It is not known whether dietary guidelines proposing a limited intake of animal protein are compatible with the adoption of circular food systems. Using a resource-allocation model, we compared the effects of circularity on the supply of animal-source nutrients in Europe with the nutritional requirements of the EAT-Lancet reference diet. We found the two to be compatible in terms of total animal-source proteins but not specific animal-source foods; in particular, the EAT-Lancet guidelines recommend larger quantities of poultry meat over beef and pork, while a circular food system produces mainly milk, dairy-beef and pork. Compared with the EAT-Lancet reference diet, greenhouse gas emissions were reduced by up to 31% and arable land use reduced by up to 42%. Careful consideration of the feasible substitutability between animal-source foods is needed to define potential roles of animal products in circular human diets.
The global food system is responsible for about a quarter of all human-induced greenhouse gas (GHG) emissions, one-third of global terrestrial acidification and the majority of global eutrophication, and is occupying 40% of the world’s ice- and desert-free land1,2. The global trend of a growing affluent population, thereby shifting diets towards resource-intensive foods (for example, meat), is raising concerns that the Earth’s biophysical limits will be exceeded3. To halt this progression, numerous healthy and environmentally friendly dietary guidelines have been proposed4,5,6,7. Such dietary guidelines aim to improve health outcomes by reducing the risk of non-communicable diseases (for example, cardiovascular disease, colorectal cancer and type 2 diabetes), while simultaneously reducing environmental impacts (for example, GHG emissions, deforestation, eutrophication and biodiversity loss)3,5,8. One prominent example of healthy and environmentally sustainable dietary guidelines is the one proposed by the EAT-Lancet Commission. Compared with conventional diets consumed in the European Union and the United Kingdom (EU-27 + UK) the EAT-Lancet dietary guidelines contain increased quantities of plant-source food, such as vegetables, legumes and nuts, and decreased quantities of animal-source food, such as meat, milk, eggs and fish4.
The foods that European societies consume, and the way in which these foods are produced, contribute substantially to destabilizing several planetary boundaries9,10. Although there is a general consensus that the consumption of animal-source food in the EU-27 + UK should decrease, there is no consensus about the degree of reduction of animal-source food to achieve environmentally sustainable diets11. Some studies suggest that it would be best for the planet if we were to consume only plant-source foods (for example, ref. 12), while others show that farm animals reared under a circular paradigm can play a crucial role in feeding humanity13,14,15,16,17. Circular food systems aim to optimally utilize resources by prioritizing arable land to produce plant biomass for human consumption, thus avoiding feed–food competition18,19. Currently about 40% of our global arable land area is used to produce high-quality feed for farm animals, which to a large extent is human-edible20. From a resource-efficiency point of view farm animals could instead be fed what is currently considered low-opportunity-cost biomass (LCB). LCB includes co-products from the food industry (for example, wheat middlings or slaughter waste from farm animals which is currently prohibited), food waste and grassland resources15. In the current food system, humans cannot or do not want to consume these resources; instead, LCB can be fed to farm animals to increase their resource-use efficiency and potentially reduce the environmental impact of animal-source food17,21.
Our aim was to assess whether adhering to the circularity principle of feeding LCB to farm animals within the EU-27 + UK is compatible with the recommended animal-source food consumption in healthy and environmentally friendly dietary guidelines. We took a reference diet derived from the EAT-Lancet guidelines as an example of a future healthy diet that was the product of a food system with environmental impacts that remained within planetary boundaries4. To adhere to circularity principles applied to the EU-27 + UK, animals were fed co-products and food waste resulting from the plant-source fraction of the EAT-Lancet dietary guidelines (Fig. 1). In addition, grassland resources and slaughter by-products from farm animals could be used as animal feed. A resource-allocation model was used to distribute the LCB among animal production systems (dairy, beef, pigs, broilers, laying hens, Atlantic salmon and Nile tilapia) to maximize protein production while respecting recommended animal-source food intake levels of the EAT-Lancet dietary guidelines and to calculate land use and GHG emissions. We did not consider the economic consequences of feeding LCB to livestock. Crop and animal production systems in the EU-27 + UK were based on current management and yields (that is, kg per hectare or kg per animal). The nutrient adequacy of any changes to the EAT-Lancet dietary guidelines was assessed against the European Food Safety Agency (EFSA) human nutrient intake requirements22. Four explorative theoretical scenarios were investigated (Table 1), which assess the impacts of changing diets on land use and GHG emissions (although we remain aware that agricultural practices are driven by a larger array of factors): (1) an EAT-Lancet reference scenario which represented the EAT-Lancet dietary guidelines in their current form (EL Reference); (2) a healthier wholegrain diet with a fixed composition of animal-source food (EL Circular Wholegrain Fixed); (3) a refined grain diet with a fixed composition of animal-source food (EL Circular Refined-grain Fixed); (4) a wholegrain diet with an unrestrained quantity of animal-source food to demonstrate the production potential of animals fed LCB (EL Circular Wholegrain Potential). The EL Circular Wholegrain Fixed and EL Circular Refined-grain Fixed scenarios offer insights into how grain consumption can influence the role of animals when adopting circularity principles. Consuming wholegrains is preferred from a health perspective; however, consuming refined grains results in additional by-products for animal feed derived from cereal processing15,23. This is meant as an example because processing often impacts the potential production of animals fed LCB and health, for example, rice or potatoes with or without peels. The EL Circular Wholegrain Fixed and EL Circular Wholegrain Potential Scenarios provide insight into the debate about which and how many animals to keep in a circular food system and the trade-offs and synergies with health recommendations.
