References

1. Lewandowski et al. argue that the "[...] fossil-energy savings are highest where miscanthus biomass is used as construction material (our analysis uses the example of insulation material)." Lewandowski et al. 2016, p. 20.
2. Nsanganwimana et al. 2014, p. 125.
3. Lackowski 2019.
4. "Producing rhizomes for propagation in the United Kingdom climate takes at least two growing season, this entails clearing the production ground of weeds, plowing in spring and tilling the ground to a fine seed bed like tilth before planting the rhizomes with a potato type planter. [...] In the spring following the second growth year, the rhizomes are harvested using a modified potato harvester, hand or semi-automatically sorted and cut into viable pieces, 20–40 g. [...] One ha of rhizomes produces enough material to plant 10–30 ha of crop with the same modified potato type planter. Lower quality rhizomes, tested by sprouting tests, would require 80–90 g rhizomes (private communication, M. Mos)." Hastings et al. 2017, pp. 5–6.
5. New Energy Farms 2021.
6. "Our work is showing, depending on the hybrid type, one ha (hectare) of seed production can produce enough seed for ∼1000–2000 ha of planting, depending on parental combinations, two orders of magnitude greater than rhizome propagation. [...] [A]n 85–95% establishment rate is achieved." Hastings et al. 2017, p. 6.
7. "Seeds are sown by machine and raised in the greenhouse (Figure 3A) before being planted out in the field (Figure 3B). It is anticipated that seed-based establishment methods will prove most effective for the scaling up of miscanthus production because they have the following advantages: · With increasing market demand, large quantities can easily be provided, once seed production has been well developed · Short growing period for plantlets: Only 8–10 weeks from seed to final product (plugs) · Plug production is energy efficient (no need for refrigerators) · Low establishment costs" Lewandowski et al. 2016, p. 15.
8. "Results show that new hybrid seed propagation significantly reduces establishment cost to below £900 ha−1 [...]. The breakeven yield was calculated to be 6 Mg [Mg/megagram equals metric ton] DM [dry matter] ha−1 y−1 [hectare per year], which is about half average United Kingdom yield for Mxg; with newer seeded hybrids reaching 16 Mg DM ha−1 in second year United Kingdom trials. These combined improvements will significantly increase crop profitability. The trade-offs between costs of production for the preparation of different feedstock formats show that bales are the best option for direct firing with the lowest transport costs (£0.04 Mg−1 km−1) and easy on-farm storage. However, if pelleted fuel is required then chip harvesting is more economic. [...] The specific cost of rhizome and plug planting are similar as they are relatively labor intensive whereas seed drilling, is predicted to halve the cost." Hastings et al. 2017, pp. 1, 8.
9. Nsanganwimana et al. 2014, p. 130.
10. McCalmont et al. 2017, p. 503.
11. "C4 species characteristically demonstrate improved efficiency in nitrogen (N) and water-use [28,29]. Specifically, C4 species can show N-use efficiencies twice those of C3 species." Anderson et al. 2014, p. 73.
12. "Nitrogen fertilizer is unnecessary and can be detrimental to sustainability, unless planted into low fertility soils where early establishment will benefit from additions of around 50 kg N ha−1. [...] N2O emissions can be five times lower under unfertilized Miscanthus than annual crops, and up to 100 times lower than intensive pasture land. Inappropriate nitrogen fertilizer additions can result in significant increases in N2O emission from Miscanthus plantations, exceeding IPCC emission factors although these are still offset by potential fossil fuel replacement." McCalmont et al. 2017, p. 503.
13. "Plastic mulch film reduced establishment time, improving crop economics. [...] The mulch film trial in Aberystwyth showed a significant (P < 0.05) difference between establishment rates for varying plant densities with the cumulative first 2-year mean yield almost doubling under film as shown in Table 3. Using film adds £100 per ha and 220 kg CO2 eq. C ha−1, to the cost of establishment. The effect of this increase is to reduce the establishment period of the crop by 1 year in Aberystwyth environmental conditions, similar reduction in establishment times were observed at the other trial sites and also in Ireland (O’Loughlin et al., 2017). [...] With mulch film agronomy the latest seeded hybrids establish far more quickly with significantly higher early yields (years 1 and 2) compared to commercial Mxg in the United Kingdom delivering a breakeven return on investment at least a year earlier." Hastings et al. 2017, pp. 1, 9, 14–15.
14. "The planting of seed-derived plugs proved to be most successful method for miscanthus establishment on marginal soils. Covering the plants with a plastic film accelerates their growth. The film keeps the humidity in the topsoil and increases the temperature. This is beneficial for the plants, especially on light soils with a higher risk for drought stress and in cool temperatures." Lewandowski et al. 2016, p. 14.
15. Miguez et al. 2011, p. 516.
16. "Crop productivity is determined as the product of total solar radiation incident on an area of land, and the efficiencies of interception, conversion and partitioning of that sunlight energy into plant biomass. [...] Beale and Long demonstrated in field trials in southeastern England that εc,a was 0.050–0.060, 39% above the maximum value observed in C3 species. Furthermore, when εc is calculated in terms of total (i.e., above-ground and below-ground) M. x giganteus biomass production (εc,t), it reaches 0.078, which approaches theoretical maximum of 0.1. Studies performed in the midwestern USA by Heaton et al. reported a similar efficiency of intercepted PAR (0.075)." Anderson et al. 2014, p. 73.
17. "Water‐use efficiency is among the highest of any crop, in the range of 7.8–9.2 g DM (kg H2O)−1. - Overall, water demand will increase due to high biomass productivity and increased evapotranspiration at the canopy level (e.g. ET up from wheat by 100–120 mm yr−1). - Improved soil structures mean greater water‐holding capacity (e.g. up by 100–150 mm), although soils may still be drier in drought years. - Reduced run‐off in wetter years, aiding flood mitigation and reducing soil erosion. - Drainage water quality is improved, and nitrate leaching is significantly lower than arable (e.g. 1.5–6.6 kg N ha−1 yr−1 [for] Miscanthus, 34.2–45.9 [for] maize/soya bean)." McCalmont et al. 2017, p. 504.
18. "Beale et al. (1999) compared their results to the water‐use efficiency of a C3 biomass crop, Salix viminalis, reported in Lindroth et al. (1994) and Lindroth & Cienciala (1996), and suggest that WUE for Miscanthus could be around twice that of this willow species. Clifton‐Brown & Lewondowski (2000) reported figures from 11.5 to 14.2 g total (above‐ and belowground) DM (kg H2O)−1 for various Miscanthus genotypes in pot trials, and this compares to figures calculated by Ehdaie & Waines (1993) with seven wheat cultivars who found WUE between 2.67 and 3.95 g total DM (kg H2O)−1. Converting these Miscanthus values to dry matter biomass per hectare of cropland would see ratios of biomass to water use in the range of to 78–92 kg DM ha−1 (mm H2O)−1. Richter et al. (2008) modelled harvestable yield potentials for Miscanthus from 14 UK field trials and found soil water available to plants was the most significant factor in yield prediction, and they calculated a DM yield to soil available water ratio at 55 kg DM ha−1 (mm H2O)−1, while just 13 kg DM ha−1 was produced for each 1 mm of incoming precipitation, likely related to the high level of canopy interception and evaporation. Even by C4 standards these efficiencies are high, as seen in comparisons to field measurements averaging 27.5 ± 0.4 kg aboveground DM ha−1 (mm H2O)−1 for maize (Tolk et al., 1998)." McCalmont et al. 2017, p. 501.
19. "In terms of energy production intensity, Miscanthus biomass produces more net energy per hectare than other bioenergy crops at around 200 GJ ha−1 yr−1, especially arable [maize for biogas 98, oil seed rape for biodiesel 25, wheat and sugar beet ethanol 7–15 (Hastings et al., 2012)]. Felten et al. (2013) calculated similar figures, reporting 254 GJ ha−1 yr−1 for Miscanthus." McCalmont et al. 2017, p. 493.
20. Heaton, Hartzler & Barnhart 2010, p. 2.
21. Hastings et al. 2009a, p. 180.
22. SRF yield for willow and poplar in the UK lies in the range of 10–12 tonnes dry matter per hectare per year according to Proe, Griffiths & Craig 2002, pp. 322–323. In a willow yield meta study Fabio et al. quote willow trials in Sweden yielding 8, 13 and 14 tonnes. In the UK, the authors quote two willow trials, both yielding 10 tonnes, and one trial in Ireland yielding 8-10 tonnes. See Fabio & Smart 2018 table 1 and 2, page 551 and 552. The willow yield datapoints (location not given) in Figure 2, p. 554 show a mean yield of approximately 6–7 tonnes per hectare per year. In table 3, page 557, 6 studies is quoted, with a mean yield of 10 tonnes per hectare per year. Aylott et al. collected data from 49 test sites for willow and poplar in the UK, and conclude: "Field trial results shown that observed SRC yield varied significantly between genotype and rotation (Table 1). The highest yields were recorded in willow over the two rotations, with the 16 genotypes averaging 9.0 odt [oven dry tonne] ha−1 yr−1 compared with 6.3 odt ha−1 yr−1 for the poplar genotypes. The highest‐yielding parental line was the Swedish S. vimanlis × S. schwerinii, which displayed consistently high yields over both rotations and a high resistance to rust. This parent line included the highest‐yielding single genotype, Tora, with an average yield across both rotations of 11.3 odt ha−1 yr−1." Aylott et al. 2008, p. 363. Modelling for the future, Aust et al. estimate a mean yield of 14 tonnes for SRC willow and poplar produced on arable land in Germany, see Aust et al. 2014, p. 529. Willow and poplar need fertilizer to achieve these yields, Fabio et al. reports 92–400 kg nitrogen per hectare per year for the yields reported in their article. See Fabio & Smart 2018, pp. 551–552. Hastings et al. used computer modelling software to estimate miscanthus, willow and poplar yields for Great Britain, and concluded with mean yields in the narrow range 8.1 to 10.6 dry tonnes per hectare per year for all these plants, with miscanthus taking the middle position. Miscanthus had the highest yield in the warmer southwest, and adjusting the computer model for the expected warmer climate in 2050 made miscanthus the top yielding crop for a larger area: "As the climate warms through the time‐slices, there is a yield increase and thus a larger area where Miscanthus is the highest yielder of the feed‐stocks considered." Hastings et al. 2014, pp. 108, 119.
