Grasslands provide grass and fodder to sustain the growing need for ruminant meat and milk. Soil nutrients in grasslands are removed through withdrawal in these livestock products and through animal manure that originates from grasslands and is spread in croplands. This leads to loss of soil fertility, because globally most grasslands receive no mineral fertilizer. Here we show that phosphorus (P) inputs (mineral and organic) in global grasslands will have to increase more than fourfold in 2050 relative to 2005 to achieve an anticipated 80% increase in grass production (for milk and meat), while maintaining the soil P status. Combined with requirements for cropland, we estimate that mineral P fertilizer use must double by 2050 to sustain future crop and grassland production. Our findings point to the need to better understand the role of grasslands and their soil P status and their importance for global food security.
Global food demand will rise rapidly in the coming decades1,2,3. In particular, meat and milk consumption are projected to increase markedly due to rising incomes and decreasing prices3,4,5,6,7, especially in developing countries8. The global area of permanent grassland (3.3 billion hectares)9 covers 26% of the Earth’s ice-free land, and provides an important contribution to global food security by supplying proteins and energy to ruminants. Between 1970 and 2005 the world’s grasslands expanded by about 4%. Grassland degradation is likely to accelerate given the expected growth of livestock production10, overgrazing and consequent soil erosion, nutrient deficiency, weed encroachment and desertification.
Sustainably meeting global food demand is one of humanity’s grand challenges11, and P is increasingly considered to be a new global sustainability issue because of its finite reserves12. Like nitrogen, P is a major limiting nutrient in agriculture13,14 and is removed from arable and grassland soils by crop and grass withdrawals and erosion. Soil P removed in the harvest needs to be replaced by weathering and inputs through organic (mostly manure) and mineral fertilizers to sustain crop and grass production15,16.
Most global studies on the agricultural P cycle focus on arable land17,18,19,20. However, we are not aware of any global study addressing the P cycle in grasslands and its connection with croplands. In this paper we assess grassland P budgets between 1970 and 2005, as well as P requirements to sustain projected future grass production. We consider soil P budgets to assess changes in soil fertility, and the budget for the grassland system to assess the P exchange between grasslands and croplands (Fig. 1). The classification of livestock production systems (intensive and pastoral) and grassland systems is shown in Supplementary Fig. 1.
This study focuses on P, but it is evident that nutrient management will have to consider all nutrient requirements in grazing systems, including nitrogen, potassium and many other (micro-) nutrients.
Our general conceptual framework for P budgeting in grasslands focuses on grazing systems including the key P inflows and outflows of four compartments within the grassland system boundary: grassland-based livestock population, grassland-based livestock manure, soil (including weathering) and grass (Fig. 1). Our calculations include all countries of the world. We distinguished two categories of grasslands, that is, those occurring in mixed (and landless) livestock production systems (denoted as intensive systems) and those in pastoral systems. The difference between intensive and pastoral systems is in the P exchange between grassland and croplands through feed and manure. Most pastoral systems are in developing countries, and typically there is little exchange of nutrients between these pastoral systems and croplands (little feed import or manure export). However, there is P withdrawal in the various products (milk, meat, wool, skin and so on). The intensive ruminant systems are mixed, that is, they rely on grass, often supplemented with feed produced in croplands, and part of the manure produced in these systems is collected (in ‘kraal’ or animal houses) and spread in the backyard farms or croplands. Where P in manure exported from grassland thus exceeds the P in feed, there is net P transfer from grassland to cropland. The pastoral systems are extensive everywhere and generally located in dry or cold climates in remote regions away from human populations and croplands. In contrast, the intensive (mixed) systems generally feature in more favourable climates, but their productivity varies from country to country; in industrialized countries they are generally intensive with high productivity of grasslands and animals and large feed requirements, and they are less intensive in developing countries (with limited feed use, often low-quality feed such as crop residues, and relatively low grass and animal productivity).
Using the Dynamic Phosphorus Pool Simulator (DPPS)15 model we simulated historical P uptake in grasslands and then calculated the amount of P needed for meeting the global grass requirement in intensive and pastoral systems until 2050 according to the Rio+20 scenario, avoiding soil P deficits and surpluses21. This research is the first study that estimates soil P budgets in grasslands at the global scale and hence allows the assessment of total future P requirements of agriculture. The P budget of the grassland system was found to be negative between 1970 and 2005 in most of the world regions. Thus, to meet anticipated growth of ruminant production and associated grass requirement, the nutrient status of grassland soils needs to be improved to increase productivity of existing grasslands and to avoid expansion of grassland areas. We estimate that P inputs (mineral and organic) will have to increase more than fourfold in 2050 (relative to 2005) to meet the projected demand for ruminant products as targeted in the Rio+20 (ref. 21) scenario for 2050.
Agronomic soil P budget
Historical data show that soil P uptake by grass in intensive and pastoral grazing systems exceeded P application (input) through fertilizer and manure in most parts of the world (Fig. 2). Both uptake and applications were relatively low during the period 1970–2005 in most regions of the world (≈5 kg ha−1 per year or less) in contrast to the more intensive grazing systems of Western and Eastern Europe (Fig. 2). Specifics for the intensive and pastoral systems are shown in Supplementary Figs 2 and 3, respectively.
Between 1970 and 2005 cumulative inputs of P in Eastern Europe (38 Tg P; Tg=teragram=1012 g) and Western Europe (56 Tg P) were slightly larger than the cumulative grass uptake of 34 and 49 Tg P, respectively; North America and Oceania had a balanced P budget. By contrast, cumulative soil P uptake by grass in Africa (76 Tg P), Asia (191 Tg P) and Latin America (96 Tg P) exceeded P inputs, particularly in Asia (65, 72 and 82 Tg P, respectively) over the same period (calculations are based on Fig. 2 and grassland area shown in Table 1).
Manure was the most important input of P for grassland soils worldwide and mineral fertilizer P application was systematically much smaller than P in manure in all world regions (Table 1). During the 1970–2005 period only 23 Tg of mineral fertilizer P was applied to global grassland soils, which is similar to the global use of mineral P fertilizers in croplands of 18.5 Tg P in just the single year of 2010 (ref. 22). Europe alone accounted for almost 80% of the global cumulative mineral P fertilizer use in grassland.
Grassland system P budget
Manure P excretion is an input in the soil P budget (Fig. 1), but in the grassland system it is in fact partly an internal cycling of P, as it partly originates from grass P uptake from the soil. Manure P application from non-ruminants (external manure), fertilizer P, atmospheric P deposition and P in imported feed are considered grassland system P inputs and manure P exported from grassland to cropland, P that leaves grasslands via livestock products, P in the other use of manure (for non-agricultural purposes) and erosion are included as grassland system P outputs.
