Beneficial management practices and mitigation of greenhouse gas emissions in the agriculture of the Canadian Prairie: a review
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Climate change is one of the main global issues of modern time. Ever increasing demand for food/feed and the need for higher environmental standards require shaping of the agricultural activities toward ecological and more sustainable efficient systems. One of the principal ways of attaining higher productivity and environmental standards is identification and adoption of beneficial management practices (BMP) by reviewing the conventional agricultural activities. The BMP are agricultural practices that promote sustainable land stewardship and maintain/increase profitability of farms. The BMP are from both crop and animal production systems and tradeoffs between the two systems could provide several opportunities in reducing, removing and/or avoiding of greenhouse gases (GHG) emissions. Despite that, few reviews have presented them together. This review covers GHG emissions related to the BMP in the crop and animal production systems of farms relevant to Canadian Prairie. These BMP include: (1) use of inorganic N fertilizers, (2) livestock and feed management, (3) manure management, (4) cropping systems, (5) tillage practices and (6) improved pasture and grazing management. In addition, sources of variations, quantification methods and adoptability are discussed. Quantified GHG emissions from direct and indirect measurements of researches from Canada and other part of the world are included. Since most experiments are conducted under multiple biophysical scenarios while adopting various methodologies, summarizing the findings was difficult. The effect of BMP on GHG is determined by ecological processes. Such determinants are discussed and knowledge gaps are identified. Integration of crop and livestock production systems could further lead toward higher energy and resource use efficiency; hence less GHG emissions.
KeywordsBMP Canadian Prairie Cropping systems GHG Livestock Pasture
1. Introduction . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 2
2. Inorganic nitrogen fertilizers . . . . . . . . . . . . . . . . . . . 3
2.1. Conventional inorganic nitrogen fertilizers . . . . . 3
2.3. Rate, placement and timing options . . . . . . . . . . 5
3. Livestock . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 6
3.1. Enteric fermentation . . . . . . . . . . . . . . . . . . . . 6
3.1.1. Feeding management . . . . . . . . . . . . . . . . 7
3.1.2. Forage: grain ratio and restricted feed intake . . . . . . . . . . . . . . . . . . . . . . . . . 8
3.1.3. Nutritional manipulations. . . . . . . . . . . . 8
3.1.4. Growth promoters, ionophores, and organic acids . . . . . . . . . . . . . . . . . . . . . . . . . . 8
3.1.5. Feed processing . . . . . . . . . . . . . . . . . . . 9
3.1.6. Genetic selection . . . . . . . . . . . . . . . . . . 9
3.2. Manure . . . . . . . . . . . . . . . . . . . . . . . . . . . . 9
3.3. Greenhouse gases emissions from manure applied soil . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 9
3.4. Net greenhouse gases emissions from animal agriculture . . . . . . . . . . . . . . . . . . . . . . . . . . 10
4. Cropping systems . . . . . . . . . . . . . . . . . . . . . . . . . . 10
4.1. Inclusion of pulses . . . . . . . . . . . . . . . . . . . . . . . 11
4.2. Rotational forage . . . . . . . . . . . . . . . . . . . . . . . 11
4.3. Cover crops . . . . . . . . . . . . . . . . . . . . . . . . . . 12
4.4. Tillage . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 12
5. Pasture management . . . . . . . . . . . . . . . . . . . . . . . . 13
5.1. Permanent cover . . . . . . . . . . . . . . . . . . . . . . . 13
5.2. Grazing management . . . . . . . . . . . . . . . . . . . . . 13
6. Intergration of crop–livestock systems . . . . . . . . . . 14
7. Biofuel . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 14
8. Boundaries of net greenhouse gases computations and limitations . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 14
9. Conclusions . . . . . . . . . . . . . . . . . . . . . . . . . . . . . 15
10. References . . . . . . . . . . . . . . . . . . . . . . . . . . . . 15
The major causes of global warming are greenhouse gases (GHG) emitted to the atmosphere and the most common GHG in agriculture are nitrous oxide (N2O), methane (CH4) and carbon dioxide (CO2). These forms of chemicals have various potency of global warming potentials for 100 years (i.e. N2O (298), CH4 (25) and CO2 (1)) (Foster et al. 2007) and are usually expressed to the equivalence potency of global warming potential of CO2 (CO2e). The global technical mitigation potential from agriculture, excluding fossil fuel offsets from biomass by 2030, considering all gases is estimated at approximately 5500–6000 Mt CO2e year−1. In 2008, about 37 Mt CO2e of the net emissions from agriculture were from N2O, with the remaining 25 Mt CO2e coming from CH4 (Environment Canada 2010). On the other hand, through photosynthesis and carbon sequestration agriculture is a net sink for CO2 emissions (Smith et al. 2008a).
In accordance with the Kyoto protocol, Canada has to reduce its emissions, in various economic sectors, to 6% below the 1990 levels between the 2008 and 2012. The on-farm management practice is one of these economic sectors (Desjardins et al. 2001). Agricultural related GHG emissions in 1990 totalled 89.9 Mt CO2e (Kulshreshtha et al. 2000) and about half of this came from soils amended with manure (Kebreab et al. 2006) and the rest from livestock, application of N fertilizers and other farm activities. The emissions from Canadian agricultural activities are estimated to increase to 97 Mt CO2e, mainly due to increased livestock production and off-farm transportation/storage, by 2010 (Kulshreshtha et al. 2000).
The Canadian Prairie includes the provinces of Manitoba, Saskatchewan, and Alberta. In 2006, the farm land area under agricultural production was estimated at 54.8 million ha. Most of the farms in the Canadian Prairie have specialized either in crop or livestock production systems. In 2006, 46% of the farms were operating on crop production and 51% on livestock production (Statistics Canada 2006). The main crops are wheat, oilseed, pulse and other grains. Beef, hog and dairy are the major animals in the livestock production. It is widely believed that the numbers of farms that integrate crop and livestock production systems are very small.
Rochette et al. (2008) estimated the mean N2O emission of the Canadian Prairie from 1990 to 2005 using the Intergovernmental Panel on Climate Change (IPCC) country-specific methodologies (Tier I and Tier II). The emissions were grouped according to sources as follows: N fertilizer (9.21), manure (1.52), crop residue (6.06), change perennial to annual crops (0.19), soil tillage practices (−1.48), summer fallow (2.14), organic soil (0.01), moist landscape (2.08), grazing animals (4.62), irrigation (0.61), all soils sources (24.99), animal waste management (5.04) and indirect sources (6.27). The total agricultural emission was estimated at 36.3 Gg N2O-N. On the other hand, the main sources of CH4 emission are from ruminant animals, flooding, animal waste management and biomass burning (Mosier et al. 1998). In 2002, CH4 emission was estimated at 26% of the total agricultural emission (Kebreab et al. 2006). In addition, most agricultural lands have lost their antecedent soil organic carbon pools, which is estimated to range from 20 to 60 Mg C ha−1 (Lal 2001).