23. For yield estimates see FAO's "The global outlook for future wood supply from forest plantations", section 2.7.2 – 2.7.3. Scot's pine, native to Europe and northern Asia, weighs 390 kg/m3 oven dry (moisture content 0%). The oven dry weight of eucalyptus species commonly grown in plantations in South America is 487 kg/m3 (average of Lyptus, Rose Gum and Deglupta). The average weight of poplar species commonly grown in plantations in Europe is 335 kg/m3 (average of White Poplar and Black Poplar. http://www.fao.org/3/X8423E/X8423E08.htm#TopOfPage
24. Smil 2008, p. 75-76.
25. Forest Research 2019, pp. 69-71.
26. IPCC 2019b, p. 4.34 – 4.41.
27. Miscanthus yield software Miscanfor calculates a yield decline of 33% between autumn peak and winter harvest. See Hastings et al. 2009, p. 186. This calculation is confirmed by Roncucci et al. which found a dry mass yield decrease of 32–38% for their test crops when harvest was delayed until winter. See Roncucci et al. 2015, p. 1002. Clifton-Brown et al. found a mean yield reduction of 0.3% per day in the period between peak autumn yield and winter harvest, see Clifton‐Brown, Breuer & Jones 2007, p. 2305.
28. "The majority of the literature reporting dry biomass yield for M. x giganteus originates from European studies. Ceiling peak biomass yields in established stands of M. x giganteus have approached 40 t dry matter (DM) ha−1 in some European locations, although it may take 3–5 years to achieve these ceiling yields. Across Europe, harvestable yields of up to 25 t DM ha−1 from established stands of M. x giganteus have been reported in areas between central Germany and southern Italy, while peak yields in central and northern Europe have ranged between 10–25 t DM ha−1, and in excess of 30 t DM ha−1 in southern Europe. A quantitative review of established M. x giganteus stands across Europe reported a mean peak biomass yield of 22 t DM ha−1, averaged across N rates and precipitation levels." Anderson et al. 2014, p. 79.
29. Roncucci et al. 2015, p. 1004.
30. Smil 2015, p. 81.
31. «A factor of approximately two converts dry matter to carbon (Michel et al., 2006) and 10 from t ha−1 to kg m−2. [...] Figure 2 shows global predictions of Miscanthus NPP from the viability simulation. The calculated values range from 0.5 kg C m−2 yr−1 in boreal region to between 1 and 2 kg C m−2 yr−1 in mid-latitudes and 3 and 5 kg C m−2 yr−1 in the tropics.»Hughes et al. 2010, pp. 82–83.
32. EU MAGIC spreadsheet 2021.
33. Shepherd et al. 2020, p. 295.
34. Shepherd et al. 2020, p. 298.
35. Zhang et al. measured a bana grass (napier variant) yield of 74 tonnes per hectare per year with light fertilisation and 1000 mm rainfall. Zhang et al. 2010, pp. 96, 98 (table 1).
36. Hoshino et al. measured a napier yield of 75.6 tonnes per hectare per year the second year of growth under heavy fertilisation and with rainfall level 1000 mm annually. Hoshino, Ono & Sirikiratayanond 1979, pp. 310, 311, 315.
37. Vicente-Chandler et al. found that heavily fertilized napiergrass produced 75,661 pounds of dry matter per acre per year when cut at 90-day intervals, equivalent to 84.8 tonnes per hectare per year. Vicente-Chandler, Silva & Figarella 1959, p. 202.
38. "The total water requirements are approximately 100 mm (4 inches) per month rainfall equivalent. [...] The yield of Giant King Grass depends on the time between harvests. For example, a six-month harvest of tall Giant King Grass, one can expect to obtain 80 or more US tons per acre (180 metric tons per hectare) of fresh grass at approximately 70-75% moisture. For two harvests per year, double these figures." Viaspace 2020.
39. Mackay quotes yields of 360 wet tonnes per hectare per year, but does not quantify moisture content. Mackay 2020.
40. "From the second year of Miscanthus planting, crops were annually harvested on the verge of shoot in late March or the beginning of April. Mean Miscanthus yield was 15 Mg dry mass (d.m.) ha−1 y−1, which remained nearly constant from the fourth year of establishment." Felten & Emmerling 2012, p. 662.
41. McCalmont et al. 2017, p. 497.
42. "The yields used in the calculation of GHG emissions and crop economics this study used mean yields of 12–14 Mg ha−1 y−1 that have been observed from Mxg from current commercial plantings observed in the United Kingdom (private communication, M. Mos). We have assumed a logistic yield increase for establishment year yields and a linear decline in yield after 15 years Lesur et al. (2013). Inter-annual yield variation, due to weather conditions, as observed in long term trials (Clifton-Brown et al., 2007) and modeled Miscanthus yields for the United Kingdom, using weather data from 2000 to 2009 (Harris et al., 2014) using the MiscanFor model (Hastings et al., 2009, 2013) indicates that the weather related standard deviation of inter-annual yield variation in the United Kingdom is of the order 2.1 Mg ha−1 y−1 for a mean yield of 10.5 Mg ha−1 y−1 for the whole of the United Kingdom. The modeled yields are generally pessimistic as they calculate rain-fed yields and do not account for ground water support that is available in many United Kingdom arable farms." Hastings et al. 2017, p. 4.
43. "The Asia-Pacific Economic Cooperation (APEC) estimates that marginal lands make up approximately 400 million hectares across Asia, the Pacific Islands, Australia, and North America. Other estimates put the global marginal land area anywhere from 1100 to 6650 million hectares, depending on the parameters used to describe marginal (e.g., "non-favored agricultural land", "abandoned or degraded cropland", or arid, forested, grassland, shrubland, or savanna habitats). The potential area available in the USA for cellulosic biomass crops and low-input, high-diversity native perennial mixtures ranges from 43 to 123 million hectares. The differences in these estimates reflect the inconsistencies in the usage of the term "marginal land", despite its common use in the bioenergy industry and literature. Marginal lands are often described as degraded lands that are unfit for food production and/or of some ambiguously poor quality and are often termed unproductive. Unproductive soils are characterized by unfavorable chemical and/or physical properties that limit plant growth and yield, including low water and nutrient storage capacity, high salinity, toxic elements, and poor texture. Further difficulties encountered in marginal landscapes include shallow soil depth due to erosion, poor drainage, low fertility, steep terrain, and unfavorable climate. Despite the poor quality of marginal land and the potential problems it could present for its production, biomass is unlikely to be grown on high-quality land that is economically viable for traditional crops." Quinn et al. 2015, pp. 1–2.
44. «Estimates of marginal/degraded lands currently considered available for bioenergy range from 3.2–14.0 Mkm2, depending on the adopted sustainability criteria, land class definitions, soil conditions, land mapping method and environmental and economic considerations (Campbell et al. 2008; Cai et al. 2011; Lewis and Kelly 2014).» IPCC 2019c.
45. EU MAGIC 2021.
46. It takes 30 days with a mean temperature of below −3.4 °C before the soil temperature fall to below −3.4 °C. See Hastings et al. 2009b, p. 184. Quinn et al. state that "[m]iscanthus × giganteus leaf area and yield reduced under drought stress, but water availability does not affect shoot production or plant height at the beginning of the growing season. [p. 4]. [...] Miscanthus × giganteus biomass and rhizome viability unaffected by flooding [p. 5]. [...] Salinity above 100 mM affected Miscanthus × giganteus growth, with rhizomes > roots > shoots in order of increasing sensitivity (rhizomes least sensitive). Plants grown from larger rhizomes initially were less sensitive. [p. 8]. [...] The lethal temperature at which 50 % (LT50) of Miscanthus × giganteus rhizomes were killed was −3.4 °C, which can be problematic especially during first winter. [...] Miscanthus × giganteus shows unusual cold tolerance for a C4 species. [p. 10] [...] Because C4 and CAM species have inherent mechanisms to resist heat stress, it makes sense to consider biomass crops with these photosynthetic pathways (see Table 5) [page 11]. [...] Our literature review has revealed several "all purpose" biomass crops that are moderately or highly tolerant of multiple environmental stressors (Table 6). For example, Andropogon gerardii, Eucalyptus spp., Miscanthus spp., Panicum virgatum, Pinus spp., Populus spp., Robinia pseudoacacia, and Spartina pectinata were shown to be moderately or highly tolerant of four or more stress types [p. 14]." Quinn et al. 2015, pp. 4, 5, 8, 10, 11, 14.
47. Nsanganwimana et al. 2014, p. 124.
48. "Most saline soils covering 539 567 km2 in the European geographical area can be used to grow Miscanthus with up to an estimated 11% reduction in yield; a further 2717 km2 can be used with an estimated 28% reduction in yield, and only, 3607 km2 will produce a yield reduction greater that 50%." Stavridou et al. 2017, p. 99.
49. "Rhizome D.W. [dry weight] and the ratios of root/rhizome and below‐/above‐ground D.W. were not affected by increased salinity, and only, the root D.W. was significantly reduced at the highest salt concentration (22.4 dS m−1 NaCl) (Table 1). Płażek et al. (2014) showed a similar response in M. × giganteus, with reduction only in roots D.W. at 200 mm NaCl and no changes in rhizomes D.W. below 200 mm NaCl. This ability of perennial grasses to maintain below‐ground biomass under stress conditions could preserve sufficient reserves for the following growing season (Karp & Shield, 2008); while this may be physiologically relevant for transitory stresses like drought, it remains to be seen how this response affects year on year yield under the accumulative stress effect of salinity." Stavridou et al. 2017, p. 100.
50. "The highest biomass yields as well as the highest GHG- and fossil-energy savings potentials (up to 30.6 t CO2eq/ha*a [CO2 equivalents per hectare per year] and 429 GJ/ha*a [gigajoule per hectare per year], respectively) can be achieved on non-marginal sites in Central Europe. On marginal sites limited by cold (Moscow/Russia) or drought (Adana/Turkey) savings of up to 19.2 t CO2eq/ha*a and 273 GJ/ha*a (Moscow) and 24.0 t CO2eq/ha*a and 338 GJ/ha*a (Adana) can be achieved." Lewandowski et al. 2016, p. 19.
