dataesr/scientific-paragraphs-categorization huggingface dataset:
Soil texture and crop type A summary of soil texture and crop type data is presented in Tables  2  and 3. For the N 2 O dataset, silt loam was the most common soil texture, representing 59% of dataset, followed by clay loam (9. 5%), sandy loam (9. 5%), and clay (6. 8%). The remaining 15% was either represented by other soil textural classes (∼8%) or not determined (∼7%). Regarding crop type, 90% of the N 2 O data was obtained from studies conducted on grass, followed by cereal (4. 7%), residue/stubble (3. 2%), "other" crop, and "no" crop. For the NH 3 dataset, clay was the most dominant soil texture (25% of observations), followed by sandy loam (13. 5%); loam (12%); and then sand, loamy sand, and clay loam, each representing 11% of the observations. The remaining 17% was represented by other soil textural classes.
Manure application method A summary of data collated on the method of manure application to land is provided in Table  4. This analysis was limited to mechanically applied manures and excludes urine and dung, which are directly deposited by grazing livestock. For the N 2 O dataset, surface broadcast ("broadcast") was the most common manure application method (72%). Many of these N 2 O studies have assessed potential co-benefits or pollution swapping associated with reduced NH 3 emissions from low-trajectory techniques such as trailing shoes and hoses and application methods such as shallow injection (e. g. ,  Chadwick et al. , 2011; Dell, Meisinger, & Beegle, 2011; Thomsen, Pedersen, Nyord, & Petersen, 2010; Webb et al. , 2010). Briefly, trailing hoses apply liquid manure to the vegetation close to the ground in parallel bands; manure Other -8 Note.
Urine and dung data were excluded. is not deposited between the bands. Trailing shoes part the crop or grass leaves and stems to apply the manure on the soil surface in parallel bands. Shallow injection of manure involves cutting a slot into the soil and injecting the slurry, commonly to a soil depth of 50 mm  (Pain & Menzi, 2011). For the NH 3 studies, the method of manure application has been a particular focus of a large number of these studies. Broadcast application represented 48% of the NH 3 dataset, followed by trailing hose and trailing shoe (27 and 11%, respectively). Other manure application methods represented ≤15% of the total data. A similar result was reported in the ALFAM2 database  (Hafner et al. , 2018) , which is not surprising, given the ALFAM2 dataset represents 54% of the NH 3 data in the current DATAMAN field dataset.
Variables collated in the N 2 O and NH 3 dataset Variables collated in the N 2 O and NH 3 dataset are presented in Table  5. Here, we limit the database observations to those including an EF value (i. e. , excluding "control" or nil N treatments) and classify the availability of each variable using arbitrary categories of (a) >85% representation and (b) between 50 and 85% representation. For the N 2 O dataset, only three variables (manure DM, manure N load, and soil texture) were available in conjunction with the EF values for more than 85% of the land-applied manure data. For urine and dung deposition by grazing livestock, this degree of representation was limited to only two variables (manure N load and soil texture). For 50-85% representation, data for 12 variables (manure N concentration, manure organic C concentration, manure pH, manure TAN, soil N, soil organic C, soil pH soil bulk density [BD], soil clay, soil texture, air temperature, and total rainfall) were available for land-applied manure EF values, whereas urine and dung had nine variables (soil N, soil organic C, soil pH, soil BD, soil clay, air temperature, total rain, VWC, and WFPS) available.
The information described above suggests that studies evaluating the effect of direct deposition of urine and dung on N 2 O emissions generally report more information on soil variables rather than excreta composition variables, whereas studies evaluating N 2 O emissions from land-applied manure reported a broader range of variables relating to soil and manure characteristics. For the NH 3 dataset, variables with >85% representation in association with land-applied manure EF values included manure DM, manure pH, manure total N and TAN load, and soil texture. For urine and dung, the same degree of representation (>85%) was met by only three variables: manure N load, soil clay, and soil texture. For 50-85% representation, six variables (manure total N and TAN concentration, soil pH, soil BD, soil clay, and windspeed) included data in association with land-applied manure EF values, whereas dung and urine deposition had six variables, all associated with soil properties (NO 3 , NH 4 , total N, organic C concentration, pH, and BD).
