dataesr/scientific-paragraphs-categorization huggingface dataset:
, 2016) , whereas d 56 Fe values reported for hydrothermal fluids range from -0. 69‰ to +0. 28‰  (Beard et al. , 2003; Severmann et al. , 2004; Rouxel et al. , 2008 Rouxel et al. , , 2016;; Bennett et al. , 2009). The likely reason for this is that the d 56 Fe composition of hydrothermal dFe is modified on mixing with seawater due to precipitation of Fe sulfides, oxidation of Fe(II) to Fe(III), and Fe(III)-oxyhydroxide formation (e. g. ,  Welch et al. , 2003; Rouxel et al. , 2008 Rouxel et al. , , 2016;; Bennett et al. , 2009; Roy et al. , 2012). Here we study the evolution of d 56 Fe during mixing between hydrothermal fluids and seawater, presenting the first compilation of d 56 Fe in hydrothermal fluids, buoyant and nonbuoyant plumes at two vent sites, E2 and E9N, located on the East Scotia Ridge (see the GSA Data Repository 1  for sample site descriptions and sampling strategies).
Total (dissolved + particulate) concentrations of Fe (tFe) are, on average, 40% ± 10% and 70% ± 30% lower at E2 and E9N, respectively, than calculated, assuming that Fe is conserved during mixing between the end-member vent fluid and seawater (Fig. 1 ). Partitioning of Fe between different size fractions, and d 56 Fe values, may, however, be slightly modified in the interval between sampling and processing (see the Data Repository).
ACKNOWLEDGMENTS This work was supported by UK Natural Environment Research Council (NERC) National Capability funds and the Graduate School of the National Oceanography Centre, Southampton. Research cruises JC042 and JC055 were funded by NERC consortium grant NE/D01249X/1. We thank the Captain and crew of RRS James Cook for support on both cruises. We also thank D. Green and B. Alker for shipboard and onshore laboratory assistance, K. Nakamura for the loan of his Eh sensor, and two anonymous reviewers for their considered and constructive reviews.
A PANalytical instrument was used for XRD studies, using a 0. 02°2h step and an angular range from 5 to 100°. Crystalline phase determination was carried out using the International Center for Diffraction Data database (ICDD) and the Xpert High Score plus software (PANalytical, Almelo, the Netherlands) for phase matching. Determination of lattice parameters was carried out using a full-pattern matching method (Le Bail function) with the help of the Fullprof suite program. 25 pert High Score software was also used to perform Rietveld refinements to obtain phase weight ratios starting with the unit cell parameters determined from the previous refinement methods. In all cases the differences in unit cell parameters between the two methods were found to be far below the values of associated uncertainties.
ACKNOWLEDGMENTS S. R. G. C. , A. C. , and M. E. F. are grateful for funding from the  Lloyd's Register Foundation , a charitable foundation helping to protect life and property by supporting engineering-related education, public engagement, and the application of research. E. Z. S, D. H. , and W. E. L. work was funded as part of the  EPSRC Carbides for Future Fission Environments (CAFFE)  consortium ( EP/M018563/1 ;  EP/M018768/1 ).
Alleles, sequence types and clonal complexes (cc) were assigned using the Neisseria MLST database (available on http://neisseria. org). The level of expression of fHbp was quantified by ELISA using anti-fHbp antibodies as previously described  [29]. The characteristics of Nm invasive strains, all isolated from TPD patients between 1999 and 2015, were compared to those of carriage and invasive strains from the general French population, using the data of a carriage study conducted in 2008 in Normandy by the NRCM and those of all invasive strains of the general population in 2008  [30].
The most frequent clonal complexes were cc23 (n=14; 26%), cc22 (n=6; 11%) and cc41/44 (n=5; 9%). Thirteen out of 14 strains from cc23 were from group Y isolates. Hyperinvasive clonal complexes (i. e. cc11, cc32, cc41/44 and cc269) were responsible for 21% of the invasive cases in TPD patients (Table  1 ). No correlation was found between a type of TPD and a specific capsular group/clonal complex. The study of the variable regions (VR) of porA genes showed 15 and 21 different VR1 and VR2 respectively. Sequencing of the variable region of fetA gene also revealed high diversity with 20 different variable regions. MIC to penicillin G of 49 meningococcal cultured isolates was also determined and 39% of these isolates exhibited reduced susceptibility which was confirmed by the presence of altered penA gene (data not shown).
