dataesr/scientific-paragraphs-categorization huggingface dataset:
FUNDING  Spanish Ministerio de Economía y Competitividad (MINECO)  [ CTQ2011-26665  and  CTQ2014-52633-P  to J. M. P. C. ];  Comunidad Aut ónoma de Madrid  [ CPI/0265/2008  to S. M. L. ];  Federation of European Biochemical Societies (FEBS)  [ FEBS Summer Fellowship  to S. M. L. ];  Ligue Contre le Cancer  ( Equipe Labellisée 2014 );  Centre National pour la Recherche Scientifique ;  CERBM-IGBMC; Investissements d'Avenir   ANR-10-IDEX0002-02  [ ANR-10LABX-0030-INRT ];  French Infrastructure for Integrated Structural Biology (FRISBI)  [ ANR-10-INSB-05-01 ]; INSTRUCT as part of the  European Strategy Forum on Research Infrastructures. The open access publication charge for this paper has been waived by  Oxford University Press -NAR Editorial Board  members are entitled to one free paper per year in recognition of their work on behalf of the journal.
Whether the structure of ecological communities can exhibit stability over macroevolutionary timescales has long been debated. The similarity of independently evolved Anolis lizard communities on environmentally similar Greater Antillean islands supports the notion that community evolution is deterministic. However, a dearth of Caribbean Anolis fossils-only three have been described to datehas precluded direct investigation of the stability of anole communities through time. Here we report on an additional 17 fossil anoles in Dominican amber dating to 15-20 My before the present. Using data collected primarily by X-ray microcomputed tomography (X-ray micro-CT), we demonstrate that the main elements of Hispaniolan anole ecomorphological diversity were in place in the Miocene. Phylogenetic analysis yields results consistent with the hypothesis that the ecomorphs that evolved in the Miocene are members of the same ecomorph clades extant today.
We evaluated the probability of assignment of each fossil to the ecomorph classes using DFA. Because of variation in which elements were preserved in the fossils, DFAs were performed separately for each fossil (Table  S3 ). In each case, a DFA was performed using variables from the modern specimens, which included only the variables that were also available for the fossil, and the assignment of a fossil to an ecomorph was determined based on this subset of variables from modern specimens. DFA was performed using a common (within-) covariance matrix for all groups (linear DA) in JMP Pro v. 10 (SAS Institute Inc. ). Phylogenetic Analysis. We scored the 20 amber fossils for the morphological characters used by Poe  (22)  to infer anole phylogeny, using X-ray micro-CT scans, photographs, and direct observations.
4. 07  (47)  to confirm the correct translation frame. Sequence coding for transfer RNAs was aligned manually following Kumazawa and Nishida's (48) model of tRNA secondary structure. One hundred bases corresponding to sections of the tRNAs and the origin of light-strand replication were excluded from the analyses due to ambiguous alignment. The final matrix analyzed included 4,873 bases, 91 morphological characters, and 181 extant taxa (174 Anolis and 7 outgroup species). All 181 species were scored for morphological characters; 140 also had molecular data. The resulting data matrix was analyzed using parsimony and Bayesian methods. To reduce the computational time that results from large amounts of missing data in the amber fossils, we inferred a topology for the extant species and then used that topology as a backbone topological constraint (which allows species not included in the constraint tree to be placed freely in the topology) to infer the phylogenetic position of the amber fossils.
The topology for the extant species was inferred with PAUP* v. 4. 0b10 (49) using parsimony on the combined dataset (181 species: 91 morphological characters and 4,873 DNA bases). We used equal costs for state transformations, except for multistate ordered morphological characters, which were weighted such that the range of each character equals 1. We performed 2,000 replicates of random stepwise addition, with default settings for all other options. We then performed a separate parsimony analysis for each amber fossil by including each fossil in the combined matrix for the extant species, imposing the topological constraint, and using a single replicate of random stepwise addition (other options left on default settings). We combined the results for all of the fossils in a single summary tree (Fig.