Supply of animal-source foods
Our analysis revealed that animals exclusively fed LCB were unable to provide the combination of meat, milk, eggs and fish recommended in the EAT-Lancet dietary guidelines, largely due to an insufficient quantity of high-quality LCB. In total, the reference diet derived from the EAT-Lancet dietary guidelines contained 71 g of meat and fish, 250 g of milk and 13 g of eggs per capita per day. It was, nevertheless, possible to fulfil the ‘total’ recommendations by adjusting the share of meat and fish while respecting the healthy range. The reference value for pork, for example, is 7 g, while the healthy range is 0–14 g pork per capita per day.
In the EL Circular Wholegrain Fixed scenario, the recommended quantities of milk and fish could be met while meat was only 1% short; eggs were 100% short of meeting the recommended intake in the EAT-Lancet dietary guidelines. No eggs were produced in the EL Circular Wholegrain Fixed scenario. In the EL Circular Refined-grain Fixed scenario, the recommended quantities of meat, milk, eggs and fish could be met and exceeded (meat and fish, 12%) due to the additional LCB available from the refining of grains (for example, wheat bran). However, adjusting the shares of meat and fish was still required. Compared to the EL Circular Wholegrain Fixed, the EL Circular Refined-grain Fixed scenario could produce more poultry meat (12 g versus 2 g of poultry meat) and meet the recommended intake of eggs in the EAT-Lancet dietary guidelines (13 eggs per capita per day). From a health perspective, the consumption of poultry meat is preferred over the consumption of beef and pork4. Broilers and laying hens, however, were limited in their ability to upcycle all types of LCB and mainly required the co-products from refined grains. This creates a trade-off between consuming healthy wholegrains or producing healthy white poultry meat and eggs.
The EL Circular Wholegrain Potential scenario showed the optimal allocation of LCB (in terms of maximizing protein production) to different animals (Fig. 2). This scenario resulted in an increase in pork production (to 44 g per capita per day) due to the ability of pigs to convert low-quality co-products and food waste into animal-source food. Milk production also increased (to 523 g per capita per day) as dairy cattle are efficient converters of LCB (especially grassland) to protein. Increased milk production increased the supply of cull cows which produced additional beef. The increase of pork and milk was at the expense of poultry and fish production, thus showing a trade-off between optimally utilizing LCB and producing the preferred white meat.
Nutrient supply for human consumption
Our results showed that all EL Circular scenarios increased the supply of eicosapentaenoic acid (EPA)/docosahexaenoic acid (DHA), zinc, iron, vitamin B12 and protein compared to the EL Reference. The supply of calcium and energy was only increased compared to the EL Reference in the EL Circular Wholegrain Potential scenario.
Compared to the EFSA dietary nutrient requirements, the EL Circular Wholegrain Fixed, EL Circular Refined-grain Fixed scenarios and the EL Reference did not meet zinc, calcium and vitamin B12 requirements (Fig. 3 and Supplementary Information). Notably, the EL Reference also fails to meet EPA/DHA average nutrient requirements (Fig. 3). The EL Circular Wholegrain Potential did meet the calcium and vitamin B12 requirements but not zinc, however, largely due to an increase in milk production (250 g versus 523 g). For all nutrients except EPA/DHA (due to less fish), nutrient supply was greatest in the EL Circular Wholegrain Potential scenario. Besides calcium and fat, all three circularity diets outperformed the EAT-Lancet diet on available nutrients.
