3.D - Agricultural Soils

Last updated on 20 Mar 2020 11:16 (cf. Authors)

NFR-Code Name of Category Method AD EF Key Category 1 State of reporting
3.D Agricultural Soils
consisting of / including source categories
3.D.a.1 Inorganic N-fertilizers (includes also urea application) T2 (NH3), T1 (for NOx) NS,RS D (NH3), D (NOx) L & T: NOx, NH3
3.D.a.2.a Animal manure applied to soils T2, T3 (NH3), T1 (for NOx) M CS (NH3), D (NOx) L & T: NOx, NH3
3.D.a.2.b Sewage sludge applied to soils T1 (for NH3,NOx) NS, RS D (NH3), D (NOx) no key category
3.D.a.2.c Other organic fertilisers applied to soils (including compost) T2 (for NOx, NH3) M CS L & T: NH3 | T: NOx
3.D.a.3 Urine and dung deposited by grazing animals T1 (for NH3, NOx) NS,RS D no key category
3.D.c Farm-level agricultural operations including storage, handling and transport of agricultural products T1 (for TSP, PM10, PM2.5,) NS, RS D L & T: TSP, PM10
3.D.d Off-farm storage, handling and transport of bulk agricultural products NA & for Black Carbon, NR
3.D.e Cultivated crops T2 (NMVOC) NS, RS D no key category
3.D.f Agriculture other including use of pesticides T2 (HCB) NS D L & T: HCB

Country specifics

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NH3 and NOx

In 2018, the category of agricultural soils emitted 336.4 kt NH3 or 55.4 % of the total agricultural NH3 emissions in Germany (606.7 kt NH3). The main contributions to the total NH3 emissions from agricultural soils are the application of manure (3.D.a.2.a), with 196.6 kt (58.5 %) and the application of inorganic N-fertilizers (3.D.a.1) with 73.5 kt (21.9 %).

Application of sewage sludge (3.D.a.2.b) contributes 0.6 % or 1.9 kt NH3.

The application of residues from the digestion of energy crops (3.D.a.2.c) leads to 55.7 kt NH3 or 16.5 %. N excretions on pastures (3.D.a.3) have a share of 8.7 kt NH3 or 2.6 %.

NH3 emissions from application of residues from the digestion of energy crops are excluded from emission accounting by adjustment as they are not considered in the NEC and Gothenburg commitments (see Chapter 11 - Adjustments and Emissions Reduction Commitments).

In 2018, agricultural soils were the source of 98.6 % (116.9 kt) of the total of NOx emissions in the agricultural category (118.6 kt). The NOx emissions from agricultural soils are mostly due to application of inorganic fertilizer (3.D.a.1) (50.5 %) and manure (3.D.a.2.a) (34.2 %). Application of residues from digested energy crops (3.D.a.2.c) contributes 11.8 % to agricultural soil emissions, 4.8 % are due to excretions on pastures (3.D.a.3). Emissions from application of sewage sludge (3.D.a.2.b)) contribute 0.5 %.

All NOx emissions from the agricultural category are excluded from emission accounting by adjustment as they are not considered in the NEC commitments (see Chapter 11 - Adjustments and Emissions Reduction Commitments).

NMVOC

In 2018, the category of agricultural soils contributed 7.8 kt NMVOC or 2.4 % to the total agricultural NMVOC emissions in Germany. The only emission source was cultivated crops (3.D.e). All NMVOC emissions from the agricultural category are excluded from emission accounting by adjustment as they are not considered in the NEC commitments.

TSP, PM10 & PM2.5

In 2018, agricultural soils contributed, respectively, 28.6 % (17.4 kt), 57.0 % (17.4 kt) and 15.0 % (0.7 kt) to the total agricultural TSP, PM10 and PM2.5 emissions (61.1 kt, 30.6 kt, 4.5 kt, respectively). The emissions are reported in category 3.D.c (Farm-level agricultural operations including storage, handling and transport of agricultural products).

3.D.a.1 - Inorganic N-fertilizers

The calculation of NH3 and NOx (NO) emissions from the application of inorganic fertilizers is described in Haenel et al. (2020), Chapter 11.1, [1].

Activity Data

German statistics report the amount of fertilizers sold. Assuming that the change of fertilizers stocked is small compared with the amount of fertilizers sold, the amount of fertilizer sold is taken to be the amount of fertilizer applied.