3. 2. 3 (51). We executed four independent runs of 50 million generations with a random starting tree, a sampling frequency of 1,000 generations, and remaining parameters left at default values. We partitioned data by morphology, codon position, and tRNAs (11 partitions) and estimated the model for each partition using jModeltest v. 2. 1. 4 (52). To confirm an appropriate sampling interval and that stationarity was achieved after discarding the first 25% of the sampled trees, we examined effective sample size values using TRACER v1. 5  (53) , compared the average SD of split frequencies between chains, and examined thepotential scale reduction factor (PSRF) of all of the estimated parameters for the four runs combined. We estimated a maximum clade credibility (MCC) tree and created a series of partial constraints so that we could enforce the MCC topology of extant species as a strict constraint in downstream analyses that included fossil taxa.
ACKNOWLEDGMENTS. We thank those who allowed us access to amber fossils for study:  G. Bechly ,  J. Calbeto ,  L. Costeur ,  M. Cusanovich ,  G. Greco ,  M. Greco ,  D. Grimaldi ,  M. Halonen , and  J. Work. We especially thank  E. Morone  for providing access to more than half of the fossils examined for this study. We thank  J. Klaczko , and  G. Gartner  for providing support and discussions and  J. Casart  for assisting with data collection. Scan data were also provided by  R. Boistel ,  M. Polcyn ,  L. Jacobs ,  M. Colbert , and  R. Ketcham. We thank the  National Science Foundation  for support.
Analysis The pictures obtained by the high speed camera are postprocessed with the software VIC2D in order to measure the displacement of the substrates. The direct measurement on the bonded joint is not possible due to its small thickness. The relative displacements are then measured on substrates according to Y -axis (loading direction). According to a rigid substrate assumption, the measurements of the displacement are done on the top substrate at point A and on the bottom substrate at point B (Fig. 5 ). DN and DT respectively are the normal relative displacement, and the tangential relative displacement between A and B according to the x and y frame. FN and FT are the corresponding normal and tangential strength to the adhesive bond. The strain rates are then obtained from relative displacements DN and DT by the following expressions: εyy = d dt ln 1 + DN e (1) εxy = d dt 1 2 tan -1 DT e (2) with e the adhesive thickness.
The present research work call FASTLITE assembly has been supported by the "Programme véhicule du future" from Projets d'Investissements d'Avenir coordinated by ADEME, the International Campus on Safety and Intermodality in Transportation, the Region Nord Pas de Calais, the European Community, the Delegation Regionale a la Recherche et a la Technologie, the Ministere de l'Enseignement Superieur et de la Recherche, and the Centre National de la Recherche Scientifique: the authors gratefully acknowledge the support of these institutions.
Boundary conditions and loading The structures were placed outside for the THM test and all the environmental conditions were recorded in the field from the time of casting. The variations of external temperature, relative humidity, wind speed and solar radiation (on a horizontal sensor) for the three tests are available in the database. The geographical orientation of the specimen is also detailed on the following figure and the azimuth of each vertical face is given in Table  2. The structure was insulated during the two first days after casting. Two zones with slightly different insulation can be distinguished: -Zone 1 (upper and lower faces of the structure): Formwork was in plywood and the isolation was in polystyrene (see Table  3 ). -Zone 2 (lateral faces): The same materials were used (with the same thickness) but the formwork was reinforced by aluminium bars which created "weak points" in the isolation (see Table  3 ).
Storage of the results The results presented and discussed in this paper are stored in CHEOPS database. CHEOPS is a dedicated database gathering together experimental and numerical quality information, to help engineers and researchers to improve their knowledge and develop efficient models and simulation tools. The information is organised and presented through the CHEOPS GUI website dedicated in order to help scientists to efficiently access the information they need (https://cheops. necs. fr) Five chapters could be found on the home page of each test: Summary, Geometry, Materials, Procedures and Measures. "Summary" contains a short description of the simulation, keywords and some images which will help the user to see quickly what kind of simulation has been done. In the "Geometry" chapter, the user will find a description of the specimen geometry and photos/drawings in jpg or pdf format.
