the use of probiotics, novel plant extracts, and the development of vaccines. Thus, there is still a major role for research and development in this area.
Differences between regions can arise due to the state of development of the agricultural industry, the resources available and legislation. For example, the scope to use specific agents and dietary additives in ruminants is much greater in developed than in the developing regions because of cost, opportunity (e.g., it is easier to administer products to animals in confined systems than in free ranging or nomadic systems), and availability of the technology ( US-EPA, 2006a [NPR] ). Furthermore, certain technologies are not allowed in some regions, for example, ionophores are banned from use in animal feeding in the EU, and genetically modified crops are not approved for use in some countries.
Trends in GHG emissions in the agricultural sector depend mainly on the level and rate of socio-economic development, human population growth, and diet, application of adequate technologies, climate and non-climate policies, and future climate change. Consequently, mitigation potentials in the agricultural sector are uncertain, making a consensus difficult to achieve and hindering policy making. However, agriculture is a significant contributor to GHG emissions ( Section 8.2 ). Mitigation is unlikely to occur without action, and higher emissions are projected in the future if current trends are left unconstrained. According to current projections, the global population will reach 9 billion by 2050, an increase of about 50% over current levels ( Lutz et al., 2001 [JoC] ; Cohen, 2003 [JoC] ). Because of these increases and changing consumption patterns, some analyses estimate that the production of cereals will need to roughly double in coming decades ( Tilman et al., 2001 [JoC, MoS] ;( Roy et al., 2002; ) Green et al., 2005 [JoC] ). Achieving these increases in food production may require more use of N fertilizer, leading to possible increases in N2O emissions, unless more efficient fertilization techniques and products can be found ( (Galloway, 2003; ) ( Mosier, 2002 ) ). Greater demands for food could also increase CH4 emissions from enteric fermentation if livestock numbers increase in response to demands for meat and other livestock products. As projected by the IMAGE 2.2 model, CO2, CH4, and N2O emissions associated with land use vary greatly between scenarios ( Strengers et al., 2004 [MoS, ARC] ), depending on trends towards globalization or regionalization, and on the emphasis placed on material wealth relative to sustainability and equity.
Some countries are moving forward with climate and non-climate policies, particularly those linked with sustainable development and improving environmental quality as described in Sections 8.6 and 8.7 . These policies will likely have direct or synergistic effects on GHG emissions and provide a way forward for mitigation in the agricultural sector. Moreover, global sharing of innovative technologies for efficient use of land resources and agricultural inputs, in an effort to eliminate poverty and malnutrition, will also enhance the likelihood of significant mitigation from the agricultural sector.
Mitigation of GHG emissions associated with various agricultural activities and soil carbon sequestration could be achieved through best management practices, many of which are currently available for implementation. Best management practices are not only essential for mitigating GHG emissions, but also for other facets of environmental protection such as air and water quality management. Uncertainties do exist, but they can be reduced through finer scale assessments of best management practices within countries, evaluating not only the GHG mitigation potential but also the influences of mitigation options on socio-economic conditions and other environmental impacts.
The long-term outlook for development of mitigation practices for livestock systems is encouraging. Continuous improvements in animal breeds are likely, and these will improve the GHG emissions per kg of animal product. Enhanced production efficiency due to structural change or better application of existing technologies is also generally associated with reduced emissions, and there is a trend towards increased efficiency in both developed and developing countries. New technologies may emerge to reduce emissions from livestock such as probiotics, a methane vaccine or methane inhibitors. However, increased world demand for animal products may mean that while emissions per kg of product decline, total emissions may increase.
Recycling of agricultural by-products, such as crop residues and animal manures, and production of energy crops provides opportunities for direct mitigation of GHG emissions from fossil fuel offsets. However, there are barriers in technologies and economics to using agricultural wastes, and in converting energy crops into commercial fuels. The development of innovative technologies is a critical factor in realizing the potential for biofuel production from agricultural wastes and energy crops. This mitigation option could be moved forward with government investment for the development of these technologies, and subsidies for using these forms of energy.
A number of agricultural mitigation options which have limited potential now will likely have increased potential in the long-term. Examples include better use of fertilizer through precision farming, wider use of slow and controlled release fertilizers and of nitrification inhibitors, and other practices that reduce N application (and thus N2O emissions). Similarly, enhanced N-use efficiency is achievable as technologies such as field diagnostics, fertilizer recommendations from expert/decision support systems and fertilizer placement technologies are developed and more widely used. New fertilizers and water management systems in paddy rice are also likely in the longer term.
Possible changes to climate and atmosphere in coming decades may influence GHG emissions from agriculture, and the effectiveness of practices adopted to minimize them. For example, atmospheric CO2 concentrations, likely to double within the next century, may affect agro-ecosystems through changes in plant growth rates, plant litter composition, drought tolerance, and nitrogen demands (e.g., Long et al., 2006 [JoC] ;( Henry et al., 2005; ) ( van Groenigen et al., 2005; ) ( Jensen and Christensen, 2004; ) ( Torbert et al., 2000; ) ( Norby et al., 2001 ) ). Similarly, atmospheric nitrogen deposition also affects crop production systems as well as changing temperature regimes, although the effect will depend on the magnitude of change and response of the crop, forage, or livestock species. For example, increasing temperatures are likely to have a positive effect on crop production in colder regions due to a longer growing season ( Smith et al., 2005b [SRC] ). In contrast, increasing temperatures could accelerate decomposition of soil organic matter, releasing stored soil carbon into the atmosphere ( Knorr et al., 2005 [JoC] ; Fang et al., 2005 [JoC, SRC] ; Smith et al. 2005b [SRC] ). Furthermore, changes in precipitation patterns could change the adaptability of crops or cropping systems selected to reduce GHG emissions. Many of these effects have high levels of uncertainty; but demonstrate that practices chosen to reduce GHG emissions may not have the same effectiveness in coming decades. Consequently, programmes to reduce emissions in the agricultural sector will need to be designed with flexibility for adaptation in response to climate change.
Overall, the outlook for GHG mitigation in agriculture suggests significant potential. Current initiatives suggest that identifying synergies between climate change policies, sustainable development, and improvement of environmental quality will likely lead the way forward to realization of mitigation potential in this sector.
Albrecht, A. and S.T. Kandji, 2003: Carbon sequestration in tropical agroforestry systems. Agriculture, Ecosystems and Environment, 99, pp. 15-27. Clean