To reverse these trends, several GHG mitigation technologies in both crop and animal production systems of farms have been recommended and generally the technologies can be categorized into three main components. These are reducing emissions, enhancing removals and avoiding (displacing) emissions (Smith et al. 2008a). In agriculture, the practices are commonly known as beneficial management practices (BMP).
BMP can promote good land stewardship and sustain or increase net economic return and they have been recommended to reduce global warming potential by several researchers from Canada and other parts of the world (e.g. Desjardins et al. 2001; Adviento-Borbe et al. 2007; Johnson et al. 2007; Christopher and Lal 2007; Snyder et al. 2007). BMP are reported to improve C sequestration, reduce N losses to the environment (Jayasundara et al. 2007) and minimize aggregate stressors (i.e. nutrients, pesticides and sediments) to water bodies (Yates et al. 2007).
The main objective of the review is to evaluate and summarize the GHG mitigation potential of the BMP in the cropping and animal production systems of the Canadian Prairie.
2 Inorganic nitrogen fertilizers
The ultimate goal of N fertilizer application to soils is to increase the yield and enhance the soil N contents. Plants’ nutrient uptake is time dependent and mostly relies on the chemical availability and positional accessibility of the nutrient to the plant roots, when demanded. However, N is highly mobile and when N enters the soil solution from fertilizers, it undergoes various reactions that may lead to immobilization, leaching, volatilization, and denitrification. Notably, the potential of soil to increase N2O emission from N fertilizers is high (Rochette et al. 2008). Agronomic studies, therefore, have been targeting to optimize the selection of source, timing and methods of application to reduce such losses. Agricultural researchers are focusing on inter-seasonal plant requirement and site-specific biophysical conditions to reduce GHG emissions and costs. The outcome of such studies, in the Canadian Prairie and other parts of world, are discussed below.
Beneficial management practices (BMP) related to N fertilizer management, recommended for the province of Manitoba to reduce the GHG emission and increase the environmental stewardship (modified after Eco-ressources Consultants 2009)
Emission reduction potential
Fertilizer quantity (right rate)a
Reduce fertilizer use and reduce N2O emissions
Improves water quality, reduced fertilizer use, greater economic returns and risk of yield reduction
More research needed to establish optimum rates
Source of N fertilizer (Right product)b
Increase nutrient use efficiency and inhibitors further reduce N2O emission
Adoption may be limited; less leaching to the ground water
New N formulations using inhibitors and coatings are untested in the Canadian Prairie
Fertilizer placement (Right place)a
Affected by sources of N fertilizers, unproven when interacted with sources of N, reduce fertilizer use
Requires high level of monitoring; knowledge and equipment needed; co-benefits include water and air quality, and reduced fertilizer use
Untested in the Canadian Prairie
Not recommended as immediate mitigation practice
2.1 Conventional inorganic nitrogen fertilizers
It is estimated that 74% of the farms in the Canadian Prairie use inorganic N fertilizers (Lefebvre et al. 2005). The cost of fertilizer has a significant influence on the choice type and quantity of N fertilizer (Statistics Canada 2004). Since 1999, the cost of inorganic N fertilizer has been increasing but in the last few years it has accelerated. Urea has increased by $50 t−1 and ammonia by $900 t−1. On average, one cent increase in purchasing price is estimated to cost Canadian farmers $61 million. For instance, in Manitoba, 70% to 98% of all fertilizers are applied in the spring; this can create huge demand–supply gap, thus affecting a price (Rolfe 2007). The average price difference of urea, anhydrous ammonia and urea ammonium nitrate (UAN) solution in fall and spring between the years 2001 to 2006 was estimated at 12%, 17% and 7%, respectively (MAFRI 2008). Generally, in the Prairie, some farmers apply during fall to minimize the fertilizer costs and due to more availability of time; however the fall application of inorganic N fertilizers is often inferior to the spring application for increasing yields (Malhi et al. 2003) and create higher N losses to the environment. The inorganic N fertilizer shipments including producers, wholesale distributors and retail distributors in the Canadian Prairie between July 2007 and June 2008 were: ammonia (574,000), urea (1,623,000), urea ammonium nitrate (616, 000), and ammonium sulphate (562,000) tonnes (CFI 2009).
The estimation was further fine-tuned by excluding short period observations and the fertilizer induced emission was increased to:
N2O-N emission (kg ha−1) = 0.245 + 0.0136(Napp) which implies an emission rate of 0.245 kg N2O-N ha−1 year−1 from non fertilized soil (Helgason et al. 2005). Rochette et al. (2008) used 0.008 kg N2O-N kg−1 Napp as regional emission factor (EFreg) for the Black soil zone since the semi-arid conditions of the Prairie region resulted in very small N2O emissions vs. Fertilizer N slopes, which was not statistically significant from 0. The EFreg was obtained from the difference the mean N2O emissions at fertilizer rates of 80 kg N ha−1.
Summary—effect of nitrogen fertilizer on N2O emission
Emission (N2O-N)% of applied N
(Snyder et al. 2007),
Source of fertilizer affects the GHG emissions. Evaluation of the relative effects of source of fertilizers on crop productivity and net GHG emission could be important.
(Tenuta and Beauchamp 2003),
(Snyder et al. 2007),
(Tenuta and Beauchamp 2003),
(Snyder et al. 2007),
(Tenuta and Beauchamp 2003)
0.03–0.18 kg ha−1
(Snyder et al. 2007),
(Tenuta and Beauchamp 2003),
(Bembenek et al. 2006)
(Tenuta and Beauchamp 2003)
The GHG emission can vary with other nutrient application variables (i.e. timing, placement of application). The combination of fertilizer sources and the variables are key issues that contribute to the improvement of N use efficiency and reduction of GHG emissions. Tenuta and Beauchamp (2003) indicated the importance of methods-refinement to predict N2O emissions based on N fertilizer source use and moisture. Such a refinement may reduce the uncertainties in inventories of national estimates of N2O emissions from agriculture.
2.2 N fertilizers formulations—nitrification/urease inhibitors and enhanced efficiency fertilizers
Nitrification inhibitors (i.e. dicyandiamide (DCD), nitropyrin, 3,4 dimethyl pyrazole phosphate) (Zaman et al. 2008) and urease inhibitor such as (n-butyl)-thiophosphoric triamide (NBPT) can reduce N emissions from soils. Nitrification inhibitors slow the activity of Nitrosomonas, the genus of nitrifying bacteria responsible for the oxidation of NH4+ to NO2−, thereby can reduce NO3− leaching and N2O emissions (Zaman et al. 2008). Urease inhibitors slow down the conversion of urea into ammonia and CO2 ((NH2)2CO + H2O → 2NH3 + CO2). Agrotain is a mixed solvent additive containing NBPT used as urease inhibitor with urea or UAN and DCD is most widely used as nitrification inhibitor. In addition, fertilizers can be produced coated by polymers for similar purposes which are called slowly released fertilizers. The Environmentally Smart Nitrogen (ESN) refers to one of the most commonly used polymer-coated urea fertilizers.