Conclusions These results are part of a huge amount of data obtained from various massive tests at full scale designed to study the effect of restrained conditions on massive beams. To analyse thermo-hydro-mechanical effects, I-shaped beams were designed so as to create restrained shrinkage on the central part of the beam. A full set of measurements were used to investigate phenomena occurring inside these beams at early age. With mainly strain information (global strain and local strain in concrete and on rebars) we have deduced the force and then the stress in the concrete and rebars. From numerical simulation and a more simple elastic approach, the state in each beam section could be obtained and thus correlation between all the measures established. This huge amount of data allows the phenomenology of the concrete to be verified in such boundary conditions.
-Scale effects must be taken into account to reproduce the stress condition when the first crack occurred. -The effect of outdoor conditions strongly influenced the results obtained with the same concrete. -Correlation of the different results from various sensors was clearly established after some days, but for the early age, during the heating phase and the early cooling phase, discrepancy was observed between vibrating wires and optical fibres. All these experimental results are stored in a database and can be used for benchmarking. A complementary study of massive beams without restraining struts has also been carried out. It gives complementary results on the effect of early age strain resulting from the size of the specimens.
The equilibrium concentration ratio is typically the parameter used to estimate organism activity concentrations within wildlife dose assessment tools. Whilst this is assumed to be fit for purpose, there are scenarios such as accidental or irregular, fluctuating, releases from licensed facilities when this might not be the case. In such circumstances, the concentration ratio approach may under-or over-estimate radiation exposure depending upon the time since the release. To carrying out assessments for such releases, a dynamic approach is needed. The simplest and most practical option is representing the uptake and turnover processes by firstorder kinetics, for which organism-and element-specific biological half-life data are required. In this paper we describe the development of a freely available international database of radionuclide biological half-life values.
The database includes 1907 entries for terrestrial, freshwater, riparian and marine organisms. Biological half-life values are reported for 52 elements across a range of wildlife groups (marine=9, freshwater=10, terrestrial=7 and riparian=3 groups). Potential applications and limitations of the database are discussed. # The wildlife groups are not included in  Copplestone et al. (2013) ; * where ≥ used some data have been entered with no Latin species name, or as spp. etc.
Methods The work described here was conducted by an international working group under the auspices of the International Atomic Energy Agency's MODARIA programme (see: http://www-ns. iaea. org/projects/modaria/). The review and compilation of T1/2b values was divided amongst the group members depending upon their prior expertise (i. e. by ecosystem and/or organism). Prior to beginning the review a recording sheet, in MS Excel™, was designed to allow easy collation of the various components into the final database. The recording sheet entry fields are listed in Table  1. The wildlife group categorisations were broadly compatible with those used in the Wildlife Transfer Database (as described by  Copplestone et al. 2013 ) and subsequently by the IAEA  (Howard et al. 2013; IAEA 2014). The 'Changeover time' is defined as the time of intersection of two successive depuration curves which are governed by their respective biological half-lives when the two are plotted as regression lines on a logarithmic scale (this parameter is useful if fractions of loss in each component are not directly reported).
No attempt was made to standardise the English common names used; similarly we have not updated Latin species names, but we acknowledge that these may have changed since the original publications. The review was undertaken to identify studies reporting either T1/2b values (i. e. the time taken for the initial activity concentration in an organism, or tissue, to half) or elimination rate constants from which T1/2b (d) values could subsequently be estimated as: 1/2 1/2 1/2 ln 2 1/2b k T  (4) Some T1/2b values were estimated from reported percentages of initial activity remaining (At) at time t, where: (5) and T1/2b is subsequently estimated from k as in Equation (  4 ). values from some of the Russian language literature by fitting appropriate exponential relationships to reported data using MATCAD software.