Alcock, D. and R.S. Hegarty, 2006: Effects of pasture improvement on productivity, gross margin and methane emissions of a grazing sheep enterprise. In Greenhouse Gases and Animal Agriculture: An Update. C.R. Soliva, J. Takahashi, and M. Kreuzer (eds.), International Congress Series No. 1293, Elsevier, The Netherlands, pp. 103-106. [NPR]
Alvarez, R. 2005: A review of nitrogen fertilizer and conservative tillage effects on soil organic storage. Soil Use and Management, 21, pp. 38-52. Clean
Amon, B., T. Amon, J. Boxberger, and C. Wagner-Alt, 2001: Emissions of NH3, N2O and CH4 from dairy cows housed in a farmyard manure tying stall (housing, manure storage, manure spreading). Nutrient Cycling in Agro-Ecosystems, 60, pp. 103-113. Clean
Amon, B., V. Kryvoruchko, T. Amon, and S. Zechmeister-Boltenstern, 2006: Methane, nitrous oxide and ammonia emissions during storage and after application of dairy cattle slurry and influence of slurry treatment. Agriculture, Ecosystems & Environment, 112, pp. 153-162. Clean
Aulakh, M.S., R., Wassmann, C. Bueno, and H. Rennenberg, 2001: Impact of root exudates of different cultivars and plant development stages of rice (Oryza sativa L.) on methane production in a paddy soil. Plant and Soil, 230, pp. 77-86. Clean
Balmford, A., R.E. Green, and J.P.W. Scharlemann, 2005: Sparing land for nature: exploring the potential impact of changes in agricultural yield on the area needed for crop production. Global Change Biology, 11, pp. 1594-1605. Clean
Barak, P., B.O. Jobe, A.R. Krueger, L.A. Peterson, and D.A. Laird, 1997: Effects of long-term soil acidification due to nitrogen fertilizer inputs in Wisconscin. Plant and Soil, 197, pp. 61-69. Clean
Barthès, B., A. Azontonde, E. Blanchart, C. Girardin, C. Villenave, S. Lesaint, R. Oliver, and C. Feller, 2004: Effect of a legume cover crop (Mucuna pruriens var. utilis) on soil carbon in an Ultisol under maize cultivation in southern Benin. Soil Use and Management, 20, pp. 231-239. Clean
Batjes, N.H., 1999: Management options for reducing CO2-concentrations in the atmosphere by increasing carbon sequestration in the soil. Dutch National Research Programme on Global Air Pollution and Climate Change, Project executed by the International Soil Reference and Information Centre, Wageningen, The Netherlands, 114 pp. [NPR]
Bauman, D.E., 1992: Bovine somatotropin: review of an emerging animal technology. Journal of Dairy Science, 75, pp. 3432-3451. Clean
Beauchemin, K. and S. McGinn, 2005: Methane emissions from feedlot cattle fed barley or corn diets. Journal of Animal Science, 83, pp. 653-661. Clean
Benz, D.A. and D.E. Johnson, 1982: The effect of monensin on energy partitioning by forage fed steers. Proceedings of the West Section of the American Society of Animal Science, 33, 60 pp. Clean
Beringer, J., L.B. Hutley, N.J. Tapper, A. Coutts, A. Kerley, and A.P. O’Grady, 2003: Fire impacts on surface heat, moisture and carbon fluxes from a tropical savanna in northern Australia. International Journal of Wildland Fire, 12, pp. 333-340. Clean
Berndes, G. and P. Börjesson, 2002: Multi-functional biomass production systems. Available at: <http://www.elkraft.ntnu.no/eno/konf_pub/ISES2003/full_paper/6%20MISCELLANEOUS/O6%204.pdf> accessed 26 March 2007. [NPR]
Berndes, G., F. Fredrikson, and P. Borjesson, 2004: Cadmium accumulation and Salix-based phytoextraction on arable land in Sweden. Agriculture, Ecosystems & Environment, 103, pp. 207-223. Clean
Bhatia, A., H. Pathak, and P.K. Aggarwal, 2004: Inventory of methane and nitrous oxide emissions from agricultural soils of India and their global warming potential. Current Science, 87, pp. 317-324. Clean
Binfield, J., T. Donnellan, K. Hanrahan, and P. Westhoff, 2006: World Agricultural Trade Reform and the WTO Doha Development Round: Analysis of the Impact on EU and Irish Agriculture. Teagasc, Athenry, Galway, Ireland, 79 pp. [NPR]
Boadi, D., C. Benchaar, J. Chiquette, and D. Massé, 2004: Mitigation strategies to reduce enteric methane emissions from dairy cows: update review. Canadian Journal of Animal Science, 84, pp. 319-335. Clean
Börjesson, P. and G. Berndes, 2006: The prospects for willow plantations for wastewater treatment in Sweden. Biomass & Bioenergy, 30, pp. 428-438. Clean
Brown, D.J., K.D. Shepherd, M.G. Walsh, M.D. Mays, and T.G. Reinsch 2006: Global soil characterization with VNIR diffuse reflectance spectroscopy. Geoderma, 132, pp. 273-290. Clean
Cai, Z.C. and H. Xu, 2004: Options for mitigating CH4 emissions from rice fields in China. In Material Circulation through Agro-Ecosystems in East Asia and Assessment of Its Environmental Impact, Hayashi, Y. (ed.), NIAES Series 5, Tsukuba, pp. 45-55. [NPR, SRC]
Caldeira, K., M.G. Morgan, D. Baldocchi, P.G. Brewer, C.T.A. Chen, G.J. Nabuurs, N. Nakicenovic, and G.P. Robertson, 2004: A portfolio of carbon management options. In The Global Carbon Cycle. Integrating Humans, Climate, and the Natural World, C.B. Field, and M.R. Raupach (eds.). SCOPE 62, Island Press, Washington DC, pp.103-129. [NPR, ARC]
Cannell, M.G.R., 2003: Carbon sequestration and biomass energy offset: theoretical, potential and achievable capacities globally, in Europe and the UK. Biomass & Bioenergy, 24, pp. 97-116. Clean
Cassman, K.G., A. Dobermann, D.T. Walters, and H. Yang, 2003: Meeting cereal demand while protecting natural resources and improving environmental quality. Annual Review of Environment and Resources, 28, pp. 315-358. [ARC]
Cerri, C.C., M. Bernoux, C.E.P. Cerri, and C. Feller, 2004: Carbon cycling and sequestration opportunities in South America: the case of Brazil. Soil Use and Management, 20, pp. 248-254. Clean
Chadwick, D.R., 2005: Emissions of ammonia, nitrous oxide and methane from cattle manure heaps: effect of compaction and covering. Atmospheric Environment, 39, pp. 787-799. Clean
Christensen, J.H., B. Hewitson, A. Busuioc, A. Chen, X. Gao, I. Held, R. Jones, R.K. Kolli, W.-T. Kwon, R. Laprise, V. Magaña Rueda, L. Mearns, C.G. Menéndez, J. Räisänen, A. Rinke, A. Sarr and P. Whetton, 2007: Regional Climate Projections. In: Climate Change 2007: The Physical Science Basis. Contribution of Working Group I to the Fourth Assessment Report of the Intergovernmental Panel on Climate Change [Solomon, S., D. Qin, M. Manning, Z. Chen, M. Marquis, K.B. Averyt, M. Tignor and H.L. Miller (eds.)]. Cambridge University Press, Cambridge, United Kingdom and New York, NY, USA. [NPR, MoS, 2007]
Clark, H., C. Pinares, and C. de Klein, 2005: Methane and nitrous oxide emissions from grazed grasslands. In Grassland. A Global Resource, D. McGilloway (ed.), Wageningen Academic Publishers, Wageningen, The Netherlands, pp. 279-293. [NPR]
Clemens, J. and H.J. Ahlgrimm, 2001: Greenhouse gases from animal husbandry: mitigation options. Nutrient Cycling in Agroecosystems, 60, pp. 287-300. Clean
Clemens, J., M. Trimborn, P. Weiland, and B. Amon, 2006: Mitigation of greenhouse gas emissions by anaerobic digestion of cattle slurry. Agriculture, Ecosystems and Environment, 112, pp. 171-177. Clean
Cole, C.V., J. Duxbury, J. Freney, O. Heinemeyer, K. Minami, A. Mosier, K. Paustian, N. Rosenberg, N. Sampson, D. Sauerbeck, and Q. Zhao, 1997: Global estimates of potential mitigation of greenhouse gas emissions by agriculture. Nutrient Cycling in Agroecosystems, 49, pp. 221-228. [MoS]
Conant, R.T., K. Paustian, and E.T. Elliott, 2001: Grassland management and conversion into grassland: Effects on soil carbon. Ecological Applications, 11, pp. 343-355. Clean
Conant, R.T., K. Paustian, S.J. Del Grosso, and W.J. Parton, 2005: Nitrogen pools and fluxes in grassland soils sequestering carbon. Nutrient Cycling in Agroecosystems, 71, pp. 239-248. Clean
Connor, D.J., 2004: Designing cropping systems for efficient use of limited water in southern Australia. European Journal of Agronomy, 21, pp. 419-431. Clean
Crutzen, P.J., 1995: The role of methane in atmospheric chemistry and climate. Proceedings of the Eighth International Symposium on Ruminant Physiology. Ruminant Physiology: Digestion, Metabolism, Growth and Reproduction, Von Engelhardt, W., S. Leonhard-Marek, G. Breves, and D. Giesecke (eds.), Ferdinand Enke Verlag, Stuttgart, pp. 291-316. [NPR]