In the Canadian Prairie, fall applied N are subject to time-course dynamics of temperature and emissions. The inhibitors and coated N fertilizers could be important by providing farmers wider time-spectrum for N application at early fall with minimum risk of volatilization until the soil freezes. Similarly, such fertilizers when applied in spring could be important in delaying the release of N till the crop demand is high. However, the effect may be affected by soil temperature and soil type. Tiessen et al. (2006) concluded, from experiment in Red River Valley, that fall banded urea containing both DCD and NBPT slowed nitrification by 50% and increased retention of fertilizer N as NH4+ in the fall. Thus, suggested even if fall applied urea without inhibitors is banded, addition of inhibitors could improve the N recovery and retention further. Similarly, fall applied ESN under high soil moisture conditions can produce the same yield while reducing N2O emission. The cost of ESN is estimated to be 10% higher than urea (Keith, R. Pers. Comm., OMAF, ON). The effectiveness of inhibitors could depend on biophysical factors such as soil texture, temperature and/or organic content. The temporal effectiveness of inhibitors in relation to soil aeration, soil bulk density and oxygen concentration on reduction of GHG emissions needs further research.
2.3 Rate, placement and timing options
Several studies agree that the amount of N lost through N2O increases with increasing level of fertilizer applications (Malhi and Lemke 2007; Dobbie and Smith 2003; Stehfest and Bouwman 2006). The three important factors that can affect the N use efficiency and GHG emissions are rate, spatial placement and timing.
Statistics Canada (2004) showed that only 22% of the farms in the Canadian Prairie test their soil at least once a year and 34% less than once a year, and the rest (44%) had not tested their soils for a few years. It is commonly known that the N status varies even within a field; however most producers are not differentiating the nutrient status spatially. This could lead to gross mismatch of requirement to the blanket applications on particular spots across the field. Therefore, to avoid unnecessary doses, to reduce the likelihood of N2O emissions and to optimize the delivery of nutrient to the plant roots, site-specific application could be more judicious management option.
The average amount of N2O emission, in an 8-year field study in Saskatchewan from side banding of urea (at application rates range of 40 to 120 kg N ha−1), was quantified to be 580 g N ha−1, while in the control it was 155 g N ha−1 (Malhi and Lemke 2007). Application of N increased crop biomass (i.e. barley, wheat and canola) by 40% approximately and enhanced root biomass (up to 45 cm soil depth) by 32%.
N fertilizers can be applied in various placement methods. The major groups are banding and broadcasting. There are several methods of banding (i.e. drill with the seed, side banding, mid-row banding, sub-surface banding into the soil prior to seeding, surface banding and nesting). Broadcasting can be performed either broadcast without incorporation or broadcast with incorporation into soil. According to Lefebvre et al. (2005), the percentage share of methods of application for the year 2001, in the Canadian Prairie, were 11% (injected or knife), 1% (post plant top or side dressing), 46% (applied with the seed), 20% (banding), 21% (broadcast) and 1% (others). Only 10% of the farmers adopted a nutrient management plan.
Timing is a crucial issue of N management in agricultural fields. Fall application can be further divided into three periods namely early, mid and late. Spring application can be divided into early and late spring. In some cases, it could be applied both in the fall and spring by splitting the total recommended amount into partial doses. Fall application usually gives similar yield to that of the spring application, but N loses in fall application are higher. In the Canadian Prairie, fall applied N are subjected to time-course interaction of temperature and volatilization. To slow the N loss through nitrification before freezing and thus increase N use efficiency in spring, Tiessen et al. (2006) suggested delaying application of fall banded N until mid-October.
The efficiency of fertilizer N use could be optimized by proper selection of rate, source of the fertilizer, timing and type of plant. For instance, drilling with the seed is related to high risk of seed damage when uncoated urea is used and the application of urease inhibitors could reduce seed damage. Malhi et al. (2003) reported that polymer-coated urea was the most effective followed by Agrotain in comparison to uncoated urea when seed-row placed on wheat and canola. Malhi et al. (2008) concluded that there were few differences in the agronomic performance of flax from urea vs. anhydrous ammonia and side-band vs. mid-row band. They suggested that broadcast urea can be less effective than side-banded urea, and fall banded N can be inferior to spring-banded N.
Nitrogen fertilizers are highly dynamic in soil and, particularly, frequent diagnosis of soil N status is required. Duke (2006) suggested that testing the nitrate status of the soil during the early growing season of corn, when the plant requirement is high, could reduce the N application rate by 15%, thus reducing N2O emission. This is because whenever the applications of N fertilizers exceed the ecosystem N uptake capacity (i.e. which can be estimated from pre-planting measurements of residual N and net input–output balances) it would largely increase the NO3− and N2O emission (Grant et al. 2006).
Field emissions of N2O and CO2 are related to thaws. It was estimated annually that 70% of the N2O and 10–25% of the C budget are emitted during the spring thaw. The emissions during winter thaw were also considerable. The relationship between the N2O fluxes and soil temperature was especially greatest at the surface (air and soil temperature at 5 cm) and decreases with soil depth (Furon et al. 2008). This finding has an important implication to fine tune N placement methods. Wagner-Riddle et al. (2008a) found that 15NO3− applied to the soil surface layer (0 to 5 cm) resulted in N2O fluxes at spring thaw that were 1.5 to 5 times higher than when applied at depths of 12 to 17 cm.
The potential to reduce GHG emissions by optimization of nutrient management could be enhanced through proper selection of sources, applying the right rate, and improvement in placement techniques as well as choosing the appropriate timing of inorganic N fertilizers. The presently used 1% (IPCC 2006) of N2O-N emission from the applied inorganic N fertilizer is general and it needs to be refined for each of the fertilizer sources, placement and timing options. Most likely, the GHG emissions could also be affected by the interaction matrix of the nutrient management options mentioned above.