51. Zhang et al. 2020.
52. China's coal based energy consumption was 81.67 EJ in 2019 (52% of the worldwide consumption). See page 47. BP 2020.
53. Clifton-Brown, Breuer & Jones 2007, p. 2296–2297.
54. Yost et al. 2017, pp. 684, 688.
55. "Shoot death means that in a given year, there will be limited yield but a recovery the following year. Rhizome kill means that the crop needs to be replanted. [...] For drought conditions, we calculate the time below the wilting point: if this exceeds 30 days, then the shoot is killed for that year, if it exceeds 60 days for M. × giganteus the rhizome is killed and the crop destroyed. This was based upon a growing chamber water stress experiment with M. × giganteus (Clifton‐Brown and Hastings, unpublished data). This is extended to 60 and 120 days for M. sinensis." Hastings et al. 2009b, p. 161.
56. "In the second year of growth (2011) crops growing in SiC [silty-clay-loam] soil showed a significantly higher aboveground dry yield (Table S1) compared to crops growing in SL [sandy loam] soil (19.1 vs. 10.9 Mg ha−1) (Fig. 2a). [...] General trends in biomass productivity were amplified in the third growing year (2012), when miscanthus growing in SL soil was severely influenced by the summer drought which led to premature aboveground senescence, leaf loss and inhibition of flowering. Hence, averaged over the three harvest dates, dry biomass yield in the SL soil was one order of magnitude lower than in the SiC soil (24.6 vs. 3.9 Mg ha−1). [...] The results obtained in our experiments confirmed the importance of water availability in determining satisfactory miscanthus yields in a Mediterranean environment. In fact, miscanthus plantations in soils characterized by a poor water holding capacity (i.e. SL soil) were severely affected after three growing years, with harvestable dry yields lower than 5 Mg ha−1. [...] Roncucci et al. 2015, pp. 1001, 1004. Stričević et al. make a similar point, adding root depth to the equation: "Water availability for Miscanthus depended equally on precipitation and accumulated soil moisture, such that yields were generally a reflection of root depth and soil characteristics. For example, the yields recorded at Ralja were lower than those achieved at Zemun because of the restrictive soil layer in the former case [at 1.1 m] and the inability of Miscanthus to develop deeper roots. The importance of soil and root depth for the simulation of plant production has been corroborated by other researchers (Raes et al., 2009)." See Stričević et al. 2015, pp. 1205.
57. Stričević et al. make a contrasting point however: "Each year Miscanthus increased its above‐ground biomass and root depth [...]. In the first 2 years Miscanthus formed rhizomes and root growth was slow. In the third year, there was enough moisture in the more fertile surface layer of soil, such that root depth was smaller than expected. The next 3 years were dry, so in search for water the roots considerably increased their depth (up to 2.3 m), which was consistent with data collected from other experiments (Neukirchen et al., 1999; Riche & Christian, 2001)." See Stričević et al. 2015, pp. 1207.
58. "Mantineo et al. (2009) stated how irrigation in the first 3 years after the establishment affected miscanthus belowground growth and size, and the same authors found good aboveground yields during the fourth and fifth years (around 27 and 18 Mg ha−1) when no irrigation was given. These findings are corroborated by Mann et al. (2013b) who investigated the root system dynamics of miscanthus in response to rainfed and irrigated conditions, and highlighted no roots development below a depth of 1.2 m under rainfed conditions, while given supplemental irrigation during the establishment, miscanthus was able to develop roots 3 m down. Therefore, miscanthus growth patterns in sandy‐loam soil (Experiment 1) highlighted the importance of supplying irrigation water also during the years following the establishment. However, in soils characterized by a good water holding capacity (Experiment 2), revealed that irrigation water had no influence on crop productivity. Previous studies conducted in the Mediterranean (central and southern Italy) comparing irrigated and rainfed miscanthus crops gave ambiguous results. In fact, in southern Italy, two‐ and three‐year old crops responded to irrigation only when water supply exceeded 440 mm (Cosentino et al., 2007) or when precipitation during the growing season was rather limited (around 400 mm) (Mantineo et al., 2009). The importance of precipitation for miscanthus grown in Mediterranean was confirmed by Petrini et al. (1996) who compared rainfed and irrigated miscanthus in two different locations in central Italy. In 2‐year old crops no differences in the aboveground yield were recorded at the site with a higher precipitation (>420 mm), while a 58% increase in aboveground dry yield was observed in irrigated miscanthus at the site with a lower precipitation (around 313 mm). Finally, in our experimental site, Ercoli et al. (1999), when comparing the effect of irrigation and nitrogen fertilization on miscanthus yield, observed an increase in about 20% (+4.5 Mg ha−1) in irrigated vs. rainfed plots harvested in autumn. This is consistent with our results: when precipitation during the growing season was rather low (~164 mm) and similar to that reported by Ercoli et al. (1999) (~173 mm), plots receiving irrigation increased their dry yield by around 15% compared to rainfed plots. Conversely, in 2012 when precipitation was much greater (~400 mm) miscanthus under ET0 and ET75 yielded nearly the same." Roncucci et al. 2015, pp. 1005–1006,.
59. Stričević et al. 2015, pp. 1204–1205. However, in table 2, page 1208, the stated rainfall levels for the 20–25 tonne yields is even lower; 220, 220 and 217 mm. It is unclear why the authors went for the 300-400 mm estimation instead of 220 mm.
60. This yield is a result of a computer simulation, it is not an actual measured yield. The authors used FAO's freely available yield prediction software AquaCrop to calculate yield under optimal conditions: "Although Miscanthus generally achieves high yields even when its water supply is low, it responds very well to irrigation, increasing biomass yield by as much as 100% (Cosentino et al., 2007). In Serbia's ecological circumstances, Miscanthus had enough water during the first 3 years of research, but it was under water stress over short periods in the fourth, fifth, and sixth years. To check whether the model generated realistic biomass levels when the water supply was nonlimiting, the file called 'Generation of irrigation schedule' was used and the option 'Replenish when 80% readily available water depleted' was selected. As such, if irrigation is applied, the dates of irrigation and amounts of water need to be entered so that they are accounted for in the water balance. In the present example, instead of entering the dates of irrigation and amounts of water, the model determined how much water was needed and when, to achieve potential yields. The same input data with the addition of irrigation water generated a yield of 42 Mg ha−1, which matched those recorded in Greece and Italy under irrigation and constraint free‐conditions, in similar climatic circumstances and with similar crop densities (Cosentino et al., 2007; Danalatos et al., 2007)." See Stričević et al. 2015, pp. 1206–1207. http://www.fao.org/aquacrop/en/
61. Nsanganwimana et al. 2014, p. 126.
62. Nsanganwimana et al. 2014, p. 128.
63. "Miscanthus grown on contaminated soils can contain higher shoot TE [trace elements; metals and metalloids] concentrations, but the TF [translocation factor], which is for the most part less than 1, indicates that root-to-shoot TE transfer is minimized (Table 3). The combination of this trait with low BCF [bio concentration factor] and higher TE concentrations in roots than in shoots demonstrates the capacity to contain TE in soils. Owing to the perennial growth and its ability to stabilize TE and degrade some organic pollutants, Miscanthus could potentially limit pollutant transfer into different environmental compartments by reducing (1) pollutant leaching from the root zone and groundwater contamination, (2) pollutant run-off (water erosion) and surface water contamination, (3) dust emission into the atmosphere due to wind erosion and seasonal soil tillage, and (4) pollutant transfer into plant AG [above ground] parts and thus transfer into food chains. Therefore, as non-food crops, Miscanthus forms a potential resource for phytomanagement of contaminated areas, with the option of TE phytostabilization and/or organic pollutant degradation, hence the opportunity to reduce both human and environmental risks." Nsanganwimana et al. 2014, p. 129.
64. Nsanganwimana et al. 2014, p. 129.
65. Nsanganwimana et al. 2014, p. 131.
66. Clifton-Brown et al. 2017, p. 2.
67. Smil 2015, p. 211, box 7.1.
68. Smil 2015, p. 170.
69. Smil 2015, p. 2095 (kindle location).
70. Smil 2015, p. 91.
71. Smil 2015, p. 89.
72. Smil 2015, p. 227.
73. Smil 2015, p. 228.
74. Smil 2015, p. 90.
75. Smil 2015, p. 229.
76. Smil 2015, pp. 80, 89.
77. Smil 2015, p. 85.
78. Smil 2015, p. 86.
79. Schwarz 1993, p. 413.
80. Flores et al. 2012, p. 831.
81. Ghose 2011, p. 263.
82. Cf. Smil's estimate of 0.60 W/m2 for the 10 t/ha yield above. The calculation is: Yield (t/ha) multiplied with energy content (GJ/t) divided by seconds in a year (31 556 926) multiplied with the number of square metres in one hectare (10 000).
83. "The raw material for wood pellets is woody biomass in accordance with Table 1 of ISO 17225‑1. Pellets are usually manufactured in a die, with total moisture content usually less than 10 % of their mass on wet basis." ISO (International Organization for Standardization) 2014a.
84. "The raw material for non-woody pellets can be herbaceous biomass, fruit biomass, aquatic biomass or biomass blends and mixtures. These blends and mixtures can also include woody biomass. They are usually manufactured in a die with total moisture content usually less than 15 % of their mass." ISO (International Organization for Standardization) 2014b.
85. Transmission loss data from the World Bank, sourced from IEA. The World Bank 2010.
86. van den Broek 1996, p. 271.
87. Additionally, Smil estimates that newly installed photovoltaic solar parks reaches 7–11 W/m2 in sunny regions of the world. Smil 2015, p. 191.
88. Milner et al. 2016, p. 320.
89. "Soil carbon stocks are a balance between the soil organic matter decomposition rate and the organic material input each year by vegetation, animal manure, or any other organic input." McCalmont et al. 2017, p. 496.
90. Clifton‐Brown, Breuer & Jones 2007, p. 2297.
91. Agostini, Gregory & Richter 2015, p. 1058, fig. 1.
92. Zang et al. 2017, p. 262, 269.
93. Dondini et al. 2009, pp. 414, 419–420.
94. Poeplau & Don 2014, p. 335.
95. Harris, Spake & Taylor 2015, p. 31.
96. "SOC [soil organic carbon] derived from crop inputs will be lower during the early years of establishment (Zimmermann et al., 2012) with disturbance losses of resident C3 carbon outpacing C4 inputs when planted into grassland." McCalmont et al. 2017, p. 496.