Dalal, R.C., W. Wang, G.P. Robertson, and W.J. Parton, 2003: Nitrous oxide emission from Australian agricultural lands and mitigation options: a review. Australian Journal of Soil Research, 41, pp. 165-195. Clean
DeAngelo, B.J., F.C. de la Chesnaye, R.H. Beach, A. Sommer, and B.C. Murray, 2006: Methane and nitrous oxide mitigation in agriculture. Multi-Greenhouse Gas Mitigation and Climate Policy, Energy Journal, Special Issue #3.Available at: <http://www.iaee.org/en/publications/journal.aspx> accessed 26 March 2007. [NPR, ARC]
DeFries, R.S., J.A. Foley, and G.P. Asner, 2004: Land-use choices: balancing human needs and ecosystem function. Frontiers in Ecology and Environment, 2, pp. 249-257. Clean
Denman, K.L., G. Brasseur, A. Chidthaisong, P. Ciais, P.M. Cox, R.E. Dickinson, D. Hauglustaine, C. Heinze, E. Holland, D. Jacob, U. Lohmann, S Ramachandran, P.L. da Silva Dias, S.C. Wofsy and X. Zhang, 2007: Couplings Between Changes in the Climate System and Biogeochemistry. In: Climate Change 2007: The Physical Science Basis. Contribution of Working Group I to the Fourth Assessment Report of the Intergovernmental Panel on Climate Change [Solomon, S., D. Qin, M. Manning, Z. Chen, M. Marquis, K.B. Averyt, M.Tignor and H.L. Miller (eds.)]. Cambridge University Press, Cambridge, United Kingdom and New York, NY, USA. [NPR, ARC, 2007]
Derner, J.D., T.W. Boutton, and D.D. Briske, 2006: Grazing and ecosystem carbon storage in the North American Great Plains. Plant and Soil, 280, pp. 77-90. Clean
Dias de Oliveira, M.E., B.E. Vaughan, and E.J. Rykiel, Jr., 2005: Ethanol as fuel: energy, carbon dioxide balances, and ecological footprint. BioScience, 55, pp. 593-602. Clean
Díaz -Zorita, M., G.A. Duarte, and J.H. Grove, 2002: A review of no-till systems and soil management for sustainable crop production in the subhumid and semiarid Pampas of Argentina. Soil and Tillage Research, 65, pp. 1-18. Clean
Diekow, J., J. Mielniczuk, H. Knicker, C. Bayer, D.P. Dick, and I. Kögel-Knabner, I. 2005: Soil C and N stocks as affected by cropping systems and nitrogen fertilization in a southern Brazil Acrisol managed under no-tillage for 17 years. Soil and Tillage Research, 81, pp. 87-95. Clean
Díez, J.A., P. Hernaiz, M.J. Muñoz, A. de la Torre, A. Vallejo, 2004: Impact of pig slurry on soil properties, water salinization, nitrate leaching and crop yield in a four-year experiment in Central Spain. Soil Use and Management, 20, pp. 444-450. Clean
Dohme, F.A., A. Machmuller, A.Wasserfallen, and M. Kreuzer, 2001: Comparative efficiency of various fats rich in medium-chain fatty acids to suppress ruminal methanogenesis as measured with Rusitec. Canadian Journal of Animal Science, 80, pp. 473-482. Clean
Eidman, V.R., 2005: Agriculture as a producer of energy. In Agriculture as a Producer and Consumer of Energy, J.L. Outlaw, K.J. Collins, and J.A. Duffield (eds.), CABI Publishing, Cambridge, MA, pp.30-67. [NPR]
European Climate Change Programme, 2001: Agriculture. Mitigation potential of Greenhouse Gases in the Agricultural Sector. Working Group 7, Final report, COMM(2000)88. European Commission, Brussels, 17 pp. [NPR]
European Environment Agency, 2006: How much biomass can Europe use without harming the environment? EEA Briefing 2/2006. Available at: <http://reports.eea.europa.eu/briefing_2005_2/en> (accessed 26 March 2007). [NPR]
Ewert, F., M.D.A. Rounsevell, I. Reginster, M. Metzger, and R. Leemans, 2005: Future scenarios of European agricultural land use. I: estimating changes in crop productivity. Agriculture, Ecosystems and Environment, 107, pp. 101-116. [MoS]
Fawcett, A.A. and R.D. Sands. 2006: Non-CO2 Greenhouse Gases in the Second Generation Model. Multi-Greenhouse Gas Mitigation and Climate Policy, Energy Journal, Special Issue #3, pp 305-322. Available at: <http://www.iaee.org/en/publications/journal.aspx> accessed 26 March 2007. [MoS]
Fedoroff, N.V. and J.E. Cohen, 1999: Plants and population: is there time? Proceedings of the National Academy of Sciences USA, 96, pp. 5903-5907. Clean
Feng, W., G.X. Pan, S. Qiang, R.H. Li, and J.G. Wei, 2006: Influence of long-term fertilization on soil seed bank diversity of a paddy soil under rice/rape rotation. Biodiversity Science, 14 (6), pp. 461-469. [SRC]
Ferris, C.P., F.J. Gordon, D.C. Patterson, M.G. Porter, and T. Yan, 1999: The effect of genetic merit and concentrate proportion in the diet on nutrient utilization by lactating dairy cows. Journal of Agricultural Science, Cambridge 132, pp. 483-490. Clean
Fisher, M.J., I.M. Rao, M.A. Ayarza, C.E. Lascano, J.I. Sanz, R.J. Thomas, and R.R. Vera,1994: Carbon storage by introduced deep-rooted grasses in the South American savannas. Nature, 371, pp. 236-238. [JoC]
Foley, J.A., R. DeFries, G. Asner, C. Barford, G. Bonan, S.R. Carpenter, F.S. Chapin, M.T. Coe, G.C. Dailey, H.K. Gibbs, J.H. Helkowski, T. Holloway, E.A. Howard, C.J. Kucharik, C. Monfreda, J.A. Patz, I.C. Prentice, N. Ramankutty, and P.K. Snyder, 2005: Global consequences of land use. Science, 309, pp. 570-574. [JoC]
Follett, R.F., 2001: Organic carbon pools in grazing land soils. In The Potential of U.S. Grazing Lands to Sequester Carbon and Mitigate the Greenhouse Effect. R.F. Follett, J.M. Kimble, and R. Lal (eds.), Lewis Publishers, Boca Raton, Florida, pp. 65-86. [NPR]
Follett, R.F., J.M. Kimble, and R. Lal, 2001: The potential of U.S. grazing lands to sequester soil carbon. In The Potential of U.S. Grazing Lands to Sequester Carbon and Mitigate the Greenhouse Effect, R.F. Follett, J.M. Kimble, and R. Lal (eds.), Lewis Publishers, Boca Raton, Florida, pp. 401-430. [NPR]
Follett, R.F., S.R. Shafer, M.D. Jawson, and A.J. Franzluebbers, 2005: Research and implementation needs to mitigate greenhouse gas emissions from agriculture in the USA. Soil and Tillage Research, 83, pp. 159-166. Clean
Fujino, J., R. Nair, M. Kainuma, T. Masui, and Y. Matsuoka, 2006: Multi-gas mitigation analysis on stabilization scenarios using AIM global model. Multi-Greenhouse Gas Mitigation and Climate Policy, Energy Journal, Special Issue #3, pp 343-354. Available at: <http://www.iaee.org/en/publications/journal.aspx> (accessed 26 March 2007). [MoS, ARC]
Galloway, J.N., 2003: The global nitrogen cycle. Treatise on Geochemistry, 8, pp. 557-583. Clean
Galloway, J.N., F.J. Dentener, D.G. Capone, E.W. Boyer, R.W. Howarth, S.P. Seitzinger, G.P. Asner, C.C. Cleveland, P.A. Green, E.A. Holland, D.M. Karl, A.F. Michaels, J.H. Porter, A.R. Townsend, and C.J. Vörösmarty, 2004: Nitrogen cycles: past, present, and future. Biogeochemistry, 70, pp. 153-226. [MoS]
Galloway, J.N., J.D. Aber, J.W. Erisman, S.P. Seitzinger, R.W. Howarth, E.B. Cowling, and B.J. Cosby, 2003: The nitrogen cascade. Bioscience, 53, pp. 341-356. Clean
Gilland, B., 2002: World population and food supply. Can food production keep pace with population growth in the next half-century? Food Policy, 27, pp. 47-63. Clean
Gonzalez-Avalos, E. and L.G. Ruiz-Suarez, 2001: Methane emission factors from cattle in Mexico. Bioresource Technology, 80, pp. 63-71. Clean
Gregorich, E.G., P. Rochette, A.J. van den Bygaart, and D.A. Angers, 2005: Greenhouse gas contributions of agricultural soils and potential mitigation practices in Eastern Canada. Soil and Tillage Research, 83, pp. 53-72. Clean
Guo, L.B. and R.M. Gifford, 2002: Soil carbon stocks and land use change: a meta analysis. Global Change Biology, 8, pp. 345-360. Clean
Hansen, L.B., 2000: Consequences of selection for milk yield from a geneticist’s viewpoint. Journal of Dairy Science, 83, pp. 1145-1150. Clean
Helgason, B.L., H.H. Janzen, M.H. Chantigny, C.F. Drury, B.H. Ellert, E.G. Gregorich, Lemke, E. Pattey, P. Rochette, and C. Wagner-Riddle, 2005: Toward improved coefficients for predicting direct N2O emissions from soil in Canadian agroecosystems. Nutrient Cycling in Agroecosystems, 71, pp. 87-99. [MoS, SRC]
Henry, H.A.L., E.E. Cleland, C.B. Field, and P.M. Vitousek, 2005: Interactive effects of elevated CO2, N deposition and climate change on plant litter quality in a California annual grassland. Oecologia, 142, pp. 465-473. Clean