The total P budget of the grassland system was negative in 1970 and 2005 in most of the regions; only Eastern Europe and Oceania had (small) P surpluses (Table 1). Globally, grassland systems received an estimated 125 Tg of P (from external manure, mineral P, atmospheric deposition and feed) between 1970 and 2005. Over the same period, estimated global cumulative P outputs (P in manure exported to cropland, livestock products, the other use of manure and erosion) were 264 Tg P, which caused a negative P budget of −139 Tg for grassland systems between 1970 and 2005.
Phosphorus transfers between grasslands and croplands
Two flows are involved in the P transfers between grassland and cropland systems, that is, ‘Livestock feed (from croplands)’ and ‘Spreading (of manure) in croplands’ (Figs 1 and 3). On the one hand, grassland-based ruminants consume feed produced in croplands, which effectively imports P into the grassland systems. On the other hand, P is effectively transferred from grasslands to croplands when manure from ruminants is used as organic fertilizer in the latter systems.
Feed use varied between different world regions (Fig. 4). Africa and Oceania had a maximum rate of feed use of only 0.1 kg P per ha per year in 2005 (Table 1), while Western Europe’s feed use (4 kg P per ha per year) was around seven times the global rate (0.6 kg P per ha per year) in 2005 (Table 1 and Fig. 4a). The feed P import to the grassland systems in Asia and Latin America remained minimal at 0.7 and 0.2 kg P per ha per year, respectively, in 2005. North America’s feed input rate was 1.9 kg P per ha per year in 2005 (Table 1 and Fig. 4).
North America (with 14.5 Tg), Asia (13.3 Tg), Eastern Europe (11.7 Tg) and Western Europe (8.2 Tg) were responsible for about 90% of cumulative global feed use (53.4 Tg) in 1970–2005. In contrast, the imported P from croplands to grassland (as livestock feed) in Latin America (3.4 Tg), Africa (2.1 Tg) and Oceania (0.4 Tg) accounted for only 10% of the global total (1970–2005).
In 1970, the application of manure to cropland soils varied from 0.1 kg P per ha per year in Oceania to 4.5 kg P per ha per year in Western Europe (Table 1 and Fig. 4g,h). The maximum manure P export to croplands occurred in 1980 in Western Europe (4.9 kg P per ha per year) followed by Eastern Europe (3.7 kg P per ha per year). The other world regions reached rates of only 1.8 kg P per ha per year (Asia) and 1.7 kg P per ha per year (North America) or less in 2005. Cumulative global use of manure as fertilizer in croplands for the 1970–2005 period was 113 Tg of P. Asia alone was responsible for 44% of the global number, with a total of 50 Tg P. Africa (11.7 Tg P), Eastern (11.3) and Western Europe (11.5) had an almost equal share in the global P export from grassland to cropland (≈10% each). Cumulative transfer of P to cropland (1970–2005) was only 1.7 Tg in Oceania, 14.3 Tg in Latin America and 12.6 Tg in North America.
Historical trends of annual P feed imports to grasslands and manure exports from grasslands to croplands for the intensive grassland system for the period 1970–2005 are shown in Supplementary Fig. 4.
Future demand of P in grassland
We used the DPPS model15 to estimate P application rates (mineral fertilizer and manure) needed to achieve projected future grass production under the Rio+20 scenario21. Rio+20 projects a substantial increase in required global grass production and P uptake between 2005 and 2050 from 4.6 to 8.3 kg per P per ha due to the rapid increase in global ruminant meat and milk consumption and production (Fig. 5). This increase in grass production can come from either expansion of grasslands or enhanced productivity. Here we assume no expansion of the grassland area, so raising grass production will only be possible if the P status of soils under grassland is improved. With this assumption, the DPPS model estimates that to achieve the 2050 target grass production, 375 kg P per ha is required between 2006 and 2050, resulting in a cumulative global P requirement of 1,220 Tg (Fig. 5). According to the Rio+20 scenario, 650 Tg of this cumulative P input can be supplied through manure. To achieve the target grass production and P uptake until 2050 and assuming no expansion of grasslands, the rest of the required cumulative P input (570 Tg) needs to come from mineral P fertilizer. The 2.5–97.5 percentiles of the required P uptake in global grasslands under the Rio+20 scenario are, respectively, 810 and 1,500 Tg, for the period 2006–2050.
This paper presents the first estimates of global and regional soil P budgets in grasslands. In terms of production, mixed and landless systems are dominant for all ruminants (73% of beef, 92% of milk, 65% of mutton and goat meat and nearly all monogastrics production); however, in terms of area usage, the pastoral systems are covering more than 80% of the global grassland area23. Although the contribution of grass to total dry matter intake by all animals is projected to decrease from 50 to 45% between 2005 and 2050 (Rio+20 data), the total amount of grass needed for the increased livestock production will increase substantially. Assuming no area expansion, this means that grasslands will need improved nutrient management, with inputs of P in balance with N and other nutrients.
The share and absolute amounts of P in manure transferred from grassland to croplands are much larger for intensive than for pastoral grassland systems (Table 2). The estimated cumulative global use of manure originating from grassland to fertilize croplands during the 1970–2005 period was 113 Tg of P, Asia alone being responsible for 44%. For instance in China, the grazing system was confronted with a severe P deficit problem due to the massive transfers of P in the form of manure, while grasslands were hardly fertilized24,25. North America and Eastern Europe were the only regions that showed a cumulative net P transfer from cropland to grasslands, that is, 1.9 and 0.4 Tg P, respectively (calculated from Fig. 4). Our estimations for the different P flows generally show a fair agreement with values reported in the literature.
P in ruminant meat and milk represents a small amount compared with P in the manure, reflecting the low P conversion efficiency in ruminant systems. Although soil stocks of P in grasslands are substantial26, there is a systematic loss of soil fertility through export in manure to cropland that may aggravate current rates of soil degradation across most of the global grasslands. More grass production can be achieved, while avoiding grassland expansion and deforestation, through mineral P fertilization (and maintaining a balance between nitrogen, P and potassium13,27), adequate management of livestock and manure, and soil conservation to control P loss through erosion. More ruminant production in intensive systems based on crop feed concentrates, or less manure transfer from grasslands to croplands, will both require more P use in the world’s croplands.
