1. Introduction
Noise pollution represents a great public concern. Long-term exposure to high noise levels (>85 dB) have been associated with many direct health effects, even leading to hearing loss [1,2], or to non-hearing effects when exposure is at low-medium levels [3,4]. In this case, transportation noise can induce annoyance [5,6,7,8], sleep disturbance with awakening [9,10], cognitive impairment [11,12,13], physiological stress reactions [14], endocrine imbalance and cardiovascular disorders [15,16,17,18]. Moreover, exposure to noise can reduce both workers’ and students’ performance [19,20,21]. Higher levels of stress among subjects exposed to noise level higher than 55 dB (A) and increased occurrence of cardiovascular diseases associated with noise level greater than 65 dB (A) have also been reported [22]. Most of all, hypertension is the leading risk factor for cardiovascular morbidity and mortality worldwide [23]. Indeed, hypertension is a major risk factor for premature death and disability from heart disease, stroke, peripheral vascular disease and kidney failure [24,25,26]. A meta-analysis [24] evidenced a significant rise in prevalence of hypertension per increase of 5 dB (A) of equivalent road traffic noise level A weighted over a 16 h period (LAeq,16h) (Odds Ratio (OR) = 1.03; 95% confidence interval (CI): 1.01–1.06). Moreover, results on the association between long-term exposure to noise and blood pressure (BP) are still heterogeneous [27,28,29,30]. A possible explanation was provided by Babisch [31,32,33], who suggested that an increase in the level of adrenaline, noradrenaline and cortisol in response to noise-induced stress could result in peripheral vasoconstriction, increased heart rate and a rise in arterial blood pressure. A lack of data on multiple sources of noise and cardiovascular outcomes is still an issue in the scientific literature.
Health impact assessment studies estimated that 104 million U.S. citizens have sufficient annual noise exposure to be at risk of noise-related health effects [34]. In Europe, even 15 years after the implementation of the Environmental Noise Directive [35], 40% of the European population remains exposed to road traffic noise levels over 55 dB (A) of Lden (average noise level over a 24 h period) and 15% to levels greater than 65 dB (A). Road traffic remains the most widespread source in the urban environment, followed by railway noise, with 22 million people exposed to noise levels higher than 55 dB (A) of Lden [36], then by aircraft noise with more than 4 million people, and industrial noise with 1 million people exposed. The scientific community has studied how different sources generate noise and how to mitigate this with innovative solutions, especially in an urban context with its main sources being road traffic [37,38], railway traffic [39], airport [40,41], industries [42,43] and port activities [44,45], where present.
The impact of air traffic noise is particularly relevant during take-off and landing phases [46,47] if ground taxing operations are incorrectly managed [48]. Specific studies have been dedicated to aircraft noise’s relation with sleep disturbances and annoyance [49,50,51], while others, including the HYENA and SERA projects, focused on blood pressure and the risk of hypertension [46,52,53,54]. The HYENA project aimed at assessing the impacts on cardiovascular health of noise generated by air traffic and road traffic near six European airports. The results showed significant exposure–response association between night-time aircraft noise, daily road traffic noise and prevalence of “heart disease and stroke” and hypertension
Railways received specific attention in the ALPNAP study [55,56], where significant associations between railway noise and sleep medication intake were shown, especially for people exposed to 60 dB Lden. While the study was performed in an Alpine valley characterized by very specific noise conditions, other authors studied the association of railway noise with sleep disturbance [4,57]. Furthermore, railway noise is often related to vibrations, which induce other negative effects on sleep [58,59]. In a previous study [60], the authors showed that railway noise maps underestimate noise exposure and people are disturbed by unconventional noises such as brakes, squeals, whistles, and screeches, which are usually not considered in noise modelling. The underestimation of noise and the presence of vibration resulted in an increase of the percentage of highly annoyed people (%HA) with respect to the traditional noise dose–effect curves.
In an urban context, recreational noise plays an important role in citizens’ disturbance, even if it has not yet been well studied yet. In recent years more attention has been paid to the topic [61], but most of studies have only focused on campus students [62]. While the relation of recreational noise to cardiovascular outcomes still needs study, the insurgence of tinnitus, hearing loss and noise-induced hearing-threshold shift due to high levels of music were investigated [63,64] and connections were found by different authors [65].