Hess, H.D., T.T. Tiemann, F. Noto, J.E. Carulla, and M. Kruezer, 2006: Strategic use of tannins as means to limit methane emission from ruminant livestock. In Greenhouse Gases and Animal Agriculture: An Update, C.R. Soliva, J. Takahashi, and M. Kreuzer (eds.). International Congress Series No. 1293, Elsevier, The Netherlands, pp. 164-167. [NPR]
Hindrichsen, I.K., H.R. Wettstein, A. Machmüller, and M. Kreuzer, 2006: Methane emission, nutrient degradation and nitrogen turnover in dairy cows and their slurry at different production scenarios with and without concentrate supplementation. Agriculture, Ecosystems and Environment, 113, pp. 150-161. Clean
Hoogwijk, M., A. Faaij, R. van den Broek, G. Berndes, D. Gielen, and W. Turkenburg, 2003: Exploration of the ranges of the global potential of biomass for energy. Biomass and Bioenergy, 25, pp. 119-133. [ARC]
Huston, M.A. and G. Marland, 2003: Carbon management and biodiversity. Journal of Environmental Management, 67, pp. 77-86. Clean
IPCC, 1996: Climate change 1995: The Science of Climate Change. Contribution of Working Group I to the Second Assessment Report of the Intergovernmental Panel on Climate Change (IPCC). Cambridge University Press, Cambridge. [NPR]
IPCC, 2001a: Climate Change 2001: The Scientific Basis. Contribution of Working Group I to the Third Assessment Report of the Intergovernmental Panel on Climate Change [Houghton, J.T., Y. Ding, D.J. Griggs, M. Noguer, P.J. van der Linden, X. Dai, K. Maskell, and C.A. Johnson, (eds.)], Cambridge University Press, 881 pp. [NPR]
IPCC, 2001b: Climate Change 2001: Mitigation: Contribution of Working Group III to the Third Assessment Report of the Intergovernmental Panel on Climate Change [Metz, B., O. Davidson, R. Swart, and J. Pan, (eds.)], Cambridge University Press, 752 pp. [NPR]
IPCC, 2007: Climate Change 2007: Impacts, Adaptation and Vulnerability. Contribution of Working Group II to the Fourth Assessment Report of the Intergovernmental Panel on Climate Change [Parry, M.L., O.F. Canziani, J.P Palutikof, P.J. van der Linden, C.E. Hanson (eds.)]. Cambridge University Press, Cambridge, United Kingdom and New York, NY, USA. [NPR, 2007]
Izaurralde, R.C. and C.W. Rice, 2006: Methods and tools for designing pilot soil carbon sequestration projects. In Carbon Sequestration in Soils of Latin America, Lal, R., C.C. Cerri, M. Bernoux, J. Etchvers, and C.E. Cerri (eds.), CRC Press, Boca Raton, pp. 457-476. [NPR, SRC]
Izaurralde, R.C., W.B. McGill, J.A. Robertson, N.G. Juma, and J.J. Thurston, 2001: Carbon balance of the Breton classical plots over half a century. Soil Science Society of America Journal, 65, pp. 431-441. Clean
Jackson, R.B., E.G. Jobbágy, R. Avissar, S. Baidya Roy, D. Barrett, C.W. Cook, K.A. Farley, D.C. le Maitre, B.A. McCarl, and B.C. Murray 2005: Trading water for carbon with biological carbon sequestration. Science, 310, pp. 1944-1947. [JoC, SRC]
Jensen, B., B.T. Christensen, 2004: Interactions between elevated CO2 and added N: effects on water use, biomass, and soil 15N uptake in wheat. Acta Agriculturae Scandinavica, Section B 54, pp. 175-184. Clean
Johnson, D.E., G.M. Ward, and J. Torrent, 1991: The environmental impact of bovine somatotropin (bST) use in dairy cattle. Journal of Dairy Science, 74S, 209 pp. Clean
Johnson, D.E., H.W. Phetteplace, and A.F. Seidl, 2002: Methane, nitrous oxide and carbon dioxide emissions from ruminant livestock production systems. In Greenhouse Gases and Animal Agriculture, J. Takahashi, and B.A. Young (eds.), Elsevier, Amsterdam, The Netherlands, pp. 77-85. [NPR]
Johnson, K.A. and D.E. Johnson, 1995: Methane emissions from cattle. Journal of Animal Science, 73, pp. 2483-2492. Clean
Jones, C.D., P.M. Cox, R.L.H. Essery, D.L. Roberts, and M.J. Woodage, 2003: Strong carbon cycle feedbacks in a climate model with interactive CO2 and sulphate aerosols. Geophysical Research Letters, 30, pp. 32.1-32.4. [MoS]
Jordan, E., D. Kenny, M. Hawkins, R. Malone, D.K. Lovett, and F.P. O’Mara, 2006b: Effect of refined soy oil or whole soybeans on methane output, intake and performance of young bulls. Journal of Animal Science, 84, pp. 2418-2425. [SRC]
Jordan, E., D.K. Lovett, F.J. Monahan, and F.P. O’Mara, 2006a: Effect of refined coconut oil or copra meal on methane output, intake and performance of beef heifers. Journal of Animal Science, 84, pp. 162-170. [SRC]
Jordan, E., D.K. Lovett, M. Hawkins, J. Callan, and F.P. O’Mara, 2006c: The effect of varying levels of coconut oil on intake, digestibility and methane output from continental cross beef heifers. Animal Science, 82, pp. 859-865. [SRC]
Junginger, M., A. Faaij, A. Koopmans, R. van den Broek, and W. Hulscher, 2001: Setting up fuel supply strategies for large scale bio-energy projects - a methodology for developing countries. Biomass & Bioenergy, 21, pp. 259-275. [ARC]
Kamra, D.N., N. Agarwal, and L.C. Chaudhary, 2006: Inhibition of ruminal methanogenesis by tropical plants containing secondary compounds. In Greenhouse Gases and Animal Agriculture: An Update, C.R. Soliva, J. Takahashi, and M. Kreuzer (eds.). International Congress Series No. 1293, Elsevier, The Netherlands, pp. 156-163. [NPR]
Kang, G.D., Z.C. Cai, and X.Z. Feng, 2002: Importance of water regime during the non-rice growing period in winter in regional variation of CH4 emissions from rice fields during following rice growing period in China. Nutrient Cycling in Agroecosystems, 64, pp. 95-100. [SRC]
Kasimir-Klemedtsson, A., L. Klemedtsson, K. Berglund, P. Martikainen, Silvola, and O. Oenema, 1997: Greenhouse gas emissions from farmed organic soils: a review. Soil Use and Management, 13, pp. 245-250. Clean
Kebreab, E., K. Clark, C. Wagner-Riddle, and J. France, 2006: Methane and nitrous oxide emissions from Canadian animal agriculture: A review. Canadian Journal of Animal Science, 86, pp. 135-158. Clean
Kemfert, C., T.P. Truong, and T. Bruckner. 2006: Economic impact assessment of climate change-A multi-gas investigation with WIAGEM-GTAPEL-ICM. Multi-Greenhouse Gas Mitigation and Climate Policy, Energy Journal, Special Issue #3. Available at: <http://www.iaee.org/en/publications/journal.aspx> accessed 26 March 2007. [NPR]
Kennedy, P.M. and L.P. Milligan, 1978: Effects of cold exposure on digestion, microbial synthesis and nitrogen transformation in sheep. British Journal of Nutrition, 39, pp. 105-117. Clean
Khalil, M.A.K. and M.J. Shearer, 2006. Decreasing emissions of methane from rice agriculture. In Greenhouse Gases and Animal Agriculture: An Update. Soliva, C.R., J. Takahashi, and M. Kreuzer (eds.), International Congress Series No. 1293, Elsevier, The Netherlands, pp. 33-41. [NPR]
Kim, M-K. and B.A. McCarl, 2005: Uncertainty Discounting for Land-Based Carbon Sequestration. Presented at International Policy Forum on Greenhouse Gas Management April 2005 Victoria, British Columbia. [NPR, SRC]
Koga, N., T. Sawamoto, and H. Tsuruta 2006: Life cycle inventory-based analysis of greenhouse gas emissions from arable land farming systems in Hokkaido, northern Japan. Soil Science and Plant Nutrition, 52, pp. 564-574. Clean
Korontzi, S., C.O. Justice, and R.J. Scholes, 2003: Influence of timing and spatial extent of savannah fires in southern Africa on atmospheric emissions. Journal of Arid Environments, 54, pp. 395-404. Clean
Kreuzer, M. and I.K. Hindrichsen, 2006: Methane mitigation in ruminants by dietary means: the role of their methane emission from manure. In Greenhouse Gases and Animal Agriculture: An Update. C.R. Soliva, J. Takahashi, and M. Kreuzer (eds.). International Congress Series No. 1293, Elsevier, The Netherlands, pp. 199-208. [NPR]
Külling, D.R., H. Menzi, F. Sutter, P. Lischer, and M. Kreuzer, 2003: Ammonia, nitrous oxide and methane emissions from differently stored dairy manure derived from grass- and hay-based rations. Nutrient Cycling in Agroecosystems, 65, pp. 13-22. Clean
Kumar, P. 2001: Valuation of Ecological services of Wetland Ecosystems: A Case Study of Yamuna Floodplains in the Corridors of Delhi. Mimeograph, Institute of Economic Growth, Delhi, India, 137 pp. [NPR, SRC]
Kurkalova, L., C.L. Kling, and J. Zhao, 2004: Multiple benefits of carbon-friendly agricultural practices: Empirical assessment of conservation tillage. Environmental Management, 33, pp. 519-527. Clean