Acknowledgements The work of  Intel  and  CEA-Leti  is partially supported by the  European Commission  under Horizon 2020 projects  FANTASTIC-5G  ( GA 671660 ) and  Flex5Gware  ( GA 671563 ). The work of CTTC was partially supported by the  European Commission  under the project  EMPhAtiC  ( GA 318362 ) and currently partially supported by the  Generalitat de Catalunya  ( 2014 SGR 1551 ) and by the  Spanish Government  under project  TEC2014-58341-C4-4-R.
Shipping of edible fats and oils into Europe is permitted in bulk tanks, provided that the previous cargo is included in a positive list. The European Commission requested EFSA to evaluate the acceptability as previous cargoes for fats and oils the substances calcium lignosulphonate, methyl acetate, ethyl tertbutyl ether (ETBE) and ammonium sulphate. The evaluation was based on the same criteria as those used for the evaluation of the substances currently on the list in the Annex to Commission Directive 96/ 3/EC as acceptable previous cargoes for edible fats and oils. Methyl acetate and ETBE meet the criteria for acceptability as previous cargoes. Due to uncertainties, mainly with regard to the composition and toxicity of the low molecular mass fraction, and the fact that the toxicological database is limited to the 40-65 grade and does not cover all grades of calcium lignosulphonate shipped as previous cargoes, the EFSA Panel on Contaminants in the Food Chain (CONTAM Panel) concluded that calcium lignosulphonate does not meet the criteria for acceptability as a previous cargo.
Data retrieved by search For the present evaluation of the substances as acceptable previous cargoes, the CONTAM Panel considered literature made publicly available until 18 April 2016. The evaluation is based on available studies/information from literature searches carried out on public databases, e. g. PubMed, the International Uniform Chemical Information Database (IUCLID), the European Chemicals Agency (ECHA), evaluations made by the national and international bodies, e. g. the World Health Organization (WHO). A comprehensive search for literature was conducted for peer-reviewed original research published pertaining to the toxicity and allergenicity of the compounds. Reviews were also considered for the current risk assessment. The CONTAM Panel considered the previous assessment on calcium lignosulphonate as a previous cargo (EFSA CONTAM Panel, 2011) as comprehensive, covering all relevant publications up to that date.
It considered that the available data were insufficient to establish an ADI and that long-term toxicity studies were needed to elucidate whether the histiocytosis in the mesenteric lymph nodes of the rats observed in the 90-day study may progress into a more adverse state with time. Contact allergy to calcium lignosulphonate has been described in EFSA 2010 for one single case (EFSA ANS Panel, 2010). In 2011, the ANS Panel considered that the new information provided by the petitioner did not address the questions raised by the Panel in 2010 and that the requested chronic toxicity study of at least 12 months was still needed (EFSA ANS Panel, 2011). In 2011, the CONTAM Panel evaluated calcium lignosulphonate (unspecified grade) as a acceptable previous cargo. The toxicological database was considered to have several data gaps (long-term toxicity, carcinogenicity and limited data on reproductive toxicity).
Therefore, the ANS Panel considered that this study cannot be used to the safety evaluation of calcium lignosulphonate (40-65) and consider that a chronic toxicity study of at least 12 months is needed. A Pathology Working Group of independent consulting pathologists was convened to re-assess the sections of the lymph nodes, Peyer's patches and liver, and to re-examine all lymphoid tissues. Additional evaluation of the clinical pathology data and evaluation of the animal health certificates from the regular screening programme of the performing laboratory was also done. The conclusions were published together with other study results by  Thiel et al. (2013). In the initial evaluation, large focal/multifocal aggregates of foamy histiocytes were observed in the mesenteric lymph nodes of exposed animals.
Summary and conclusion The data on calcium lignosulphonate (highly purified 40-65 grade) did not provide evidence of genotoxicity, immunotoxicity, skin sensitisation or allergenicity. A NOAEL of 2,000 mg/kg bw per day (the highest dose tested) was determined in a 90-day dietary rat study. However, there are several data gaps, mainly with regard to the composition and toxicity of the low molecular mass fraction. Moreover, the toxicological database is limited to the 40-65 grade and does not cover all grades of calcium lignosulphonate shipped as previous cargoes. Therefore, the CONTAM Panel concluded that calcium lignosulphonate does not meet the criteria as previous cargo.
