dataesr/scientific-paragraphs-categorization huggingface dataset:
Where a FWHM value has been measured, corresponding to an object selected by SExtractor in that band, it is displayed in the three columns on the right-hand side. In the final column, we flag the candidates from  Bowler et al. (2012)  that have been re-selected here, with a number corresponding to the order of the candidates in  Bowler et al. (2012). Only two of the original ten candidates (268511 and 95661) do not lie within the deep strips, however we remeasured the photometry using the improved data reductions of the full field. Candidate 95661 was included in the  Bowler et al. (2012)  sample as a result of the large errors on the photometric redshift of z = 6. 13 +0. 38  -0. 27 , but is now excluded from our new sample as a z < 6. 5 galaxy with best-fitting photometric redshift of z = 6.
GALAXY SIZES Lyman-break galaxies are known to be smaller at highredshift, with the median half-light radius for faint (0. 1-1L * ) galaxies being r 1/2 < 1 kpc at z = 7  (Oesch et al. 2010; Huang et al. 2013). Confirmation of the existence of a clear size-magnitude relation (as observed at lower redshift) becomes challenging at z > 6, because of the restricted luminosity baseline over which sizes can be accurately measured. For example, the few tens of galaxies at z > 7 detected and measured in the HUDF by  Oesch et al. (2010)  and more recently in the UDF12 dataset by  Ono et al. (2013)  typically have sizes at the limit of the resolution of HST (< 0. 1 arcsec, which corresponds to a physical size of d < 0. 5 kpc at z = 7). By incorporating the wider-area CANDELS data,  Grazian et al. (2012)  were able to determine a size-magnitude relation at z = 7 extending to MUV -21.
2, where we analyse HST imaging of four galaxies in the UltraVISTA sample that are consistent with being a point source in the groundbased data (highlighted in cyan on Fig. 4 ), and find strong evidence that they have extended low surface brightness features. From the final UDS sample of four galaxies, two appear resolved in the z -band imaging (see Fig. 4 ), including the known extended z = 6. 595 galaxy Himiko, which is the The measured FWHM as a function of magnitude for the UltraVISTA and UDS galaxy samples in the top and bottom row respectively. Each column shows the results for the z and J-bands, with the galaxy candidates presented as the blue circles. The four galaxies that lie within the COSMOS CANDELS imaging are shown as cyan circles. The magnitudes presented for the real and artificial sources are raw 1.
However, because the circular apertures we used for photometry in the spaceand ground-based data are designed to enclose around 70-80% of the flux of a point source, in the case of a resolved galaxy, more of the flux will spread beyond the aperture in the higher resolution HST imaging compared to the groundbased imaging where the seeing dominates over the intrinsic FWHM. We created model galaxy profiles to predict the magnitude offset we would expect between the VISTA and WFC3 imaging for an extended profile as compared to a point source. A magnitude offset of 0. 4 mag could be reproduced if the simulated galaxy with an exponential profile (Sersic index n = 1) had a half-light radius of r 1/2 = 1 kpc. Such a profile would result in 0. 05 mag being lost from the ground-based aperture (increased to 0.
THE LUMINOSITY FUNCTION The result of the analysis presented above is a sample of 34 z 7 galaxies with M1500 -21. 2, selected from the 1. 65 deg 2 of imaging within the UltraVISTA and UDS fields. In Table  5. The measured photometry and errors for the four z 7 galaxies in our sample that lie within the area of HST imaging provided by the CANDELS COSMOS survey. The measurements from the UltraVISTA J and H data were made in a 1. 8-arcsec diameter circular aperture and corrected to the 80% enclosed flux level. The J 125 and H 160 photometry was measured in a 0. 6-arcsec diameter circular aperture, which corresponds to 80% enclosed flux for a point source. The object ID 211127 appears barely resolved in the WFC3 imaging based on a measured FWHM close to the typical resolution of 0. 20-arcsec, but as shown in Fig.