Our estimate of the global P input required in grasslands of 1,220 Tg P for the 2005–2050 period includes P from both mineral fertilizer and animal manure. In 2050, globally 24 Tg per year of mineral P fertilizer will be needed to avoid loss of soil fertility and declining grassland productivity. Sattari et al.15 estimated that to increase crop production by 55% (this is the estimation based on the Global Orchestration scenario of the Millennium Ecosystem Assessment (MEA)28) in 2050 relative to 2005, P from mineral and organic fertilizer has to increase by only 20% due to the so-called residual soil P effect. Thus, excluding the share of manure P (32%) from the total required P, the estimated global mineral fertilizer P requirement in croplands was 20.8 Tg per year in 2050 (ref. 15). This indicates significant opportunities to increase crop production, with less than proportional increases of P use and associated environmental impacts. By contrast, we estimate here that to realize an anticipated 80% increase in grassland production (for milk and meat), the P input from fertilizer (mineral and organic) will have to increase fourfold. Thus, the amount of mineral fertilizer P needed in cropland and grassland systems in total is estimated to be 45 Tg per year in 2050, corresponding to 350 Tg phosphate rock. For the entire agricultural system (crop and grass production), we estimate that relative to 2005 mineral P fertilization needs to more than double by 2050. In the next four decades, a global cumulative amount of mineral fertilizer P of 1,390 Tg is required, accounting for 820 Tg P for cropland soils15 (2008–2050) and 570 Tg P for grassland soils (2005–2050), to achieve the projected global food production in 2050. This implies that up to 2050, 10,700 Tg of phosphate rock will need to be mined across the globe to produce the P fertilizer for the agricultural and food production sectors.
Livestock grazing systems are far more complex than crop production systems, and the available data on grass production are scarce (see Methods section). For example, Food and Agricultural Organization provides livestock production, animal stocks, numbers of slaughtered animals and milking cows, carcass weights and milk yield per animal22, but lacks data on the age distributions of animals and more importantly, data on grass production and management and grass withdrawal by grazing and mowing. Similarly, most national statistics lack such data29,30. Our sensitivity analysis revealed that the global model results for the total grazing system are strongly sensitive to animal stocks, excretion rates and the initial labile and stable soil P pools, which are known to be uncertain31 (Supplementary Table 8). Yet, our modelling results and data analysis suggest that negative P budgets in the world’s grassland soils can be an obstacle when intensifying grassland production. This comprehensive analysis underlines the necessity to adopt nutrient management strategies, balancing P, nitrogen and other nutrients for croplands and grasslands. It also shows the urgent need for empirical data on grass production, fertilization and nutrient withdrawal.
We coupled two models in our study, that is, the soil P budget model (Fig. 1) and the DPPS model, to reproduce the soil P budget for the 1970–2005 period and to estimate future P requirements in grasslands. The soil P budget model considers two system boundaries: the grassland system boundary and the grassland soil boundary. Phosphorus is leaving the grassland systems’ boundary via animal products (mainly meat and milk), livestock manure and runoff or erosion. On the other hand there is P import from cropland into grassland through animal feed.
Within the grassland soil boundary, we distinguish different sources of soil P inputs, including manure generated inside the grasslands and spread in the grasslands (grassland-based, internal, livestock manure; Fig. 1), manure produced by pigs and poultry outside the grassland boundaries (non-grassland-based, external, livestock manure; Fig. 1), mineral P fertilizer (only in intensive livestock production systems, see section below) and P from weathering and atmospheric deposition. Grass P uptake, runoff and erosion are regarded as P outflows from the grassland soil (Fig. 1). Manure generated within the grassland boundaries is assigned to three uses: spreading in grassland soil, spreading in croplands and other uses of manure. The net transfer of P between croplands and grasslands over the period 1970–2005 is the difference between P imported to grassland from cropland through livestock feed, and P export from grassland to cropland in the form of manure (Fig. 1 and Supplementary Fig. 1). The DPPS model is presented in detail below.
All abbreviations used in the soil P budget model are explained in Table 3, and Table 4 describes the P flows, the animal categories and the data sources. The data used in this paper as well as the DPPS model are available on: http://models.pps.wur.nl/content/DPPS-Grassland.
Livestock production systems and animal groups
In their global classification, Seré and Steinfeld32 distinguished livestock production systems (LPSs) and mixed farming production systems (MPS). LPS includes systems in which more than 90% of dry matter fed to animals comes from rangelands, pastures, annual forages and purchased feed. MPS are systems in which more than 10% of the dry matter fed to animals comes from crop by-products or stubble, or more than 10% of the total value of production comes from non-livestock farming activities32. They further distinguished four subgroups: landless LPS; grassland LPS; rainfed MPS and irrigated MPS (Supplementary Fig. 1a). They collected data on buffaloes, cattle, goats, pigs, poultry and sheep population numbers and meat and milk production in each system. Later, Bouwman et al.23 modified the classification from Seré and Steinfeld32 for their global analysis of ruminant production systems. Landless LPS and MPS were merged into mixed-landless systems (or intensive systems) while grassland LPS was renamed into pastoral systems (Supplementary Fig. 1b,c).
Following Bouwman et al.23, in the present study also two production systems were distinguished, that is, grasslands in mixed and landless (referred to as intensive hereafter) and extensive pastoral LPSs. Within each system, two groups of animals were considered: ‘grassland-based livestock’ including asses, buffaloes, camels, dairy cattle, horses, mules, non-dairy cattle, sheep and goats, and ‘non-grassland-based livestock’ including pigs and poultry (Fig. 3). Owing to lack of data, it was not possible to include all animal categories for all the calculations (Table 4). Furthermore, non-grassland-based livestock categories were not included in products’ P flow calculations since in our definition they are not located within the grassland system boundaries (Fig. 1).
The P flows considered for different animal categories and their data sources are listed in Table 4. Phosphorus inflows to the grasslands comprise feed, P fertilizer, external manure P and atmospheric deposition; P outflows from grasslands boundaries include P in livestock products, exported manure to croplands, other use of manure P and P in runoff or erosion.
Long-term livestock production data (meat and milk) were obtained from the Integrated Model to Assess the Global Environment (IMAGE)33, which is based on FAOSTAT22 data; the average P content of meat and milk and various animal parts was obtained from the literature23.
The animal stocks within pastoral and intensive livestock production systems and their P excretion rates were used to calculate the total P in manure within the two systems (see section on livestock manure P).
The amount of feed for each country, year and animal category was estimated based on IMAGE33 output data and on the use of grass and feed crops and energy requirements of the different animal categories).
The total mineral P applications to grasslands in mixed and landless livestock production systems for 1970–2005 were from IMAGE at the country scale, based on FAOSTAT and the International Fertilizer Association34,35).
Weathering and atmospheric deposition as P inflows to grasslands and soil P erosion and runoff as P outflows were estimated from literature review and IMAGE output data. The sections below provide more details on the methods and data used for the various model components.
Livestock production data include milk, meat and livestock by-products. Livestock by-products include adipose tissue, skeleton, viscera, blood, skin, hair and digestive content. Country-scale meat production data for non-dairy cattle and sheep and goats, as well as milk production were obtained from FAOSTAT22. Meat and milk production for buffaloes, horses, asses, mules and camels was not included due to lack of data. The total amount of P in livestock products is the sum over P in milk, meat and livestock by-products.