GHG and land use impacts
Overall, GHG emissions were 31% and 23% lower in the EL Circular Wholegrain Fixed and EL Circular Refined-grain Fixed scenario compared with the EL Reference diet. The reduction in emissions was due to the avoided emissions related to the production of animal feed (for example, nitrous oxide (N2O) from nitrogen fertilization) and the EL Circular Wholegrain Fixed scenario requiring less grain production (that is, more grain was destined for human consumption, due to no refining). Figure 4 shows GHG emissions and animal-source food protein produced from all three EL Circular scenarios and the EL Reference diet. Higher quantities of animal-source food (and therefore protein) were produced in the EL Circular Wholegrain Potential and lower quantities in the EL Circular Wholegrain Fixed scenarios which influenced GHG emissions (Fig. 4). The EL Circular scenarios include a default GHG emission value (according to the Intergovernmental Panel on Climate Change (IPCC) tier 2 approach) and a range of uncertainty to reflect the uncertainty in GHG emissions. Optimally utilizing LCB (to maximize protein production from animal-source food) in the EL Circular Wholegrain Potential scenario increased default GHG emissions to 483 kg CO2e per capita per year from 390 kg CO2e per capita per year in the EL Circular Refined-grain Fixed scenario (largely due to an increase in milk and pork production, Supplementary Information). The types of animal-source food produced impacted the ratio of GHG emissions; in the EL Circular Wholegrain Potential scenario additional dairy increased the contribution of methane (CH4) to total GHG emissions (Figs. 2 and 4). The default GHG emission values of all scenarios were within the safe operating space of the planetary boundaries’ framework (511 kg CO2e for food production per capita per year4). In all EL Circular scenarios, the upper limit to the range of uncertainty was beyond the safe operating space (Fig. 4).
Overall, cropland use was lower in all EL Circular scenarios than in the EL Reference diet (Fig. 5). However, it is important to note that cropland use for the EAT-Lancet reference scenario was based on a global cropland use average and could overestimate EU cropland use per capita; all EL Circular scenarios were based on EU cropland-use data specific for the EU. Further, utilizing cropland to produce animal feed also led to an increase in land use in the EAT-Lancet reference scenario. Cropland use was lowest in the EL Circular Wholegrain Fixed and EL Circular Wholegrain Potential scenarios due to the use of wholegrains requiring less land (that is, lower amounts of co-products from wheat result in less land required), although differences with using refined grain were marginal. Grassland use of the EL Circular Wholegrain Fixed and EL Circular Refined-grain Fixed were similar while the EL Circular Wholegrain Potential scenario resulted in higher grassland use because the use of grassland resources was increased for milk production (Fig. 3).
The production of milk and beef in circular food systems is highly dependent on the availability of grassland. Variation exists in the data on the quantity and quality of current grassland in the EU-27 + UK depending on the study and definition of grassland (that is, between managed and natural grassland) and available data sources. We compared the animal-source food output (for example, milk) of the EL Circular Wholegrain Potential scenario with different areas of managed grassland resulting from three different studies/models24,25,26. Milk production and beef (from dairy cattle) ranged, respectively, from 291 to 748 and 11 to 32 g per capita per day (Supplementary Information). Including natural grasslands could further increase the output of animal-source food.
Our results show that the overall quantity of animal-source protein in the EAT-Lancet dietary guidelines can be met, but that the precise levels of inclusion of different animal-source foods in such a diet cannot be achieved by only feeding LCB to animals. The extent to which the recommended quantities of animal-source food could be met largely depended on the availability of LCB. The EL Circular Wholegrain Fixed scenario versus the EL Circular Refined-grain Fixed scenario revealed that the role animals can play in circular food systems will be narrowed as we move towards healthier consumption of plant-source foods. With today’s food consumption patterns, several food groups are consumed in highly processed forms, resulting in additional by-products on the one hand, but increasing the risk for non-communicable diseases on the other hand27. The example employed here, wheat, results in by-products such as wheat bran and wheat germ if wheat is consumed in a refined manner. If it is, however, consumed as wholegrain, as recommended in the EAT-Lancet dietary guidelines, no by-products occur. Potatoes, vegetables and fruits would be other examples; if potatoes, for example, are industrially processed, their peel can be collected and used as animal feed.
Although dietary guidelines could not be met, it was possible to meet the nutrient recommendations when the EAT-Lancet diet restrictions were removed (that is, the EL Circular Wholegrain Potential scenario). Comparing the two EL Circular Fixed scenarios with the EL Circular Wholegrain Potential scenario showed that some animal species were more efficient at upcycling LCB (for example, dairy cattle and pigs) than others (for example, poultry). Grass resources, for example, were utilized most efficiently by dairy cattle because ruminants are well adapted to value this feed. Wet or fibrous food leftovers are used most efficiently by pigs, which are known to have a high feed intake capacity. Milk, furthermore, includes relatively high amounts of calcium, and beef and pork are high-quality sources of bioavailable vitamin B12 and zinc28. In other words, each animal has its own unique capacity to convert LCB into specific nutrients. The nutrients provided by animals are of high bioavailability and some, such as vitamin B12 and the omega-3 fatty acids EPA and DHA, are predominantly provided by animal-source foods and are almost absent in plant-source foods28.