97. Likewise, N2O (nitrous oxide) emissions vary strongly with prior land use, crop maturity, and fertilzation rate, however "[...] postestablishment emissions from perennial crops were generally much lower than emissions from annual crops [...] we conclude that targeting low carbon soils for perennial bioenergy crop cultivation will reduce soil carbon losses in the short‐term and promote soil carbon sequestration in the long‐term. Globally, it is proposed that managing land to promote such sequestration, and avoid loss, may be a valuable tool in the mitigation of climate change (Lal, 2003)." Whitaker et al. 2018, pp. 152, 154.
98. "Any soil disturbance, such as ploughing and cultivation, is likely to result in short-term respiration losses of soil organic carbon, decomposed by stimulated soil microbe populations (Cheng, 2009; Kuzyakov, 2010). Annual disturbance under arable cropping repeats this year after year resulting in reduced SOC levels. Perennial agricultural systems, such as grassland, have time to replace their infrequent disturbance losses which can result in higher steady-state soil carbon contents (Gelfand et al., 2011; Zenone et al., 2013)." McCalmont et al. 2017, p. 493.
99. "Tillage breaks apart soil aggregates which, among other functions, are thought to inhibit soil bacteria, fungi and other microbes from consuming and decomposing SOM (Grandy and Neff 2008). Aggregates reduce microbial access to organic matter by restricting physical access to mineral-stabilised organic compounds as well as reducing oxygen availability (Cotrufo et al. 2015; Lehmann and Kleber 2015). When soil aggregates are broken open with tillage in the conversion of native ecosystems to agriculture, microbial consumption of SOC and subsequent respiration of CO2 increase dramatically, reducing soil carbon stocks (Grandy and Robertson 2006; Grandy and Neff 2008)." IPCC 2019a, p. 393.
100. Felten & Emmerling 2012, p. 661.
101. "Five options have large mitigation potential (>3 GtCO2e yr–1) without adverse impacts on the other challenges (high confidence). These are: increased food productivity; reduced deforestation and forest degradation; increased soil organic carbon content; fire management; and reduced post-harvest losses. [...] Increasing soil carbon stocks removes CO2 from the atmosphere and increases the water-holding capacity of the soil, thereby conferring resilience to climate change and enhancing adaptation capacity. [...] Since increasing soil organic matter content is a measure to address land degradation (see Section 6.2.1), and restoring degraded land helps to improve resilience to climate change, soil carbon increase is an important option for climate change adaptation. With around 120,000 km2 lost to degradation every year, and over 3.2 billion people negatively impacted by land degradation globally (IPBES 2018), practices designed to increase soil organic carbon have a large potential to address adaptation challenges (Table 6.23)." IPCC 2019d, p. 591, 572, 591.
102. Dondini et al. 2009, p. 422. The authors do not quantify the above-ground dry mass yield, instead the median of McCalmont's 10-15 tonnes estimation for the whole of the UK is used here (see McCalmont et al. 2017, p. 497), together with Kahle et al.'s miscanthus carbon content estimation of 48% (see Kahle et al. 2001, table 3, page 176.
103. Milner et al. 2016, table 4, page 322, 323. Given the mean UK dry mass yield of 12.5 tonnes per hectare (see McCalmont et al. 2017, p. 497), together with Kahle et al.'s miscanthus carbon content estimation of 48% (see Kahle et al. 2001, table 3, page 176.
104. Nakajima et al. 2018, p. 1. In general, lower net accumulation rates for young plantations are to be expected, because of accelerated carbon decay and therefore CO2 emissions at the time of planting (see Soil carbon input/output. The authors quote a dry mass yield of 25.6 (± 0.2) tonnes per hectare per year. Carbon content estimation 48% (see Kahle et al. 2001, table 3, page 176).
105. The 16 year Miscanthus site had 106 tonnes of below-ground carbon per hectare. Control site 1 had 91 tonnes of below-ground carbon, control site 2 had 92 tonnes. Mean difference to the control sites 15.5 tonnes. For above-ground carbon, the total harvested dry matter per hectare for the 16 year site was 114 tonnes, or 7.13 tonnes per year. After 16 years, the total belowground carbon derived from Miscanthus (C4) had reached 18 tonnes, equivalent to 29% of the total inputted Miscanthus carbon over the years, in the form of fallen leaves, rhizomes and roots. The mean miscanthus-derived carbon input per year was 1.13 tonnes. Hansen et al. 2004, pp. 102–103.
106. "[...] it seems likely that arable land converted to Miscanthus will sequester soil carbon; of the 14 comparisons, 11 showed overall increases in SOC over their total sample depths with suggested accumulation rates ranging from 0.42 to 3.8 Mg C ha−1 yr−1. Only three arable comparisons showed lower SOC stocks under Miscanthus, and these suggested insignificant losses between 0.1 and 0.26 Mg ha−1 yr−1." McCalmont et al. 2017, p. 493.
107. "The correlation between plantation age and SOC can be seen in Fig. 6, [...] the trendline suggests a net accumulation rate of 1.84 Mg C ha−1 yr−1 with similar levels to grassland at equilibrium." McCalmont et al. 2017, p. 496.
108. Given the EU average peak yield of 22 tonnes dry matter per hectare per year (approximately 15 tonnes during spring harvest). See Anderson et al. 2014, p. 79). 15 tonnes also explicitly quoted as the mean spring yield in Germany, see Felten & Emmerling 2012, p. 662. 48% carbon content; see Kahle et al. 2001, table 3, page 176.
109. «The variation of total SOM rates of change in the first 5 years after planting Miscanthus was very high, ranging from −4 to 7 mg C ha−1 yr−1 (Fig. 4b). A similar finding was reached elsewhere for the first 2–3 years after Miscanthus planting: −6.9 to 7.7 mg C ha−1 yr−1 (Zimmerman et al., 2011). The variation of annual SOM change decreased with time and was negligible after 15 years (Fig. 4b).»Zang et al. 2017, p. 267.
110. Nunes, Matias & Catalão 2017, p. 27.
111. Bridgeman et al. 2010, p. 845.
112. "[...] [M]iscanthus had different chemical properties to that of ordinary wood pellets and requires specific boiler technologies to handle its alternative burning nature [...]. There are various boiler manufacturers and suppliers who claim they would be happy to utilise miscanthus in their boilers and will stand over the warranty with its use. However not every boiler supplier is happy to use miscanthus. Invariably if the boiler can utilise miscanthus it can also deal with less troublesome fuels such as wood but not the other way around." Caslin, Finnan & Easson 2010, pp. 31, 32.
113. "Biomass production costs for miscanthus are presently too high to compete commercially with fossil fuels on an energy basis. The high biomass production costs for miscanthus result from insufficient development of agricultural production technology, accompanied by additional costs for agricultural inputs, land and labor for a relatively low-value biomass. Although they are amortized over a production period of 10–25 years, initial establishment costs for miscanthus are still comparatively high. This is because the only commercially available genotype Miscanthus × giganteus is a triploid hybrid that does not produce viable seeds. Consequently, costly establishment via rhizome or in vitro propagation has to be performed (Xue et al., 2015). Miscanthus is also new to farmers and they have neither the knowledge nor the technical equipment to cultivate it. Thus, inefficient production technology is currently limiting its widespread uptake as a biomass crop. There are no stable markets for miscanthus biomass and relevant applications are low-value. Farmers are hesitant to cultivate miscanthus because it involves dedicating their fields to long-term biomass production. They will only be willing to do this once biomass markets are stable or if long-term contracts are available (Wilson et al., 2014). The main use of lignocellulosic biomass from perennial crops is as a solid fuel for heat and power generation—a comparatively low-value use, its profitability being ultimately determined by the price of fossil fuels. In Europe, subsidies are generally necessary for bioenergy products to be able to compete in retail energy markets—with the notable exception of forest wood and forestry by-products that cannot be used for wood material products. Therefore, also higher-value applications for miscanthus biomass are required in order to provide attractive market options. There are no miscanthus varieties adapted to different site characteristics and biomass use options. In Europe, Miscanthus × giganteus is the only genotype commercially available. Major barriers to the breeding of miscanthus varieties are the high costs involved and the long breeding periods, necessary because most yield- and quality-relevant parameters are not quantifiable until after the establishment phase of 2–3 years." Lewandowski et al. 2016, p. 2.
114. "Miscanthus can be harvested by cutting with a conditioner mower and baling in large Heston bales or round bales and then chipped out of the bales. It can also be chipped by a maize Kemper header on harvest. However the problem with this type of harvest is the crops low bulk density of approx 50 – 130 kg/m3. The crop is very bulky and will take up a lot of storage space on harvest. Additionally, storage of chips may be problematic if the chips are too small or too wet as heating may occur. The other potential problem with the miscanthus is due to its fluffy nature in chip form it can potentially bridge or get blocked while feeding into the boiler combustion zone. However a suitable auger feed in mechanism will overcome this issue. [...] When transporting miscanthus in bulk chipped form it can be transported in 96 m3 loads. Most operators report minimum loads of 11.5 tonnes per load at 20% moisture indicating a bulk density of about 120 kg/m3 which equates to €1.60 per GJ of energy delivered." Caslin, Finnan & Easson 2010, pp. 31, 33.
115. "Large rectangular and round balers are capable of producing bales with a dry matter density of between 120 and 160 kg/m3 and weighing between 250 and 600kg." Caslin, Finnan & Easson 2010, p. 22. In addition, Huisman 2001, p. 2098 quotes 250 kg/m3 for high density balers.
116. Huisman 2001, p. 2098.
117. Wild 2015, p. 72.
118. Smil 2015, p. 13.
119. Torrefaction benefits.
120. "Briquetting reduces electricity consumption in densification by almost 50% in respect to pelleting (Personal Communication, Wolfgang Stelte). In this case, the energy consumption advantage of the torrefaction chain versus the WWP chain almost doubles to 10,3%. The GHG advantage increases accordingly, to a 33% reduction of torrefied wood briquettes (TWB) compared to WWP, as can be seen in Figure 9." Wild & Visser 2018, pp. 16–17.