Beneficial management practices (BMP) related to livestock management, recommended for the province of Manitoba to reduce the GHG emission and increase the environmental stewardship (modified after Eco-ressources Consultants 2009)
Emission reduction potential
Efficiency affected by several factors; depending on strategy or up to 50% reduction compared with mature pasture
Increase to producers of $57–$282 t−1 of GHGs emitted has been projections depend on feeding strategy
Increasing efficiency of feed conversion
Depend on several factors; 20–40% reductions in N2O emissions; mitigates 0.42–0.5 t CO2e m−3 of manure
Methane captured can offset fossil fuel use
Efficiency affected by several factors; mitigates up to 0.69 t CO2e m−3 of manure
Increase to producers of $4 t−1 of GHGs emitted
Leakage from cover; incomplete combustion
Improved handling/barn cleand
Projected reduction on prairie up to 26000 t; 20–40% N2O reduction by improving manure management
Removing fall application of manure estimated to cost $237 per tonnes of GHG emitted
May result in higher N in manure
Unproven; emits 0.24–0.40 t CO2e t−1 of manure
More research needed
3.1 Enteric fermentation
Enteric CH4 production arises principally from microbial fermentation of hydrolysed dietary carbohydrates such as cellulose, hemicelluloses, pectin and starch and the amount of CH4 emission from animals depends on type and amount of feed ingested. The loss of CH4 from animals is not only an environmental concern. Methane emissions represent an energetic loss that impacts on profitability of livestock production through reduced feed conversion efficiency (Moe and Tyrrell 1979; France and Kebreab 2008). The amount of CH4 produced by an animal is influenced by many factors including dietary factors such as type of carbohydrate in the diet, level of feed intake, and degree of saturation of lipids in the diet (Kebreab et al. 2006). Mitigation strategies to reduce enteric CH4 emissions from cattle has been extensively reviewed by Boadi et al. (2004a) and updated by Kebreab et al. (2006). Therefore, mitigation strategies will be discussed here briefly and will focus on recent studies and those that are relevant to the Canadian Prairie’s animal production systems.
3.1.1 Feeding management
Several practices have been conducted as a BMP in the Canadian Prairie to improve the feeding management of livestock. These include: improved management of perennial forage stands, stockpiling perennials, crop aftermath, and annuals for fall grazing, swath grazing and bale grazing (Havens and Lastiwka 2008). Wittenberg and Boadi (2001) suggested promotion of high quality forages in ruminant feeding and grazing systems to reduce GHG emissions. The management of grazing, pasture or feedlot has an impact on GHG emissions. A comparative study was conducted by McCaughey et al. (1997) on stocking rate and rotational or continuous grazing of crossbred yearling steers which grazed 60% alfalfa, 40% grass pastures and managed by rotational or continuous grazing at each of heavy and lightly stocked rates. The authors reported that continuously grazed, heavily stocked pasture resulted in lowest CH4 emissions 242.2 L day−1 per animal, and the highest emissions per animal were 306.7 L day−1 from continuously grazed lightly stocked pasture. However, when CH4 production measurements were compared on per kilogram of body weight gained basis, no differences were found between the grazing treatments with the average of 0.69 ± 0.06 L kg BW−1 day−1. Bannink et al. (2010) compared various types of grass management using a mechanistic model and reported that the lowest CH4 emission was established for early cut, high fertilized grass silage and high fertilized grass herbage. The highest emission was found for late cut, low-fertilized grass silage.
Harper et al. (1999) observed that cattle grazed on low-quality, high-fibre pasture produced higher CH4 production (about four times) compared to cattle fed high-grain diets. This corresponds to the conversion of 7.7 to 8.4% of gross energy (GE) into CH4 for low-quality-fibre diet and only 1.9 to 2.2% for high-grain diets. The conversion rates are similar to those indicated by Kebreab et al. (2008) but higher (for the former) and lower (for the latter, respectively) in comparison to IPCC estimates. Ominski et al. (2006) also found that CH4 emissions were influenced by pasture quality and availability, as highest emissions were observed when the quality was low and dry matter availability was limited (11% of GE). The addition of grains, such as corn, barley or wheat, to the diet could reduce CH4 emissions per unit of animal product.
However, an imbalance in the nutrient content of the feed consumed, such as shortfall in the amount of protein or mineral, can increase the amount of CH4 produced. Cattle fed in a feedlot usually emit less CH4 than grazing cattle as a result of increased grain consumption and the ration is formulated to meet the animal’s nutrient requirement (Kebreab et al. 2006). Harper et al. (1999) reported CH4 emission of 0.23 kg (animal)−1 day−1 for cattle grazing on pasture and 0.07 kg (animal)−1 day−1 for the same cattle type fed a highly digestible, high-grain diet.
3.1.2 Forage:grain ratio and restricted feed intake
Most of the literature show that feeding diets with low forage:grain ratio is an effective means of reducing CH4 output per unit live weight gain and improves feed conversion efficiency. For example, Boadi et al. (2004b) reported a 42% lower CH4 production from steers fed low forage:grain ratio compared to those fed high forage:grain ratio and overall CH4 production ranged from 0.9 to 6.9% and from 0.7 to 4.9% GE intake, respectively. Kirkpatrick et al. (1997) reported that restricting feed intake significantly lowered CH4 production compared to ad libitum fed beef cattle. The authors reported 2.5% of GE lower CH4 emissions in cattle on restricted diet.
3.1.3 Nutritional manipulations
Addition of fats, particularly medium chain fatty acids to animal feed have been shown to reduce enteric CH4 production. This is most likely due to reduced total H2 supply in the rumen through a reduction of the total amount of rumen fermented organic matter following defaunation, a shift towards propionate production and provision of an alternative H2 sink through bio-hydrogenation. In a recent Canadian study, Odongo et al. (2007c) showed that a 5% inclusion of myristic acid (medium chain fatty acid) resulted in 36% reduction (from 608.2 to 390.6 ± 56.46 L day−1) in CH4 production, further confirming a study by McGinn et al. (2004) who reported a 21% reduction by adding sunflower oil to the diet. A concern regarding addition of fat into diet is the alteration of fatty acid profile in milk fat. However, Odongo et al. (2007c) showed that addition of myristic acid did not alter the conjugated linoleic acid and trans-18:1 fatty acid profile in milk. Using North American diets as an input, Kebreab et al. (2008) calculated CH4 emission from diets containing 4.5% diet and reported a reduction of emissions by at least 1% of GE intake.
Many studies have demonstrated that types of carbohydrates consumed affect CH4 production. Hindrichsen et al. (2004) reported that supplements with higher non-cellular polysaccharides (such as guar gum and starch) favoured propionate-forming microbes and therefore diverted H2 away from methanogens. Simple sugars promote acetate and butyrate formation at the expense of propionate, which provides H2 for methanogens and therefore increases CH4 production. Mills et al. (2001) showed that diets with starch considerably lowered CH4 production compared to diets with sugars.