The EL Circular scenarios, and in particular the EL Circular Wholegrain Potential scenario, showed that animals raised in a circular food system can play an essential role in providing nutrients. This is in line with earlier findings of, for example, Röös et al.29, van Hal et al.15 and van Zanten et al.14. None of those studies, however, assessed the importance of the dietary recommendations. Our results clearly show that although the EL Circular Wholegrain Potential scenario met all the nutrient recommendations except that of zinc, it exceeded the intake of beef and pork. Evidently, a healthy diet is not only defined by the sum of its nutrients. In fact, since the majority of the EL Reference diet was kept constant and clear bounds were set for the animal-source foods, the endowment for a healthy diet can nevertheless be approximated. However, findings from cohort studies suggest that the occurrence of several non-communicable diseases, such as cardiovascular disease, was associated with a relatively high intake of red meat, that is, beef and pork (for example, ref. 30). The higher recommended amounts of poultry as compared with beef in the EL Reference diet was justified by the fact that poultry meat does not show associations with increased mortality, and poultry fat moreover provided a higher content of essential polyunsaturated fatty acids (21% versus 4%)4. The above illustrates that although it is important to optimize essential nutrients from animal-source food, following upper limits of dietary guidelines is essential to avoid dietary-related diseases.
Our results furthermore showed that when circularity principles were adopted, GHG emissions and land use could be reduced compared with the EAT-Lancet diet because feed–food competition was avoided. In Willett et al.4, broilers perform better than, for example, beef from an environmental perspective due to their favourable feed conversion ratio. However, Willett et al.’s assessment is based on impact intensities (for example, GHG emissions per kg of food product) calculated for the current system; it was not considered whether the feed for broilers would also have been suitable as food for humans, or whether the area on which it was grown would have been suitable to grow food for humans. Our analysis clearly shows that as soon as we move towards a circular food system, and hence restrict the role for animals in converting LCB, broilers can no longer compete with, for example, cattle. This has consequences for any dietary guidelines (local or national) that aim to reduce environmental impacts, beyond the global EAT-Lancet diet. This does not mean that broilers cannot play a role in circular food systems, but it demonstrates that the broilers of today are less suited to convert LCB. This stresses the importance of adapting future breeding goals and feeding strategies towards the ability of animals to utilize LCB. This is essential because our results showed that animals can reduce their environmental impact (and the impact of the entire food system) if they increase their efficiency in converting LCB into healthy food.
Our study and model focused on feeding LCB, including food waste, to animals as a principle of circularity. Preventing food waste in the first instance or revalorizing food waste as food should always remain the priority; only when this is not possible should food waste be used as animal feed31. In other countries (for example, Japan and South Korea), food waste is successfully fed to monogastric animals after a processing and sterilization step before feeding32. In our case we assumed 35% of food waste available is suitable to be fed to animals32. The nutrient content of food waste is highly dependent on the food consumed and discarded, a weighted average based on the amount of food consumed in the human diet and the proportion wasted. By combining these products into one mix the feed value in terms of energy and protein of higher-quality waste products (for example, grains) is diluted by lower-quality waste products (for example, vegetables). Expanding the model employed to separate streams of food waste may increase the amount of animal-source food produced due to a greater availability of high-quality LCB. Further expanding the optimization model to include plant-source food production within the EAT-Lancet diet could offer further opportunities to reduce GHG emissions and land use. In addition, more circularity principles could be captured, including returning nutrients in manure and crop residues to the soil. Applying alternative objective functions (for example, minimizing GHG emissions while meeting the nutrient requirements of the human diet) could also influence the animal production systems selected.
Finally, it is important to consider the importance of future technologies for our results33. In our work we followed the assumptions made by Willett et al.4. It was, for example, assumed that fossil energy was replaced by renewable-energy sources, causing no CO2 emissions, while crop and grass yields were based on current yields and management (obtained from the Miterra-Europe Model and Carlson et al.34). In the coming decades, crop yields might be expected to continue to increase due to ongoing technological developments35,36. Increased crop yields would not, however, alter the main findings of our study because this study focused on the utilization choice of LCB, of which the amount is independent from crop yields. A change in crop yield would affect the environmental impacts of the remaining plant-source food needed to fulfil nutritional requirements. Increased crop yields may lead to lower land-use requirements per capita in each of the scenarios. The impacts of increased crop yields on GHG emissions are less clear. Achieving higher yields is likely to require more nutrient inputs (especially nitrogen37), with associated increases in GHG emissions per tonne of product, but technological developments may also increase nutrient-use efficiencies and thereby play a compensatory role.