Table 1: AD for the estimation of NH3 and NOx emissions from application of inorganic fertilizers

2020_3D_Table_1.PNG

Methodology

NH3 emissions from the application of inorganic fertilizers are calculated using the Tier 2 approach according to EMEP (2016)-3D-14ff [10], distinguishing between various fertilizer types, see Table 2. For NOx, the Tier 1 approach described in EMEP (2016) [10]-3D-11ff is applied.

Emission factors

The emission factors for NH3 depend on fertilizer type, see EMEP (2016)-3D-15 [10]. Table 2 lists the EMEP emission factors for the fertilizers used in the inventory. In order to reflect average German conditions the emission factors for cool climate and a pH value lower than 7 was chosen.

Table 2: NH3-EF for inorganic fertilizers
Inorganic fertilizers, emission factors in kg NH3 per kg fertilizer N
Fertilizer type EF
calcium ammonium nitrate 0.008
nitrogen solutions (UREA AN) 0.098
urea 0.155
ammonium phosphates 0.050
other NK and NPK 0.050
other straight fertilizers 0.010

For NOx, the simpler methodology by EMEP (2016)-3D-11ff [10] was used. The emission factor 0.040 from EMEP, 2016-3D, Table 3.1 has the units of kg N2O per kg fertilizer N and was derived from Stehfest and Bouwman (2006), [8] . The German inventory uses the emission factor 0.012 kg NO-N per kg N derived from Stehfest and Bouwman (2006). This is equivalent to an emission factor of 0.03943 kg NOx per kg fertilizer N (obtained by multiplying 0.012 kg NO-N per kg N with the molar weight ratio 46/14 for NO2: NO). The inventory uses the unrounded emission factor.

Table 3: Emission factor for NOx emissions from fertilizer application
Emission factor kg NO-N per kg fertilizer N kg NOx per kg fertilizer N
EFfert 0.012 0.039

Trend discussion for Key Sources

In the last four years (and in the last two years in dramatic fashion) fertilizer sales have decreased. Emissions have fallen accordingly. This is even more the case with NH3 than with NOx, as total NH3 from the application of mineral fertilizers is very strongly correlated with the amount of urea applied (R2 = 0.93), the sales of which have decreased more than for all other mineral fertilizers.

Recalculations

No recalculations were necessary with respect to NH3 and NOx emissions from inorganic fertilizers, as there were no changes in activity data and emission factors.

Planned improvements

No improvements are planned at present.

3.D.a.2.a - Animal manure applied to soils

In this sub category Germany reports the NH3 and NOx (NO) emissions from application of manure (including application of anaerobically digested manure). For an overview see Haenel et al. (2020), Chapter 11.2, [1].

Activity data

The calculation of the amount of N in manure applied is based on the N mass flow approach (see 3.B). It is the total of N excreted by animals in the housing and the N imported with bedding material minus N losses by emissions of N species from housing and storage. Hence, the amount of total N includes the N contained in anaerobically digested manures to be applied to the field.

The frequencies of application techniques and incorporation times as well as the underlying data sources are described in Haenel et al. (2020), Chapter 3.4.3, [1]. The frequencies are provided e. g. in the NIR 2020 [11], Chapter 19.3.2.

Table 4: AD for the estimation of NOx emissions from application of manure

2020_3D_Table_4.PNG

Methodology

NH3 emissions from manure application are calculated separately for each animal species in the mass flow approach by multiplying the respective TAN amount with NH3 emission factors for the various manure application techniques. For details see [3-b-manure-management 3.B] and Haenel et al. (2020), Chapter 4 to 8 and 11.3, [1].
For NOx emissions from manure application the inventory calculates NO-N emissions (see Haenel et al. (2020), Chapter 11.2, [1] that are subsequently converted into NOx emissions by multiplying with the molar weight ratio 46/14. The Tier 1 approach for the application of inorganic fertilizer as described in EMEP (2016)-3D-11ff [10] is used, as no specific methodology is available for manure application.

Emission factors

Table 5 shows the time series of the overall German NH3 IEF defined as the ratio of total NH3-N emission from manure application to the total amount of N spread with manure.

Table 5: IEF for NH3–N from application of manure

2020_3D_Table_5.PNG

For NOx the same emission factor as for the application of inorganic fertilizer was used (see Table 3).