Frequency and distribution of variables For the N 2 O dataset, EF values were typically between 0 and 2% (Figure  3  ha -1 ) varied widely, with typical application rates of 100-1,200 kg N ha -1. However, there were 12 observations (0. 4% of all data) where the N load was between 2,000 and 3,900 kg N ha -1. These data were derived from urine (11 observations) and dung (one observation) studies where either high urine and dung volumes and/or high urine N concentrations were used. Manure DM content was typically between 0. 3 and 20%, with urine and dirty water having values of <1%; slurry typically ranging from 1 to 10%; and dung, farmyard manure, solid manure, broiler litter, and layer manure typically >10%. Manure total N content was generally between 0. 5 and 8 kg N t -1 fresh weight (FW), with lower values associated with dirty water and urine and higher values associated with dung, farmyard manure, and broiler litter.
Manure organic C content was typically between 5 and 90 kg C t -1 FW, whereas manure C/N ratio varied widely (from 2 to 35). Regarding soil variables relating to the N 2 O dataset, soil pH was typically between 5 and 7, whereas soil N and organic C content ranged between 0. 07 and 0. 55% and between 2 and 7%, respectively. Soil clay content and soil bulk density were generally between 5 and 35% and between 0. 6 and 1. 4 g cm -3 , respectively. The WFPS and VWC, each averaged over the first 30 d following manure application to land, was typically between 25 and 90% and between 20 and 60% v -1 , respectively. Climate variables showed a wide variation, with average air temperature over the first 30 d ranging between 6 and 30 ˚C and total rainfall in the first 30 d ranging from 0 to 150 mm. For the NH 3 dataset, EF values were typically between 10 and 40% of the total N applied but had a positively skewed distribution with some very large EF values (Figure  4 ).
We identified 10 observations where EF values ranged between 100 and 245%, which were reported in studies evaluating the soil application of swine and cattle slurry (eight and two observations, respectively). Seven of these observations relate to broadcast application of slurry, with the remaining derived from trailing hose (2) and closed slot (1) slurry application. These observations, also reported in the ALFAM2 database  (Hafner et al. , 2018) , suggest that NH 3 was volatilized from other sources in addition to the applied slurry (e. g. , soil) and/or large errors associated with the measurement technique, including manure characterization; eight of the observations were made using wind tunnels, whereas the remaining two were made using a micrometeorological method. Manure N load, manure DM, N content soil organic C, and soil clay also showed a positively skewed distribution but with a greater frequency of data, at approximately 100 kg N ha -1 , 5% DM, 5 kg N t -1 FW, 5% soil organic C concentration, and 5% clay concentration, respectively.
Manure organic C concentration, manure C/N ratio, and soil N concentration showed a multimodal distribution, suggesting these variables were derived from groups of studies with different features, possibly due to the wide range of countries, animals, and manure type included in the field database. Soil pH and soil BD showed a symmetric distribution of data, with mean values of approximately 6 and 1. 2 Mg m -3 , respectively. Air temperature shows a normal distribution of data (0-30 ˚C), with a greater number of data between 7 and 20 ˚C. Total rainfall over the entire experiment, which averaged 25 d duration, was typically lower than 40 mm. Although the database has undergone a data entry quality control process, there are still uncertainties in the measurements. Therefore, data should still be critically evaluated before use.
Implications of the database We have collated into a single database N 2 O and NH 3 EFs and ancillary data from land-applied livestock manure and direct deposition of urine and dung, sourced from field studies conducted in 25 countries across the globe. Although every continent (except Antarctica) is represented, the database is imbalanced, with nearly 90% of the data derived from only eight countries (United Kingdom, New Zealand, Canada, Brazil, Ireland, Denmark, Kenya, and The Netherlands). Furthermore, the purpose of most experiments has been to investigate specific scenarios, with no attempt to cover all scenarios in a balanced way. Composite EFs based on a meta-analysis of collated studies are therefore likely to be biased because of this imbalance, and care should be taken to investigate possible biases.
To expand the diverse range of livestock production systems captured in the database, we encourage further studies in temperate dry and in tropical wet and dry regions, given the low representation from these regions in the database (2, 4, and 4% of the total database, respectively). Although the database structure includes 94 variables, there are many gaps due to studies not reporting all these variables. This is not surprising, given each field study had different objectives and therefore had different data requirements. However, to ensure that results can be used in meta-analyses for refinement of EF values, model development, or assessing mitigation options, we encourage researchers to include the reporting of crucial manure as well as climate and soil variables (see  Hafner et al. [2018]  and de Klein et al.