(1976) ,  Whicker & Schultz (1982) ,  Stara et al. (1971)  and  DiGregorio et al. (1978). The freshwater ecosystem review of  Alonzo (2009)  was used as the primary source of freshwater information with additional work focussing on identifying appropriate publications subsequent to the year 2000. For the marine ecosystem, the important reviews were those of Vives i Batlle et al. (2007; 2008; 2009)  (covering principally 99 Tc, 129 I, 137 Cs, 239,240 Pu and 241 Am), CIESM (  2002 ) EPA (2013)  Gomez et al. (1987)  and  Phillips & Russo (1978). For the terrestrial environment, whilst they are not wild animals, data from the domesticated dog (Canis lupus familiaris) and cat (Felis silvestris catus) have been included in the database as these are unlikely to be collated anywhere else and are of relevance to some ln 100 species of wildlife; farm animal data were excluded from the database with the exception that it is possible that some goose and duck data originate from domesticated species.
Quality control An independent quality check was conducted by co-authors not involved in the actual data compilation. As a minimum, 10% of the entered data were confirmed by going back to the source reference. Additionally, for some key data sources all entries were checked. Any A column was added to the database to record which entries had been quality controlled (approximately 40% of entries were quality controlled as described above). The database was also reviewed for duplicate entries and the few identified were removed. Some (n=165), predominantly freshwater, ecological half-life (i. e. parameter describing the overall rate of reduction in radionuclide levels of animals in contaminated environments) data for Cs and Sr were identified during the review and these have been retained within the database (as a separate datasheet).
Results The database resulting from the review is freely available  (Beresford et al. 2015c;  http://doi. org/10. 5285/b95c2ea7-47d2-4816-b942-68779c59bc4d); this contains all reference details and hence these are not repeated in this paper. The database contains 1907 entry lines split between organisms from three generic ecosystems as follows: marine (n=547); freshwater (n=530); and terrestrial (n=743). Additionally there are 87 entries for riparian organisms which live in both freshwater and terrestrial ecosystems (i. e. amphibians and some species of reptiles and birds). Sixty-five entries from the Japanese literature were for 'brackish water' species, in the database these are classified as marine ('Brackish species' appears within the notes column to identify the entries). Table  2  summarises the available T1/2b values by wildlife group (as defined in  Copplestone et al.
(2013) ) and by generic ecosystem. In some instance entries may be for different tissues from the same study. We should also note that it is likely that the database entries are a mix of mean values and single data. The compiled database contained T1/2b values for a total of 52 elements (27 for freshwater, 48 for terrestrial, 24 for marine and 10 for riparian) (Table  2 ). For all three ecosystems data for Cs were the most numerous entries (Figure  1 ), with some commonality in the other dominant elements (i. e. Co, Sr, Ru and Mn). Iodine data were relatively numerous within the terrestrial and marine organism data, but not within the freshwater data. Relatively more Co values were available for freshwater and marine organisms than for terrestrial organisms; in the marine ecosystem these data originate primarily for Japanese literature.
The large number of data classified as 'other' within Figure  1  for terrestrial organisms reflects the greater number of elements for which data are available for this ecosystem (see Table  2 ) and that few data are available for many of these. For marine organisms, entries for Tc were relatively numerous; no data for the element were available for freshwater or terrestrial organism. Differences between data availability are in-part driven by different radioecological issues between the ecosystems and potentially by the focus of some of the key review sources used to begin to establish the database (e. g. Tc was a focus of the review of marine data by Vives i Batlle et al. (  2007 )). Data on biological half-lives ranged from single components of loss to up to four components (i. e. four T1/2b values) of loss recorded for some entries.
g. Cs). Supplementary information entered was, in some instances, sparse (e. g. few data on sex) though many entries recorded study length (n=885), temperature (n=845), live-weight (n=844) and age (n=904). With respect to age, entries were available for different live-stages such as tadpole, fry and larvae. The database is too diverse in terms of organisms, elements, administration routes and how T1/2b values are presented (i. e. number of loss components) to attempt any analyses in this paper.