(2013)  note that they are unable to actually measure a volume density as low as ∼ 10 -8 /mag/Mpc 3 from their dataset, and the anomalously low position of their brightest data-point could be an artefact of their chosen method of fitting the LF. Simply assuming the two brightest galaxies (WHM5 and WHM29) that occupy the M1350 = -22. 5 bin could have been selected in the full survey volume of 10 7 Mpc 3 , we estimate the measured value of the number density from the CFHTLS analysis and present this point in Fig. 8. The brightest bin from this work and  Willott et al. (2013)  both contain a small number of objects and hence are sensitive to Poisson errors and cosmic variance, however within the errors, our determination of the bright-end of the z = 7 LF is not in conflict with that found at z = 6 by  Willott et al.
Cosmic variance The derived LF can vary depending on the dimensions of the survey field observed, as a result of the underlying largescale density fluctuations within the Universe. We find more galaxies within the UltraVISTA ultra-deep data than in the UDS field, which covers a similar area of sky. The interpretation is complicated, however, by the lower selection efficiency of the UDS dataset compared to UltraVISTA, as a result of the substantially shallower Y -band imaging in the field. Moreover, because we require that a candidate galaxy be detected at > 2σ significance in the Y -band, our sample from the UDS field is significantly less complete for galaxies   2009 ) that were obtained from a similar photometric redshift fitting approach to the work presented here. We estimate the number density of M 1500 = -22.
Contribution of faint z = 7 quasars Around the peak of the quasar number density at z = 3, there is evidence that the very brightest end of the galaxy LF is contaminated by quasars  (Bian et al. 2013). There are large uncertainties in the faint-end of the z > 3 quasar LF, and the faint-end of the z = 7 QLF is completely unknown due to a lack of datasets with the required depth over an adequate area on the sky for detection (see  Willott et al. 2010). In Fig. 9 , we compare the galaxy LF at z = 7 to the known QLF at z = 5 and z = 6 and the extrapolation of the z = 7 QLF beyond the absolute magnitude of the faintest quasar found at z = 7 with M1700 = -25. 5  (Venemans et al. 2013). The bright-end of the QLF can be estimated from the four z > 6. 5 quasars known, which includes one from the UKIDSS-LAS found by  Mortlock et al.
2010) , with a sensitivity of 12µJy per beam. The UDS field has X-ray imaging from the Subaru/XMM-Newton deep survey  Ueda et al. (2008) , to depths of 6×10 -16 ergs/s/cm 2 /Hz in the 0. 5-2. 0 keV channel and 5 × 10 -15 ergs/s/cm 2 /Hz in the 2-10 keV channel. We find no radio or X-ray counterparts for any of the galaxies within our sample, when comparing to the publicly available catalogues within each field derived from the datasets described above. We also perform a stack of the objects in the VLA-COSMOS imaging and again find no detection to a limit of ∼ 12 µ Jy per beam. The average quasar SEDs from  Shang et al. (2011)  suggests that if one of our candidates was a typical radio-loud quasar, it would just be detectable in the X-ray and radio imaging (see Figure  6  of  Ouchi et al. 2009b ).
ACKNOWLEDGEMENTS RAAB and JSD acknowledge the support of the  European Research Council  via the award of an Advanced Grant. JSD acknowledges the support of the  Royal Society  via a  Wolfson Research Merit Award. JSD acknowledges the contribution of the EC  FP7   SPACE  project  ASTRODEEP (Ref. No:  312725 ). RJM acknowledges the support of the  Leverhulme Trust  via the award of a Philip Leverhulme research prize. RJM acknowledges the support of the  European Research Council  via the award of a Consolidator Grant (PI McLure). ABR acknowledges the support of the  UK Science & Technology Facilities Council. HM acknowledges support of the PNCG. BMJ and JPUF acknowledge support from the  ERC-StG  grant  EGGS-278202. The  Dark Cosmology Centre  is funded by the  Danish National Research Foundation.
Introduction: In resource-poor areas, infectious diseases may be important causes of morbidity among individuals infected with the Human T-Lymphotropic Virus type 1 (HTLV-1). We report the clinical associations of HTLV-1 infection among socially disadvantaged Indigenous adults in central Australia. Methodology and Principal Findings: HTLV-1 serological results for Indigenous adults admitted 1 st January 2000 to 31 st December 2010 were obtained from the Alice Springs Hospital pathology database. Infections, comorbid conditions and HTLV-1 related diseases were identified using ICD-10 AM discharge morbidity codes. Relevant pathology and imaging results were reviewed. Disease associations, admission rates and risk factors for death were compared according to HTLV-1 serostatus. HTLV-1 western blots were positive for 531 (33.