[2020] , respectively, for suggested NH 3 and N 2 O reporting criteria). Analysis of the current version of the field database will be reported in a subsequent study; this will also help to identify key variables for reporting in future studies. This is the first iteration of the field database (Version 1. 0); however, it is envisaged that this database will expand over time, initially as part of a follow-on project called "Mitigating greenhouse gas Emissions from Livestock Systems" or "MELS"  (EraNet Joint Call, 2018). This follow-on project will increase the opportunities for improving our knowledge of key drivers, developing more detailed EF values for manure sources across different climatic zones and livestock systems, and evaluating mitigation strategies. Please contact the corresponding author if you wish to contribute data.
CONCLUSION The DATAMAN "field" database contains information on N 2 O and NH 3 EFs for land-applied manure and direct deposition of urine and dung. The database is comprised of 5,632 observations, with N 2 O representing 56% and NH 3 representing 44% of the data, and includes soil, manure, and climate data collated from studies conducted in a wide range of countries. The database could be used (a) to estimate EF values and identify key drivers, (b) for future refinement of EF values for the IPCC Emission Factor Database and for reporting national inventories, (c) for improving empirical and/or process-based models aimed at estimating N 2 O and NH 3 EFs from different animal and manure types, and (d) for assessing potential GHG and NH 3 mitigation strategies for a wide range of manure application and grazing systems.
Histogram of manure, soil and climate variables for all manure type included in the N 2 O database. The y axis shows frequency (count). BD, bulk density; DM, dry matter; FW, fresh weight; Manure C, manure organic C; TAN, total ammoniacal N; RAN, readily available N (uric acid, ammonium, and nitrate); VWC (%, 30 d), volumetric water content over first 30 d following manure application; WFPS (%, 30 d), water-filled pore space over first 30 d following manure application F I G U R E 4 Histogram of manure, soil and climate variables for all manure type included in the NH 3 database. The y axis shows frequency (count). BD, bulk density; DM, dry matter; FW, fresh weight; Manure C, manure organic C; TAN, total ammoniacal N; RAN, readily available N (uric acid, ammonium, and nitrate); VWC (%, 30 d), volumetric water content over first 30 d following manure application; WFPS (%, 30 d), water-filled pore space over first 30 d following manure application.
F Histogram of manure, soil and climate variables for all manure type included in the N 2 O database. The y axis shows frequency (count). BD, bulk density; DM, dry matter; FW, fresh weight; Manure C, manure organic C; TAN, total ammoniacal N; RAN, readily available N (uric acid, ammonium, and nitrate); VWC (%, 30 d), volumetric water content over first 30 d following manure application; WFPS (%, 30 d), water-filled pore space over first 30 d following manure application F I G U R E 4 Histogram of manure, soil and climate variables for all manure type included in the NH 3 database. The y axis shows frequency (count). BD, bulk density; DM, dry matter; FW, fresh weight; Manure C, manure organic C; TAN, total ammoniacal N; RAN, readily available N (uric acid, ammonium, and nitrate); VWC (%, 30 d), volumetric water content over first 30 d following manure application; WFPS (%, 30 d), water-filled pore space over first 30 d following manure application.
• Livestock manure management systems are important sources of greenhouse gas and NH 3 emissions. • The DATAMAN project aims to relate key variables with emissions and to refine emission factors. • We built a database on N 2 O and NH 3 emissions from land-applied manure and livestock excreta. Core Ideas • This field database contains 5,632 observations compiled from 184 studies and 25 countries. • The DATAMAN field database is available at http://www. dataman. co. nz. et al. , 2018), ELFE (Vigan et al. , 2019), and the 2019 refine- ment of the 2006 IPCC guidelines (IPCC, 2019). The U. K. studies (Chadwick et al. , 2018; Thorman et al. , 2020) can be found in the archived data sources of the United King- dom's Agricultural and Environmental Data Archive (AEDA, Data collection was carried out from September 2018 to March 2020.
During this time, information on N 2 O and NH 3 emissions from excreta (dung and urine) and land- applied manure was sourced from published peer-reviewed research, theses (undergraduate and postgraduate), and con- ference papers. Searches were performed using different Web- based platforms such as Web of Science, ScienceDirect, Sci- elo, and Google Scholar. Keywords included three search terms: (a) manure type (solid manure, farmyard manure, slurry, solid, broiler litter, urine, dung), (b) animal (dairy cat- tle, beef cattle, sheep, goat, pig, broiler), and (c) gas (N 2 O, NH 3 , CH information extracted from existing datasets that had been collated for developing either country-specific EFs (e. g. , Chadwick et al. , 2018; Krol et al. , 2016; Thorman et al. , 2020; van der Weerden et al. , 2016,2020) or continental/global EFs (e.