121. Wild & Visser 2018, p. 13.
122. Torrefied biomass has a moisture content of 1-5% (coal has 10-15%). The reason there is still some moisture in torrefied mass in spite of its hydrophobic quality, is small cracks or fissures in the pellets or briquettes that makes it possible for moisture to enter. Wild 2015, pp. 72, 74.
123. Wild 2015, p. 73.
124. Li et al. 2018, p. 181.
125. Bridgeman et al. 2010, p. 3912.
126. "Flame stability can be further exacerbated by differences in particle size as large particle sizes can act as heat sinks, increasing the resonance time of the particle before ignition and influencing the balance of heat loss and heat release. For a stable flame in a pulverised coal operation, pulverisation of fuel to 70% below 75 µm is typically required. [It is required to reduce at least 70% of the total amount of particles to below 75 µm in size.] The ease in which fuels can be pulverised to 70% below 75 µm is described using the Hardgrove Grindability Index (HGI). Coals typically lie between 30 (increased resistance to pulverization) and 100 (more easily pulverised) on the scale. The HGI for the unprocessed Miscanthus and processed bio-coals are given in Table 3. The unprocessed Miscanthus has an HGI of zero which essentially implies under the test conditions, that no fuel would reach the desired 75 µm and thus, assuming co-milling, there would be either a greater energy requirement for milling to achieve 75 µm or the pulverised fuel particles would be greater than 75 µm in diameter." Smith et al. 2018, p. 551.
127. Ndibe et al. 2015, p. 177.
128. Bridgeman et al. 2010, p. 3916. Smith et al. measured a HGI of 150 for Miscanthus pre-treated with hydrothermal carbonisation, sometimes called "wet" torrefaction: "The HGI of 150 (see Table 3) for the samples processed at 250 °C also imply that the fuel will easily pulverise and there should be limited issues with flame stability brought about though larger particle diameters encountered with untreated biomass." Smith et al. 2018, p. 554.
129. Cremers et al. 2015, p. 11.
130. "On average, coals used in UK power stations have a HGI around 40–60; the La Loma coal tested in this work falls within this range with a HGI of 46." Williams et al. 2015, p. 382.
131. Wild & Visser 2018, p. 17.
132. Ndibe et al. 2015, p. 189.
133. Ren et al. 2017, p. 38.
134. Johansen et al. 2011, p. B.
135. "Inorganics can be a particular issue for Miscanthus during combustion as large amounts of alkali and alkaline metals, particularly potassium and sodium, along with sulphur and chlorine influence ash chemistry and influence the behaviours of the fuel in terms of its tendency to corrode equipment and cause slagging, fouling and in certain furnaces bed agglomeration. [...] Fouling is a phenomenon brought about when potassium and sodium, in combination with chlorine, partially evaporate when exposed to radiant heat and form alkali chlorides which condense on cooler surfaces such as heat exchangers. These deposits don't just reduce heat exchanger efficiency; they also play a major role in corrosion as these deposits can react with sulphur in the flue gas to form alkali sulphates releasing chlorine. This chlorine has a catalytic effect which results in the active oxidation and corrosion of the furnace material." Smith et al. 2018, pp. 554, 556.
136. "In the combustion of miscanthus, the inorganic constituents remain as ash. The typical total ash content of miscanthus is in the range of 2.0% to 3.5%. In grate-fired combustion systems, the coarser ash is discharged as bottom ash while the finer ash fraction leaves the combustion zone with the off-gas as fly ash. Because of the low ash melting temperature, which is strongly correlated with the potassium and chloride content of the ash, the combustion temperature is kept as low as possible." Lanzerstorfer 2019, pp. 1–2.
137. "Slagging is a phenomenon brought about though the melting of ash when ash deposits are exposed to radiant heat, such as flames in a furnace. As most furnaces are designed to remove ash as a powdery residue, having a high ash melting temperature is often desirable. Otherwise it has a higher tendency to fuse into a hard glassy slag, known as a clinker, which can be difficult to remove from the furnace. [...] The AFT is a qualitative method of assessing the propensity of a fuel to slag and works by heating an ash test piece and analysing the transitions in the ash chemistry. Key transitions include; (i) shrinkage, which predominantly represents the decomposition of carbonates in hydrothermally derived chars, (ii) deformation temperature, essentially representing the onset point at which the powdery ash starts to agglomerate and starts to stick to surfaces, (iii) hemisphere, whereby ash is agglomerating and is sticky and (v) flow, whereby the ash melts. For most power stations, slagging becomes problematic between the deformation and hemisphere temperature." Smith et al. 2018, p. 554.
138. "For Miscanthus to best fit the combustion quality requirements, it is conventionally harvested during the late winter or early spring in the UK, after which the crop has fully senesced and nutrients have been remobilised into the rhizome. [...] Moreover while late harvested Miscanthus samples have improved fuel quality, with lower nitrogen, chlorine, ash and alkaline metal content, the results presented in Baxter et al., [2] indicate that slagging, fouling and corrosion is still most probable in most crops. Thus, the reduction in nutrients brought about by overwintering is still insufficient to lead to safe combustion [...]." Smith et al. 2018, p. 546.
139. Saleh 2013, p. 100. Saleh also found an approximate 65% reduction for straw. Likewise, Ren et al. found that "[...] 59.1 wt%, 60.7 wt% and 77.4 wt% of the chlorine contents of olive residues, DDGS and corn straw, respectively, were released during torrefaction". Ren et al. 2017, p. 40.
140. Ren et al. 2017, p. 45.
141. Kambo & Dutta 2015, p. 752.
142. Johansen et al. found that "[...] Cl [chlorine] is the main facilitator for K [potassium] release through sublimation [direct gas release] of KCl [potassium chloride] [...]." Potassium chloride is the "[...] dominant Cl species found in biomass, [...]" and it remains stable in the solid phase until temperatures reach 700-800 °C. Note that a small amount (5-10 %) of potassium release has been observed at temperatures below 700 °C. At the threshold point, "[...] the high temperature release of K [potassium] in the form of KCl [potassium chloride] is equivalent to the available amount of total Cl [chlorine] in the feedstock fuel." In other words, the "[...] K [potassium] release seems to be limited by the quantity of available Cl [chlorine]." Thus, it is mainly the bonding with chlorine that makes it possible for potassium to become a gas and foul the inside of the combustion equipment; the release of potassium "[...] will cease as the fuel, undergoing pyrolysis or combustion, reaches a state of complete dechlorination." At this point, potassium will instead fuse with silicates and aluminiosilicates at approximately 800 °C, and will be retained in the ash. Johansen et al. 2011, pp. 4961, 4962, 4968.
143. Li et al. 2018, p. 182.
144. "Recent studies by Reza et al. and Smith et al. have reported of the fate of inorganics and heteroatoms during HTC [hydrothermal carbonisation] of Miscanthus and indicate significant removal of the alkali metals, potassium and sodium, along with chlorine. [...] Analysis of ash melting behaviour in Smith et al., showed a significant reduction in the slagging propensity of the resulting fuel, along with the fouling and corrosion risk combined. [...] Consequently HTC offers the potential to upgrade Miscanthus from a reasonably low value fuel into a high grade fuel, with a high calorific value, improved handling properties and favourable ash chemistry. [...] HTC at 250 °C can overcome slagging issues and increase the ash deformation temperature from 1040 °C to 1320 °C for early harvested Miscanthus. The chemistry also suggests a reduction in fouling and corrosion propensity for both 250 °C treated fuels." Smith et al. 2018, pp. 547, 556.
145. Ribeiro et al. 2018, pp. 12, 13.
146. "The environmental costs and benefits of bioenergy have been the subject of significant debate, particularly for first‐generation biofuels produced from food (e.g. grain and oil seed). Studies have reported life‐cycle GHG savings ranging from an 86% reduction to a 93% increase in GHG emissions compared with fossil fuels (Searchinger et al., 2008; Davis et al., 2009; Liska et al., 2009; Whitaker et al., 2010). In addition, concerns have been raised that N2O emissions from biofuel feedstock cultivation could have been underestimated (Crutzen et al., 2008; Smith & Searchinger, 2012) and that expansion of feedstock cultivation on agricultural land might displace food production onto land with high carbon stocks or high conservation value (i.e. iLUC) creating a carbon debt which could take decades to repay (Fargione et al., 2008). Other studies have shown that direct nitrogen‐related emissions from annual crop feedstocks can be mitigated through optimized management practices (Davis et al., 2013) or that payback times are less significant than proposed (Mello et al., 2014). However, there are still significant concerns over the impacts of iLUC, despite policy developments aimed at reducing the risk of iLUC occurring (Ahlgren & Di Lucia, 2014; Del Grosso et al., 2014)." Whitaker et al. 2018, p. 151.
147. "The impact of growing bioenergy and biofuel feedstock crops has been of particular concern, with some suggesting the greenhouse gas (GHG) balance of food crops used for ethanol and biodiesel may be no better or worse than fossil fuels (Fargione et al., 2008; Searchinger et al., 2008). This is controversial, as the allocation of GHG emissions to the management and the use of coproducts can have a large effect on the total carbon footprint of resulting bioenergy products (Whitaker et al., 2010; Davis et al., 2013). The potential consequences of land use change (LUC) to bioenergy on GHG balance through food crop displacement or 'indirect' land use change (iLUC) are also an important consideration (Searchinger et al., 2008)." Milner et al. 2016, pp. 317–318.
148. "While the initial premise regarding bioenergy was that carbon recently captured from the atmosphere into plants would deliver an immediate reduction in GHG emission from fossil fuel use, the reality proved less straightforward. Studies suggested that GHG emission from energy crop production and land-use change might outweigh any CO2 mitigation (Searchinger et al., 2008; Lange, 2011). Nitrous oxide (N2O) production, with its powerful global warming potential (GWP), could be a significant factor in offsetting CO2 gains (Crutzen et al., 2008) as well as possible acidification and eutrophication of the surrounding environment (Kim & Dale, 2005). However, not all biomass feedstocks are equal, and most studies critical of bioenergy production are concerned with biofuels produced from annual food crops at high fertilizer cost, sometimes using land cleared from natural ecosystems or in direct competition with food production (Naik et al., 2010). Dedicated perennial energy crops, produced on existing, lower grade, agricultural land, offer a sustainable alternative with significant savings in greenhouse gas emissions and soil carbon sequestration when produced with appropriate management (Crutzen et al., 2008; Hastings et al., 2008, 2012; Cherubini et al., 2009; Dondini et al., 2009a; Don et al., 2012; Zatta et al., 2014; Richter et al., 2015)." McCalmont et al. 2017, p. 490.