These geographic differences in HTLV-1 associated mortality might reflect environmental conditions in resource poor areas that predispose to recurrent respiratory tract infections and expose HTLV-1 carriers to other pathogens, such as Mycobacterium tuberculosis  [39]  and S. stercoralis  [12]. The retrospective nature of this study results in a number of limitations. First, patients with HTLV-1 related diseases were identified from discharge morbidity codes. Attempts were made to identify other patients with these conditions by contacting specialist medical units to which such patients are referred; however, cases may have been missed if these were not coded or referred appropriately. Consequently, our data are likely to underestimate the actual burden of HTLV-1 related diseases in this population.
Residual styrene present in polystyrene food packaging may migrate into food at low levels. To assure safe use, safe exposure levels are derived for consumers potentially exposed via food using No/Low Adverse Effect Levels from animal and human studies and assessment factors proposed by European organisations (EFSA, ECHA, ECETOC). Ototoxicity and developmental toxicity in rats and human ototoxicity and effects on colour discrimination have been identified as the most relevant toxicological properties for styrene health assessments. Safe exposure levels derived from animal studies with assessment factors of EFSA and ECHA were expectedly much lower than those using the ECETOC approach. Comparable safe exposure levels were obtained from human data with all sets of assessment factors while ototoxicity in rats led to major differences.
Safe exposure levels (SEL) are derived for consumers exposed to S via food. The toxicological endpoints that are nowadays considered as most relevant are taken into consideration, namely ototoxicity and colour vision disturbance in humans as well as postnatal developmental effects in rats. Especially the database for ototoxicity is robust in experimental animals and humans and concordant under qualitative and even quantitative aspects. Division of the NOAELs/LOAELs for these toxicity benchmarks by appropriate AFs leads to different SELs. This paper concentrates on AFs recently proposed by  EFSA (2012) ,  ECHA (2012)  and  ECE-TOC (2010)  and therefore the results primarily relate to the European regulatory environment. The SELs will then allow defining a Specific Migration Limit (SML) for the migration of S into food.
For GPPS and HIPS migration of S into 3% acetic acid or 10% ethanol was generally below 100 lg/kg, but reached 75-590 lg/kg in olive oil after 10 days at 40 °C. With EPS extracted for 2 h/70 °C somewhat higher concentrations were found (up to 340 lg/kg in olive oil), but clearly lower concentrations at 10 d/5 °C (up to 40 lg/kg in sunflower oil)  (O'Brian, 2001). 2. Food surveillance: In 5 sets of a total diet study covering 100 categories of food (UK MAFF, 1999) S was detected at low levels of up to 14 lg/kg. Using consumption data from the National Food Survey the dietary exposure of consumer was estimated to be 0. 03-0. 05 lg/kg bw/d (1. 8-3 lg/person/d). In a previous study (UK  MAFF, 1994)  covering 248 food samples packed in a variety of pack types the concentrations of S were generally in the range of <1-60 lg/kg with the exception of a ''low fat'' table spread (97 lg/kg) and milk and cream products sold as small portions ($10 g) for tea and coffee (23-230 lg/kg).
Point of departure The first step in the derivation of a SML is the definition of SELs for consumers to migrants (herein S) from packaging into food. The calculation of a SEL is generally based on the NOAELs/LOAELs, the points of departure, obtained in experimental animals or epidemiological studies. In studies on experimental animals the selection of a NOAEL or LOAEL is straightforward, as these are defined by the doses selected for the experiment. Both ECHA (2012) and ECETOC (2010) specifically note that differences exist in the nature of data from animal versus epidemiological studies. In animal tests the doses are predefined leading to precise values for the NOAEL and the LOAEL. The true threshold apparently lies somewhere between the two values. In the case of epidemiological studies, exposures generally cannot be exactly defined and rather exposure categories forming a continuum are estimated.
AF for interspecies extrapolation In the absence of chemical-specific data on toxicokinetics and/ or -dynamics EFSA (2012) applies a total AF of 10, subdivided into a factor of 4 for toxicokinetics and of 2. 5 for toxicodynamics. EFSA uses body weight as a scale for interspecies extrapolation while other organisations, including ECHA (2012) and ECETOC (2010), have proposed allometric scaling based on differences in metabolic rate per body weight. For the oral exposure route the same total default AF of 10 is proposed by ECHA and EFSA for the extrapolation from rats to humans. This factor is subdivided by ECHA for rats into a subfactor of 4 for allometric scaling, but this subfactor varies according to the species under consideration, for example 7 for mice. The factor for allometric scaling is not applicable if both, experimental animals and humans are exposed by inhalation.