3.1.4 Growth promoters, ionophores, and organic acids
Natural growth promoters such as testosterone, estradiol, and progesterone, and synthetic ones such as melengestrol acetate, trenbolone acetate, and zeranol are used in livestock production. Growth promoters could increase feed use efficiency, reduce land requirements and reduce GHG per unit of product. Grain feeding combined with growth promoters resulted in about 40% reduction in GHG per pound of beef compared to grass feeding (excluding N2O), with the growth promoters accounting for 25% of the reduction observed (Avery and Avery 2008). In a long-term experiment in Ontario, Odongo et al. (2007a) observed a reduction of CH4 production using monensin by 7% (when expressed in g day−1) and by 9% (when expressed as g (kg body weight)−1) in lactating dairy cows. This is in agreement with an experiment in Alberta by McGinn et al. (2004) who reported a 9% reduction of CH4 emission per kg of dry matter intake due to the use of monensin. In the former study by Odongo et al. (2007a), the application of monensin reduced milk fat percentage by 9% and milk protein percentage by 4%. Odongo et al. (2007b) reported that monensin was at least partly effective in inhibiting the bio-hydrogenation of unsaturated fatty acids in the rumen and consequently increased the percentage of n−6 and n−3 polyunsaturated fatty acid and conjugate linoleic acid in milk, thus enhancing the nutritional properties of milk with regard to human health. The effect of organic acids (such as malate and fumarate) in reducing CH4 output is not conclusive. In their review, Castillo et al. (2004) from in vitro studies concluded that inclusion of organic acids has the potential to reduce methanogenesis but McGinn et al. (2004) did not observe significant effects of adding yeast and fumaric acid on CH4 emissions.
3.1.5 Feed processing
Methane emissions from steam flaked vs. cracked corn component-fed (which includes corn silage, mixed hay, and corn) cows on a commercial dairy farm in Ontario were compared. The cracked corn ration reduced CH4 emissions by 14% (616 vs. 704 L CH4 day−1, cracked corn vs. steam flaked, respectively). These results suggest that enteric CH4 emissions from dairy cows can be reduced significantly using simple dietary manipulation strategies and shifting the site of digestion from the rumen to the small intestine (Odongo et al. 2006).
3.1.6 Genetic selection
A few measured experiments in Alberta have shown that beef cattle differ in their residual feed intake (RFI, the difference between the intake of metabolisable energy (ME) intake and ME required for maintenance and gain; e.g. Okine et al. 2003; Nkrumah et al. 2006). The authors found that cattle with low RFI reduced CH4 production by 28% compared to those with high RFI and suggested that traits which are related to individual differences in microbial population in the rumen could be heritable. Similarly, Pinares-Patiño et al. (2003) from a controlled grazing experiment observed most of the differences associated with CH4 production were intrinsic animal differences which could be heritable. It is possible that the effect of genetic selection may be related to variation in digestion instead of variation in ME utilization by the animal.
Manure is a complex matrix consisting of a phenomenal concentration of micro-organisms (comprising of bacteria, protozoa and fungi). In Canada, manure is stored over several months; with an estimated 14% of livestock operations using liquid storage, 69% using solid storage and 24% keep their animals on pasture year-round or spreading manure daily (Statistics Canada 2003). Next to enteric fermentation, manure storage is one of the most significant source of CH4. Gas emissions from animal manures vary with type of animal, diet, management of manure and climatic conditions (NRC 2003). Due to these factors, and the paucity of measurements in Canadian conditions, livestock-related manure emission estimates of these gases are very uncertain (Janzen et al. 1998). In one of the few studies available on manure contribution to GHG emission, the effect of diet formulation was shown to influence the C:N ratio of excreted manure, which in turn, has the potential to influence the extent of CH4 released from stored manure. For example, Rejis (2007) showed that feeding diets high in fibre and low in protein results in slurry with relatively high C:N ratio and low inorganic N:total N which can give microbes substrates that can be converted to CH4 during storage. In fact, Huang et al. (2010) predicted high C substrates in manure to yield high amount of CH4 production during anaerobic storage. Cattle consuming high forage diets produce manure with a higher content of partially digested cell wall material, which escaped microbial degradation and subsequent release of C as compared to cattle consuming higher grain (Boadi et al. 2002).
3.3 Greenhouse gases emissions from manure applied soil
Beef, swine and poultry are the major livestock groups in the Canadian Prairie and manure application is one of the most important nutrient management strategies. However, the main concern of manure application is associated with GHG emissions (Jarecki et al. 2008). On a category basis, domestic animals are estimated to contribute directly 32% (19 Mt), manure management 17% (10 Mt), and soils (partly manure amended) 50% (30 Mt CO2e) of Canadian agricultural emissions. Given the importance of livestock-related GHG contribution, there is a potential for BMP that take animal production, manure management and field application of manure into consideration to mitigate Canadian agricultural emissions in general and western Canada specifically (Kebreab et al. 2006).
Increasing nutrient utilization of livestock from feed by incorporating enzymes such as phytase (Jongbloed et al. 1992) has been a strategy to reduce nutrient load in the excreta. This modifies the chemical composition of manure (Velthof et al. 2003) and reduced the mineral N (NH4-N and NO3-N) by 6.3–9.8% when expressed as a percentage of the Total N of manure (Pillai et al. 2009) therefore, GHG emissions from manure applied soils. Little quantitative information on the effect of manure composition changes on GHG emissions is available mainly because of the lack of integration of the GHG emissions from soils with the processes at the animal level. Recently, reduced GHG emission was observed from manure of pigs fed diets supplemented with phytase on Manitoban clay soil (Yitbarek et al. 2009).
3.4 Net greenhouse gases emissions from animal agriculture
It has to be emphasized that decisions to reduce GHG emissions from animal agriculture need to be taken based on the net emissions after considering emissions due to feed production, feed transportation, enteric emissions, manure storage, and application to soil and calculated per unit of product produced (milk, meat etc.) and/or per unit of area occupied. Stewart et al. (2009) compared whole-farm emissions per unit of protein output of 11 management systems based, in part, on equations recommended by IPCC. The authors showed that compared to the baseline management scenario, pasturing cattle on alfalfa-grass had the largest decrease (0.39 to 0.66 Mg CO2e (Mg protein)−1) in emissions for all locations. Feeding lower quality forage over winter had the greatest increase in emissions per unit protein on northern and southern Alberta, with increases 1.08 and 1.14 Mg CO2e (Mg protein)−1, respectively. Eliminating the fertilization of forages resulted in the largest increase (2.40 Mg CO2e (Mg protein)−1) in emissions per unit protein on a Saskatchewan farm, while reducing the fertilizer rate by half for all crops showed the largest increase (2.19 Mg CO2e (Mg protein)−1) on a Manitoba farm. Schils et al. (2006) concluded that full accounting system could show how N management reduce the GHG emissions in dairy farm and agriculture as a whole. The authors calculated a reduction of the N surplus per kg milk with 1 g N, through reduced fertilizer use and reduced grazing time, diminished the GHG emissions per kg milk with approximately 29 g CO2e.