We demonstrated that feeding LCB to animals has the potential to reduce GHG emissions and land use. Our results showed that the quantity of animal-source protein in EAT-Lancet dietary guidelines could be met, but that the precise animal-source food composition of the EAT-Lancet dietary guidelines could not be met by only feeding LCB to animals. Dietary guidelines recommend poultry meat over beef and pork, whereas in a circular food system mainly milk, dairy-beef and pork are produced. Careful consideration of the feasible substitutability between animal-source foods is urgently needed to define the role of animal products in the human diet. In this way the circularity principle of only feeding animals with LCB can be integrated into healthy and environmentally sustainable diets to further reduce environmental impacts.
In this study we extended the resource-allocation model developed by van Hal et al.15 to include GHG emissions and land use. This model allocates co-products, food-waste resources (from the EAT-Lancet example diet derived from the EAT-Lancet dietary guidelines4) and grassland resources. We compared environmental impacts of the EL Reference diet with three EL Circular scenarios. Each scenario varied based on the type of grain (wholegrain or refined grain) and the animal-source food composition (Table 1).
Adjustments to the EAT-Lancet diet
We took a reference diet developed by the EAT-Lancet Commission (derived from the EAT-Lancet dietary guidelines) as a starting point for this study. To better reflect the EU diet, some adjustments were made to grain consumption (that is, more wheat and less rice; the total quantity of grain remained unchanged) based on FAOSTAT4,38.
LCB from the EAT-Lancet diet
To calculate the amount (that is, tonnes) and area of crop required, and co-products available, reverse calculations were made using food consumption. Quantities of co-products (for example, wheat bran) from crops (for example, wheat) were calculated using FAO technical conversion factors39,40. In some scenarios grains were refined to increase the availability of co-products as animal feed and to better reflect current dietary habits (for example, wheat bran; Table 1). Quantities of food waste were calculated using food waste fractions developed by Gustavsson et al.41. This process was performed for each of the EU-27 + UK countries.
Resource allocation model
The model of van Hal et al.15 is a resource-allocation model of the EU-27 + UK developed in General Algebraic Modelling System v.30.3. The objective of the model is to maximize animal protein output from a given availability of animal feeds while meeting the nutritional requirements of the animals.
Animal systems include livestock (dairy cattle, beef cattle, pigs, broiler chickens and laying hens) and farmed fish (Atlantic salmon and Nile tilapia). The two fish systems are a proxy for a range of species with similar characteristics (for example, rainbow trout for Atlantic salmon). Livestock systems include three productivity levels (high, medium and low) while farmed fish only include a high productivity level. The model included the parent stocks (for example, sows in the pig system) and reproduction stocks (for example, heifers in the dairy system) to account for the entire life cycle of the animal. The nutritional requirements of livestock and farmed fish can be found in the Supplementary Information.
Livestock and farmed fish were exclusively fed co-products, food waste, grassland resources and animal by-products, referred to as LCB. In our model, co-products and animal by-products could be traded between EU-27 + UK countries, while food waste and grassland must be used in the country in which it is produced. The availability of co-products and food waste was set by the EAT-Lancet reference.
Thirty-five percent of the available food waste could be fed to animals as a wet feed, which is considered achievable if the feeding of food waste to animals were to be legalized32. Food waste could only be consumed by monogastric animals and fish due to food safety risks32. The availability of European grassland was based on the Miterra-Europe model26, and it was assumed grassland could only be consumed by ruminants. Our analysis only included managed grassland due to the uncertainty in quantity and quality of natural grasslands in Europe.
The availability of animal by-products was a fraction of the predicted live weight output of each livestock system (reported in ref. 42). Cannibalism was prevented in livestock systems; in farmed fish systems cannibalism was allowed due to the species being a proxy of a range of species. This enabled intraspecies recycling of by-products from farmed fish, meaning farmed fish can consume by-products of the same species. The nutritional value of LCB for livestock was obtained from the Dutch animal feed board, known as the CVB system43; the nutritional value of LCB for farmed fish was obtained from the International Aquaculture Feed Formulation Database44.
In addition to aquaculture, the model includes capture fisheries. Capture fisheries produce fish for human consumption and fish by-products (for example, fish meal) which can be fed in the animal systems. Quantities of capture fisheries (that is, harvested fish in tonnes of fresh fish) were limited to the maximum sustainable yield.