AF for intraspecies extrapolation based on animal data For the majority of chemicals reliable human data are not available and the assessment has to rely on information from animals only. This is likely the basis for the default AF of 10 proposed by EFSA (2012) to calculate SELs for consumers exposed via food. The same AF of 10 is used by ECHA (2012) for intraspecies extrapolation to the general population. To derive an AF for intra-human variability based on actual data and not only on default assumptions, ECETOC (2010) analysed the distribution of human data available from the literature and arrived at the conclusion that an AF of 5 is appropriate for extrapolations from animal data to the general population. If the point of departure is the NOAEL of a study in rats, the procedure of EFSA (2012) and ECHA (2012) leads to a total AF of 100 while that of ECETOC to 20.
On the other hand, AFs lower than the standard assessment factors may be used when some of the factors that cause the intraspecies variation are covered in the target population. But apart from referring to expert judgment, no further guidance is provided what numerical AFs may be used in specific situations. More guidance on this issue is given by ECETOC (2010). For extrapolation from worker data to the general population an AF of 3 is proposed (note: in the accompanying table an AF of 2 is given). Additional AFs may be necessary for a study substantially influenced by healthy worker effect that may result in an overestimation of the NOAEL (AF 2) or for a small study size (AF 3). For this latter case an example is given, namely the derivation of an occupational exposure limit based on volunteer studies with a limited number of participants.
Relevant toxicological endpoints On the basis of the UK Risk Assessment Report  (RAR, 2008)  and the literature update provided in the Chemical Safety Report (according to the REACH requirements) a number of studies have been identified that are potentially relevant to human health assessments. A large database is available for S to assess its internal disposition in the body and toxicological properties. Of particular importance for evaluating toxicity concerns for long term exposures such as ingestion in food include considerations for mutagenicity/genotoxicity, carcinogenicity, reproductive and developmental toxicity and repeated exposure target organ effects. The metabolic profile of S in mice, rats and humans has been well defined in a large number of studies and provides the basis for extrapolation of toxicity data from experimental animals to humans.
Derivation of SMLs 4. 1. Point of departure: ototoxicity in rats 4. 1. 1. Inhalation route When using ototoxicity data derived from rat inhalation studies, the following aspects are necessarily considered: -Species sensitivity: the rat is the most sensitive species as compared to the other species investigated (hamsters). These species differences could be related to the metabolic turnover of the parent organic solvent that is the ultimate chemical moiety causing hearing deficits. There is a close similarity in metabolism between rats and humans, as a single inhalation exposure to S led to very similar blood levels for rats and humans (Ramsey and  Young, 1978). Therefore, rat data will be used for this endpoint. -Exposure duration: In the RAR (2008) it is concluded that ''ototoxicity appears after relatively short exposures (1 week) and that continued treatment (4 weeks up to 19 months) does not enhance the intensity of the ototoxic response.
Therefore studies without data for former, most probably high exposures cannot be used to reliably define a NOAEL or LOAEL. Triebig et al (2009)  investigated 128 laminators from a boat building plant in comparison to 127 matched controls of the same plant. Exposure analysis was based on biological monitoring (using urinary mandelic and phenylglyoxylic acid; MA + PGA) to avoid any confounding by personal protection measures. The biomonitoring data was then transformed to airborne concentrations of S in ppm. Biological monitoring showed that the controls working in the same plant were exposed to very low levels of S. Thus a comparison was made between three groups of low (N = 99), medium (N = 118) and high (N = 31) exposed workers with calculated mean exposure concentrations of 1. 7-3. 4, 7.
e. 10 m 3 /person (ECHA, 2012); -correction for absorption in the respiratory tract (70%). resulting in estimations of: 72 Â 5/7 Â 10 Â 0. 7 = 860 mg/person/d, corresponding to 12. 3 mg/kg bw/d (for 40 ppm), and to 430 mg/person/d, corresponding to 6. 15 mg/kg bw/d (for 20 ppm). As these points of departure are derived from data for humans, only an intraspecies AF is applicable that should take into account that part of the total intra-human variability is already covered by the variability within the workforce investigated. As described above this situation is not considered by EFSA (  2012 ) and no detailed guidance is given by ECHA (2012). Thus guidance on how to address this factor presently can only be obtained from ECETOC (2010). Their default approach is an AF of 3 for extrapolation of worker data to the general population, provided that the study population is representative, the study group is sufficiently large and the study data are adequate.