149. "Significant reductions in GHG emissions have been demonstrated in many LCA studies across a range of bioenergy technologies and scales (Thornley et al., 2009, 2015). The most significant reductions have been noted for heat and power cases. However, some other studies (particularly on transport fuels) have indicated the opposite, that is that bioenergy systems can increase GHG emissions (Smith & Searchinger, 2012) or fail to achieve increasingly stringent GHG savings thresholds. A number of factors drive this variability in calculated savings, but we know that where significant reductions are not achieved or wide variability is reported there is often associated data uncertainty or variations in the LCA methodology applied (Rowe et al., 2011). For example, data uncertainty in soil carbon stock change following LUC has been shown to significantly influence the GHG intensity of biofuel production pathways (Fig. 3), whilst the shorter term radiative forcing impact of black carbon particles from the combustion of biomass and biofuels also represents significant data uncertainty (Bond et al., 2013)." Whitaker et al. 2018, pp. 156–157.
150. Zang et al. 2017, p. 269, fig. 6.
151. See Whitaker et al. 2018, p. 156. For calculations, see appendix S1
152. See Emmerling & Pude 2017, pp. 275–276. Emmerling & Pude paraphrase Felten et al. 2013. For yield, carbon sequestration and GHG calculations, see Felten et al. 2013, pp. 160, 166, 168.
153. "Whilst these values represent the extremes, they demonstrate that site selection for bioenergy crop cultivation can make the difference between large GHG [greenhouse gas] savings or losses, shifting life‐cycle GHG emissions above or below mandated thresholds. Reducing uncertainties in ∆C [carbon increase or decrease] following LUC [land use change] is therefore more important than refining N2O [nitrous oxide] emission estimates (Berhongaray et al., 2017). Knowledge on initial soil carbon stocks could improve GHG savings achieved through targeted deployment of perennial bioenergy crops on low carbon soils (see section 2). [...] The assumption that annual cropland provides greater potential for soil carbon sequestration than grassland appears to be over‐simplistic, but there is an opportunity to improve predictions of soil carbon sequestration potential using information on the initial soil carbon stock as a stronger predictor of ∆C [change in carbon amount] than prior land use." Whitaker et al. 2018, pp. 156, 160.
154. "Fig. 3 confirmed either no change or a gain of SOC [soil organic carbon] (positive) through planting Miscanthus on arable land across England and Wales and only a loss of SOC (negative) in parts of Scotland. The total annual SOC change across GB in the transition from arable to Miscanthus if all nonconstrained land was planted with would be 3.3 Tg C yr−1 [3.3 million tonnes carbon per year]. The mean changes for SOC for the different land uses were all positive when histosols were excluded, with improved grasslands yielding the highest Mg C ha−1 yr−1 [tonnes carbon per hectare per year] at 1.49, followed by arable lands at 1.28 and forest at 1. Separating this SOC change by original land use (Fig. 4) reveals that there are large regions of improved grasslands which, if planted with bioenergy crops, are predicted to result in an increase in SOC. A similar result was found when considering the transition from arable land; however for central eastern England, there was a predicted neutral effect on SOC. Scotland, however, is predicted to have a decrease for all land uses, particularly for woodland due mainly to higher SOC and lower Miscanthus yields and hence less input." Milner et al. 2016, p. 123.
155. "In summary, we have quantified the impacts of LUC [land use change] to bioenergy cropping on SOC and GHG balance. This has identified LUC from arable, in general to lead to increased SOC, with LUC from forests to be associated with reduced SOC and enhanced GHG emissions. Grasslands are highly variable and uncertain in their response to LUC to bioenergy and given their widespread occurrence across the temperate landscape, they remain a cause for concern and one of the main areas where future research efforts should be focussed." Harris, Spake & Taylor 2015, p. 37 (see also p. 33 regarding SOC variations). The authors note however that "[t]he average time since transition across all studies was 5.5 years (Xmax 16, Xmin 1) for SOC" and that "[...] the majority of studies considered SOC at the 0–30 cm profile only [...]." Harris, Spake & Taylor 2015, pp. 29–30. Low carbon accumulation rates for young plantations are to be expected, because of accelerated carbon decay at the time of planting (due to soil aeration), and relatively low mean carbon input to the soil during the establishment phase (2-3 years). Also, since dedicated energy crops like miscanthus produce significantly more biomass per year than regular grasslands, and roughly 25% of the carbon content of that biomass is successfully added to the soil carbon stock every year (see Net annual carbon accumulation), it seems reasonable to expect that over time, soil organic carbon will increase also on converted grasslands. The authors quote a carbon building phase of 30-50 years for perennials on converted grasslands, see Harris, Spake & Taylor 2015, p. 31.
156. Agostini, Gregory & Richter 2015, p. 1068.
157. Anderson-Teixeira et al. 2012, pp. 2039–2040.
158. "After centuries of burning wood for energy or processing forage into horse power, the first generation of bioenergy feedstocks were food crops, such as maize, oil seed rape, sugar cane, and oil palm, used to produce bioethanol and biodiesel. These required a high input in terms of fertilizer and energy, which increased their carbon footprint (St. Clair et al., 2008). In addition, the carbon cost of converting the food crop feedstock to bioethanol or biodiesel was significant with a low ratio of energy produced to energy input, high GHG cost and a low productivity in terms of GJ of energy per hectare of land (Hastings et al., 2012). Another drawback of using food crops for energy production is the pressure put on the balance of supply and demand for these feedstocks which can impact the cost of food (Valentine et al., 2011) and the increase of indirect land use change (ILUC) to increase the arable cropped area (Searchinger et al., 2008) which consequentially increases their environmental footprint. The second generation bioenergy crop Miscanthus almost always has a smaller environmental footprint than first generation annual bioenergy ones (Heaton et al., 2004, 2008; Clifton-Brown et al., 2008; Gelfand et al., 2013; McCalmont et al., 2015a; Milner et al., 2015). This is due to its perennial nature, nutrient recycling efficiency and need for less chemical input and soil tillage over its 20-year life-cycle than annual crops (St. Clair et al., 2008; Hastings et al., 2012). Miscanthus can be grown on agricultural land that is economically marginal for food crop production (Clifton-Brown et al., 2015)." Hastings et al. 2017, p. 2.
159. "A systematic review and meta-analysis were used to assess the current state of knowledge and quantify the effects of land use change (LUC) to second generation (2G), non-food bioenergy crops on soil organic carbon (SOC) and greenhouse gas (GHG) emissions of relevance to temperate zone agriculture. Following analysis from 138 original studies, transitions from arable to short rotation coppice (SRC, poplar or willow) or perennial grasses (mostly Miscanthus or switchgrass) resulted in increased SOC (+5.0 ± 7.8% and +25.7 ± 6.7% respectively)." Harris, Spake & Taylor 2015, p. 27.
160. "Our work shows that crop establishment, yield and harvesting method affect the C. cost of Miscanthus solid fuel which for baled harvesting is 0.4 g CO2 eq. C MJ−1 for rhizome establishment and 0.74 g CO2 eq. C MJ−1 for seed plug establishment. If the harvested biomass is chipped and pelletized, then the emissions rise to 1.2 and 1.6 g CO2 eq. C MJ−1, respectively. The energy requirements for harvesting and chipping from this study that were used to estimate the GHG emissions are in line with the findings of Meehan et al. (2013). These estimates of GHG emissions for Miscanthus fuel confirm the findings of other Life Cycle Assessment (LCA) studies (e.g., Styles and Jones, 2008) and spatial estimates of GHG savings using Miscanthus fuel (Hastings et al., 2009). They also confirm that Miscanthus has a comparatively small GHG footprint due to its perennial nature, nutrient recycling efficiency and need for less chemical input and soil tillage over its 20-year life-cycle than annual crops (Heaton et al., 2004, 2008; Clifton-Brown et al., 2008; Gelfand et al., 2013; McCalmont et al., 2015a; Milner et al., 2015). In this analysis, we did not consider the GHG flux of soil which was shown to sequester on average in the United Kingdom 0.5 g of C per MJ of Miscanthus derived fuel by McCalmont et al. (2015a). Changes in SOC resulting from the cultivation of Miscanthus depend on the previous land use and associated initial SOC. If high carbon soils such as peatland, permanent grassland, and mature forest are avoided and only arable and rotational grassland with mineral soil is used for Miscanthus then the mean increase in SOC for the first 20-year crop rotation in the United Kingdom is ∼ 1–1.4 Mg C ha−1 y−1 (Milner et al., 2015). In spite of ignoring this additional benefit, these GHG cost estimates compare very favorably with coal (33 g CO2 eq. C MJ−1), North Sea Gas (16), liquefied natural gas (22), and wood chips imported from the United States (4). In addition, although Miscanthus production C. cost is only < 1/16 of the GHG cost of natural gas as a fuel (16–22 g CO2 eq. C MJ-1), it is mostly due to the carbon embedded in the machinery, chemicals and fossil fuel used in its production. As the economy moves away from dependence on these fossil fuels for temperature regulation (heat for glasshouse temperature control or chilling for rhizome storage) or transport, then these GHG costs begin to fall away from bioenergy production. It should be noted, the estimates in this paper do not consider either the potential to sequester C. in the soil nor any impact or ILUC (Hastings et al., 2009)." Hastings et al. 2017, pp. 12–13.
161. "Perennial Miscanthus has energy output/input ratios 10 times higher (47.3 ± 2.2) than annual crops used for energy (4.7 ± 0.2 to 5.5 ± 0.2), and the total carbon cost of energy production (1.12 g CO2-C eq. MJ−1) is 20–30 times lower than fossil fuels." McCalmont et al. 2017, p. 489.