Lal, R. and J.P. Bruce, 1999: The potential of world cropland soils to sequester C and mitigate the greenhouse effect. Environmental Science and Policy, 2, pp. 177-185. Clean
Lal, R., 1999: Soil management and restoration for C sequestration to mitigate the accelerated greenhouse effect. Progress in Environmental Science, 1, pp. 307-326. Clean
Lal, R., 2001a: World cropland soils as a source or sink for atmospheric carbon. Advances in Agronomy, 71, pp. 145-191. Clean
Lal, R., 2001b: Potential of desertification control to sequester carbon and mitigate the greenhouse effect. Climate Change, 15, pp. 35-72. Clean
Lal, R., 2002: Carbon sequestration in dry ecosystems of West Asia and North Africa. Land Degradation and Management, 13, pp. 45-59. Clean
Lal, R., 2003: Global potential of soil carbon sequestration to mitigate the greenhouse effect. Critical Reviews in Plant Sciences, 22, pp. 151-184. Clean
Lal, R., 2004b: Soil carbon sequestration to mitigate climate change. Geoderma, 123, pp. 1-22. Clean
Lal, R., 2004d: Carbon sequestration in soils of central Asia. Land Degradation and Development, 15, pp. 563-572. Clean
Lal, R., 2005: Soil carbon sequestration for sustaining agricultural production and improving the environment with particular reference to Brazil. Journal of Sustainable Agriculture, 26, pp. 23-42. Clean
Lal, R., R.F. Follett, and J.M. Kimble, 2003: Achieving soil carbon sequestration in the United States: a challenge to the policy makers. Soil Science, 168, pp. 827-845. Clean
Le Mer, J. and P. Roger, 2001: Production, oxidation, emission and consumption of methane by soils: a review. European Journal of Soil Biology, 37, pp. 25-50. Clean
Leng, R.A., 1991: Improving Ruminant Production and Reducing Methane Emissions from Ruminants by Strategic Supplementation. EPA Report no. 400/1-91/004, Environmental Protection Agency, Washington, D.C. [NPR]
Li, C., S. Frolking, and K. Butterbach-Bahl, 2005: Carbon sequestration in arable soils is likely to increase nitrous oxide emissions, offsetting reductions in climate radiative forcing. Climatic Change, 72, pp. 321-338. [JoC, MoS]
Liebig, M.A., J.A. Morgan, J.D. Reeder, B.H. Ellert, H.T. Gollany, and G.E. Schuman, 2005: Greenhouse gas contributions and mitigation potential of agricultural practices in northwestern USA and western Canada. Soil & Tillage Research, 83, pp. 25-52. Clean
Lila, Z.A., N. Mohammed, S. Kanda, T. Kamada, and H. Itabashi, 2003: Effect of sarsaponin on ruminal fermentation with particular reference to methane production in vitro. Journal of Dairy Science, 86, pp. 330-336. Clean
Long, S.P., E.A. Ainsworth, A.D.B. Leakey, J. Nosberger, and D.R. Ort, 2006: Food for thought: lower-than-expected crop yield stimulation with rising CO2 concentrations. Science, 312, pp. 1918-1921. [JoC]
Lovett, D., S. Lovell, L. Stack, J. Callan, M. Finlay, J. Connolly, and F.P. O’Mara, 2003: Effect of forage/concentrate ratio and dietary coconut oil level on methane output and performance of finishing beef heifers. Livestock Production Science, 84, pp. 135-146. [SRC]
Lovett, D.K. and F.P. O’Mara, 2002: Estimation of enteric methane emissions originating from the national livestock beef herd: a review of the IPCC default emission factors. Tearmann, 2, pp. 77-83. [MoS, SRC]
Lovett, D.K., L. Shalloo, P. Dillon, and F.P. O’Mara, 2006: A systems approach to quantify greenhouse gas fluxes from pastoral dairy production as affected by management regime. Agricultural Systems, 88, pp. 156-179. [SRC]
Machado, P.L.O.A. and C.A. Silva, 2001: Soil management under no-tillage systems in the tropics with special reference to Brazil. Nutrient Cycling in Agroecosystems, 61, pp. 119-130. Clean
Machado, P.L.O.A. and P.L. Freitas 2004: No-till farming in Brazil and its impact on food security and environmental quality. In Sustainable Agriculture and the International Rice-Wheat System, R. Lal, P.R. Hobbs, N. Uphoff, D.O. Hansen (eds.), Marcel Dekker, New York, pp. 291-310. [NPR]
Machmüller, A., C.R. Soliva, and M. Kreuzer, 2003: Methane-suppressing effect of myristic acid in sheep as affected by dietary calcium and forage proportion. British Journal of Nutrition, 90, pp. 529-540. Clean
Machmülller, A., D.A. Ossowski, and M. Kreuzer, 2000: Comparative evaluation of the effects of coconut oil, oilseeds and crystalline fat on methane release, digestion and energy balance in lambs. Animal Feed Science and Technology, 85, pp. 41-60. Clean
Madari, B., P.L.O.A. Machado, E. Torres, A.G. Andrade, and L.I.O. Valencia, 2005: No tillage and crop rotation effects on soil aggregation and organic carbon in a Fhodic Ferralsol from southern Brazil. Soil and Tillage Research, 80, pp. 185-200. Clean
Manne, A.S. and R.G. Richels, 2004: A multi-gas approach to climate policy. In The Global Carbon Cycle. Integrating Humans, Climate, and the Natural World, C.B. Field and M.R. Raupach (eds.). SCOPE 62, Island Press, Washington DC, pp. 439-452. [NPR, ARC]
Marland, G., R.A. Pielke Jr., M. Apps, R. Avissar, R.A. Betts, K.J. Davis, P.C. Frumhoff, S.T. Jackson, L.A. Joyce, P. Kauppi, J. Katzenberger, K.G. MacDicken, R.P. Neilson, J.O. Niles, D.S. Niyogi, R.J. Norby, N. Pena, N. Sampson, and Y. Xue, 2003a: The climatic impacts of land surface change and carbon management, and the implications for climate-change mitigation policy. Climate Policy, 3, pp. 149-157. [JoC, ARC]
McCrabb, G.C., 2001: Nutritional options for abatement of methane emissions from beef and dairy systems in Australia. In Greenhouse Gases and Animal Agriculture, J. Takahashi and B.A. Young (eds.), Elsevier, Amsterdam, pp 115-124. [NPR]
McCrabb, G.J., M. Kurihara, and R.A. Hunter, 1998: The effect of finishing strategy of lifetime methane production for beef cattle in northern Australia. Proceedings of the Nutrition Society of Australia, 22, 55 pp. Clean
McGinn, S.M., K.A. Beauchemin, T. Coates, and D. Colombatto, 2004: Methane emissions from beef cattle: effects of monensin, sunflower oil, enzymes, yeast, and fumaric acid. Journal of Animal Science, 82, pp. 3346-3356. Clean
McSwiney, C.P. and G.P. Robertson, 2005: Nonlinear response of N2O flux to incremental fertilizer addition in a continuous maize (Zea mays L.) cropping system. Global Change Biology, 11, pp. 1712-1719. Clean
Miglior, F., B.L. Muir, and B.J. Van Doormaal, 2005: Selection indices in Holstein cattle of various countries. Journal of Dairy Science, 88, pp. 1255-1263. Clean
Millennium Ecosystem Assessment, 2005: Ecosystems and Human Well-Being: Current State and Trends. Findings of the Condition and Trends Working Group. Millennium Ecosystem Assessment Series, Island press, Washington D.C., 815 pp. [NPR]
Mills, J.A.N., E. Kebreab, C.M. Yates, L.A. Crompton, S.B. Cammell, M.S. Dhanoa, R.E. Agnew, and J. France, 2003: Alternative approaches to predicting methane emissions from dairy cows. Journal of Animal Science, 81, pp. 3141-3150. [MoS]
Moe, P.W. and H.F. Tyrrell, 1979: Methane production in dairy cows. Journal of Dairy Science, 62, pp. 1583-1586. Clean
Monteny, G.-J., A. Bannink, and D. Chadwick, 2006: Greenhouse gas abatement strategies for animal husbandry. Agriculture, Ecosystems and Environment, 112, pp. 163-170. Clean
Monteny, G.J., C.M. Groenestein, and M.A. Hilhorst, 2001: Interactions and coupling between emissions of methane and nitrous oxide from animal husbandry. Nutrient Cycling in Agroecosystems, 60, pp. 123-132. Clean
Mooney, S., J.M. Antle, S.M. Capalbo, and K. Paustian, 2004: Influence of project scale on the costs of measuring soil C sequestration. Environmental Management, 33(S1), pp. S252-S263. Clean
Mosier, A. and C. Kroeze, 2000: Potential impact on the global atmospheric N2O budget of the increased nitrogen input required to meet future global food demands. Chemosphere-Global Change Science, 2, pp. 465-473. [MoS]
Mosier, A.R., 2001: Exchange of gaseous nitrogen compounds between agricultural systems and the atmosphere. Plant and Soil, 228, pp. 17-27. Clean
Mosier, A.R., 2002: Environmental challenges associated with needed increases in global nitrogen fixation. Nutrient Cycling in Agroecosystems, 63, pp. 101-116. Clean