Number of observations Continent Country N 2 O emission factors NH 3 emission factors Summary of the database for NH 3 and N 2 O emission factors following land-applied manure or direct deposition of urine and dung of livestock animals Europe Austria 5 7 Belgium 3 - Denmark - 213 France - 43 Germany 11 125 Ireland 153 68 Italy - 82 Netherlands 18 183 Norway - 9 Sweden 15 49 Switzerland - 46 United Kingdom 557 1,339 Total 761 2,164 The Americas Argentina 6 - Brazil 177 59 Canada 54 207 Chile 2 10 Colombia 10 - Nicaragua 2 - United States 93 16 Total 344 292 Oceania Australia 26 - New Zealand 1,788 8 Total 1,814 8 Africa Kenya 201 - Zimbabwe 13 - Total 214 - Asia China 17 - Japan 16 1 Total 33 1 Grand total 3,167 2,465 T A B L E 1.
Characterization of the catalysts Elemental analysis: The nitrogen and sulfur elemental analysis was performed on an Eurovector Elemental Analyzer using sulphanilamide B2131-2 as reference (0. 4-1. 44 mg). The sample was placed in a tin capsule and weighed using a microbalance (1. 0420 mg sample). Helium 5. 0 was used as carrier gas. Set-up conditions of the method were: carrier-110 kPa, purge-80 mL/min, oxygen-15 mL, ΔpO2=35 kPa, oxidation time-6. 6 sec, sample delay-5 sec, front furnance-980 ᵒC. The temperature in the GC oven was set to 100 0 C. Gas chromatography coupled with a thermal conductivity detector (TCD) was used to separate and identify the resulted gases, respectively. The results were interpreted using the 5. 1 Callidus software. Copper has been analyzed using Inductively Coupled Plasma Optical Emission Spectroscopy (ICP-OES) on an Agilent 5110 SVDV ICP-OES.
Acknowledgements The authors thank the  UEFISCDI  for continued funding through the projects  PN-III-337 P1-1. 2-PCCDI-2017-0541 1/2018 ,  PN-III-P4-ID-PCCF-2016-338 0088 17/2021 , and  PN-III-P4-ID-PCE-2020-1532. ZA and VIP thank  Marie Sklodowska-Curie GRANT CCIMC , No. 860322. Keywords: L-and D-valmet ligands as organocatalysts• Cu-complexated by valmet as homogeneous catalysts• heterogeneous GO immobilized Cu-complex catalysts • Henry, cyanosilylation and aldol reactions.
Stability measurements were finally performed at 650 1C after cooling the reactor to this temperature. Chosen experiments were repeated to ensure reproducibility of catalytic results under the used conditions. The catalytic performance was established from the gas composition at the exit of the reactor monitored with an INFICON micro GC equipped with a TCD and two parallel channels (Molecular sieve and Plot U). The data are reported from 0 to 13 h of reaction (stability test) in terms of: -reactants conversions, estimated from the equation ''X conversion (%) = (C in À C out )/C in '', where C in and C out represent the inlet and outlet concentrations of CH 4 or CO 2 gases, respectively, -''H 2 : CO (mole ratio) = M H 2 : M CO '', where M H2 and M CO are the molar concentrations of the formed H 2 and CO products.
Physicochemical characterization techniques Powder X-ray diffraction patterns (PXRD) were recorded on a BRUKER type D8 diffractometer equipped with a Cu Ka irradiation source (l = 1. 5405 nm) and operating at 30 kV and 10 mA. The acquisitions were done in a 2y range of 5 to 901. Crystalline phase identification was based on comparison with standard PXRD files published by the international center for diffraction data (ICDD). Thermogravimetric analysis was performed on a TA SDT Q600 instrument working in horizontal mode. One of the two alumina pan was filled with about 20 mg of sample while the other (reference) pan was kept empty. The analysis was carried out in air flow (50 ml min À1 ) from room temperature to 900 1C with a ramping rate of 5 1C min À1. Textural properties were evaluated from nitrogen adsorption-desorption isotherms recorded at À198 1C with a BELSORP-max apparatus.