Trend discussion for Key Sources

Both NH3 and NOx emissions from the application of animal manures are key sources. Total NOx is calculated proportionally to the total N in the manures applied which remarkably decreased from 1990 to 1991 due to the decline in animal numbers following the German reunification (reduction of livestock numbers in Eastern Germany). Since then the amount of N in manure applied shows no significant trend (1005 +/- 30 Gg N), see Table 4 and therefore there is no trend in the NOx emissions.
For total NH3 emissions even after 1991 there is a slight negative trend. This is due to the increasing use of application practices with lower NH3 emission factors.
For both gases, emissions are slightly decreasing since 2015. This is due to the fact that cattle and swine animal numbers are declining.

Recalculations

Table REC-1 shows the effects of recalculations on NH3 and NOx emissions. The overall recalculation effects are relatively small. The biggest impact has the update of the N excretions of suckler cows (recalculation No 4, see main agricultural page) and pullets (No 10). Smaller effects, and only on NH3 emissions, derive from the modified consideration of the trailing shoe application in the inventory model GAS-EM (No 14). Other recalculations only have a minor impact and recalculations 1, 12, 13, 15 and 16 do not result in any effect on emissions from manure application. Further details on recalculations are described in Haenel et al. (2020), Chapter 3.5.2.

Table REC-1: Comparison of the NH3 and NOx emissions of the submissions (SUB) 2020 and 2019

2020_3D_Table_2_REC.PNG

Planned improvements

No improvements are planned at present.

3.D.a.2.b – Sewage sludge applied to soils

The calculation of NH3 and NOx (NO) emissions from application of sewage sludge is described in Haenel et al. (2020), Chapter 11.4, [1].

Activity data

N quantities from application of sewage sludge were calculated from data of the German Environment Agency and (since 2009) from data of the Federal Statistical Office (see Table 6). Hence, there was no need to use the “per capita” activity data as proposed by EMEP (2016)-3.D, Table 3-1 [10].

Table 6: AD for the estimation of NH3 and NOx emissions from application of sewage sludge

2020_3D_Table_6.PNG

Methodology

A tier 1 methodology is used (EMEP, 2016, 3D, Chapter 3.3.1 [10]). NH3 and NOx emissions are calculated by multiplying the amounts of N in sewage sludge applied with the respective emission factors.

Emission factors

EMEP (2016)-3.D, Table 3-1 [10] provides Tier 1 emissions factors for NH3 and NOx emissions from application of sewage sludge. However, it must be noted that the units of the NH3 emission factor provided in EMEP (2016)-3.D, Table 3-1 [10] are incorrect. It must read 0.13 kg NH3 per kg N applied instead of 13 kg NH3 per capita, see EMEP (2016)-3.D, Appendix A1.2.2.1. The German inventory uses the equivalent emission factor in NH3-N units which is 0.11 kg NH3-N per kg N applied (cf. the derivation of the emission factor described in the appendix of EMEP (2016)-3D, page 25-26, [10]).
For NOx the same emission factor like for the application of inorganic fertilizer was used (see Table 3).

Trend discussion for Key Sources

NH3 and NOx emissions from the application of sewage sludge are no key sources.

Recalculations

Table REC-2 shows the effects of recalculations on NH3 and NOx emissions. The only change compared to last year’s submission occurs for the year 2017, due to the update of the activity data (recalculation No 13, see main agricultural page. Further details on recalculations are described in Haenel et al. (2020), Chapter 3.5.2.

Table REC-2: Comparison of the NH3 and NOx emissions of the submissions (SUB) 2020 and 2019

2020_3D_Table_3_REC.PNG

Planned improvements

No improvements are planned at present.

3.D.a.2.c - Other organic fertilizers applied to soils

This sub category describes Germany’s NH3 and NOx (NO) emissions from application of residues from digested energy crops. For details see Haenel et al. (2020), Chapters 10.2 and 11.3 [1].

Activity data

Activity data is the amount of N in residues from anaerobic digestion of energy crops when leaving storage. This amount of N is the N contained in the energy crops when being fed into the digestion process minus the N losses by emissions of N species from the storage of the residues (see 3.I). N losses from pre-storage are negligible and there are no N losses from fermenter (see Haenel et al. (2020), Chapter 10.2.1).