162. "The results in Fig. 3c show most of the land in the UK could produce Miscanthus biomass with a carbon index that is substantially lower, at 1.12 g CO2-C equivalent per MJ energy in the furnace, than coal (33), oil (22), LNG (21), Russian gas (20), and North Sea gas (16) (Bond et al., 2014), thus offering large potential GHG savings over comparable fuels even after accounting for variations in their specific energy contents. Felten et al. (2013) found Miscanthus energy production (from propagation to final conversion) to offer far higher potential GHG savings per unit land area when compared to other bioenergy systems. They found Miscanthus (chips for domestic heating) saved 22.3 ± 0.13 Mg [tonnes] CO2-eq ha−1 yr−1 [CO2 equivalents per hectare per year] compared to rapeseed (biodiesel) at 3.2 ± 0.38 and maize (biomass, electricity, and thermal) at 6.3 ± 0.56." McCalmont et al. 2017, p. 500.
163. "The costs and life-cycle assessment of seven miscanthus-based value chains, including small- and large-scale heat and power, ethanol, biogas, and insulation material production, revealed GHG-emission- and fossil-energy-saving potentials of up to 30.6 t CO2eq C ha−1 y−1 and 429 GJ ha−1 y−1, respectively. Transport distance was identified as an important cost factor. Negative carbon mitigation costs of –78€ t−1 CO2eq C were recorded for local biomass use. The OPTIMISC results demonstrate the potential of miscanthus as a crop for marginal sites and provide information and technologies for the commercial implementation of miscanthus-based value chains. [...] The overall biomass transport distance was assumed to be 400 km when bales were transported to the bioethanol plant or to the plant producing insulation material as well as in the value chain 'Combined heat and power (CHP) bales.' For the value chains 'CHP pellets' and 'Heat pellets' the bales were transported 100 km to a pelleting plant and from there the pellets were transported 400 km to the power plants. The average farm-to-field distance was assumed to be 2 km. This transport distance is also assumed for the value chain 'heat chips' in which a utilization of the chips as a biomass fuel on the producing farm was assumed. Because of the higher biomass requirements of the biogas plant an average transport distance of 15 km from field to plant was assumed." Lewandowski et al. 2016, pp. 2, 7.
164. "The highest biomass yields as well as the highest GHG- and fossil-energy savings potentials (up to 30.6 t CO2eq/ha*a and 429 GJ/ha*a, respectively) can be achieved on non-marginal sites in Central Europe. On marginal sites limited by cold (Moscow/Russia) or drought (Adana/Turkey) savings of up to 19.2 t CO2eq/ha*a and 273 GJ/ha*a (Moscow) and 24.0 t CO2eq/ha*a and 338 GJ/ha*a (Adana) can be achieved. The GHG and fossil-energy savings are highest where miscanthus biomass is used as construction material (our analysis uses the example of insulation material). A high GHG- and fossil-energy-saving potential was also found for domestic heating on account of the short transportation distance. Pelleting is only advantageous in terms of the minimization of GHG emissions and energy consumption where biomass is transported over a long distance, for example for heat and power production in CHP. Pelleting requires additional energy, but at the same time reduces the energy required for transport due to its higher density. The lowest GHG- and fossil-energy-saving potentials were found for power production via the biogas pathway, followed by bioethanol. However, this result is strongly influenced by the assumptions that (a) only 50% of the available heat is used and (b) transport distance from the field to the biogas plant is relatively long (15 km). A biogas chain with 100% heat utilization and lower transportation distances would perform better. It can be concluded that for power generation from miscanthus biomass, the most favorable pathway is combustion for base load power, and biogas to cover peak loads." Lewandowski et al. 2016, pp. 19–20.
165. Poeplau & Don 2014, p. 327.
166. "In 2015, a workshop was convened with researchers, policymakers and industry/business representatives from the UK, EU and internationally. Outcomes from global research on bioenergy land‐use change were compared to identify areas of consensus, key uncertainties, and research priorities. [...] Our analysis suggests that the direct impacts of dedicated perennial bioenergy crops on soil carbon and nitrous oxide are increasingly well understood and are often consistent with significant life cycle GHG mitigation from bioenergy relative to conventional energy sources. We conclude that the GHG balance of perennial bioenergy crop cultivation will often be favourable, with maximum GHG savings achieved where crops are grown on soils with low carbon stocks and conservative nutrient application, accruing additional environmental benefits such as improved water quality. The analysis reported here demonstrates there is a mature and increasingly comprehensive evidence base on the environmental benefits and risks of bioenergy cultivation which can support the development of a sustainable bioenergy industry." Whitaker et al. 2018, p. 150.
167. Felten & Emmerling 2011, p. 167.
168. "Felten & Emmerling (2011) compared earthworm abundance under a 15‐year‐old Miscanthus plantation in Germany to cereals, maize, OSR, grassland, and a 20‐year‐old fallow site (after previous cereals). Species diversity was higher in Miscanthus than that in annual crops, more in line with grassland or long‐term fallow with management intensity seen to be the most significant factor; the lower ground disturbance allowed earthworms from different ecological categories to develop a more heterogeneous soil structure. The highest number of species was found in the grassland sites (6.8) followed by fallow (6.4), Miscanthus (5.1), OSR (4.0), cereals (3.7), and maize (3.0) with total individual earthworm abundance ranging from 62 m−2 in maize sites to 355 m−2 in fallow with Miscanthus taking a medium position (132 m−2), although differences in abundance were not found to be significant between land uses. There is some trade‐off in this advantage for the earthworms however; the high‐nitrogen‐use efficiency and nutrient cycling which reduces the need for nitrogen fertilizer and its associated environmental harm means that, despite large volumes being available, Miscanthus leaf litter does not provide a particularly useful food resource due to its low‐nitrogen, high‐carbon nature (Ernst et al., 2009; Heaton et al., 2009) and earthworms feeding on this kind of low‐nitrogen material have been found in other studies to lose overall mass (Abbott & Parker, 1981). In contrast, though, the extensive litter cover at ground level under Miscanthus compared to the bare soil under annual cereals was suggested to be a potentially significant advantage for earthworms in soil surface moisture retention and protection from predation." McCalmont et al. 2017, p. 502.
169. "Our results show that young miscanthus stands sustain high plant species diversity before the canopy closure. Species richness was found to correlate negatively with the density of the stands and to be lower in mature plantations. However, even the 16-year-old, dense miscanthus plantations supported up to 16 different weed species per 25-m2 plot, accounting for up to 12% of the plantation. The literature data support this finding: Miscanthus stands are usually reported to support farm biodiversity, providing habitat for birds, insects, and small mammals (Semere and Slater, 2007a; Bellamy et al., 2009). Studies by Semere and Slater (2007b) have shown biodiversity in miscanthus to be higher than in other crop stands, but still lower than in open field margins." Lewandowski et al. 2016, p. 15.
170. "The diverse ground flora which can inhabit the soil beneath a mature miscanthus canopy will provide food for butterflies, other insects and their predators. Skylarks, meadow pipits and lapwings use miscanthus, as well as 37 other species of birds including wren, linnet and goldfinch that feed on the grass seeds. Once the leaves are shed in winter, a suitable habitat is provided for yellowhammers. Open areas between stools provide ideal habitat for birds such as skylarks and meadow pipits." Caslin, Finnan & Easson 2010, p. 37.
171. "Our study suggests that miscanthus and SRC willows, and the management associated with perennial cropping, would support significant amounts of biodiversity when compared with annual arable crops. We recommend the strategic planting of these perennial, dedicated biomass crops in arable farmland to increase landscape heterogeneity and enhance ecosystem function, and simultaneously work towards striking a balance between energy and food security." Haughton et al. 2016, p. 1071.
172. "Bellamy et al. (2009) looked at bird species and their food resources at six paired sites in Cambridgeshire comparing Miscanthus plantations up to 5 years old with winter wheat rotations in both the winter and summer breeding seasons. The authors found that Miscanthus offered a different ecological niche during each season; most of the frequently occurring species in the winter were woodland birds, whereas no woodland birds were found in the wheat; in summer, however, farmland birds were more numerous. More than half the species occurring across the sites were more numerous in the Miscanthus, 24 species recorded compared to 11 for wheat. During the breeding season, there was once again double the number of species found at the Miscanthus sites with individual abundances being higher for all species except skylark. Considering only birds whose breeding territories were either wholly or partially within crop boundaries, a total of seven species were found in the Miscanthus compared to five in the wheat with greater density of breeding pairs (1.8 vs. 0.59 species ha−1) and also breeding species (0.92 vs. 0.28 species ha−1). Two species were at statistically significant higher densities in the Miscanthus compared to wheat, and none were found at higher densities in the wheat compared to Miscanthus. As discussed, the structural heterogeneity, both spatially and temporally, plays an important role in determining within‐crop biodiversity, autumn‐sown winter wheat offers little overwinter shelter with ground cover averaging 0.08 m tall and very few noncrop plants, whereas the Miscanthus, at around 2 m, offered far more. In the breeding season, this difference between the crops remained evident; the wheat fields provided a uniform, dense crop cover throughout the breeding season with only tram lines producing breaks, whereas the Miscanthus had a low open structure early in the season rapidly increasing in height and density as the season progressed. Numbers of birds declined as the crop grew with two bird species in particular showing close (though opposite) correlation between abundance and crop height; red‐legged partridge declined as the crop grew, whereas reed warblers increased, and these warblers were not found in the crop until it had passed 1 m in height, even though they were present in neighbouring OSR fields and vegetated ditches. In conclusion, the authors point out that, for all species combined, bird densities in Miscanthus were similar to those found in other studies looking at SRC willow and set‐aside fields, all sites had greater bird densities than conventional arable crops. It is through these added resources to an intensive agricultural landscape and reductions in chemical and mechanical pressure on field margins that Miscanthus can play an important role in supporting biodiversity but must be considered complementary to existing systems and the wildlife that has adapted to it. Clapham et al. (2008) reports, as do the other studies here, that in an agricultural landscape, it is in the field margins and interspersed woodland that the majority of the wildlife and their food resources are to be found, and the important role that Miscanthus can play in this landscape is the cessation of chemical leaching into these key habitats, the removal of annual ground disturbance and soil erosion, improved water quality, and the provision of heterogeneous structure and overwinter cover." McCalmont et al. 2017, pp. 502–503.