These prerequisites are basically met by the  Triebig et al. (2009)  data so that the default AF of 3 may be applicable. But there are two specific features mentioned by ECETOC that may lead to a modification (increase) of this default AF: -If the study may be substantially influenced by a healthy worker effect an additional factor of 2 may become necessary. But as stated above, it cannot be assumed that a healthy worker effect could have played any major role in this study. Thus, there is no need for this additional factor of 2. -If the study size is small, especially the subgroup defining the NOAEL, an additional factor of 3 may be used. Whether the study size is to be regarded as small (a total 128 exposed laminators and thereof 31 highly exposed subjects) cannot be decided by objective criteria.
And finally, after ECHA (2012) has recently published its guideline how to derive NOAELs from epidemiological studies, closely resembling that of ECETOC (  2010 ), this should be the basis for future assessments. Therefore, on balance it was decided to place emphasis on actual data, i. e. to accept 40 ppm as the point of departure. The appropriate AF for extrapolating worker data to the general population, 10 as the default AF of EFSA (2012) and ECHA (2012), 3 as the standard approach of ECETOC (2010) or 9 derived by a modification in accordance with considerations of ECETOC. The use the factor of 9 appears most appropriate, although this factor might still be too conservative for the basis from the Triebig study. Thus the SEL of 95. 6 mg/person/d (1. 37 mg/kg bw/d) is best justified from a scientific point of view.
Conclusion; derivation of a Specific Migration Limit (SML) The derivation of a SML includes consideration of: 1. The total intake of food (or liquid) in kg food/person/d that may be consumed by different subgroups of the population, e. g. adults, children, pregnant women. For the purpose of this assessment a default value of 1 kg food/person/d for adults will be used as proposed by the Scientific Committee on Food (EC SCF, 2001). 2. The safe exposure level (SEL) that is the daily exposure of a consumer to a substance that will not lead to adverse health effects (in mg substance/kg bw/d or mg substance/person/d). The SELs given preference under the aspects mentioned above are summarised in Table  7. As can be seen from Table  7  there is a large difference in SELs derived from animal data based on the default AFs of EFSA and ECHA in comparison to those of ECETOC.
Although the AFs of ECE-TOC are scientifically justified, the approach of EFSA/ECHA is recommended here as these SELs are very similar to those obtained from data in humans. Under this premise all SELs are in the same range (90-120 mg/person/d) for the different endpoints under consideration. -ototoxicity, rats; -developmental toxicity, rats; -ototoxicity, humans; -colour vision deficiency, humans. giving strong support for an overall and consistent SEL of about 90 mg/person/d. The most robust database is available for ototoxicity for which the NOAELs/LOAELs have well been established in experiments in animals with supporting evidence from observational studies in workers, both of which lead to very similar SELs. Using the assumption of a consumption of 1 kg food/d for adult humans a concentration of 90 mg S/kg food can be considered safe.
A total of 1193 proteins were identified in our experiment (Supplemental Data Set 1). Quantitative information calculated by ProfileAnalysis was linked to the identified peptides using mass and retention times as assignment criteria, which resulted in 893 quantitated proteins (Supplemental Data Set 2). Changes in protein levels were considered to be significant statistically if the ratios were beyond the 95% confidence interval. A total of 258 proteins were thus classified as displaying altered abundance, of which 162 were upregulated after TAG accumulation (Supplemental Data Set 3) and 96 were downregulated (Supplemental Data Set 4).
(C) Immunoblotting analysis of protein levels of BCAT2, BCAT3, BCKDH1, and MCC2 at 36 and 60 h. Cell lysate aliquots were made and normalized by intracellular protein concentration. Fold increases of protein levels from 36 to 60 h, determined using Image J software, are also shown. Normalization is shown in Supplemental Figure  6.