Table 7: AD for the estimation of NH3 and NOx emissions from application of residues from anaerobic digestion of energy crops

2020_3D_Table_7.PNG

Methodology

The NH3 emissions are calculated the same way as the NH3 emissions from application of animal manure (3.D.a.2.a). The frequencies of application techniques and incorporation times as well as the underlying data sources are provided e. g. in the NIR 2020 [11], Chapter 19.3.2. The amounts of TAN in the residues applied are obtained from the calculations of emissions from the storage of the digested energy crops (3.I).

For NOx emissions from application of residues the Tier 1 approach for the application of inorganic fertilizer as described in EMEP (2016)-3D-11 [10] is used. The inventory calculates NO emissions that are subsequently converted into NOx emissions by multiplying with the molar weight ratio 46/30.

Emission factors

For NH3 the emission factors for untreated cattle slurry were adopted, see Haenel et al. (2020), Chapter 10.2, [1]. As the NOx method for fertilizer application is used for the calculation of NOx emissions from the application of residues, the emission factor for fertilizer application was used (see Haenel et al. (2020), Chapter 11.1 [1])

Table 8 shows the implied emission factors for NH3 emissions from application of residues from digested energy crops.

Table 8: IEF for NH3-N

2020_3D_Table_8.PNG

Trend discussion for Key Sources

The application of residues from anaerobic digestion of energy crops is a key source for NH3. Emissions are dominated by the amounts of N in the substrates fed into the digestion process and to a lesser extent by the increased use of application techniques with lower emission factors. They have become important since about 2005 and have risen sharply until 2013. Since then, they have changed little each year and tend to decrease slightly in the last few years. The latter is mostly due to a small negative trend of the amounts of energy crops digested.

Recalculations

Table REC-3 shows the effects of recalculations on NH3 and NOx emissions. Differences to last year’s submission are mostly due to the update of activity data (recalculation No 12, see main agricultural page. Smaller effects, and only on NH3 emissions, derive from the modified consideration of the trailing shoe application in the inventory model GAS-EM (No 14). Further details on recalculations are described in Haenel et al. (2020), Chapter 3.5.2.

Table REC-3: Comparison of the NH3 and NOx emissions of the submissions (SUB) 2020 and 2019

2020_3D_Table_4_REC.PNG

Planned improvements

No improvements are planned at present.

3.D.a.3 - Urine and dung deposited by grazing animals

The calculation of NH3 and NOx (NO) emissions from N excretions on pasture is described in Haenel et al. (2020), Chapter 11.5 [1].

Activity data

Activity data for NH3 emissions during grazing is the amount of TAN excreted on pasture while for NOx emissions it is the amount of N excreted on pasture. Table 9 shows the N excretions on pasture. The TAN excretions are derived by multiplying the N excretions with the relative TAN contents provided in 3.B, Table 2.

Table 9: N excretions on pasture

2020_3D_Table_9.PNG

Methodology

NH3 emissions from grazing are calculated by multiplying the respective animal population (3.B, Table 1) with corresponding N excretions and relative TAN contents (3.B, Table 2) and the fraction of N excreted on pasture (Table 9). The result is multiplied with the animal specific emission factor (Table 10). NO emissions are calculated the same way with the exception that the emission factor is related to N excreted instead of TAN.

Emission Factors

The emission factors for NH3 are taken from EMEP (2016)-3B-29, Table 3.9 [10]. They relate to the amount of TAN excreted on pasture. Following the intention of EMEP, 2016-3D, Table 3.11 [10], the inventory uses for NOx the same emission factor as for the application of inorganic fertilizer (see Table 3). In order to obtain NOx emissions (as NO2) the NO-N emission factor of 0.12 kg NO-N per kg N excreted is multiplied by 46/14.

Table 10: Emission factors for emissions of NH3 and NO from grazing
Emission factors
Dairy cows 0.10 kg NH3-N per kg TAN excreted
Other cattle 0.06 kg NH3-N per kg TAN excreted
Horses 0.35 kg NH3-N per kg TAN excreted
Sheep, goats 0.09 kg NH3-N per kg TAN excreted
All animals 0.012 kg NO-N per kg N excreted

++Trend discussion for Key Sources
Emissions from urine and dung deposited by grazing animals are no key sources.

