Overview
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Key numbers
The worker extracted the full PDF text with layout preservation twice and compared extraction hashes before commit. The following lines are copied from numeric/table-bearing regions of the PDF and retain the source units and wording where legible:
- values. The predicted geometric mean PbBs were 2.17 ( ± 1.24) μg/dL for soil with PDD, 1.95
- geometric mean PbB of 2.46 ( ± 0.99) μg/dL. In contrast to all other IEUBK model studies to our
- common application of the IEUBK model, results in predicted PbB about 22% (range 0 to 52%)
- Model to total Pb intake for a child aged 1–2 years was 0.09% for air, 42% for diet, 5.3% for water
- and 42% for soil and dust. Our results indicate that it is feasible to use alternative measures of soil
- 100 residences. The number of observation-occasions ranged from 2 to 13 per subject, with
- a mean of 9. In order to assess variations in the relationship between observed and predicted
- values for children of different ages, six groups were created: under 1 year (n = 32), 1- < 2
- comparison (described below in Section 2.3.1), soil as mg/kg, dust sweepings as mg/kg, diet
- from the 10 studies reported in Table 1 of the Succop et al. (1998) paper where both interior
- Succop et al. (1998) paper ranged from 0.21 to 0.65 with a geometric mean of 0.31. Besides
- the other simulations listed in Table 1 we ran simulations to compare with observed PbB
- study (as in simulation 1 in Table 1), (iii) the same data with the “Succop” factor applied to
- Approximately 90% of the houses were built prior to 1980 so there was the possibility of Pb
- houses, paint with concentrations above 1% Pb was found in 25 of the 100 houses and
- Lindern et al. (2016). We used the default ingestion rates and bioavailability (30% for soil
- 34 ± 5% with a range of 25–43% but as these results are similar to the IEUBK default values
- suggestion of a reviewer, using a bioavailability of 50%. The geometric mean increases in
- predicted PbB in using a bioavailability of 50% instead of 30% is +0.88% for soil with
- study: “Assuming an absolute bioavailability of 34%, the IEUBK model predicts a
- lead in blood of 5 μg/dL and 2.1% exceeding 10 μg/dL. Assuming an absolute
- bioavailability of 50% (the NEPM default assumption) the IEUBK model predicts a
- μg/dL (NHMRC, 2015) and 2.3% exceed a BLL of 10 μg/dL, the former Australian
- measured Sydney median ANSTO air lead data from 2002 to 2006 and recently collected
- following section. The geometric means are: 2.17 ( ± 1.24) μg/dL and median value of 2.21
- μg/dL for soil with PDD; 1.95 ( ± 1.17) μg/dL and median value of 2.02 μg/dL for soil with
- are in good agreement with the observed geometric mean PbB of 2.46 ( ± 0.99) μg/dL and
- median of 2.38 μg/dL although, as stated above, increasing the bioavailability to 50% gives
- small increases in geometric mean predicted PbB for soil with PDD of 2.3 μg/dL and 2.50
- values ranged from 1.46 to 1.93. The two greatest IQRs were for sweeps and wipes (1.93)
- In Fig. 4, the dark bars show the medians of the observed and predicted values of PbB, while
- However, while none of the four differences was significant in the (n = 28). In the other age
- The rank correlations between the observed and predicted PbB values ranged from 0.059 to
- soil with handwipe (Fig. 7). For example, the average predicted PbB ‘default dust’ was 22%
- model, Biesieda and Hubichi (1999) obtained geometric mean predicted PbBs of 9.3 to 9.6
- μg/dL in 4 Polish cities whereas the observed PbB geometric mean was 6.7 μg/dL.
- dietary and soil/dust contribute equally to PbB levels with geometric means of 42% and
- water are low at 0.09% and 5.3% respectively. The mean values are quite different from
- those reported for Chinese cities by Li et al. (2016) of 83% (57–94%) for diet and 15% (3–
- 42%) for soil/dust and Zhong et al. (2017) of 73 ± 12% for diet and 25 ± 11% for soil/dust
- analyses (Section 4.3) showed that the variance without dust sweepings and soil was 1.6%
- (compared with 4.6% when included in the model), indicating their lower contribution to the
Methods (brief)
- location but indoor dust, usually collected by vacuum cleaning, is not always measured
- because of cost and invasiveness to the residents. When not collected, estimates of the Pb
- sample the top layers of soil (e.g., 5 cm) for estimating surface dust Pb concentration. It is
- in 2001. Samples of blood and urine and environmental materials were analysed for a suite
- of 20 elements using inductively coupled plasma methods resulting in ~7000 samples from
- to determine the validity of using alternative measures of exposure of dust collected in petri
- Samples were collected at 6-monthly intervals at residences located at varying distances
- children, whose age ranged from 0.29 to 2.4 years at the time of first sample collection.
- Soil samples and exterior dust sweepings (using dust pan and broom over ~1 m2) from front
- and back areas around the houses were collected in zip-lock plastic bags at 6-month intervals
- sampling (Shim et al., 2014). All food eaten within a 6-day time frame was sampled. Fully
- flushed drinking water samples were collected from the kitchen faucet. The protocols for
- sample collection and preparation are described in Gulson et al. (1997). Hand wipes for each
- hand of the children were collected into cleaned polyethylene centrifuge test tubes prior to,
- frequented areas of the house (child’s bedroom, living/ play room) were collected over 6-
- blood samples from the same child for multiple years were collected by a trained paediatric
- Vacutainer blood collection set consisting of 12″ tubing with multiple sample Luer adapter
- Details of sample preparation and analyses are given in Gulson et al. (2006).
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Update history
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