Acknowledgements The authors sincerely acknowledge the  ERANET EU-FP7 initiative , the national  ANR (France) ,  CNRS-L (Lebanon)  and  MIUR (Italy)  agencies for their support and funding through the  SOL-CARE  ( Energy-065 ) project (JC-ENERGY-2014 first call). The  University of Balamand Research Council  is also thanked for the BIRG 02/2016 contribution. Sandra Casale  is warmly thanked for her invaluable contribution to the electron microscopy observations. Jean-Marc Krafft  is warmly thanked for his contribution to the RAMAN spectroscopy analyses of the spent catalysts. AM gratefully acknowledges the Erasmus + Programme Countries scholarship for her stay at the  Sorbonne University.
Several electrochemical parameters were measured for each thorium content and the results were compared with published data  [19] [20] [21]. In these experiments, the presence of the dissolved oxygen was analysed and observed before the carrier melt purification. In the second step, a LiF-ThF 4 eutectic salt (78. 0-22. 0 mol. %) was prepared and characterised by CV and LSV techniques using a gold working electrode to detect the possible oxygen content in ThF 4.
The experimentally accessible potential E M X y /M of the species MX y in a real, non-standard state is lower than the standard electrode potential due to the interaction of the species with the solvent, i. e. , its solvation. The difference between E 0 M X y /M and E M X y /M depends on an activity of the species a ( M X y ) and thus also on the activity coefficient γ ( M X y ) according to the Eq. (  4 ) a ( M X y ) = x ( M X y ) γ ( M X y ) , ( 4 ) Table  1  Results of calculation of the standard potentials using JR-CMSD database and data for pure compounds at a reaction temperature of 850 °C. where x ( M X y ) is a concentration of the species MX y expressed as its molar fraction.
(  10 ) : E = E LiF/Li -E T h F 4 /T h = E 0 LiF/Li -E 0 T h F 4 /T h + RT 4 F ln a ( LiF ) 4 a ( T h F 4 ) (10) The activities of thorium and lithium metals a ( T h ) and a ( Li ) in Eq. (  6 ) and (  9 ) are equal to 1 and the unknown activities of fluoride ions a ( F -) mathematically cancel out each other by the deduction of the equations. The difference of equilibrium potentials E was experimentally measured using cyclic voltammetry, while the standard potentials E 0 LiF/Li and E 0 ( T h F 4 /T h ) were calculated with the FactSage software using a Joint Research Centre Molten Salt Database (JRCMSD, developed at JRC Karlsruhe), where the data for pure compounds were adopted from [  [40]  ,  [41]  ]. The values of the standard potentials E 0 were derived from the calculation of the Gibbs enthalpies G 0 of the corresponding chemical reactions at the reaction temperature of 850 °C using the relation  (11) : E 0 = -G 0 /nF ( 11 ) The obtained values of the standard potentials, the corresponding chemical reactions and the values of the Gibbs enthalpies are given in Table  1  for both redox systems of interest ThF 4 /Th and LiF/Li, together with the calculated values for the system CaF 2 /Ca in order to additionally prove that the melt decomposition limit is corresponding to the less stable LiF/Li system.
The activity a ( LiF ) in the used LiF-CaF 2 eutectic solvent was also calculated using the FactSage software and the JRCMSD database to be 0. 798, which agrees with the published value calculated for temperature 876 °C in  [42]. The activity value is very close to the mole fraction of LiF in the mixture (0. 795), which indicates that the excess Gibbs energy for the solution formation is small and the activity coefficient of LiF at the given conditions is almost equal to unity. The E value of -0. 46 V was experimentally obtained from the cyclic voltammetry measurements described above in Section 3. 3 as a difference between the equilibrium potentials Th(IV)/Th and Li(I)/Li. These potentials were graphically evaluated from the cathodic peaks of the measured cyclic voltammograms, not using the initial current slope likely indicating formation of surface alloys prior the pure metals deposition, as discussed above in Section 3.
The above-described approach has been used in this work to evaluate the activity coefficient of ThF 4 in LiF-CaF 2 eutectic melt by measuring a difference between the Th(IV)/Th electrode potential and the melt decomposition potential, corresponding to the Li(I)/Li red-ox couple. The ThF 4 activity coefficient has been determined using the calculated activity of LiF in the LiF-CaF 2 solvent and the LiF/Li and ThF 4 /Th standard potentials. The obtained value is in the expected order of magnitude and comparable to the published data on activity coefficients of actinides in molten fluoride media. Therefore, we conclude that the presented method can be used for experimental determination and comparison of activities and activity coefficients of different solutes in any fluoride melt, for which the above-mentioned thermodynamic data required for the calculation, are available.