The present study aims to evaluate the impact that different noise sources have on the health of citizens in terms of blood pressure (BP) and hypertension. A sample of 517 citizens living in the city of Pisa, Italy, was chosen for blood pressure measurements and a structured questionnaire. The city of Pisa was a good test site for the study because of its complex structure in terms of noise sources, including all the previously mentioned transportation sources, with an important airport very close to the inhabited areas, and major roads and railway stretches crossing the residential area. The exposure to all of these sound sources was considered as a whole or individually in order to evaluate their eventual correlation with health parameters. In a public health context, the results obtained could be used by institutions and citizens to prevent exposure to specific noise sources.
2. Materials and Methods
2.1. Sample Selection
The study sample includes 517 subjects, 37–72 years of age at the time of interview, previously selected for the SERA project (study on the effects of airport noise) [66] and the SERA-FA project (study on the effects of airport, railway and recreational noise) [67]. For both projects, the population sample was recruited through a random selection, stratified by gender, age and main sound source from the database of addresses provided by the local General Registry Office. The subjects were extracted uniformly considering sex, age and potential exposure to the principal noise sources according to the noise map of the city. Subsequently, up to three substitutions were selected in order to replace the non-respondents and those who refused to participate.
In the SERA project, the population was recruited in 2012 in a cross-sectional study, with a random sample of adults (45–70 years of age) living in Pisa and exposed to different average noise levels. A first set was exposed to at least 55 dB (A) of airport Lden, a second was exposed to 50 dB (A) of both airport and traffic Lden, a third was exposed to at least 55 dB (A) of traffic Lden and the last was not exposed to significant noise levels from these main sources. Participants were subjected to blood pressure measurements and to a structured questionnaire using the model adopted in the HYENA study [52]. This included questions on house characteristics, possible protection from noise, windows, socio-demographic conditions, occupational noise exposure, dietary habits, lifestyle factors, smoking, noise annoyance, sleep conditions and noise sensitivity.
From 2014 to 2016 more participants, aged 37–72, were added to the SERA-FA study in order to include subjects exposed to at least 55 dB(A) of railway Lden and subjects exposed to at least 55 dB (A) of recreational noise, in terms of Lnight. The same protocol as the SERA project was used, but two sections were added to the questionnaire in order to specifically investigate the exposure to railway and recreational noise.
The questionnaire campaign with the assessment of BP was carried out in 2012–2013 for the SERA project and 2014–2015 for SERA-FA participants.
2.2. Exposure Assessment
Noise exposure to the transport infrastructure (road, railway, airport) was obtained by the noise maps developed by the Environment Protection Agency for the Tuscany Region (ARPAT) according to the guidelines of the European Noise Directive 2002/49/EC (END) and the Italian Decree of 2005 (D. Lgs 194/05) [68]. Using the proper input data required by the noise model (i.e., traffic flow, speed), annual average Lden and Lnight of the single source were computed on a grid of 5 m × 5 m positioned at a height of 4 m above the ground, at a distance of 1 m from the building’s façade using the Integrated Noise Model 7.0b (INM) [69]. The overall noise exposure was also calculated as the energetic sum of the three components. These were used to estimate the percentage of residents exposed to noise levels greater than 55 dB (A) Lden and 50 dB (A) Lnight. Lden and Lnight were calculated. The German national method VBEB [70] was used as methodology to assign population to noise levels, as a study reported [71] how this better describes real exposure for epidemiological studies, with respect to the method proposed by the END. VBEB distributes the population among the receiver points located around buildings equally, and determines an exposure proportional to noise levels along all the building’s façades, while the END assigns the maximum level from all the points around the corresponding building, which is usually on the most exposed façade [72]. The meteorological parameters considered in the model, such as air temperature, atmospheric pressure, wind speed and relative humidity, were measured by weather stations located in the city of Pisa. Moreover, a measurement campaign for railway noise was conducted in two different parts. In 2013–2014 [73], measurements were performed along the railway lines in 31 places within the city of Pisa with the aim of validating the railway noise map. A class 1 sound level meter, compliant with IEC 61672-1 [74], was placed at a height of 1.5 m and 1 m away from the most exposed façade, recording the A-weighted equivalent continuous sound level (LAeq) with a time step equal to one second. From February to April 2015, the number of measurement points was increased, with another 27 short term and seven measurements providing daily and nightly value for noise exposure. A comparison between noise measurements and the noise map showed that railway infrastructure affects the surrounding areas differently than forecasted, due to the presence of unconventional noise from maneuvering, loading and unloading, truck movements, braking, squeals, whistles, arrivals and departures of trains, speakers, passengers, internal work, generators, bells, crossings, etc. [60]. The resulting differences have been used to correct the citizens’ exposure to railway noise.