Human nutrient supply
To ensure that changes in the quantity and composition of animal-source food in the EAT-Lancet diet did not reduce the supply of nutrients to humans, the nutrient supply of each scenario was assessed against dietary nutrient recommendations from EFSA22. The nutrient content of each food item was based on the US Department of Agriculture food and nutrient database45.
GHG emissions and land use from animal-source food
The resource-allocation model developed by van Hal et al.15 was extended to include GHG emissions calculations. GHG emissions were based on the IPCC and Dutch GHG inventory methodologies46. It was assumed that fossil energy was replaced by renewable energy sources by 2050, causing no CO2 emissions, to keep our assumptions in line with the EAT-Lancet study4. The only contribution to land use from livestock was the grassland used as feed for ruminants. Other livestock systems were considered landless or had a very small, negligible land use because livestock are fed exclusively LCB.
GHG emission calculations were performed using a food systems approach. A food systems approach assesses emissions from the total diet as opposed to emissions per individual products in a life-cycle assessment. Emissions were limited to those occurring on the farm, including manure management, enteric fermentation and grassland production. No other animal feed emissions were considered due to the food-based allocation method47.
GHG emissions from terrestrial animals (dairy cattle, beef cattle, pigs, broiler chickens and laying hens) included CH4 and N2O from manure management. Methane emissions from manure management were calculated by multiplying volatile solid excretion by the methane conversion factor (that is, the conversion factor for each manure management system), B0 (that is, the maximum methane-producing capacity for manure) and 0.67 (that is, the conversion of methane from m3 to kg CH4)48. Volatile solid excretion was calculated using digestibility of protein and organic matter of feed consumed by the animal species49. N2O emissions from manure management included direct and indirect emissions (the latter resulting from the volatilization of ammonia and nitrogen (di)oxide) from nitrogen excretion in housing systems48. Nitrogen excretion was calculated by subtracting nitrogen retained in meat/milk/eggs from nitrogen intake.
In addition, ruminant systems included CH4 from enteric fermentation and N2O from grassland fertilization. CH4 emissions from enteric fermentation were calculated by multiplying gross energy intake by Ym (that is, percentage of gross energy in feed converted to CH4) and dividing by 55.65 (that is, the gross energy content of methane)48. N2O emissions from grassland included direct and indirect emissions (the latter resulting from the volatilization of ammonia and nitrogen (di)oxide and the leaching of nitrate) from nitrogen fertilization and manure excretion while grazing50. Grassland fertilization rates were estimated by the Miterra-Europe model based on the assumption that all organic fertilizer produced by grazing animals is applied to fodder crops (for example, grassland and fodder maize) in the same region and based on FAOSTAT data on nitrogen mineral fertilizer26.
GHG emissions from farmed fish included N2O emissions from the aquaculture system. Nitrogen in unconsumed feed and excreta (nitrogen intake minus nitrogen retained in body tissue) was multiplied by 1.8% and converted from nitrogen to N2O (ref. 51).
GHG emissions were summed into carbon dioxide equivalents (CO2e; 100 yr time horizon, 28 for biogenic CH4 and 265 for N2O (ref. 52)), and summed with plant-source food emissions (see next section) to calculate total GHG emissions. Results were given in GHG emissions per diet per capita per year.
GHG emissions and land use from plant-source food
For plant-source food, average national crop yields and nitrogen inputs per hectare were estimated using the Miterra-Europe model26 with 2017 as a reference year. For national crop yields and nitrogen inputs, direct and indirect N2O emissions were calculated using an IPCC tier 2 approach50. A food-based allocation method was applied where all GHG emissions were allocated to the main food product (for example, wheat flour)47. To calculate GHG emission intensities and crop yields at an EU level, a weighted average was applied based on harvested area in each country. Not all plant-source food was included in the Miterra-Europe model (lentils, groundnuts, tree nuts and bananas). The GHG emission intensities and crop yields per hectare were then estimated using global data, with a reference year of circa 200034. Processing of crop into edible food products and food waste along the supply chain (LCB from the EAT-Lancet diet) were then considered to calculate GHG emission intensities and land use per kg of plant-source food consumed.
Further information on research design is available in the Nature Research Reporting Summary linked to this article.
Data are available from https://doi.org/10.4121/16918732
Model code is available from https://doi.org/10.4121/16918732.
Godfray, H. C. J. et al. Food security: the challenge of feeding 9 billion people. Science 327, 812–818 (2010).