The carcass weight is the most common way of expressing livestock meat production. Carcass weight is defined as the weight left after slaughter and removal of head, skin, genitourinary organs and offals. The ratio between the carcass weight and the live weight is called the dressing percentage (DP). Live weight consists of the following fractions: muscles; adipose tissue; skeleton; viscera; blood; skin; hair; and digestive content. Live weight partitioning allows for a more accurate P accounting due to large differences in P concentration in different fractions such as bones and blood.
To allocate the total national production to mixed-landless and pastoral systems, national, annual values of the fraction allocated to mixed-landless systems (Fraction intensive) were obtained from IMAGE33. A list of countries and regions as used in the present study based on IMAGE has been shown in Supplementary Table 1.
In addition, data on DPs were obtained from Kempster et al.36, who reported 53 and 50% DP for, respectively, non-dairy cattle and for sheep and goats. Live weight partitioning fraction (LWF) data and P content of those fractions were obtained from different sources (Supplementary Table 2).
Equation (1) was used to calculate P in meat and livestock by-products:
where y denotes year, c country, s production system, a animal category and i, fraction of meat and by-products.
Phosphorus in meat and livestock by-products is denoted by PLMe (kg P). LPD and DP refer to the livestock production data (kg carcass weight) and DP (kg carcass per kg live weight), respectively. LWF (kg meat or livestock by-products per kg live weight) represents live weight partitioning and FPC refers to P content (kg P per kg meat or livestock by-products).
The total amount of P in milk was calculated by multiplying the total amount of milk production with the P content of milk, as shown in equation (2). The P content was considered to be 8.4·10−4 kg P per kg milk30.
where y denotes year, c country and s production systems.
Phosphorus in milk is expressed by PLMi (kg P). MPD and MPC refer to the milk production data (kg milk) and milk phosphorus content (kg P per kg milk), respectively.
Livestock manure phosphorus
Total manure production within pastoral and intensive systems was computed from animal stocks and P excretion rates. We used P excretion rates per head for dairy and non-dairy cattle, buffaloes, sheep and goats, pigs, poultry, horses, asses, mules and camels based on various sources37,38,39,40,41 (Supplementary Table 3). We used constant excretion rates per head; in case of increasing production per head, fewer animals are needed to produce the same amount of meat or milk; total P excretion will thus decrease, and the excretion per unit of product decreases reflecting increasing conversion efficiency due to improved feeding and management. For each country, animal stocks and P in the manure for each animal category were spatially allocated across intensive and pastoral systems. For the time period 2005–2050, the distribution over these systems is provided by the Rio+20 study21.
The methodology and equations described in this section were applied to all animal categories.
The manure allocation comprises five steps: a first calculation of total excreted manure and its P content and a subsequent fractioning into four different flows (Fig. 3).
The total amount of manure P was calculated according to equation (3).
where y denotes year, c country, s production systems and a animal category).
‘Manure’ refers to the total P in manure excreted by livestock (kg P); LPN is livestock population (number of heads); ‘Excretion rate’ is the annual amount of P excreted for each animal category (kg P per head per year). The sum of manure for grassland-based animal categories (cattle, buffaloes, sheep, goats, camels, horses and asses) corresponds to the ‘Livestock excretion flow’ depicted in Fig. 1.
The amount of P (kg) in manure used for non-agricultural purposes (other uses) was calculated according to equation (4).
‘FrOthers’ expresses the fraction of manure used in any way so that it is effectively removed from agricultural systems, as it could be used as fuel or building material, or digested for generating energy.
From the remaining manure, the amount of P (kg) in the manure allocated to grazing was estimated by equation (5).
‘FrGrazing’ refers to the fraction of manure that is deposited in grasslands by grassland-based grazing animals. In the case of non-grassland-based species, it represents their deposition as they scavenge in grasslands.
The rest of the manure P was considered to be excreted in animal houses and stored, and available for use as organic fertilizer either in grasslands or croplands. Two fractions were calculated, ‘Grasslands’ and ‘Croplands’ as shown in equations (6) and (7), respectively.
‘FrGrass’ refers to the fraction of stored manure that is applied in grasslands as organic fertilizer.
The amount of P (kg) in the manure that is transferred from animal houses or stored manure to cropland as fertilizer was estimated by equation (7).
The sum of ‘Grazing’ and ‘Grasslands’ for grassland-based and non-grassland-based species corresponds to the internal and external manure input flows, respectively, as depicted in Fig. 1.
The values for the manure allocation fractions (other uses, grazing and application to grasslands) are listed in Supplementary Table 4.
The IMAGE model33 used FAOSTAT data on crops for feed and energy requirements of animals to estimate the amount of feed for each country, year and animal category. Only the animal categories of non-dairy cattle, dairy cattle and sheep and goats were considered for estimating feed crop use. Thus, a 100% grass ration was assumed for the rest of grassland-based animal categories (buffaloes, horses, asses, mules and camels).
IMAGE provides feed data for 11 feed items: oil crops; maize; pulses; rice; root and tuber crops; temperate cereals; tropical cereals; crop residues; and other by-products such as residues from breweries, and grass and scavenging (such as road-side grazing, food waste and so on). FAOSTAT provides data on the amount of feed crop use per country, but does not specify feed use by animal category. In IMAGE the specification of feed crop use for individual animal categories is based on feed rations that are calibrated to match FAOSTAT data on total feed use at the scale of world regions. Therefore, disaggregation of world-region feed crop use by animal category to the country scale was needed. To do so, it was assumed for each animal category that the fraction of feed crops in the ration is proportional to livestock productivity. The total amount of feed crops available for a specific animal category within a world region was thus allocated on the basis of the productivity of the animal category considered in a specific country relative to the regional productivity. Country and regional productivity were calculated for each animal category as the country and regional amount of product divided by the country and regional animal numbers, respectively. Since this calculation was done for each animal category, productivity numbers were expressed in terms of kg of carcass weight per head (for non-dairy and sheep and goats) or kg milk per head (for dairy cattle). Then, for each country the ratio between its productivity over the regional productivity was computed, which yielded a weighing factor (first term of equation (8)). With the information on the regional feed amount and the animal numbers, the regional average feed intake was calculated for each feed item and animal category. The total amount of P for each feed item for a specific animal category within a certain country was thus the product of the weighting factor times the country’s animal numbers times the regional average feed intake times the P content of the feed item. By adding up all the feed items and animal categories, the country total P amount in livestock feed crops was calculated.
where y denotes year, c country, s production systems, a animal category, f feed item and R regional data).