173. "Two studies, one at IACR-Rothamsted and another in Germany, comparing miscanthus with cereals, indicated that miscanthus seemed to provide a habitat which encourages a greater diversity of species than cereal crops. In these studies three times as many earthworms and spiders were found in the miscanthus crop, miscanthus also supported a greater diversity of spider species. One of the studies also showed that the miscanthus crop had 5 more mammal species and 4 more bird species than a crop of wheat. Spink and Britt (1998) identified miscanthus to be one of the most environmentally benign alternatives to permanent set-aside." Caslin, Finnan & Easson 2010, p. 36.
174. "Miscanthus provides cover for most of the year because, although the crop is harvested annually, it is harvested shortly before the following year's growth begins. This cover can act as a wildlife corridor linking existing habitats. Miscanthus can also act as a nesting habitat, for both ground nesting birds in the early spring e.g. sky larks, and reed nesting birds such as the reed warbler, later in the summer. Miscanthus might be a useful game cover crop and nursery for young pheasants and partridges. A minimum of nine species have been observed in miscanthus, including the brown hare, stoat, mice, vole, shrew, fox and rabbit. Many of these are a useful source of food for larger carnivores such as the barn owl." Caslin, Finnan & Easson 2010, p. 36.
175. "There is also a benefit of reduced chemical inputs and nitrate leaching associated with Miscanthus, significantly improving water quality running off farmland (Christian & Riche, 1998; Curley et al., 2009). McIsaac et al. (2010) reported that inorganic N leaching was significantly lower under unfertilized Miscanthus (1.5–6.6 kg N ha−1 yr−1) than a maize/soya bean rotation (34.2–45.9 kg N ha−1 yr−1)." McCalmont et al. 2017, p. 501.
176. "Significant reductions in leaching of dissolved inorganic nitrogen on a land surface basis are predicted to occur if land already growing maize for ethanol production is converted to a perennial feedstock (Davis et al., 2012; Iqbal et al., 2015). This reduction in leaching is attributed to lower fertilizer requirements, the continuous presence of a plant root sink for nitrogen, and the efficient internal recycling of nutrients by perennial grass species (Amougou et al., 2012; Smith et al., 2013). In support of this, Miscanthus and switchgrass assessed at a plot scale had significantly lower dissolved inorganic nitrogen leaching from subterranean drainage tiles relative to the typical maize/soy rotation, with fertilized plots of switchgrass showing little or no leaching after reaching maturity (Smith et al., 2013). Similarly, results from soil‐based measurements in the same feedstocks showed lower dissolved inorganic nitrogen relative to annual crops (McIsaac et al., 2010; Behnke et al., 2012). A recent meta‐analysis of the available literature concluded that switchgrass and Miscanthus had nine times less subsurface loss of nitrate compared to maize or maize grown in rotation with soya bean (Sharma & Chaubey, 2017). At the basin scale, displacement of maize production for ethanol by cellulosic perennial feedstock production could reduce total leaching by up to 22%, depending on the type of feedstock and management practice employed (Davis et al., 2012; Smith et al., 2013). While these previous studies provide evidence for the potential ecosystem services of transitioning to cellulosic production, it is yet to be established what the total change to dissolved inorganic nitrogen export and streamflow would be under such scenarios. Hydrological processes are tightly coupled to the nitrogen cycle (Castellano et al., 2010, 2013), are key drivers of dissolved inorganic nitrogen transport through streams and rivers (Donner et al., 2002), and are sensitive to LUC (Twine et al., 2004). Various modelling scenarios, where current land cover over the Mississippi River Basin of the United States was altered to accommodate varying proportions of switchgrass or Miscanthus, showed that the impact on streamflow was small relative to the improvement in water quality (VanLoocke et al., 2017)." Whitaker et al. 2018, pp. 157–158.
177. "Blanco-Canqui (2010) point out that this water-use and nutrient efficiency can be a boon on compacted, poorly drained acid soils, highlighting their possible suitability for marginal agricultural land. The greater porosity and lower bulk density of soils under perennial energy grasses, resulting from more fibrous, extensive rooting systems, and reduced ground disturbance, improves soil hydraulic properties, infiltration, hydraulic conductivity, and water storage compared to annual row crops. There may be potentially large impacts on soil water where plantation size is mismatched to water catchment or irrigation availability but note that increased ET and improved ground water storage through increased porosity could be beneficial during high rainfall with storage capability potentially increased by 100 to 150 mm." McCalmont et al. 2017, p. 501.
178. Lewandowski et al. 2016, p. 2.
179. "This study distils a large body of literature into simple statements around the environmental costs and benefits of producing Miscanthus in the UK, and while there is scope for further research, particularly around hydrology at a commercial scale, biodiversity in older plantations or higher frequency sampling for N2O in land-use transitions to and from Miscanthus, clear indications of environmental sustainability do emerge. Any agricultural production is primarily based on human demand, and there will always be a trade-off between nature and humanity or one benefit and another; however, the literature suggests that Miscanthus can provide a range of benefits while minimizing environmental harm. Consideration must be given to appropriateness of plantation size and location, whether there will be enough water to sustain its production and the environmental cost of transportation to end-users; its role as a long-term perennial crop in a landscape of rotational agriculture must be understood so as not to interfere with essential food production. There is nothing new in these considerations, they lie at the heart of any agricultural policy, and decision-makers are familiar with these issues; the environmental evidence gathered here will help provide the scientific basis to underpin future agricultural policy." McCalmont et al. 2017, p. 504.
180. McCalmont et al. 2017, p. 489.
181. "The approach to evaluating ES [ecosystem services] suggests that the growth of 2G bioenergy crops across GB broadly produces beneficial effects when replacing first‐generation crops (Table 1). Beneficial effects on the overall ecosystem rather than specific ES are in agreement with recent reports in the literature (Semere & Slater, 2007a,b; Rowe et al., 2009; Dauber et al., 2010). Benefits of a transition to 2G crops include increased farm‐scale biodiversity (Rowe et al., 2011), improved functional attributes such as predation (Rowe et al., 2013) and a net GHG mitigation benefit (Hillier et al., 2009). Benefits are primarily consequence of low inputs and longer management cycles associated with 2G crops (Clifton‐Brown et al., 2008; St Clair et al., 2008). The benefits may have distinct temporal patterns as establishment and harvest phases of 2G crop production are disruptive and have a short‐term negative impact on ES (Donnelly et al., 2011), although practices could be tailored to ameliorate these; however, this temporal effect has not been considered here and is similar to harvesting and planting food crops, grass or trees. [...] When land is filtered for different planting scenarios under ALC 3 and 4, >92.3% available land will offer a positive ES effect when planting Miscanthus or SRC and such transitions are likely to create a net improvement in GHG balance." Milner et al. 2016, pp. 328–329.
182. "[S]outh‐west and north‐west England were identified as areas where Miscanthus and SRC [short rotation coppice] could be grown, respectively, with favourable combinations of economic viability, carbon sequestration, high yield and positive ES [ecosystem services] benefits. Beneficial impacts were found on 146 583 and 71 890 ha when planting Miscanthus or SRC, respectively, under baseline planting conditions rising to 293 247 and 91 318 ha, respectively, under 2020 planting scenarios. [...] In Great Britain (GB), there are approximately 22.9 M ha of land in total (Lovett et al., 2014). [...] The land available for planting was calculated using constraints maps produced by Lovett et al. (2014) using social and environmental constraints based on 8 factors: road, river and urban areas; slope > 15%; monuments; designated areas; existing protected woodlands; high organic carbon soils; and areas with a high 'naturalness score' such as National Parks and Areas of Outstanding Natural Beauty. This land availability was further constrained using agricultural land classes (ALC) (Lovett et al., 2014) in GB as summarized in Table 7, accomplished by aggregating a map of the ALC data at 100 m2 raster resolution to derive total hectares of land in different ALC in each 1 km2 grid cell." Milner et al. 2016, pp. 317, 320.
183. "[...] [E]vidence does indicate that the use of low‐input perennial crops, such as SRC, Miscanthus and switchgrass, can provide significant GHG savings compared to fossil fuel alternatives provided that reasonable yields are obtained, low carbon soils are targeted (see sections 2 and 3 above), and the development context is one where tension with land use for food (and associated potential for iLUC emissions) is mitigated. There are many cases where these criteria are satisfied." Whitaker et al. 2018, p. 157.
184. "In contrast to annual crops, bioenergy from dedicated perennial crops is widely perceived to have lower life‐cycle GHG emissions and other environmental cobenefits (Rowe et al., 2009; Creutzig et al., 2015). Perennial crops such as Miscanthus and short‐rotation coppice (SRC) willow and poplar have low nitrogen input requirements (with benefits for N2O emissions and water quality), can sequester soil carbon due to reduced tillage and increased belowground biomass allocation, and can be economically viable on marginal and degraded land, thus minimizing competition with other agricultural activities and avoiding iLUC effects (Hudiburg et al., 2015; Carvalho et al., 2017). With respect to the perennial crop sugarcane, large GHG savings can be achieved due to high crop productivity and the use of residues for cogeneration of electricity, whilst the recent shift to mechanized harvest without burning in Brazil should also increase the potential for soil carbon sequestration (Silva‐Olaya et al., 2017). Nevertheless, the site‐level impacts of perennial crop cultivation on ecosystem carbon storage (resulting from dLUC) vary geographically, dependent on soil type and climate (Field et al., 2016)." Whitaker et al. 2018, p. 151.
185. "In the rush to pursue climate change mitigation strategies, the 'carbon neutrality' of bioenergy was not rigorously assessed. As more studies began to include assessment of dLUC and iLUC impacts, the credibility of first‐generation bioenergy as an environmentally sustainable, renewable energy source was damaged. In recent years, a more nuanced understanding of the environmental benefits and risks of bioenergy has emerged, and it has become clear that perennial bioenergy crops have far greater potential to deliver significant GHG savings than the conventional crops currently being grown for biofuel production around the world (e.g. corn, palm oil and oilseed rape). Furthermore, the increasingly stringent GHG savings thresholds for biofuels and bioenergy being introduced in Europe (Council Corrigendum 2016/0382(COD)) and the US (110th Congress of the United States 2007) are providing increased impetus for this transition to perennial bioenergy crops." Whitaker et al. 2018, p. 160.
186. Whitaker et al. 2018, p. 160.
187. Wilson & Heaton 2013.
188. Caslin, Finnan & Easson 2010.