4 Cropping systems
Cropping systems refer to the management of farm in space and time. Because, it allows greater carbon sequestration, intensification of the cropping system is one of the strategies used to mitigate climate change. In the Canadian Prairie, it may include: incorporation of pulses such as field peas (Pisum sativum), dry beans (Phaseolus vulgaris), soybeans (Glycine max), faba beans (Vicia faba or Faba vulgaris), lentil (Lens culinaris Medik.); and rotation of forages such as clover (Trifolium spp.), alfalfa (Medicago sativa), sweet clover (Melilotus officinalis), meadow bromegrass (Bromus riparius Rehm.), timothy (Phleum pratense) and orchard grass (Dactylis glomerata); use of cover crops such as, berseem clover (Trifolium alexandrinum), hairy vetch (Vicia villosa), winter wheat (Triticum aestivum), red clover (Trifolium pratense), annual alfalfa, Italian ryegrass (Lolium multiflorum) and sweet clover (Melilotus officinalis). In addition, tillage practices could also be considered as one of the cropping systems. Cropping systems provide not only opportunities in reducing N2O-N but also in improving energy use efficiency and in increasing carbon sequestration.
The advantages of crop intensification on environment are related to the improvement of energy use efficiency, soil quality, soil moisture and N fixation. In a typical North American farm, the consumption of energy can be broken down as follows: 36% (fuel to run the machinery), 38% (production of inorganic N fertilizer), 10% (transportation) and the rest for P and K fertilizers, seed, pesticide and production of farm equipment (Heichel 1980). This implies 74% of the energy budget of farms is allocated to fuel consumption by machinery and to N production.
Legumes are recognized for their ability to enrich N in a cropping system. The interest of growing legumes has been increasing with the rising price of N fertilizers (Bullied et al. 2002). In legume–non-legume crop sequences, the amount of N fertilizer that can be replaced depends on: (1) the quantity of legume returned to the soil, (2) the content of symbiotically fixated N in the residues, (3) the availability of N residue from legume to the subsequent crops and (4) the amount of residue incorporated to soil (Christopher and Lal 2007).
Experimental data in the Canadian Prairie showed, rotations containing 50% of perennial forage legumes decreased the non-renewable energy use by 85% and increased the energy use efficiency by 438%. In addition, relative to cereals, pulses, and oilseed rotations, they reduce the non-renewable energy use by up to 28% and increased the energy use efficiency by up to 294%. These efficiencies declined when fertilizers were applied (Hoeppner 2001). The values were obtained after converting all inputs, field operations and crop harvests into energy values using energy coefficients.
However, legumes have higher N2O and CO2 emissions compared to cereals and grasses. Some N2O may be emitted from N release as root exudates during the legume growth period (Rochette and Janzen 2005) but decomposition of residue following the growing season and in subsequent cropping season may be far more important (Helgason et al. 2005). Kagan (2000) showed 9.7 times higher N2O emissions during spring thaw in alfalfa and fallow than in native grass and wheat. Similarly, Wagner-Riddle and Thurtell (1998) found higher N2O emissions for 2 years after incorporating an alfalfa crop, which could be due to the availability of easily degradable N than from grasses. In eastern Canada, the comparison of N2O emission (kg N2O-N ha−1) from paired treatments of legume (y) and non-legume (x) crops with application of 0 to 5 and 0 to 190 kg N ha−1 year−1, respectively, was demonstrated using the regression equation: y = 0.370 + 0.617x. The authors expected less emission in western compared to eastern Canada (Helgason et al. 2005). In general, because less fertilizer is used in legume based cropping systems, the overall GHG emissions are usually less than those in fertilized monocots (Lupwayi and Kennedy 2007).
4.1 Inclusion of pulses
Pulses are annual leguminous crops yielding from one to 12 grains within a pod, according to the Food and Agriculture Organization of the United Nations. The term pulse is reserved for crops harvested solely for the dry grain. The inclusion of pulses to oil and grain crops has been increasing rapidly. The area seeded to pulses in Canada over the last decade has increased by 1,300% (Pulse Research Council 2002).
The introduction of grain legumes could impact soil organisms, including both symbiotic and non-symbiotic N-fixing bacteria, pathogens, mycorrhizae and soil fauna. In 2004, it is estimated that about 171 million kg N2 was fixed by field pea, lentil, and dry bean representing 7% of the total fertilizer N (2580 million kg) used by Canadian Prairie farmers in that year. Legumes contribute to GHG reduction by replacing the N requirement of the cropping system than without the inclusion of pulses (Lupwayi and Kennedy 2007). An experiment by Matus et al. (1997) showed that, under zero tillage N fixations by lentils and peas increased by 10 and 31%, respectively. The net annual contribution to the soil by N fixation from lentils and peas ranged from −143 to 26 kg N ha−1 and from −32 to 96 kg N ha−1, respectively. In another observation, field peas under conventional and no-till with application of 5 kg N ha−1 in the Prairie showed 0.14 and 0.08 (Swift Current, SK, 1999–2004), and 1.72 and 0.94 kg N2O-N ha−1 (Three Hills, AB, 2002–2002), respectively. A summary of N2O-N emissions during fall and spring thaw in southern Ontario ranged from 0.20 to 1.02 N2O-N ha−1 for soybean (Rochette et al. 2008).
The quantification of GHG emission and C sequestration are strategic research topics of the Pulse Research Canada. However, few research results of GHG emission are available. The N2O emission for peas growth period in Brandon with fertilizer application on previous crop, was 0.55 to 0.75 kg ha−1 (under high soil disturbance) and 0.41 to 0.68 kg ha−1 (under low soil disturbance) (Khakbazan et al. 2005). A summarized data by Snyder et al. (2007) showed that the net GHG emission from corn–soybean–wheat rotation to be 1140 (conventional tillage) and 140 (no-till) CO2e kg ha−1 year−1. In another experiment, the GHG emissions from corn-soybean rotation were 3,740 kg CO2e ha−1 year−1 (Adviento-Borbe et al. 2007). In an extensive review by Rochette and Janzen (2005) acknowledged the importance of legumes as source of N2O-N emissions and identified the above and below ground residue after harvest and the N release from root exudates during the growing seasons. The authors challenged the biological N fixation (BNF) process itself as a source of N2O-N. As a result, in the Canadian National Inventory from 1990 to 2008 the N2O-N emission from BNF was not included (Environment Canada 2010). The comparison and evaluation of GHG emissions related to pulses and crop rotation systems could be a potential research area in the future.
4.2 Rotational forage
Any plant that can be eaten by animals is considered as forage. Forage production in the northern Great Plains of the USA and Canada (Manitoba, Saskatchewan and Alberta) involves cultivated and native pasture and hay production. Farmers and ranchers use cultivated forages to compliment native range (Entz et al. 2002). Increasing use of forage crop (Desjardins et al. 2001) and feeding of high quality forages was concluded to reduce GHG emissions (Kebreab et al. 2006). The direct environmental benefits of forage crops include reducing nitrate leaching when high rate of N fertilizer is applied, stabilization of production systems (Entz et al. 2001) and higher carbon sequestration (Johnson et al. 2007; Soussana et al. 2007).