In 2011, the CONTAM Panel concluded that methanol meets the criteria for acceptability as a previous cargo (EFSA  CONTAM Panel, 2011). The CONTAM Panel considered that methanol does not pose toxicological concerns when used as a previous cargo. Methanol is not genotoxic or allergenic and high doses are required to produce a carcinogenic response in rats by the oral route. Therefore, it is unlikely that methanol would pose a risk of carcinogenicity at the levels of exposure that would occur following its use as a previous cargo. The ANS Panel reviewed the toxicity of methanol in the context of the safety assessment of aspartame (EFSA ANS Panel, 2013a). The Panel concluded that the data set on genotoxicity was limited but that the available reliable in vitro and in vivo data did not indicate a genotoxic potential for methanol.
This RfD was in addition to dietary intakes of methanol, which were included in the background exposure estimates used by the US-EPA (EFSA ANS Panel, 2013b). Methanol has recently been re-evaluated under Registration, Evaluation, Authorisation and Restriction of Chemicals (REACH) Regulation (EC) No. 1907/2006 11 (ECHA, 2015). Evaluation of the data presented in the registration dossier indicated that methanol affects prenatal development of offspring in mice and rats causing fetotoxic, embryotoxic and teratogenic effects. The Risk Assessment Committee (RAC) considered that marked differences between humans and rodents, which are critical when considering that developmental toxicity in rodents is only observed at high blood methanol concentrations (≥ 537 mg/L in mice and ≥ 1,840 mg/L in rats).
Chemical properties and use Ethyl tert-butyl ether (ETBE), also called tert-butyl ethyl ether, is a liquid with a boiling point of 73°C and solubility in water at ambient temperature of around 1. 2%. ETBE is produced by reaction of isobutylene with ethanol. Together with methyl tert-butyl ether (MTBE), ETBE is mainly used as a fuel additive in petrol to increase the octane number (maximum 15%), to reduce carbon monoxide and hydrocarbon emissions. ETBE is more expensive than MTBE and is mainly used to introduce bioethanol to the amount required by legislation. Since the structures of ETBE and MTBE are very similar, it is expected that there will be similarities in their toxicological properties. Therefore, data available on MTBE will be reported where appropriate.
The frequency of rudimentary lumbar ribs was significantly increased in the group given the highest dose of ETBE; but this was considered of no toxicological significance by the authors (the frequency was within the range of historical data of the same strain of rat (1. 1-21. 2%) used in this study, the lumbar rib was a rudimentary type and not an extra one and this variation is temporary and vanishes after birth). The NOAEL was 1,000 mg/kg bw per day, the highest dose tested, for maternal and developmental toxicity  (Aso et al. , 2014). Several other reproductive toxicity and developmental toxicity studies have been conducted in rats and rabbits exposed by gavage to doses up to 1,000 mg ETBE/kg bw per day (the highest dose tested), were reviewed by de Peyster (2010). The original Reports were not available to the CONTAM Panel.
Conclusions • Calcium lignosulphonate (CAS No 8061-52-7) The toxicological database on calcium lignosulphonate is limited to the highly purified 40-65 grade. It has several data gaps mainly with regard to the composition and toxicity of the low molecular mass fraction. The CONTAM Panel concluded that due to the uncertainties, calcium lignosulphonate does not meet the criteria as a previous cargo. • Methyl acetate (CAS No 79-20-9)   Methyl acetate is not genotoxic in in vitro reverse mutations assays. As it is metabolically hydrolysed to methanol and acetic acid, its toxicity was evaluated by that of methanol and acetic acid. The CONTAM Panel has previously concluded that methanol and acetic acid meet the criteria for acceptability as a previous cargo. The CONTAM Panel concluded that methyl acetate meets the criteria as a previous cargo.