PFE (kg P) is total amount of P in livestock feed. LPR refers to the livestock productivity (kg per head). It is calculated as the total amount of products associated with the animal category (carcass weight or milk) over the total number of animals. LPN refers to the animal numbers and the total amount of feed item used in a certain region as presented by FEED (kg). PFI (kg P per kg feed item) is the P content for a given feed item.
It is clear that part of the P in feed used in grassland-based systems is imported from other countries. Owing to lack of data we ignore feed trade, but in regions such as Western Europe, P in feed produced in croplands in other world regions may be a significant part of total feed use. However, this does not affect the global budget of the grassland-based systems, but may lead to overestimation of the net transfer from cropland to grassland within feed importing countries.
Livestock grass intake and grass P uptake
The estimation of grass uptake (and grass intake by animals) is based on a mass balance approach. At the animal level, P inputs (feed plus grass intake) equal the P outputs (manure plus products). Phosphorus in the livestock grass intake was assumed to be equal to grass P uptake from the soil. Thus, this approach ignores any P losses during mowing, transporting or stall-feeding of grass. The grass P uptake was calculated according to equation (9). The amount of feed (PFE) and products (PLMe and PLMi) were assumed to be zero for buffaloes, horses, asses, mules and camels. For these animal categories the amount of P in grass intake equals the excretion of P.
where y denotes year, c country and s production systems.
PGU (kg P) is the total grass phosphorus uptake and PFE (kg P) refers to the total amount of phosphorus (kg) in livestock feed.
Mineral phosphorus fertilization
The IMAGE data include the total use of mineral phosphorus fertilizers in grasslands for 1950, 1970, 1980, 1990, 1995, 2000 and 2005 at country level. The values are based on FAOSTAT22 and the International Fertilizer Industry Association34,35 for the period 1970–2000, and extrapolations for earlier and later years4,21. Those numbers were exclusively allocated to the mixed and landless production systems, as we assumed no use of mineral fertilizer in pastoral systems.
Soil phosphorus erosion
Soil P loss estimates were based on a recent modelling approach, which distinguishes two nutrient loss pathways to estimate P runoff and erosion42, that is, losses from recent nutrient applications (Prec) in the form of fertilizer, manure or organic matter43, and a residual or ‘memory’ (Pmem) effect related to long-term historical changes in soil nutrient stocks for the top 30 cm (refs 44, 45). The approach presented by Cerdan et al.46 based on a large database of measurements was used as a basis for calculating Pmem based on slope, soil texture and land cover type. This approach yields an average soil loss of 40 tonnes of soil per km2 year for Europe46.
Prec was calculated from P inputs and depends on slope (using the approach of Bogena et al.47) and was further modified by land use and soil texture, that is, those factors that reduce surface runoff according to Velthof et al.48,49
The initial P stock in the top 30 cm was taken from Yang et al.50 for the year 1900, and residual soil P was calculated from the soil P budget up till the year 2005 (ref. 42). All inputs and outputs of the soil balance were assumed to occur in the top 30 cm; the soil budget model replaces P enriched or depleted soil material lost at the surface by erosion with fresh soil material (with the initial soil P content) at the bottom.
Simulated cumulative P loss amounted to 33 Tg P over the 1970–2005 period, which is about 1 Tg P per year or on average 30 kg P per km2 per year. For a mean P content of soils of 0.5 kg per tonne of soil51,52 this means a soil loss of 60 ton km−2, which exceeds the European estimates by 50% due to larger erosivity of grasslands in especially tropical and (semi-)arid climates.
Estimates of erosion rates are uncertain. Erosion rates in overgrazed grasslands have been estimated to amount to 1,500 t of soil per km2 per year52,53. Such rates may locally be possible, but as a global average they seem unrealistic as they exceed the European average erosion rates of 40 t of soil per km2 per year46 by a factor of 40.
Weathering and atmospheric deposition
On the basis of the ratio of cropland area to world total land areas, Liu et al.52 calculated the amount of weathering and atmospheric deposition on croplands. Employing the same approach, we have estimated about 4.0 Tg P per year as weathering and atmospheric deposition in grasslands.
Scenario for the period 2006–2050
There are different global scenarios, such as from the Organization for Economic Cooperation and Development54, MEA28, IPCC-SRES55 and Rio+20 (ref. 21). For this study, we needed scenarios that focus on nutrients and included future food demand, production and the nutrient uptake. Particularly future production and consequently P uptake was needed as a target for selecting the appropriate scenarios. A few recent examples of scenarios that included projections of nutrient uptake are the MEA28 and more recently the Rio+20 (ref. 21) scenarios.
Future demand of P fertilizer in global croplands was calculated based on the target crop yields, given by four different MEA scenarios for 2050 (ref. 15).
Recently, van Vuuren et al.21 developed new pathways (Rio+20) to achieve global sustainability goals for food, land and biodiversity, as well as for energy and climate by 2050. The Rio+20 study describes four scenarios, that is, the Trend scenario and three challenge pathways. The Trend scenario describes possible trends in the absence of climate and sustainability policies. The three challenge pathways were designed to assess the potential to achieve sustainability goals.
We used the Rio+20 (ref. 21) Trend scenario for simulating future P requirement in grasslands. Baseline scenarios represent a continuation of current trends, with no marked changes or shifts in production and management systems, attitude towards environmental problems and so on. The Rio+20 Trend scenario is a baseline or business-as-usual scenario, and comparable with the baseline scenario of the Environmental Outlook of the Organization for Economic Cooperation and Development54, the Global Orchestration scenario of the MEA28 and the A1 scenario of IPCC-SRES55.
DPPS model description
DPPS is a simple two-pool P-model56 including labile and stable soil pools and long-term P input and output data15. The DPPS model reproduces historical grass uptake as a function of P inputs (fertilizer and manure).
P inputs are allocated to two dynamic P pools, namely the stable (PS; 20%) and the labile P pools (PL; 80%). The model simulates the P transfers between the pools, the uptake of P by the grass and the size of both pools. To calculate the dynamics of P in these two pools, two differential equations are used:
The rates of P transfer from PL to PS and vice versa are denoted by μLS and μSL, respectively (per year). The coefficient ρ refers to the total P input (mineral fertilizer and manure). The coefficients f and 1−f refer to the fraction of ρ that transfers to PL and PS, respectively. Coefficient α represents the grass P uptake fraction from PL. Parameters ω and δ are weathering and deposition inputs to PL and PS, respectively. The parameter stands for soil P erosion-runoff outflow from PL. A large μLS makes PL less available for plant uptake and a large μSL indicates that the stable pool acts as a buffer that replenishes the labile pool.