Mosier, A.R., A.D. Halvorson, G.A. Peterson, G.P. Robertson, and L. Sherrod, 2005: Measurement of net global warming potential in three agroecosystems. Nutrient Cycling in Agroecosystems, 72, pp. 67-76. Clean
Murray, R.M., A.M. Bryant, and R.A. Leng, 1976: Rate of production of methane in the rumen and the large intestine of sheep. British Journal of Nutrition, 36, pp. 1-14. Clean
Mutuo, P.K., G. Cadisch, A. Albrecht, C.A. Palm, and L. Verchot, 2005: Potential of agroforestry for carbon sequestration and mitigation of greenhouse gas emissions from soils in the tropics. Nutrient Cycling in Agroecosystems, 71, pp. 43-54. Clean
Newbold, C.J. and L.M. Rode, 2006: Dietary additives to control methanogenesis in the rumen. In Greenhouse Gases and Animal Agriculture: An Update. C.R. Soliva, J. Takahashi, and M. Kreuzer (eds.), International Congress Series No. 1293, Elsevier, The Netherlands, pp. 138-147. [NPR]
Newbold, C.J., J.O. Ouda, S. López, N. Nelson, H. Omed, R.J. Wallace, and A.R. Moss, 2002: Propionate precursors as possible alternative electron acceptors to methane in ruminal fermentation. In Greenhouse Gases and Animal Agriculture. J. Takahashi and B.A. Young (eds.), Elsevier, Amsterdam, pp. 151-154. [NPR]
Newbold, C.J., S. López, N. Nelson, J.O. Ouda, R.J. Wallace, and A.R. Moss, 2005: Proprionate precursors and other metabolic intermediates as possible alternative electron acceptors to methanogenesis in ruminal fermentation in vitro. British Journal of Nutrition, 94, pp. 27-35. Clean
Norby, R.J., M.F. Cotrufo, P. Ineson, E.G. O’Neill, and J.G. Canadell, 2001: Elevated CO2, litter chemistry, and decomposition: a synthesis. Oecologia, 127, pp. 153-165. Clean
Oelbermann, M., R.P. Voroney, and A.M. Gordon, 2004: Carbon sequestration in tropical and temperate agroforestry systems: a review with examples from Costa Rica and southern Canada. Agriculture Ecosystems and Environment, 104, pp. 359-377. Clean
Oenema, O., N. Wrage, G.L. Velthof, J.W. van Groenigen, J. Dolfing, and P.J. Kuikman, 2005: Trends in global nitrous oxide emissions from animal production systems. Nutrient Cycling in Agroecosystems, 72, pp. 51-65. Clean
Ogle, S.M. and K. Paustian, 2005: Soil organic carbon as an indicator of environmental quality at the national scale: monitoring methods and policy relevance. Canadian Journal of Soil Science, 8, pp. 531-540. [SRC]
Ogle, S.M., F.J. Breidt, and K. Paustian, 2005: Agricultural management impacts on soil organic carbon storage under moist and dry climatic conditions of temperate and tropical regions. Biogeochemistry, 72, pp. 87-121. [SRC]
Ogle, S.M., F.J. Breidt, M.D. Eve, and K. Paustian, 2003: Uncertainty in estimating land use and management impacts on soil organic storage for US agricultural lands between 1982 and 1997. Global Change Biology, 9, pp. 1521-1542. [MoS, SRC]
Ogle, S.M., R.T. Conant, and K. Paustian, 2004: Deriving grassland management factors for a carbon accounting approach developed by the Intergovernmental Panel on Climate Change. Environmental Management, 33, pp. 474-484. [SRC]
Olesen, J.E., K. Schelde, A. Weiske, M.R. Weisbjerg, W.A.H. Asman, and J. Djurhuus, 2006: Modelling greenhouse gas emissions from European conventional and organic dairy farms. Agriculture, Ecosystems and Environment, 112, pp. 207-220. [MoS]
Olsson, L. and J. Ardö, 2002: Soil carbon sequestration in degraded semiarid agro-ecosystems - perils and potentials. Ambio, 31, pp. 471-477. Clean
Pan, G.X., P. Zhou, X.H. Zhang, L.Q. Li, J.F. Zheng, D.S. Qiu, and Q.H. Chu, 2006: Effect of different fertilization practices on crop C assimilation and soil C sequestration: a case of a paddy under a long-term fertilization trial from the Tai Lake region, China. Acta Ecologica Sinica, 26(11), pp. 3704-3710. [SRC]
Patra, A.K., D.N. Kamra, and N. Agarwal, 2006: Effect of spices on rumen fermentation, methanogenesis and protozoa counts in in vitro gas production test. In Greenhouse Gases and Animal Agriculture: An Update, C.R. Soliva, J. Takahashi, and M. Kreuzer (eds.), International Congress Series No. 1293, Elsevier, The Netherlands, pp. 176-179. [NPR]
Pattey, E., M.K. Trzcinski, and R.L. Desjardins, 2005: Quantifying the reduction of greenhouse gas emissions as a result of composting dairy and beef cattle manure. Nutrient Cycling in Agroecosystems, 72, pp. 173-187. Clean
Paul, E.A., S.J. Morris, J. Six, K. Paustian, and E.G. Gregorich, 2003: Interpretation of soil carbon and nitrogen dynamics in agricultural and afforested soils. Soil Science Society of America Journal, 67, pp. 1620-1628. Clean
Paustian, K., B.A. Babcock, J. Hatfield, R. Lal, B.A. McCarl, S. McLaughlin, A. Mosier, C. Rice, G.P. Robertson, N.J. Rosenberg, C. Rosenzweig, W.H. Schlesinger, and D. Zilberman, 2004: Agricultural Mitigation of Greenhouse Gases: Science and Policy Options. CAST (Council on Agricultural Science and Technology) Report, R141 2004, ISBN 1-887383-26-3, 120 pp. [SRC]
Pérez-Ramírez, J., F. Kapteijn, K. Schöffel, and J.A. Moulijn, 2003: Formation and control of N2O in nitric acid production: Where do we stand today? Applied Catalysis B: Environmental, 44, pp. 117-151. [NPR]
Phetteplace, H.W., D.E. Johnson, and A.F. Seidl, 2001: Greenhouse gas emissions from simulated beef and dairy livestock systems in the United States. Nutrient Cycling in Agroecosystems, 60, 9-102. [MoS]
Pinares-Patiño, C.S., M.J. Ulyatt, G.C. Waghorn, C.W. Holmes, T.N. Barry, K.R. Lassey, and D.E. Johnson, 2003: Methane emission by alpaca and sheep fed on lucerne hay or grazed on pastures of perennial ryegrass/white clover or birdsfoot trefoil. Journal of Agricultural Science, 140, pp. 215-226. Clean
Reay, D.S., K.A. Smith, and A.C. Edwards, 2003: Nitrous oxide emission from agricultural drainage waters. Global Change Biology, 9, pp. 195-203. Clean
Reeder, J.D., G.E. Schuman, J.A. Morgan, and D.R. Lecain, 2004: Response of organic and inorganic carbon and nitrogen to long-term grazing of the shortgrass steppe. Environmental Management, 33, pp. 485-495. Clean
Reilly, J.M., F. Tubiello, B.A. McCarl, and J. Melillo, 2001: Climate change and agriculture in the United States. In Climate Change Impacts on the United States: US National Assessment of the Potential Consequences of Climate Variability and Change: Foundation, Cambridge University Press, Cambridge, Chapter 13, pp 379-403. [NPR, SRC]
Rice, C.W. and C.E. Owensby, 2001: Effects of fire and grazing on soil carbon in rangelands. In The Potential of U.S. Grazing Lands to Sequester Carbon and Mitigate the Greenhouse Effect. R. Follet, J.M. Kimble, and R. Lal (eds.), Lewis Publishers, Boca Raton, Florida, pp. 323-342. [NPR, SRC]
Robertson, G.P. and P.R. Grace, 2004: Greenhouse gas fluxes in tropical and temperate agriculture: The need for a full-cost accounting of global warming potentials. Environment, Development and Sustainability, 6, pp. 51-63. Clean
Robertson, G.P., 2004: Abatement of nitrous oxide, methane and other non-CO2 greenhouse gases: the need for a systems approach. In The global carbon cycle. Integrating Humans, Climate, and the Natural World, C.B. Field, and M.R. Raupach (eds.). SCOPE 62, Island Press, Washington D.C., pp. 493-506. [NPR]
Robertson, G.P., E.A. Paul, and R.R. Harwood, 2000: Greenhouse gases in intensive agriculture: Contributions of individual gases to the radiative forcing of the atmosphere. Science, 289, pp. 1922-1925. [JoC, MoS]
Robertson, L.J. and G.C. Waghorn, 2002: Dairy industry perspectives on methane emissions and production from cattle fed pasture or total mixed rations in New Zealand. Proceedings of the New Zealand Society of Animal Production, 62, pp. 213-218. Clean
Rockström, J., 2003: Water for food and nature in drought-prone tropics: vapour shift in rain-fed agriculture. Philosophical Transactions of the Royal Society of London B, 358, pp. 1997-2009. Clean
R. Moreira, R. Notstaller, P. Odell, M. Taylor, 2000: Energy Resources. In World Energy Assessment of the United Nations, J. Goldemberg et al. (eds.), UNDP, UNDESA/WEC. UNDP, New York, Chapter 5, pp. 135-171. [NPR]