Recalculations

Table REC-4 shows the effects of recalculations on NH3 and NOx emissions. Details on the agricultural recalculations can be found on the main agricultural page. By far the biggest impact has the update of the N-excretion of suckler cows (recalculation No 4, see main agricultural page. Further details on recalculations are described in Haenel et al. (2020), Chapter 3.5.2.

Table REC-4: Comparison of the NH3 and NOx emissions of the submissions (SUB) 2020 and 2019

2020_3D_Table_5_REC.PNG

Planned improvements

No improvements are planned at present.

3.D.c - Farm-level agricultural operations including storage, handling and transport of agricultural products

In this category Germany reports TSP, PM10 and PM2.5 emissions from crop production according to EMEP (2016)-3D-11 [10]. For details see Haenel et al. (2020), Chapter 11.14 [1].

Activity data

The activity data is the total area of arable and horticultural land. This data is provided by official statistics.

Table 11: AD for the estimation of TSP, PM10 and PM2.5 emissions from soils

2020_3D_Table_11.PNG

Methodology

As the Tier 2 methodology described in EMEP (2016)-3D-17 [10] cannot be used due to lack of input data, the Tier 1 methodology described in EMEP(2016)-3D-11ff [10] is used.

Emission factors

Emission factors given in EMEP (2016)-3D-12 [10] are used. The Guidebook does not indicate whether EFs have considered the condensable component (with or without).

Table 12: Emission factors for PM emissions from agricultural soils
Emission factor kg ha-1
EFTSP 1.56
EFPM10 1.56
EFPM2.5 0.06

Trend discussion for Key Sources

TSP and PM10 are key sources. Emissions depend only on the areas covered. These are relatively constant, with a very slight decrease over the past 10 years.

Recalculations

Table REC-5 shows the effects of recalculations on particulate matter emissions. All differences to last year submission result from including new crop species (recalculation No 15, see main agricultural page. Further details on recalculations are described in Haenel et al. (2020), Chapter 3.5.2.

Table REC-5: Comparison of particle emissions (TSP, PM10 & PM2.5) of the submissions (SUB) 2020 and 2019

2020_3D_Table_6_REC.PNG

Planned improvements

No improvements are planned at present.

3.D.e - Cultivated crops

In this category Germany reports NMVOC emissions from crop production according to EMEP (2016)-3D-11 [10]. For details see Haenel et al. (2020), Chapter 11.11, [1].

Activity data

The activity data is the total area of arable land and grassland. This data is provided by official statistics.

Table 13: AD for the estimation of NMVOC emissions from crop production

2020_3D_Table_13.PNG

Methodology

In EMEP (2016)-3D-15ff [10] the methodology is described how the EMEP Tier 1 EF was estimated. This methodology was adopted to estimate German emissions. It is considered a Tier 2 methodology.

Emission Factors

The emission factors for wheat, rye, rape and grass (15°C) given in EMEP (2016)-3D-16, Table A3-3 [10] were used. For all grassland areas the grass (15°C) EF is used, for all other crops except rye and rape the EF of wheat is used. Table 14 shows the implied emission factors for NMVOC emissions from crop production. The implied emission factor is defined as ratio of the total NMVOC emissions from cultivated crops to the total area given by activity data.

Table 14: IEF for NMVOC emissions from crop production

2020_3D_Table_14.PNG

Recalculations

Table REC-6 shows the effects of recalculations on NMVOC emissions. All differences to last year’s submission result from including new crop species (recalculation No 15, see main agricultural page. Further details on recalculations are described in Haenel et al. (2020), Chapter 3.5.2.

Table REC-6: Comparison of NMVOC emissions of the submissions (SUB) 2020 and 2019

2020_3D_Table_7_REC.PNG

Planned improvements

No improvements are planned at present.

Uncertainty

Details will be described in chapter 1.7.