This model considers the essential P fluxes between grass and soil with a yearly time step. It can calculate P transfer between the labile and stable soil P pools, the P uptake by grass and the pool sizes. The model can also be formulated in a target-oriented approach57, in which the (future) P uptake is a model input and the required P application a result assuming no change in grassland area.
The DPPS model successfully simulated the historical patterns of crop P uptake as a response to the application rates in all continents and the entire globe as shown by Sattari et al.15 In the present paper, the model was used to calculate future P fertilizer and manure application rates in grasslands based on target grass productions in 2050 derived from the Rio+20 Trend (baseline) scenarios21. For more details of the model see Sattari et al.15 and Wolf et al.56
Comparing the results with other studies
The estimates of global P budgets of grassland soils and P transfers between grasslands and croplands are compared in Supplementary Table 5, with those reported by other authors. Although it is not easy to compare all results obtained in this study with those in other studies, due to differences in approaches, system boundaries and the scope, a comparison of selected flows calculated here at country level with other studies is possible (Supplementary Table 5). Frequently, in literature larger values than the ones reported here are found, primarily due to inclusion of pigs and poultry, while in our study only ruminants are considered.
The sensitivity of the results to 26-model parameters was investigated for 6 output variables for the soil P budget model, and the sensitivity of two output variables of the DPPS model to variation of 13 model parameters was investigated. These output variables represent global results for P uptake by grass (Supplementary Table 6). To limit computational load in the sensitivity analysis, the Latin Hypercube Sampling (LHS) technique58 was used. LHS offers a stratified sampling method for the separate input parameters, based on subdividing the range of each of the k parameters into disjunct equiprobable intervals based on a uniform distribution. The intervals were selected on the basis of earlier analysis of the livestock system. By sampling one value in each of the N intervals according to the associated distribution in this interval, we obtained N sampled values for each parameter. The number of runs N was 500 for the soil budget model and for the DPPS model.
The sampled values for the first model parameter are randomly paired to the samples of the second parameter, and these pairs are subsequently randomly combined with the samples of the third source and so on. This results in an LHS consisting of N combinations of k parameters. The parameter space is thus representatively sampled with a limited number of samples.
LHS can be used in combination with linear regression to quantify the uncertainty contributions of the input parameters to the model outputs58,59. The output Y considered (see columns in Supplementary Tables 7 and 8) is approximated by a linear function of the parameters Xi expressed by
where βi is the so-called ordinary regression coefficient and e is the error of the approximation. The quality of the regression model is expressed by the coefficient of determination (R2), representing the amount of variation Y explained by Y−e. Since βi depends on the scale and dimension of Xi, we used the standardized regression coefficient (SRC), which is a relative sensitivity measure obtained by rescaling the regression equation on the basis of the s.d.’s σY and :
SRCi can take values in the interval [−1, 1]. SRC is the relative change ΔY/σY of Y due to the relative change ΔXi/ of the parameter Xi considered (both with respect to their s.d. σ). Hence, SRCi is independent of the units, scale and size of the parameters. A positive SRCi value indicates that increasing a parameter value will cause an increase in the calculated model output, while a negative value indicates a decrease in the output considered caused by a parameter increase.
The sum of squares of SRCi values of all parameters equals the coefficient of determination (R2), which for a perfect fit equals 1. Hence, SRCi2/R2 yields the contribution of parameter Xi to Y. For example, a parameter Xi with SRCi=0.1 adds 0.01 or 1% to Y in case R2 equals 1.
Here we discuss the SRC for 26 parameters in the soil P budget model (Supplementary Table 7) and 13 parameters in the DPPS model (Supplementary Table 8). We focus on significant SRC values exceeding 0.2, which we consider to be an important influence on the model sensitivity or an important parameter (that is, a contribution of 0.22=0.04 or about 4% to the variation of global results). Results for a similar analysis on the regional or smaller scale or different year would yield different results, depending on the P balances and local production system.
Soil budget model
The fraction of the livestock production in mixed and industrial systems (FrProdint) is very important for both P uptake in 2005 and cumulative P uptake for 1970 and 2005 in mixed respectively. pastoral systems, but not in the aggregated livestock system (Supplementary Table 7). Excretion rates and the number of animals (LPN) are important for uptake in 2005 and cumulative uptake, in each system (mixed and pastoral) and in the aggregated livestock system.
The manure deposited in grasslands, the amount that is diverted outside agricultural systems and the manure used as organic fertilizer in grasslands (represented by ‘FrGrazing’, ‘FrOthers’ and ‘FrGrass’, respectively) are not significant and not important for the sensitivity of uptake and cumulative uptake.
The kg meat or by-products per kg live weight (LWF), the DP—the ratio live weight to carcass—and the P contents of the various body parts (FPC) are all important and significant for uptake in 2005 and cumulative uptake in mixed systems and the aggregated livestock system, and for uptake in 2005 in pastoral systems. The parameter LWF is the fraction of each animal ‘product’: meat; bones; blood; and so on. Therefore, when LWF increases, P in products and thus the extraction will be higher (SRC positive). Higher values of DP lead to a lower amount of P found in the (by) products and hence less uptake. Livestock production is not only used in equation (1) but also in the calculation of feed (equation (8)). The higher the production induces an increase of feed use, since it is linked to productivity. Therefore, the increase in feed can exceed the increase in the P in products leading to a decrease in uptake (since uptake=P in products+P in manure–P in feed).
Dynamic Phosphorus Pool Simulator
Median simulated P uptake of global grasslands in 2005 is 15 Tg, with a variation of 11.0–17.6 Tg (2.5 and 97.5 percentile) as a result of variation of all the parameters in Supplementary Table 8. The cumulative P uptake (1970–2005) is 374–598 Tg around the median of 510 Tg. UU0 (initial P uptake from unfertilized soil) and UF0 (initial P uptake from fertilized soil) are the most important parameters for the sensitivity of all 13 parameters tested. UU0, UF0, α and β are all fitting parameters used to achieve the values for the size of LP and SP in year 0 of the simulation. UU0 (SRC=0.44; indicating sensitivity of 20%) and UF0 (SRC=0.64, indicating sensitivity of 41%) have a strong influence on the cumulative uptake of the total livestock system, and a smaller influence on the sensitivity of the uptake in 2005. The coefficient Cu, the maximum fraction of crop P uptake from the labile pool is an important factor for the sensitivity of the cumulative uptake but has a smaller influence on the instantaneous uptake in 2005.
P input (ρ; manure plus mineral) has a stronger influence on the sensitivity of the instantaneous uptake in 2005 than on that of the cumulative uptake. This is due to depletion of the P in the two pools, which results in a strong and growing instantaneous effect of fertilizer, which is mostly flowing into the labile pool from which uptake occurs.