Discussion There are a number of reasons why T1/2b values are required to improve radiological assessments (as discussed above). The database we describe here represents a significant resource by which we may begin to improve, or test, available assessment approaches. For some elements the database may also be useful to those assessing the exposure of wildlife to metals (e. g. the database contains T1/2b values for Ag, Cr, Hg, Pb, Zn etc. ). The application of dynamic models to environmental assessment of radioactivity could be criticised as being overly complex  (IAEA, in-press). For many planned release situations it is likely that the CRwo-media model will lead to appropriate assessments  (Strand et al. 2009; IAEA 2014). Though, as noted above, for routine aerial releases the CRwo-media model may under predict activity concentrations in organisms and the current approaches may not be optimised for all planned release scenarios.
e. contamination is not dominated by the soil-plant route assumed in the CRwo-media model). Whilst inappropriate, equilibrium CRwo-media models were applied to assess risk to biota following the Fukushima accident  (Garnier Laplace et al. 2011; Strand et al. 2014 ). Although such assessments may have aimed to be conservative, as we demonstrate above, the resultant predictions may not always have been conservative. Some attempts to conduct more relevant assessments in the marine ecosystem using dynamic models have been made  (Kryshev et al. 2012; Vives i Batlle et al. 2014 ). However, more recent analyses suggests that these models over predicted the rates of decline in fish  (Johansen et al. 2015). This was potentially because the models assumed single loss component (Vives i Batlle 2015); a more robust T1/2b database is expected to improve the parameterisation of such dynamic models.
Use of the database We envisage that the database will be useful in both parameterising and testing models. Indeed some parts of the compiled database have already been used to test allometric models for homoeothermic vertebrates  (Beresford & Vives i Battle 2013; Beresford et al. 2015b ) and reptiles  (Beresford & Wood 2014). Users of the database will need to consider their needs and the suitability of the data that it contains. For instance, we have included T1/2b values derived from studies using a number of exposure routes. However, it is probable that for some elements intravenously administered radionuclides will behave differently to those orally ingested (e. g. Mayes et al. 1996). The study length and experimental protocol (e. g. time of first measurement, frequency of measurements, time taken to reach limits of detection etc.
) can influence the resultant T1/2b values and the number of components of loss observed. Experimental protocols of insufficient length to enable multiple components of loss to be observed are likely to result in T1/2b values which under-estimate the rate of loss (and consequently over estimate organism activity concentrations) in the short-term, but, over-estimate the rate of loss in the longerterm. Beresford & Wood (2014)  present an evaluation of the database with respect to reptiles. They highlighted that some of the entries were based upon only two time points and chose not to use these data in their analyses. Future, users will need to similarly critically evaluate the data. The present database provides them with a valuable resource from which to begin this evaluation.
issues raised were investigated and corrected as required in consultation with the originators of those entries in the database. Some of the compiled data have already been used in the development of allometric approaches for terrestrial(Beresford & Wood 2014; Beresford et al. 2015b ) and marine (Vives i Batlle et al. , 2007)  wildlife and as such have been subjected to additional quality checking. In the case of the reptile data this involved confirmation of most entries into the database(Beresford & Wood 2014).
Acknowledgements We would like to thank all members of the  IAEA MODARIA Working Group 8  (http://wwwns. iaea. org/projects/modaria/)who contributed to this work in anyway, in particular the inputs of  C. L. Barnett  ( NERC-CEH ),  S. Uchida  ( NIRS ),  T. Hinton  ( IRSN, now at Fukushima University ),  J. Mihalík  ( National Radiation Protection Institute, Czech Republic ),  K. Stark  ( Stockholm University, Sweden ) and  C. Willdrot  ( BfS, Germany ) are gratefully acknowledged. The inputs of  NERC-CEH , IRSN, SCK•CEN and CIEMAT were in partfunded by the  EC STAR Network of Excellence  (http://www. star-radioecology. org/). The input of M. D. Wood was supported by a  University of Salford Vice Chancellor's Research Scholarship. We also thank  J. Chaplow  ( NERC-CEH ) for assistance in publishing the dataset associated with this paper.