3.d.f - Agriculture other including use of pesticides

(on separate page)

Bibliography
1. Haenel et al. (2020): Haenel H-D, Rösemann C, Dämmgen U, Döring U, Wulf S, Eurich-Menden B, Freibauer A, Döhler H, Schreiner C, Osterburg B & Fuß, R (2019): Calculations of gaseous and particulate emissions from German Agriculture 1990 –2018. Report on methods and data (RMD), Submission 2020. Thünen Report 77. https://www.thuenen.de/de/ak/arbeitsbereiche/emissionsinventare/
2. Reidy B. et al. (2008): Reidy B., Dämmgen U., Döhler H., Eurich-Menden B., Hutchings N.J., Luesink H.H., Menzi H., Misselbrook T.H., Monteny G.-J., Webb J. (2008): Comparison of models used for the calculation of national NH3 emission inventories from agriculture: liquid manure systems. Atmospheric Environment 42, 3452-3467.
3. Dämmgen U., Hutchings N.J. (2008): Emissions of gaseous nitrogen species from manure management - a new approach. Environmental Pollution 154, 488-497.
4. IPCC – Intergovernmental Panel on Climate Change (2006): IPCC Guidelines for National Greenhouse Gas Inventories, Volume 4 Agriculture, Forestry and Other Land Use.
5. Dämmgen U., Erisman J.W. (2005): Emission, transmission, deposition and environmental effects of ammonia from agricultural sources. In: Kuczyński T., Dämmgen U., Webb J., Myczko (eds) Emissions from European Agriculture. Wageningen Academic Publishers, Wageningen. pp 97-112.
6. Weingarten, P. (1995): Das „Regionalisierte Agrar- und Umweltinformationssystem für die Bundesrepublik Deutschland“ (RAUMIS). Berichte über die Landwirtschaft Band 73, 272-302.
7. Henrichsmeyer, W.; Cypris, Ch.; Löhe, W.; Meuth, M.; Isermeyer F; Heinrich, I.; Schefski, A.; Neander, E.; Fasterding, F.;, Neumann, M.; Nieberg, H. (1996): Entwicklung des gesamtdeutschen Agrarsektormodells RAUMIS96. Endbericht zum Kooperationsprojekt. Forschungsbericht für das BMELF (94 HS 021), Bonn, Braunschweig.
8. Stehfest E., Bouwman L. (2006): N2O and NO emission from agricultural fields and soils under natural vegetation: summarizing available measurement data and modelling of global emissions. Nutr. Cycl. Agroecosyst. 74, 207 – 228.
11. NIR (2020): National Inventory Report 2020 for the German Greenhouse Gas Inventory 1990-2018. Available in April 2020.
12. Rösemann et al. (2017): Rösemann C, Haenel H-D, Dämmgen U, Freibauer A, Döring, U, Wulf S, Eurich-Menden B, Döhler H, Schreiner C, and Osterburg B (2017), Calculations of gaseous and particulate emissions from German Agriculture 1990 – 2015. Report on methods and data (RMD), Submission 2017. Thünen Report 46, 423 p.
13. Aarhus Protocol on Persistent Organic Pollutants (2009), United Nation: Aarhus Protocol on Long-range Transboundary Air Pollution, Persistent Organic Pollutants, 1998 - Amendment - (on Annexes V and VII) Decision 2009. Status In force (since Dec 13, 2010), Annex III.
14. Stockholm Convention (2001): The Stockholm Convention on Persistent Organic Pollutants, opened for signature May 23, 2001, UN Doc. UNEP/POPS/CONF/4, App. II (2001), reprinted in 40 ILM 532 (2001) [hereinafter Stockholm Convention]. The text of the convention and additional information about POPs is available online at the United Nations Environment Programme’s (UNEP’s) POPs website.
15. PflSchG (2012): Gesetz zur Neuordnung des Pflanzenschutzgesetzes, Bundesgesetzblatt (BGBl), Jahrgang 2012, Teil I, Nr. 7, § 64.
16. Syngenta Agro (2015), Dep. „Zulassung und Produktsicherheit“, personal communication.
17. Regulation (EC) No 1107/2009: REGULATION (EC) No 1107/2009 OF THE EUROPEAN PARLIAMENT AND OF THE COUNCIL of 21 October 2009 concerning the placing of plant protection products on the market and repealing Council Directives 79/117/EEC and 91/414/EEC
18. Directive 2005/53/EC: Commission Directive 2005/53/EC of 16 September 2005 amending Council Directive 91/414/EEC to include chlorothalonil, chlorotoluron, cypermethrin, daminozide and thiophanate-methyl as active substances 2005/53/EC C.F.R. (2005).