The time constant of P transfer from labile to stable pool, μLS, is more important for the uptake in 2005 and cumulative uptake than μSL, because the transfer from the labile to the stable pool is much faster, so variation of μLS has a much larger impact on uptake in 2005 and cumulative uptake than μSL. Sensitivity to erosion (ɛ) is not significant. This is related to the initialization of the model when the initial uptake is determined by tuning the size of the slow and labile soil P pools to achieve an equilibrium and initial uptake, after this initialization erosion is no longer important because its value is small and it is almost constant. Sensitivity to the weathering rate is significant, but with a small influence.
How to cite this article: Sattari, S. Z. et al. Negative global phosphorus budgets challenge sustainable intensification of grasslands. Nat. Commun. 7:10696 doi: 10.1038/ncomms10696 (2016).
Tilman, D., Cassman, K. G., Matson, P. A., Naylor, R. & Polasky, S. Agricultural sustainability and intensive production practices. Nature 418, 671–677 (2002).
Mueller, N. D. et al. Closing yield gaps through nutrient and water management. Nature 490, 254–257 (2012).
Tilman, D., Balzer, C., Hill, J. & Befort, B. L. Global food demand and the sustainable intensification of agriculture. Proc. Natl Acad. Sci. USA 108, 20260–20264 (2011).
Bouwman, A. F. et al. Exploring global changes in nitrogen and phosphorus cycles in agriculture induced by livestock production over the 1900–2050 period. Proc. Natl Acad. Sci. USA 110, 20882–20887 (2013).
Godfray, H. C. J. et al. Food security: the challenge of feeding 9 billion people. Science 327, 812 (2010).
Kastner, T., Rivas, M. J. I., Koch, W. & Nonhebel, S. Global changes in diets and the consequences for land requirements for food. Proc. Natl Acad. Sci. USA 109, 6868–6872 (2012).
Koning, N. B. J. et al. Long-term global availability of food: continued abundance or new scarcity? Neth. J. Agric. Sci. 55, 229–292 (2008).
Steinfeld, H. et al. Livestock’s Long Shadow—Environmental Issues and Options FAO (2006).
Foley, J. A. et al. Solutions for a cultivated planet. Nature 478, 337–342 (2011).
Suttie, J. M., Reynolds, S. G. & Batello, C. Grasslands of the World Food and Agriculture Organization (2005).
West, P. C. et al. Leverage points for improving global food security and the environment. Science 345, 325–328 (2014).
Cordell, D. & Neset, T.-S. Phosphorus vulnerability: a qualitative framework for assessing the vulnerability of national and regional food systems to the multi-dimensional stressors of phosphorus scarcity. Global Environ. Change 24, 108–122 (2014).
Sattari, S. Z., van Ittersum, M. K., Bouwman, A. F., Smit, A. L. & Janssen, B. H. Crop yield response to soil fertility and N, P, K inputs in different environments: testing and improving the QUEFTS model. Field Crops Res. 157, 35–46 (2014).
Syers, J. K., Johnston, A. E. & Curtin, D. Efficiency of Soil and Fertilizer Phosphorus Use: Reconciling Changing Concepts of Soil Phosphorus Behaviour with Agronomic Information 1–110Food and Agriculture Organization of the United Nations (2008).
Sattari, S. Z., Bouwman, A. F., Giller, K. E. & Van Ittersum, M. K. Residual soil phosphorus as the missing piece in the global phosphorus crisis puzzle. Proc. Natl Acad. Sci. USA 109, 6348–6353 (2012).
Vitousek, P. M. et al. Nutrient imbalances in agricultural development. Science 324, 1519–1520 (2009).
Cordell, D., Jackson, M. & White, S. Phosphorus flows through the Australian food system: identifying intervention points as a roadmap to phosphorus security. Environ. Sci. Policy 29, 87–102 (2013).
Cooper, J. & Carliell-Marquet, C. A substance flow analysis of phosphorus in the UK food production and consumption system. Resour. Conserv. Recycl. 74, 82–100 (2013).
Antikainen, R. et al. Stocks and flows of nitrogen and phosphorus in the Finnish food production and consumption system. Agric. Ecosyst. Environ. 107, 287–305 (2005).
MacDonald, G. K., Bennett, E. M. & Carpenter, S. R. Embodied phosphorus and the global connections of United States agriculture. Environ. Res. Lett. 7, 044024 (13PP) (2012).
van Vuuren, D., Bouwman, A. F. & Lyon, S. Roads from Rio+20: Pathways to Achieve Global Sustainability Goals by 2050—Summary and Main Findings to the Full Report PBL, Netherlands Environmental Assessment Agency (2012).
FAO. Production/Crops and Resource/Fertilizer. FAOSTAT database Collections Food and Agriculture Organization of the United Nations (2014) http://faostat.fao.org/.
Bouwman, A., Van der Hoek, K., Eickhout, B. & Soenario, I. Exploring changes in world ruminant production systems. Agric. Syst. 84, 121–153 (2005).
Chen, M., Chen, J. & Sun, F. Agricultural phosphorus flow and its environmental impacts in China. Sci. Total Environ. 405, 140–152 (2008).
Sattari, S. Z., van Ittersum, M. K., Giller, K. E., Zhang, F. & Bouwman, A. F. Key role of China and its agriculture in global sustainable phosphorus management. Environ. Res. Lett. 9, 054003 (2014).
Smil, V. Phosphorus in the environment: natural flows and human interferences. Annu. Rev. Energy Environ. 25, 25–53 (2000).
Janssen, B. H. Efficient use of nutrients: an art of balancing. Field Crops Res. 56, 197–201 (1998).
Alcamo, J., Van Vuuren, D. & Cramer, W. in Ecosystems and Human Well-being: Scenarios Vol. 2, eds Carpenter S.R., Pingali P.L., Bennett E.M., Zurek M.B. 279–354Island Press (2006).
Eurostat. European Commission. Your key to European Statistics, http://ec.europa.eu/eurostat . Accessed on March 2015.
USDA. National Agricultural Statistics Service. Quick Stats ftp://ftp.nass.usda.gov/quickstats/ (retrieved on 21 March 2015).
Yang, X., Post, W. M., Thornton, P. E. & Jain, A. The distribution of soil phosphorus for global biogeochemical modeling. Biogeosci. Discuss. 9, 16347–16380 (2012).
Seré, C. & Steinfeld, H. World Livestock Production Systems. Current Status, Issues and Trends Food and Agriculture Organization of the United Nations (1996).
Stehfest, E., Van Vuuren, D. P., Kram, T. & Bouwman, A. F. Integrated Assessment of Global Environmental Change with IMAGE 3.0. Model description and policy applications. 366 p. (PBL Netherlands Environmental Assessment Agency, also available as pdf from http://www.pbl.nl/en/publications/integrated-assessment-of-global-environmental-change-with-IMAGE-3.0 (2014).