Romanenkov, V., I. Romanenko, O. Sirotenko, and L. Shevtsova, 2004: Soil carbon sequestration strategy as a component of integrated agricultural sustainability policy under climate change. In Proceedings of Russian National Workshop on Research Related to the IHDP on Global Environmental Change, November 10-12, 2004, IHDP, Moscow, Russia, pp. 180-189. [NPR, SRC]
Rose, S., H. Ahammad, B. Eickhout, B. Fisher, A. Kurosawa, S. Rao, K. Riahi, and D. van Vuuren, 2007. Land in Climate Stabilization Modeling. Energy Modeling Forum Report, Stanford University < http://www.stanford.edu/group/EMF/projects/group21/Landuse.pdf > accessed 26 March 2007. [NPR, MoS, SRC, 2007]
Rosegrant, M., M.S. Paisner, and S. Meijer, 2001: Long-Term Prospects for Agriculture and the Resource Base. The World Bank Rural Development Family. Rural Development Strategy Background Paper #1. The World Bank, Washington. [NPR]
Rounsevell, M.D.A, I. Reginster, M.B. Araújo, T.R. Carter, N. Dendoncker, F. Ewert, J.I. House, S. Kankaanpää, R. Leemans, M.J. Metzger, C. Schmit, P. Smith, and G. Tuck, 2006: A coherent set of future land use change scenarios for Europe. Agriculture Ecosystems and Environment, 114, pp. 57-68. [MoS, SRC]
Roy, R.N., R.V. Misra, and A. Montanez, 2002: Decreasing reliance on mineral nitrogen - yet more food. Ambio, 31, pp. 177-183. Clean
Rumpler, W.V., D.E. Johnson, and D.B. Bates, 1986: The effect of high dietary cation concentrations on methanogenesis by steers fed with or without ionophores. Journal of Animal Science, 62, pp. 1737-1741. Clean
Sands, R.D. and B.A. McCarl, 2005: Competitiveness of terrestrial greenhouse gas offsets: are they a bridge to the future? In Abstracts of USDA Symposium on Greenhouse Gases and Carbon Sequestration in Agriculture and Forestry, March 22-24, USDA, Baltimore, Maryland. [NPR, SRC]
Schils, R.L.M., A. Verhagen, H.F.M. Aarts, and L.B.J. Sebek, 2005: A farm level approach to define successful mitigation strategies for GHG emissions from ruminant livestock systems. Nutrient Cycling in Agroecosystems, 71, pp. 163-175. Clean
Schmidely, P., 1993: Quantitative review on the use of anabolic hormones in ruminants for meat production. I. Animal performance. Annales de Zootechie, 42, pp. 333-359. Clean
Schnabel, R.R., A.J. Franzluebbers, W.L. Stout, M.A. Sanderson, and J.A. Stuedemann, 2001: The effects of pasture management practices. In The Potential of U.S. Grazing Lands to Sequester Carbon and Mitigate the Greenhouse Effect R.F. Follett, J.M. Kimble, and R. Lal (eds.), Lewis Publishers, Boca Raton, Florida, pp. 291-322. [NPR]
Scholes, R.J. and M.R. van der Merwe, 1996: Sequestration of carbon in savannas and woodlands. The Environmental Professional, 18, pp. 96-103. Clean
Schuman, G.E., J.E. Herrick, and H.H. Janzen, 2001: The dynamics of soil carbon in rangelands. In The Potential of U.S. Grazing Lands to Sequester Carbon and Mitigate the Greenhouse Effect, R.F. Follett, J.M. Kimble, and R. Lal (eds.), Lewis Publishers, Boca Raton, Florida, pp. 267-290. [NPR, SRC]
Sheehan, J., A. Aden, K. Paustian, K. Killian, J. Brenner, M. Walsh, and R. Nelson, 2004: Energy and environmental aspects of using corn stover for fuel ethanol. Journal of Industrial Ecology, 7, pp. 117-146. Clean
Sisti, C.P.J., H.P. Santos, R. Kohhann, B.J.R. Alves, S. Urquiaga, and R.M. Boddey, 2004: Change in carbon and nitrogen stocks in soil under 13 years of conventional or zero tillage in southern Brazil. Soil and Tillage Research, 76, pp. 39-58. Clean
Six, J., S.M. Ogle, F.J. Breidt, R.T. Conant, A.R. Mosier, and K. Paustian, 2004: The potential to mitigate global warming with no-tillage management is only realized when practised in the long term. Global Change Biology, 10, pp.155-160. [SRC]
Smeets, E.M.W., A.P.C. Faaij, I.M. Lewandowski, and W.C. Turkenburg, 2007: A bottom up quickscan and review of global bio-energy potentials to 2050. Progress in Energy and Combustion Science, 33, pp. 56-106. [ARC, 2007]
Smith, J.U., P. Smith, M. Wattenbach, S. Zaehle, R. Hiederer, R.J.A. Jones, L. Montanarella, M.D.A. Rounsevell, I. Reginster, and F. Ewert, 2005b: Projected changes in mineral soil carbon of European croplands and grasslands, 1990-2080. Global Change Biology, 11, pp. 2141-2152. [SRC]
Smith, K.A. and F. Conen, 2004: Impacts of land management on fluxes of trace greenhouse gases. Soil Use and Management, 20, pp. 255-263. Clean
Smith, P., 2004b: Engineered biological sinks on land. In The Global Carbon Cycle. Integrating humans, climate, and the natural world, C.B. Field and M.R. Raupach (eds.). SCOPE 62, Island Press, Washington D.C., pp. 479-491. [NPR, SRC]
Smith, P., D. Martino, Z. Cai, D. Gwary, H.H. Janzen, P. Kumar, B. McCarl, S. Ogle, F. O’Mara, C. Rice, R.J. Scholes, O. Sirotenko, M. Howden, T. McAllister, G. Pan, V. Romanenkov, U. Schneider, S. Towprayoon, M. Wattenbach, and J.U. Smith, 2007a: Greenhouse gas mitigation in agriculture. Philosophical Transactions of the Royal Society, B., 363. doi:10.1098/rstb.2007.2184. [NPR, SRC, 2007]
Smith, P., D. Martino, Z. Cai, D. Gwary, H.H. Janzen, P. Kumar, B.A. McCarl, S.M. Ogle, F. O’Mara, C. Rice, R.J. Scholes, O. Sirotenko, M. Howden, T. McAllister, G. Pan, V. Romanenkov, U.A. Schneider, and S. Towprayoon, 2007b: Policy and technological constraints to implementation of greenhouse gas mitigation options in agriculture. Agriculture, Ecosystems and Environment, 118, pp. 6-28. [SRC, 2007]
Smith, P., D.S. Powlson, J.U. Smith, P.D. Falloon, and K. Coleman, 2000: Meeting Europe’s climate change commitments: quantitative estimates of the potential for carbon mitigation by agriculture. Global Change Biology, 6, pp. 525-539. [MoS, SRC]
Smith, P., D.S. Powlson, M.J. Glendining, and J.U. Smith, 1997: Potential for carbon sequestration in European soils: preliminary estimates for five scenarios using results from long-term experiments. Global Change Biology, 3, pp. 67-79. [MoS, SRC]
Smith, P., K.W. Goulding, K.A. Smith, D.S. Powlson, J.U. Smith, P.D. Falloon, and K. Coleman, 2001: Enhancing the carbon sink in European agricultural soils: Including trace gas fluxes in estimates of carbon mitigation potential. Nutrient Cycling in Agroecosystems, 60, pp. 237-252. [MoS, SRC]
Smith, P., O. Andrén, T. Karlsson, P. Perälä, K. Regina, M. Rounsevell, and B. Van Wesemael, 2005a: Carbon sequestration potential in European croplands has been overestimated. Global Change Biology, 11, pp. 2153-2163. [MoS, SRC]
Smith, S.J. and T.M.L. Wigley, 2006: Multi-Gas Forcing Stabilization with the MiniCAM. Multi-Greenhouse Gas Mitigation and Climate Policy, Energy Journal, Special Issue #3. Available at: <http://www.iaee.org/en/publications/journal.aspx> accessed 26 March 2007. [NPR, MoS]
Soussana, J.-F., P. Loiseau, N. Viuchard, E. Ceschia, J. Balesdent, T. Chevallier, and D. Arrouays, 2004: Carbon cycling and sequestration opportunities in temperate grasslands. Soil Use and Management, 20, pp. 219-230. Clean
Spatari, S., Y. Zhang, and H.L. Maclean, 2005: Life cycle assessment of switchgrass- and corn stover-derived ethanol-fueled automobiles. Environmental Science and Technology, 39, pp. 9750-9758. Clean
Strengers, B., R. Leemans, B. Eickhout, B. de Vries, and L. Bouwman, 2004: The land-use projections and resulting emissions in the IPCC SRES scenarios as simulated by the IMAGE 2.2 model. GeoJournal, 61, pp. 381-393. [MoS, ARC]
Tate, K.R., D.J. Ross, N.A. Scott, N.J. Rodda, J.A. Townsend, and G.C. Arnold, 2006: Post-harvest patterns of carbon dioxide production, methane uptake and nitrous oxide production in a Pinus radiata D. Don plantation. Forest Ecology and Management, 228, pp. 40-50. Clean
Tejo, P., 2004: Public Policies and Agriculture in Latin America During the 2000’s. CEPAL (Comisión Económica para América Latina), Serie Desarrollo Productivo 152 (in Spanish), Santiago, Chile, 74 pp. [NPR]
Tilman, D., J. Fargione, B. Wolff, C. D’Antonio, A. Dobson, R. Howarth, D. Schindler, W.H. Schlesinger, D. Simberloff, and D. Swackhamer, 2001: Forecasting agriculturally driven global environmental change. Science, 292, pp. 281-284. [JoC, MoS]
Torbert, H.A., S.A. Prior, H.H. Hogers, and C.W. Wood, 2000: Review of elevated atmospheric CO2 effects on agro-ecosystems: residue decomposition processes and soil C storage. Plant and Soil, 224, pp. 59-73. Clean