19. Directive 2006/76/EC: Commission Directive 2006/76/EC of 22 September 2006 amending Council Directive 91/414/EEC as regards the specification of the active substance chlorothalonil (Text with EEA relevance) 2006/76/EC C.F.R. (2006).
20. Directive 2008/69/EC: Commission Directive 2008/69/EC of 1 July 2008 amending Council Directive 91/414/EEC to include clofentezine, dicamba, difenoconazole, diflubenzuron, imazaquin, lenacil, oxadiazon, picloram and pyriproxyfen as active substances 2008/69/EC C.F.R. (2008).
21. Directive 2016/2284/EU: Directive (EU) 2016/2284 of the European Parliament and of the Council of 14 December 2016 on the reduction of national emissions of certain atmospheric pollutants, amending Directive 2003/35/EC and repealing Directive 2001/81/EC (Text with EEA relevance ).
22. Bailey, R. E., (2001): Global hexachlorobenzene emissions. Chemosphere, 43(2), 167-182.
23. BVL (2015) (Bundesamts für Verbraucherschutz und Lebensmittelsicherheit Braunschweig): persönliche Mitteilung der Wirkstoffdaten, 2015.
24. BVL (2019) (Bundesamts für Verbraucherschutz und Lebensmittelsicherheit Braunschweig): persönliche Mitteilung der Wirkstoffdaten, 2019.
25. Council Directive 91/414/EEC of 15 July 1991 concerning the placing of plant protection products on the market, https://eur-lex.europa.eu/legal-content/en/ALL/?uri=CELEX:31991L0414
26. FAO (2015): FAO (Food and Agriculture Organization of the United Nations) Specifications and Evaluations for Chlorothalonil, p 51. http://www.fao.org/agriculture/crops/thematic-sitemap/theme/pests/jmps/ps-new/en/
27. FAO (2012): FAO (Food and Agriculture Organization of the United Nations)Specifications and Evaluations for Picloram, Table 2, p. 23. http://www.fao.org/agriculture/crops/thematic-sitemap/theme/pests/jmps/ps-new/en/.
28. Ferrari, F., Klein, M., Capri, E., & Trevisan, M. (2005). Prediction of pesticide volatilization with PELMO 3.31. Chemosphere, 60 (5), 705-713.
29. Klein, M. (2017), Calculation of emission factors for impurities in organic pesticides with PELMO. Personel communication. [Description available, Umweltbundesamt, FG I 2.6,Emissionssituation].
30. IPCS (1996), Chlorothalonil. Environmental Health Criteria, 183. 145pp. WHO, Geneva, Switzerland. ISBN 92-4-157183-7. C12138614.7.
31. EMEP EB, 2012: EMEP Executive Body Decision 3/2012 in ECE/EB.AIR/111/Add.1 - Adjustments under the Gothenburg Protocol to emission reduction commitments or to inventories for the purposes of comparing total national emissions with them
URL: http://www.ceip.at/fileadmin/inhalte/emep/Adjustments/ECE_EB.AIR_111_Add.1__ENG_DECISION_3.pdf.
32. EMEP (2019): EMEP/EEA air pollutant emission inventory guidebook – 2019, EEA Report No 13/2019, https://www.eea.europa.eu/publications/emep-eea-guidebook-2019.
33. BVL (2018) (Bundesamts für Verbraucherschutz und Lebensmittelsicherheit Braunschweig): Absatz an Pflanzenschutzmitteln in der Bundesrepublik Deutschland, Ergebnisse der Meldungen gemäß § 64 Pflanzenschutzgesetz für das Jahr 2017, https://www.bvl.bund.de/SiteGlobals/Forms/Suche
34. COMMISSION IMPLEMENTING REGULATION (EU) No 540/2011 of 25 May 2011 implementing Regulation (EC) No 1107/2009 of the European Parliament and of the Council as regards the list of approved active substances. http://eur-lex.europa.eu/legal-content/EN/TXT/?uri=celex%3A32011R0541.
35. Regulation (EU) 2019/677: Commission Implementing Regulation (EU) 2019/677 of 29 April 2019 concerning the non-renewal of the approval of the active substance chlorothalonil, in accordance with Regulation (EC) No 1107/2009 of the European Parliament and of the Council concerning the placing of plant protection products on the market, and amending Commission Implementing Regulation (EU) No 540/2011, http://data.europa.eu/eli/reg_impl/2019/677/oj
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