Foley, J. A. et al. Solutions for a cultivated planet. Nature 478, 337–342 (2011).
Godfray, H. C. J. et al. Meat consumption, health, and the environment. Science 361, eaam5324 (2018).
Willett, W. et al. Food in the Anthropocene: the EAT-Lancet Commission on healthy diets from sustainable food systems. Lancet 393, 447–492 (2019).
Springmann, M. et al. Health and nutritional aspects of sustainable diet strategies and their association with environmental impacts: a global modelling analysis with country-level detail. Lancet Planet. Health 2, e451–e461 (2018).
Eme, P. E., Douwes, J., Kim, N., Foliaki, S. & Burlingame, B. Review of methodologies for assessing sustainable diets and potential for development of harmonised indicators. Int. J. Environ. Res. Public Health 16, 1184 (2019).
van de Kamp, M. E. et al. Healthy diets with reduced environmental impact? The greenhouse gas emissions of various diets adhering to the Dutch food based dietary guidelines. Food Res. Int. 104, 14–24 (2018).
Mertens, E. et al. Improving health and carbon footprints of European diets using a benchmarking approach. Public Health Nutr. 24, 565–575 (2021).
Steffen, W. et al. Planetary boundaries: guiding human development on a changing planet. Science 347, 1259855 (2015).
Campbell, B. M. et al. Agriculture production as a major driver of the earth system exceeding planetary boundaries. Ecol. Soc. 22, 4 (2017).
Frehner, A., Muller, A., Schader, C., De Boer, I. J. M. & Van Zanten, H. H. E. Methodological choices drive differences in environmentally-friendly dietary solutions. Glob. Food Sec. 24, 100333 (2020).
Poore, J. & Nemecek, T. Reducing food’s environmental impacts through producers and consumers. Science 360, 987–992 (2018).
Röös, E. et al. Greedy or needy? Land use and climate impacts of food in 2050 under different livestock futures. Glob. Environ. Chang. 47, 1–12 (2017).
Van Zanten, H. H. E. et al. Defining a land boundary for sustainable livestock consumption. Glob. Chang. Biol. 24, 4185–4194 (2018).
Van Hal, O. et al. Upcycling food leftovers and grass resources through livestock: Impact of livestock system and productivity. J. Clean. Prod. 219, 485–496 (2019).
Schader, C., Muller, A., Scialabba, N. E., Hecht, J. & Stolze, M. Comparing global and product-based LCA perspectives on environmental impacts of low-concentrate ruminant production. In Proc. 9th International Conference on Life Cycle Assessment in the Agri-Food Sector (LCA Food 2014) (eds Schenck, R. & Huizen, D.) San Francisco, California, USA, 1203–1209 (2014).
Van Kernebeek, H. R. J., Oosting, S. J., Van Ittersum, M. K., Bikker, P. & De Boer, I. J. M. Saving land to feed a growing population: consequences for consumption of crop and livestock products. Int. J. Life Cycle Assess. 21, 677–687 (2016).
Van Zanten, H. H. E., Wan Ittersum, M. K. D. & e Boer, I. J. M. The role of farm animals in a circular food system. Glob. Food Sec. 21, 18–22 (2019).
De Boer, I. J. M. & Van Ittersum, M. K. Circularity in Agricultural Production (Wageningen University & Research, 2018) https://www.wur.nl/upload_mm/7/5/5/14119893-7258-45e6-b4d0-e514a8b6316a_Circularity-in-agricultural-production-20122018.pdf
Mottet, A. et al. Livestock: on our plates or eating at our table? A new analysis of the feed/food debate. Glob. Food Sec. 14, 1–8 (2017).
Schader, C. et al. Impacts of feeding less food-competing feedstuffs to livestock on global food system sustainability. J. R. Soc. Interface 12, 20150891 (2015).
Dietary Reference Values for Nutrients. Summary Report (European Food Safety Authority, 2017).
Aune, D. et al. Whole grain consumption and risk of cardiovascular disease, cancer, and all cause and cause specific mortality: systematic review and dose–response meta-analysis of prospective studies. BMJ 353, 1–14 (2016).
Plutzar, C. et al. Changes in the spatial patterns of human appropriation of net primary production (HANPP) in Europe 1990–2006. Reg. Environ. Chang. 16, 1225–1238 (2016).
Haberl, H. et al. Quantifying and mapping the human appropriation of net primary production in Earth’s terrestrial ecosystems. Proc. Natl Acad. Sci. USA 104, 12942–12947 (2007).
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).
Elizabeth, L., Machado, P., Zinöcker, M., Baker, P. & Lawrence, M. Ultra-processed foods and health outcomes: a narrative review. Nutrients 12, 1955 (2020).