The resulting ratio of branching fraction ratios is measured in the region 1 < q 2 < 6 GeV 2 /c 4 , (2) where q 2 is the momentum transfer to the lepton system. This range is both experimentally and theoretically attractive as it excludes the B + → ψ(nS )K + resonances, and precise theoretical predictions are possible. The value of R K is measured to be  [2]  R K = 0. 745 +0. 090 -0. 074 (stat) ± 0. 036 (syst) , which is 2. 6 standard deviations below the expectation from lepton universality. It will be interesting to update this analysis adding the LHC Run 2 dataset.
Calculated OH reactivity A number of instruments for the detection of OH reactants took measurements concurrently with the OH reactivity instruments (Table  2 ). Nitrogen oxides (NO and NO 2 ) were detected by a chemiluminescence instrument (Eco Physics TR 780). CO was measured using a Piccarro cavity ringdown instrument (Picarro G2301) and by gas chromatography (GC, Trace Analytical RGA 3). Both measurements agreed within 5 %. Data from the cavity ring-down instrument were used here for calculations of the OH reactivity due to its higher accuracy. This instrument also measured methane and water vapour concentrations. Organic compounds were detected by PTR-TOF-MS (proton-transferreaction time-of-flight mass-spectrometry, Ionicon) and GC (Agilent 7890N). Measurements agreed for those species that could be detected by both instruments, such as isoprene better than 20 % with some larger discrepancies for acetaldehyde and β-caryophyllene in the second set of experiments in 2016 (Table  2 ).
Data coverage The CRM instrument from the Finnish Meteorological Institute (FMI) was used in the first campaign, but no valid measurements could be acquired due to technical problems of this instrument. Data were submitted for all other instruments for nearly all experiments and are included in the comparison. A leak in the OH injection system of the MDOUAI CRM instrument was found after the third experiments and this leak possibly led to systematic errors in the measurements in this experiment. Data from the experiment on 7 October 2015 were therefore rejected for this instrument. The sampling system of the CRM instrument from LSCE was changed on the second day of the campaign (6 October 2015). Measurements from this experiment were rejected. On 12 October 2015, the flow-tube instrument from PSU did not take measurements, except for the last 2 h due to technical problems.
Therefore, the pyrrole concentration is measured when zero air is sampled and when the light of the Pen-Ray lamp is turned on (C1-mode). This is typically done once a day. The design of the reaction volume is identical for all instruments, because they were all manufactured by the Max Planck Institute for Chemistry in Mainz. Three CRM instruments are included in this comparison, by MPI, IMT Lille Douai (MDOUAI) and LSCE. The instruments differ mainly in the exact operational conditions such as flow rate, pyrrole and OH concentration and the inlet lines (Table  1 ). The transformation of raw data into k OH values requires corrections  (Michoud et al. , 2015)  that have been characterised for each CRM instrument (Table  4 ). These corrections, described below, can significantly differ between instruments due to the different operating conditions.
The dilution factor is calculated from measured flow rates. Corrections are usually determined from instrumental characterisation in the laboratory and in the field, with the assumption that they are representative of ambient air measurements. Typical values of corrections are listed in Table  4. All groups operating a CRM used empirical functions to correct for deviations from the pseudo first-order decay for the final data evaluation  (Michoud et al. , 2015). The exact value, however, depends on the chemical composition of OH reactants (see below). Different representative mixtures are taken to characterise of this correction for the various CRM Table  4. Correction applied to the raw data. Some corrections are non-linear and depend on several parameters (such as the pyrrole and OH concentrations).
MPI CRM instrument The correction of measurements taken with the CRM by MPI for deviations from a pseudo first reaction uses results from numerical simulations. However, this can only be applied if the relative importance of the most abundant reactive compounds in the sampled air is known  (Sinha et al. , 2008). The model correction was not applicable in this comparison, because no data on the concentration ratios of the main OH reactants were known in contrast to typical situations in field campaigns. In this campaign, the empirical correction procedure was also chosen as an alternative correction procedure that was shown to be advantageous by  Michoud et al. (2015). Tests with isoprene, methanol, ethane, propane, propene and toluene were done to determine the correction factor. In addition to the corrections applied by all groups operating a CRM instrument, measurements by the MPI CRM were corrected for the presence of ambient ozone.