Totten, M., S.I. Pandya, and T. Janson-Smith, 2003: Biodiversity, climate, and the Kyoto Protocol: risks and opportunities. Frontiers in Ecology and Environment, 1, pp. 262-270. Clean
Unkovich, M., 2003: Water use, competition, and crop production in low rainfall, alley farming systems of south-eastern Australia. Australian Journal of Agricultural Research, 54, pp. 751-762. Clean
USCCSP, 2006: Scenarios of Greenhouse Gas Emissions and Atmospheric Concentrations. Report by the U.S. Climate Change Science Program and approved by the Climate Change Science Program Product Development Advisory Committee. Clarke, L., J. Edmonds, J. Jacoby, H. Pitcher, J. Reilly, R. Richels (eds.), U.S. Climate Change Science Program. [NPR]
US-EPA, 2005: Greenhouse Gas Mitigation Potential in U.S. Forestry and Agriculture. United States Environmental Protection Agency, EPA 430-R-05-006, November 2005. Washington, D.C., <http://epa.gov/sequestration/pdf/ghg_part2.pdf> accessed 26 March 2007. [NPR]
US-EPA, 2006a: Global Anthropogenic Non-CO2 Greenhouse Gas Emissions: 19902020. United States Environmental Protection Agency, EPA 430-R-06-003, June 2006. Washington, D.C., < http://www.epa.gov/nonco2/econ-inv/downloads/GlobalAnthroEmissionsReport.pdf > accessed 26 March 2007. [NPR]
US-EPA, 2006b: Global Mitigation of Non-CO2 Greenhouse Gases. United States Environmental Protection Agency, EPA 430-R-06-005, Washington, D.C. < http://www.epa.gov/nonco2/econ-inv/downloads/GlobalMitigationFullReport.pdf > accessed 26 March 2007. [NPR]
Van Groenigen, K.J., A. Gorissen, J. Six, D. Harris, P.J. Kuikman, J.W. van Groenigen, and C. van Kessel, 2005: Decomposition of 14C-labeled roots in a pasture soil exposed to 10 years of elevated CO2. Soil Biology and Biochemistry, 37, pp. 497-506. Clean
Van Nevel, C.J. and D.I. Demeyer, 1995: Lipolysis and biohydrogenation of soybean oil in the rumen in vitro: Inhibition by antimicrobials. Journal of Dairy Science, 78, pp. 2797-2806. Clean
Van Nevel, C.J. and D.I. Demeyer, 1996: Influence of antibiotics and a deaminase inhibitor on volatile fatty acids and methane production from detergent washed hay and soluble starch by rumen microbes in vitro. Animal Feed Science and Technology, 37, pp. 21-31. Clean
Van Wilgen, B.W., N. Govender, H.C. Biggs, D. Ntsala, and X.N. Funda, 2004: Response of savanna fire regimes to changing fire-management policies in a large African National Park. Conservation Biology, 18, pp. 1533-1540. Clean
Venkataraman, C., G. Habib, A. Eiguren-Fernandez, A.H. Miguel, and S.K. Friedlander, 2005: Residential biofuels in south Asia: carbonaceous aerosol emissions and climate impacts. Science, 307, pp. 1454-1456. [JoC]
Viner, D., M. Sayer, M. Uyarra, and N. Hodgson, 2006: Climate Change and the European Countryside: Impacts on Land Management and Response Strategies. Report prepared for the Country Land and Business Association, UK. Publ., CLA, UK, 180 pp. [NPR]
Waghorn, G.C., M.H. Tavendale, and D.R. Woodfield, 2002: Methanogenesis from forages fed to sheep. Proceedings of New Zealand Society of Animal Production, 64, pp. 161-171. Clean
Wallace, R.J., T.A. Wood, A. Rowe, J. Price, D.R. Yanez, S.P. Williams, and C.J. Newbold, 2006: Encapsulated fumaric acid as a means of decreasing ruminal methane emissions. In Greenhouse Gases and Animal Agriculture: An Update. Soliva, C.R., J. Takahashi and M. Kreuzer (eds.), International Congress Series No. 1293, Elsevier, The Netherlands, pp. 148-151. [NPR]
Wander, M. and T. Nissen, 2004: Value of soil organic carbon in agricultural lands. Mitigation and Adaptation Strategies for Global Change, 9, pp. 417-431. Clean
Wang, B., H. Neue, and H. Samonte, 1997: Effect of cultivar difference on methane emissions. Agriculture, Ecosystems and Environment, 62, pp. 31-40. Clean
Wang, M.X. and X.J. Shangguan, 1996: CH4 emission from various rice fields in PR China. Theoretical and Applied Climatology, 55, pp. 129-138. Clean
Wassmann, R., R.S. Lantin, H.U. Neue, L.V. Buendia, T.M. Corton, and Y. Lu, 2000: Characterization of methane emissions from rice fields in Asia. III. Mitigation options and future research needs. Nutrient Cycling Agroecosystems, 58, pp. 23-36. [MoS]
West, T.O. and G. Marland, 2003: Net carbon flux from agriculture: Carbon emissions, carbon sequestration, crop yield, and land-use change. Biogeochemistry, 63, pp. 73-83. Clean
West, T.O. and W.M. Post, 2002: Soil organic carbon sequestration rates by tillage and crop rotation: A global data analysis. Soil Science Society of America Journal, 66, pp. 1930-1946. Clean
Wolin, E.A., R.S. Wolf, and M.J. Wolin, 1964: Microbial formation of methane. Journal of Bacteriology, 87, pp. 993-998. Clean
Woodward, S.L., G.C. Waghorn, M.J. Ulyatt, and K.R. Lassey, 2001: Early indications that feeding Lotus will reduce methane emissions in ruminants. Proceedings of the New Zealand Society of Animal Production, 61, pp. 23-26. Clean
Wright, A.D.G., P. Kennedy, C.J. O’Neill, A.F. Troovey, S. Popovski, S.M. Rea, C.L. Pimm, and L. Klein. 2004: Reducing methane emissions in sheep by immunization against rumen methanogens. Vaccine, 22, pp. 3976-3985. Clean
Xiang, C.G, P.J. Zhang, G.X. Pan, D.S. Qiu, and Q.H. Chu, 2006: Changes in diversity, protein content, and amino acid composition of earthworms from a paddy soil under different long-term fertilizations in the Tai Lake Region, China. Acta Ecologica Sinica, 26(6), pp. 1667-1674. [SRC]
Xu, H., Z.C. Cai, and H. Tsuruta, 2003: Soil moisture between rice-growing seasons affects methane emission, production, and oxidation. Soil Science Society of America Journal, 67, pp. 1147-1157. [SRC]
Xu, H., Z.C. Cai, Z.J. Jia, and H. Tsuruta, 2000: Effect of land management in winter crop season on CH4 emission during the following flooded and rice-growing period. Nutrient Cycling in Agroecosystems, 58, pp. 327-332. [SRC]
Xu, S., X. Hao, K. Stanford, T. McAllister, F.J. Larney, and J. Wang, 2007: Greenhouse gas emissions during co-composting of cattle mortalities with manure. Nutrient Cycling in Agroecosystems, 78, 177-187. [SRC, 2007]
Yagi, K., H. Tsuruta, and K. Minami, 1997: Possible options for mitigating methane emission from rice cultivation. Nutrient Cycling in Agroecosystems, 49, pp. 213-220. Clean
Yan, T., R.E. Agnew, F.J. Gordon, and M.G. Porter, 2000: Prediction of methane energy output in dairy and beef cattle offered grass silage-based diets. Livestock Production Science, 64, pp. 253-263. [MoS]
Yan, X., T. Ohara, and H. Akimoto, 2003: Development of region-specific emission factors and estimation of methane emission from rice field in East, Southeast and South Asian countries. Global Change Biology, 9, pp. 237-254. [MoS]
Journal of Concern A Journal which has published articles by one or more PoCs (Person of Concern)
Model or Simulation Reference appears to be a model or simulation, not observation or experiment.
Non Peer Reviewed Reference has no Journal or no Volume or no Pages or it has Editors.
Self Reference Concern Author of a chapter containing references to own work.
Paper authored or co-authored by person who is also in list of Authors of another chapter.
Paper dated 2007, when IPCC policy stated cutoff was December 2005
The reference was probably peer reviewed.
NOTE: In the Summary of Reviewer Comments,
Accepted includes only those responses that were unambiguously Accepted.
There are other categories of responses that we have not yet quantified
due to inconsistencies of usage.
|Reviewer||Total Comments||Accepted||IPCC Roles||Papers|
|Government of Australia||60||44||0||1|
|Government of Germany||52||32||0||0|
|Government of U.S. Department of State||51||41||0||0|
|Government of Spain||23||13||0||0|
|Government of Pakistan||20||19||0||0|
|Government of Sweden||19||3||0||0|
|Government of Norwegian Pollution Control Authority||17||16||0||0|
|Government of UK||14||10||0||0|
|Government of China Meteorological Administration||14||7||0||0|
|Government of Argentina||13||6||0||0|
|Government of Switzerland||9||8||0||0|
|Government of European Community / European Commission||7||7||0||0|
|Government of New Zealand||6||3||0||0|
|Government of Japan||4||3||0||2|
|Government of France||1||0||0||0|
|Reviewer Type||Total Comments||Accepted||% Accepted|