Summary—effect of various agricultural activities on greenhouse gas emissions
Decrease forage:grain, nutritional manipulation
4.5% methane reduction
(Kebreab et al. 2008)
Reduce methane emission
0.4–4 kg N2O-N
(Ellert and Janzen 2008)
Reduce N fertilizer use, higher carbon sequestration
Legume cover crop
410 CO2e kg ha−1 year−1
(Snyder et al. 2007)
Reduce the N fertilizer requirement, and increase sequestration
0.43–0.71 Mg C ha−1 year−1
(West and Post 2002)
Increase carbon sequestration, reduce fuel consumption
Pasture management for cattle
0.39–0.66 Mg CO2e Mg−1 protein
(Stewart et al. 2009)
0.61–0.74 kg CO2e kg−1 live weight gain ha−1
(Ominski et al. 2008)
Increase animal weight gain and pasture productivity
0.62 Mg C ha−1 year−1
(Grant et al. 2004)
Increase carbon sequestration
4.3 Cover crops
Cover crops are low-growing species cultivated outside the main crop’s growth period to provide soil cover (Khan 2002). Cover crops are primarily grown to prevent soil erosion and N leaching. The Canadian Prairie generally receives a low amount of rainfall each year, which dries out and makes it susceptible to wind erosion. The total area in Alberta, Saskatchewan and Manitoba is estimated to be 30 million hectares (Larney et al. 1995) and could be exposed, if cover crops are not used. Cover crops could be legumes, non-legume broadleaves or grasses.
Annual cover crops such as berseem clover with oat can reduce excess moisture during the growing season. This clover crop could also be used for enhancing spring snowmelt infiltration, deep percolation, and early warming of the soil by having warmer soils during the winter, shallow depths of frozen soil layers, and less frozen water content within the root zone. This in turn will allow earlier farm operations (Kahimba et al. 2008). In an organic experiment in 2004 and 2005 at Carman and Clearwater, MB, Canada, wheat grown with red clover as a cover crop was moderately successful compared to hairy vetch and annual ryegrass, which competed too aggressively with the wheat crop in wet growing conditions (University of Manitoba 2006).
The soil N contribution of some of the cover crops reported was as follows: 62 kg N ha−1 (red clover), 36 to 209 kg N ha−1 (hairy vetch) (Christopher and Lal 2007), 125 kg N ha−1 (berseem clover) (Sheaffer et al. 2001). Snyder et al. (2007) showed that the net GHG emissions from corn–soybean–wheat rotation resulted in 630 (low-input with legume cover crop) and 410 (organic with legume cover crop) CO2e kg ha−1 year−1 (Table 4).
Conservation tillage and no-tillage practices could provide higher C sequestration (Johnson et al. 2007). West and Post (2002) found that a change from conventional tillage to no-tillage could sequester from 0.43 to 0.71 Mg C ha−1 year−1 (Table 4). In an experiment conducted in Saskatchewan by Malhi and Lemke (2007), N2O emissions were significantly lower from no-tillage (155 g N ha−1) than the conventional tillage (398 g N ha−1) treatments in the third year of the study. Rochette et al. (2008) summarized the effect of no-tillage on N2O emission and concluded that the net impact of the no-tillage on N2O emission to be highly dependent on local environment (i.e. climate, soil type). In addition, the lower farm operation from no-tillage practices could further improve the net GHG. Although, in long term, the C sequestration return diminishes, CO2 emissions are directly reduced since tillage fuel consumption is the greatest proportion of farming activity (Johnson et al. 2007).
Generally under Canadian Prairie production condition, there is limited study on the effect of cropping systems on the mitigation of GHG emissions, however, there is a wide understanding on the physical and hydrological effects of these BMP on soil condition which in turn affects composition and activity of the soil, and therefore, the extent of N2O production and emission from agricultural soils (Wagner-Riddle et al. 2007). Most researchers agree that mitigations based on cropping system require a long-term year-round observation of emissions to capture the interaction of crop management and weather (Wagner-Riddle et al. 2007). In dry areas adoption of no-tillage can be combined with other cropping system, which increases the C sequestration (Snyder et al. 2007).
5 Pasture management
5.1 Permanent cover
Conversion of annual cultivation to permanent cover of forage was conducted by the Prairie Farm Rehabilitation Administration’s program known as Permanent Cover Program (PCP) in 1989 to 1991. The potential of the PCP land to sequester carbon from a total area of 522,000 ha is estimated to be 5.4 to 5.7 million tonnes of carbon. There are 4.4 million ha of marginal land in Canada in annual cultivation. Therefore, if the area can be converted to permanent cover, then it could increase C sequestration by 50 million tonnes (Luiciuk et al. 2007).
Beneficial management practices (BMP) related to cropping systems, recommended for the province of Manitoba to reduce the GHG emission and increase the environmental stewardship (modified after Eco-ressources Consultants 2009)
Emission reduction potential
Results can take years and varies by region; Showed 19% reduction in one of the Canadian study; GHG reduction 0.12–0.44 CO2e t ha−1
Benefits can vary according region; improved C sequestration not a permanent solution
Research is needed to determine the net GHG emissions of the rotation systems-
Believed to have the highest potential for GHG mitigation
Improved C sequestration, soil structure, soil fertility, water quality, and reduces required inputs; not always feasible (e.g., in arid lands) and not a permanent solution
Quantitative results of the rotations are not available-
Reduce the GHG by 0.04–0.15 t CO2e ha−1
Improved C sequestration, not a permanent solution; improves soil quality
Untested in Canadian Prairie
High sequestration coefficients; carbon sequestration rates range from 0.7 to 0.9 t CO2 ha−1 year−1 for 20 years
Important for wildlife habitat and water filtration; improved water, soil quality, reduced inputs and disease
More research needed on the most efficient methods
System/method dependent; potential reductions range from 9% to 25%
Improves soil, water, air quality, productivity, C sequestration; increases costs for fencing, animal management, feed, milk production
More research needed on the most efficient methods
5.2 Grazing management
Ecological sustainable use of grazing can enhance the nutrient cycling and forage composition of grasslands (Thurow 2004). Grasslands have high soil organic matter content that supply nutrients, increase soil aggregation, limit soil erosion, and also increase cation exchange and water holding capacities. Thus, maintenance of soil organic matter is a key factor in the sustainability of grassland ecosystems (Table 5). In conventional grazing system, a single field is grazed. It is less efficient and it can be substituted by intensive rotational grazing. The latter consists of multiple small paddocks for purposeful rotation of livestock. It requires management of rest periods, estimation of carrying capacity and investments for fencing and water supply system (Stephenson et al. 2004).