This was observed for the MPI CRM instrument in this campaign. Therefore, measurements were corrected by an empirical function derived from laboratory measurements after the first data submission. Although the ozone concentration in the reaction volume was similar to the concentration in the other two CRM instruments, no ozone dependence was seen for the MDOUAI and LSCE instruments. The exact reason is not clear but might be related to different HO 2 concentrations in the instruments. The insensitivity of other CRM instruments to the ozone interference indicates that operating conditions exist for which the interference is negligible. Further investigations should be performed to characterise these conditions. In addition to the ozone correction, errors in the calculation of the dilution factor and the calibration of the pyrrole sensitivity were noticed for the MPI CRM instrument af-ter the first data submission in 2015.
A bi-exponential function was applied to measurements in a campaign in China for the FZJS instrument  (Lou et al. , 2010). Measurements of the Lille instrument that showed bi-exponential behaviour during a campaign on the campus of the University of Lille were evaluated by applying a single-exponential function. Measurements were evaluated by only using the first part of the decay curve that contained information on the faster decay  (Hansen et al. , 2015). No significant difference between this procedure and the results from a bi-exponential fit was found. The fitting of the data using a single-or bi-exponentially decay function is discussed later in the paper, as differences were observed in the returned value of the OH reactivity in this campaign at high NO x (> 20 ppbv) depending on the type of fit used.
For this reason, an additional dilution flow can be applied in order to reduce the OH reactant concentrations and improve the data quality. This was done in some instruments (FZJ, Lille) in this campaign, when the measured reactivity exceeded a threshold (e. g. > 150 s -1 for the Lille instrument) but is not required as indicated by measurements by the Leeds LP-LIF instrument. Imperfect alignment of the photolysis laser can enhance the inhomogeneities in the initial OH distribution, so that deviations from a single-exponential OH decay can also occur at low reactivity values. This was observed in this campaign in the Lille and Leeds LP-LIF instruments but recognised only at the end of (Lille) or after (Leeds) the campaign. As a consequence, the evaluation procedures were changed for measurements in this campaign in order to account for this effect.
OH reactivity measurements in the presence of monoterpenes and sesquiterpenes The third type of chemical condition tested in the campaigns was the presence of terpenes. This was done either by injecting a mixture of monoterpenes, a sesquiterpene or by flushing real plant emissions into the SAPHIR chamber. These experiments also included ozonolysis reactions of terpenes. Maximum reactivities (25 s -1 ) were lower than in other experiments in 2015. Oxidation products of the ozonolysis reactions were not measured, so that it is expected that calculated reactivities are underestimating the real reactivity. Therefore, one of the instruments (LP-LIF FZJS) is taken as reference for the comparison of the measurements. As seen in the correlation plots (Fig. 9 ) and the results of the regression analysis for data without the presence of ozone (Table  6 ), differences between measurements of the LP-LIF instruments and the other instruments are largest in these experiments compared to the other experiments.
The level of agreement varies among the three experiments (9, 14 and 16 October 2015): when the monoterpene mixture was injected, measurements by the PSU instrument are 10 to 15 % lower than measurements by the FZJS instrument, but they are 20 % higher when plant emissions are transferred into the chamber. During the continuous transfer small inhomogeneities cannot be fully excluded, but the discrepancies between measurements. Correlation between measured OH reactivities and measurements by the FZJS instrument. This subset of data includes experiments with injections of a mix of monoterpenes (α-pinene), limonene, and myrcene (9 October 2015 and 13-14 April 2016) or with the transfer of real plant emissions, which consists predominantly of monoterpenes (14 October 2015). Times when O 3 was present are indicated by bluish colours.
Summary of findings Not only were many measurements successfully performed in these campaigns but also a number of findings already led to an improvement in the data quality during the process from measurements to the final data: an ozone-dependent background signal was found for measurements of the MPI CRM; application of the correction of measurements is recommended due to the deviation from pseudo first-order conditions in CRM instruments by empirical correction factors  (Michoud et al. , 2014) ; misalignment of the photolysis laser beam in the LP-LIF instruments can lead to a complication in the data evaluation procedure. These results will also improve the precision and accuracy of measurements in the future. The findings of the comparison of the final data set are as follows: -Measurement techniques are capable of measuring OH reactivity for a range of chemical conditions that are relevant for ambient air measurements but with different levels of precision and accuracy.