FAO/IFA/IFDC. Fertilizer use by crop 4th edn Food and Agriculture Organization of the United Nations/International Fertilizer Industry Association/International Fertilizer Development Center (1999).
IFA/IFDC/FAO. Fertilizer Use by Crop 5th edn Food and Agriculture Organization of the United Nations (2003).
Kempster, T., Cuthbertson, A. & Harrington, G. Carcase Evaluation in Livestock Breeding, Production and Marketing Granada (1982).
Midwest Plan Service. Livestock Waste Facilities Handbook 2nd edn Iowa State University (1985).
Sheldrick, W., Syers, J. K. & Lingard, J. Contribution of livestock excreta to nutrient balances. Nutr. Cycling Agroecosyst. 66, 119–131 (2003).
Smith, L. W. in Handbook of Animal Science ed Putnam P. A. 280–291Academic (1991).
Van Horn, H. H., Newton, G. L. & Kunkle, W. E. Ruminant nutrition from an environmental perspective: factors affecting whole-farm nutrient balance. J. Anim. Sci. 74, 3082–3102 (1996).
Wilkerson, V. A., Mertens, D. R. & Casper, D. P. Prediction of excretion of manure and nitrogen by Holstein dairy cattle. J. Dairy Sci. 80, 3193–3204 (1997).
Beusen, A. H. W., Van Beek, L. P. H., Bouwman, A. F., Mogollón, J. M. & Middelburg, J. J. Coupling global models for hydrology and nutrient loading to simulate nitrogen and phosphorus retention in surface water. Description of IMAGE-GNM and analysis of performance. Geoscientific Model Development 8, 4045–4067 doi:4010.5194/gmd-4048-4045-2015 ( http://www.geosci-model-dev.net/4048/4045/2015/ ) (2015).
Hart, M. R., Quin, B. F. & Nguyen, M. L. Phosphorus runoff from agricultural land and direct fertilizer effects: A review. J. Environ. Qual. 33, 1954–1972 (2004).
McDowell, R. W. & Sharpley, A. N. Approximating phosphorus release from soils to surface runoff and subsurface drainage. J. Environ. Qual. 30, 508–520 (2001).
Tarkalson, D. D. & Mikkelsen, R. L. Runoff phosphorus losses as related to soil test phosphorus and degree of phosphorus saturation on Piedmont soils under conventional and no-tillage. Commun. Soil Sci. Plant Anal. 35, 2987–3007 (2004).
Cerdan, O. et al. Rates and spatial variations of soil erosion in Europe: a study based on erosion plot data. Geomorphology 122, 167–177 (2010).
Bogena, H., Kunkel, R., Schobel, T., Schrey, H. P. & Wendland, F. Distributed modeling of groundwater recharge at the macroscale. Ecol. Model. 187, 15–26 (2005).
Velthof, G. L. et al. Integrated assessment of nitrogen losses from agriculture in EU-27 using MITERRA-EUROPE. J. Environ. Qual. 38, 402–417 (2009).
Velthof, G. L., Oudendag, D. A. & Oenema, O. Development and Application of the Integrated Nitrogen Model MITERRA-EUROPE 102 (Alterra, Wageningen UR, The Netherlands; EuroCare, University of Bonn, Germany; ASG, Wageningen UR, The Netherlands, Wageningen, 2007).
Yang, Z., Post, W. M., Thornton, P. E. & Jain, A. The distribution of soil phosphorus for global biogeochemical modeling. Biogeosciences 10, 2525–2537 (2010).
Liu, Y. The Human Intensified Global Phosphorus Flows and Environmental Impacts. Report No. IR-06-081, 25 (International Institute for Applied Systems Analysis, Laxenburg, Austria (2006).
Liu, Y., Villalba, G., Ayres, R. U. & Schroder, H. Global phosphorus flows and environmental impacts from a consumption perspective. J. Ind. Ecol. 12, 229–247 (2008).
Liu, M., Yu, Z., Liu, Y. & Konijn, N. T. Fertilizer requirements for wheat and maize in China: the QUEFTS approach. Nutr. Cycling Agroecosyst. 74, 245–258 (2006).
OECD., OECD Environmental Outlook to 2050: The Consequences of Inaction 350 Organization for Economic Cooperation and Development (2012).
Nakicenovic, N. et al. Special Report on Emissions Scenarios Cambridge Univ. Press (2000).
Wolf, J., De Wit, C. T., Janssen, B. H. & Lathwell, D. J. Modeling long-term crop response to fertilizer phosphorus. I. The model. Agron. J. 79, 445–451 (1987).
Van Ittersum, M. & Rabbinge, R. Concepts in production ecology for analysis and quantification of agricultural input-output combinations. Field Crops Res. 52, 197–208 (1997).
Saltelli, A., Chan, K. & Scott, E. M. Sensitivity Analysis Wiley (2000).
Saltelli, A., Tarantola, S., Campolongo, F. & Ratto, M. Sensitivity Analysis in Practice. A Guide to Assessing Scientific Models Wiley (2004).
IPCC. IPCC Guidelines for National Greenhouse Gas Inventories (IPCC NGGIP Programme, IPCC-TSU/IGES). Institute for Global Environmental Strategies (IGES), Hayama, Japan on behalf of the IPCC, Hayama, Japan, 2006.
We thank Ken Giller for carefully reading an earlier version of the manuscript and useful comments. We are grateful to the late Hugo van der Meer for helpful and critical discussions; unfortunately he passed away before publication of this paper. This project was funded by Wageningen University and Research Centre Programme KB4 (Plant Research International and Livestock Research Centre) and the C.T. de Wit Graduate School for Production Ecology and Resource Conservation (PE&RC).
The authors declare no competing financial interests.
About this article
Cite this article
Sattari, S., Bouwman, A., Martinez Rodríguez, R. et al. Negative global phosphorus budgets challenge sustainable intensification of grasslands. Nat Commun 7, 10696 (2016). https://doi.org/10.1038/ncomms10696
This article is cited by
Nature Geoscience (2023)
Sustainable conversion of saturated adsorbents (SAs) from wastewater into value-added products: future prospects and challenges with toxic per- and poly-fluoroalkyl substances (PFAS)
Environmental Science and Pollution Research (2022)
A Global Meta-analysis Reveals that Nitrogen Addition Alters Plant Nutrient Concentration and Resorption in Grassland Ecosystems
Journal of Soil Science and Plant Nutrition (2022)
Journal of Soils and Sediments (2022)
Arbuscular mycorrhizal enhancement of phosphorus uptake and yields of maize under high planting density in the black soil region of China
Scientific Reports (2021)