Murphy, S. P. & Allen, L. H. Nutritional importance of animal source foods. J. Nutr. 133, 3932S–3935S (2003).
Röös, E. et al. Protein futures for Western Europe: potential land use and climate impacts in 2050. Reg. Environ. Chang. 17, 367–377 (2017).
Etemadi, A. et al. Mortality from different causes associated with meat, heme iron, nitrates, and nitrites in the NIH-AARP Diet and Health Study: population based cohort study. BMJ 357, j1957 (2017).
Papargyropoulou, E., Lozano, R., Steinberger, J. K., Wright, N. & Ujang, Z. Bin The food waste hierarchy as a framework for the management of food surplus and food waste. J. Clean. Prod. 76, 106–115 (2014).
zu Ermgassen, E. K. H. J., Phalan, B., Green, R. E. & Balmford, A. Reducing the land use of EU pork production: where there’s swill, there’s a way. Food Policy 58, 35–48 (2016).
Herrero, M. et al. Innovation can accelerate the transition towards a sustainable food system. Nat. Food 1, 266–272 (2020).
Carlson, K. M. et al. Greenhouse gas emissions intensity of global croplands. Nat. Clim. Chang. 7, 63–68 (2017).
Rijk, B., van Ittersum, M. & Withagen, J. Genetic progress in Dutch crop yields. Field Crops Res. 149, 262–268 (2013).
Fischer, T., Byerlee, D. & Edmeades, G. Crop yields and global food security. Will yield increase continue to feed the world? Eur. Rev. Agric. Econ. 43, 191–192 (2016).
Schils, R. et al. Cereal yield gaps across Europe. Eur. J. Agron. 101, 109–120 (2018).
FAOSTAT (FAO, 2019) http://www.fao.org/faostat/en/#home
Vellinga, T. V. et al. Methodology used in feedprint: a tool quantifying greenhouse gas emissions of feed production and utilization. Livest. Res. Rep. 674, 121 (2013).
Technical Conversion Factors for Agricultural Commodities (FAO, 1996).
Gustavsson, J., Cederberg, C., Sonesson, U., Otterdijk, R. & Meybeck, A. Global Food Losses and Food Waste—Extent, Causes and Prevention (2011).
van Hal, O. Upcycling Biomass in a Circular Food System: The Role of Livestock and Fish. PhD thesis, Wageningen University (2020) https://doi.org/10.18174/524412
Spek, J. W. & Van Wesemael, D. CVB Feed Table 2021 (CVB, 2021) www.cvbdiervoeding.nl
International Aquaculture Feed Formulation Database (IAFFD, 2018).
Food and Nutrient Database (US Department of Agriculture, 2020).
L. A. Lagerwerf, A. Bannink, C. van Bruggen, C. M. Groenestein, J. F. M. Huijsmans, WOt-technical report 148 J. W. H. van der Kolk, H. H. Luesink, S. M. van der Sluis, G. L. Velthof & J. Vonk Methodology for Estimating Emissions from Agriculture in the Netherlands—Update 2019 (Statutory Research Tasks Unit for Nature & the Environment, 2019) https://library.wur.nl/WebQuery/wurpubs/549203
Van Hal, O., Weijenberg, A. A. A., De Boer, I. J. M. & Van Zanten, H. H. E. Accounting for feed–food competition in environmental impact assessment: towards a resource efficient food-system. J. Clean. Prod. 240, 118241 (2019).
IPCC Guidelines for National Greenhouse Gas Inventories Ch. 10, 87 (IPCC, 2006).
Zom, R. L. G. & Groenestein, C. M. Excretion of volatile solids by livestock to calculate methane production from manure. RAMIRAN 2015, 16th International Conference Rural-Urban Symbiosis, 8th - 10th September 2015, Hamburg, Germany (2015).
IPCC Guidelines for National Greenhouse Gas Inventories Ch. 11, 54 (2006).
MacLeod, M. J., Hasan, M. R., Robb, D. H. & Mamun-Ur-Rashid, M. Quantifying greenhouse gas emissions from global aquaculture. Sci Rep. 10, 11679 (2020).
IPCC. Climate Change 2013: The Physical Science Basis (eds Stocker, T. F. et al.) (Cambridge Univ. Press, 2013) https://www.ipcc.ch/report/ar5/wg1/
The authors declare no competing interests.
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van Selm, B., Frehner, A., de Boer, I.J.M. et al. Circularity in animal production requires a change in the EAT-Lancet diet in Europe. Nat Food 3, 66–73 (2022). https://doi.org/10.1038/s43016-021-00425-3
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