The results of experiments conducted in Manitoba from 2003 to 2005 to identify BMP and to improve the productivity of grassland system showed that application of hog manure could improve productivity of grassland pasture without increasing net GHG emissions. The application of manure increased the N2O and CO2 emissions from 63 (control) to 196 and 250 kg CO2e ha−1 (split and fall hayed) treatments. However, the pasture productivity and additional animal weight gain was enhanced. Thus, the net N2O and CH4 emissions were unaffected by manure treatment when expressed as kg CO2e kg−1 live weight gain ha−1 over the study period (0.633 Control, 0.613 Split and 0.738 Fall kg CO2e kg−1 live weight gain ha−1) (Table 5).
In addition, root growth resulted in capture of 900 kg C ha−1 (i.e. 3300 CO2e ha−1), which is more than the associated CH4 and direct/indirect N2O emissions (876 CO2e ha−1) (Ominski et al. 2008). Another experiment from Alberta that investigated enhancement of dry biomass productivity concluded that three harvest can be attained from intercropping of spring and winter cereals i.e. a silage or green feed crop in the production year, re-growth for fall pasture in the production year, and spring pasture in the following year (Ford et al. 2007).
The potential and co-benefits of BMP in cropping systems and pasture management are summarized in Table 5. Pulses and forages in rotation and permanent cover are highly recommended. The effect of cover crops on GHG emissions needs to be conclusive for those conditions in the Canadian Prairie.
6 Integration of crop–livestock systems
Like in many parts of the Northern America, majority farmers in the Canadian Prairie have specialized either in crop or animal production systems. There is mounting evidence that this approach is neither profitable for producers nor good for environment (Tanaka et al. 2008). This has created depletions of soil nutrients in the earlier and excess accumulations in the later. With decreasing economic margins, higher energy and inorganic N fertilizer costs, declining soil organic matter levels, increasing concerns over the long-term sustainability of many contemporary agricultural systems, and greater regulation of agricultural practices, it is time to reconsider the potential benefits of integrating crop and livestock production (Russelle et al. 2007). In addition to the other ecological benefits, the integration of crop–livestock could provide several advantages to mitigate GHG emissions. Novak and Fiorelli (2009) identified three ways how the GHG emissions could be mitigated in mixed crop dairy systems. These are: (1) increase energy efficiency or saving of fuel (i.e. reducing distances manure and feed are transported), (2) improve N use efficiency and (3) biogas production through anaerobic digestion of manure. Recently, Thelen et al. (2010) reduced the net global warming potential (GWP) by −986 g CO2e m−2 year−1 by integrating livestock manure with a corn-soybean bioenergy production. The main attributes for the outcome were increasing the short-term carbon sequestration and reducing the GHG emission in the system. Long-term experimental trials to optimize the integration of crop and livestock production systems in the Canadian Prairie need to include quantification of GHG emissions to capture the mitigation opportunities that could obtain from tradeoffs.
The contribution of biofuel to the reduction of GHG emissions is largely controversial. Searchinger et al. (2008) estimated the GHG emission could double for corn-based ethanol and could be 50% more for biofuel from switchgrass taking over corn-land. On the other hand, Goldemberg and Guardabassi (2009) argued that ethanol from sugarcane can reduce the GHG emissions. It is widely accepted that biofuel is important to national energy security and generation of income to rural areas, whenever higher ratios of energy prices to food prices are expected. However, the less net saving of fossil fuel, high agricultural input, competition for land (Keyzer et al. 2008) and intergovernmental and/or interprovincial taxes (Walburger et al. 2006) are among the main concerns. The availability of straw in the region is relatively high, and farmers annually prepare fields by burning straws on-site. An alternative method could be burning of the straw in oxygen limited combustion by a process known as pyrolysis. Such method could provide energy and biochar which is a promising stable carbon by-product of burned biomass that improves the chemical and physical properties of soils (Sohi et al. 2009).
8 Boundaries of net greenhouse gases computations and limitations
The GHG emissions from agricultural activities are diverse in source and the spatiotemporal variability is high. In addition, research approaches vary in boundary of the system, spatial scale, time of observation and methodologies. This could make the computational effort difficult.
Although there is wide agreement that process-based mathematical models play a crucial role, questions that arise on where to set the spatial boundary of quantification and how to integrate and visualize the cascade of agricultural activities on the GHG emissions are not well understood. Janzen et al. (2006) proposed the virtual farm concept which is boundary explicit, considering a single farm as a fundamental unit and constructed of descriptor (which characterize the farm), algorithms (which calculate emissions) and an integrator (which links the algorithms to each other and the descriptor).
Despite continuous research in the last few decades to quantify GHG emissions related to the BMP, most studies had short periods of observation and diverse methodologies. Therefore, many studies have reported a wide range of values for N2O emissions compared to the IPCC prediction of 2006 (Snyder et al. 2007). The most effective monitoring methods of emissions from agricultural activities related to soil and plants are emission chambers- and tower-based (i.e. eddy covariance) measurements. However, extrapolation of the outcome of the research to larger scale (i.e. regional, provincial) needs process-based models representing the processes at the sources of the emissions to account for the spatiotemporal variability of weather, soil condition and agricultural management. Limitations arise in creating predictive models, both from the complexity of integrating the large number of processes and lack of understanding of some of the biophysical processes (Smith et al. 2008b). Therefore, research is globally ongoing to develop valid methodology for deriving more site-specific emission factors (Grant et al. 2006).
On the other hand, GHG emissions related to animals are measured using respiration chamber or calorimeter, portable analyser, polythene tunnel, isotope dilution technique, gas tracer technique, and micrometeorological mass balance technique (Kebreab et al. 2006). The authors suggested standardization of measurement techniques in Canada to simplify the building of a national database that allow easy comparison and accurate estimations. This includes parameters that are essential for the development of predictive models in manure composition and characterization (Wagner-Riddle et al. 2008b).
Integration of farming systems for more efficient use of natural resources per unit of agricultural product is the centre of environmental sustainability. There are several BMP in crop and animal production systems for the Canadian Prairie farms that address various environmental concerns. However, the GHG emissions of these BMP need to be evaluated. Standardization of experimental observations may improve reliability of aggregated data, site-specific emission factors and simulation models. Specially, computation of intra-annual and trans-production systems (i.e. cropping and animal production) resource tradeoffs at farm or community levels could provide reduction of the net GHG emission of farms, thus improve further the reliability and accuracy.
We thank the Manitoba Sustainable Agriculture Practices Program—R & D Components for funding the review.
This article is distributed under the terms of the Creative Commons Attribution Noncommercial License which permits any noncommercial use, distribution, and reproduction in any medium, provided the original author(s) and source are credited.
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