At present, no model can simulate recreational noise, thus a specific measurement campaign which lasted for 18 months was conducted in order to assess the areas within the city of Pisa more subject to this source, such as the city center. Noise data were acquired with the wireless sensor network for real-time noise mapping used in the SENSEable project [75]. LAeq was acquired simultaneously in six different positions with a temporal base equal to one second, averaged in day-time periods. The measurement points were selected [76] based on the number of residents, in order to optimize the search for similar environments from an acoustic point of view. These are the largest areas possible in which it is possible to assume that the sound pressure level varies within 5 dB (A). The monthly average LAeq was calculated, eliminating occasional sound events, rain and wind. Recreational noise was defined as that part of noise that exceeded the road traffic noise level resulting from the noise map of the area, as this is the only other noise source affecting the city center. Further details on elaboration and stability can be found in the literature [77]. Estimates were then calculated using the main European indicators (Lden, Lnight), with standard deviation as a measure of uncertainty, and were assigned to citizens living in similar environments from an acoustic point of view.
Geographical coordinates were assigned to subjects using a common GIS software. For the addresses geocoding, the normalization and georeferencing service of the Tuscany Region has been used. Residents were classified depending on the superposition of noise maps (Lden < 55, 55–59, 60–64, 65–69, ≥70).
2.3. Assessment of the Outcome
Trained interviewers measured systolic blood pressure (SBP) and diastolic blood pressure (DBP) at subject’s homes after at least five minutes of rest in a seated position keeping both feet on the ground, using an automatic Omron M6 Comfort model (OMRON, Tokyo, Japan) with cuff attached to right or left upper arm (preferably right) [78]. The visits were performed during day-time from Monday to Friday. The staff assessed SBP and DBP three times at each home visit, with the first measurement recorded at the beginning of the interview after 5 min rest, and the second after a further minute, in according with recommendations of the American Heart Association [79]. The third measurement was at the end of the interview, approximately 45 min later. Home visits were distributed over the day in order to account for possible diurnal variations in BP. Two additional measurements were self-made by subjects in the evening of the same day and in the morning of the following day. The average of the 5 measurements provided the SBP and DBP values used in the analysis.
2.4. Covariates
An evaluation of the possible major confounders was performed among the variables which can be risk factors for hypertension and possibly associated with noise exposure, in order to eventually exclude them from the model. The potential confounders or effect modifiers that we have evaluated were the usual health indicators (physical activity and body mass index—BMI), sociodemographic characteristics (sex, age, education and employment status), lifestyle habits (smoking and alcohol), other noise sources different than mean noise exposure, work-related noise exposure, noise sensitivity value based on standardized ten questions [80,81] and home conditions (double-glass windows, other noise protections, construction year of the house). Subjects also indicated their annoyance to noise on a 11-point scale for each source on a list of ten: this parameter was evaluated as a potential effect modifier of the investigated relationship.
2.5. Statistical Analyses
Standard statistical methods were applied using STATA 14.2 [82]. In addition to SBP and DBP, the prevalence of hypertension based on the self-reported diagnosis was calculated, together with the use of antihypertensive medication or blood pressure measurements reporting SBP ≥ 140 mmHg and DBP ≥ 90 mmHg. This criterion is recommended by the World Health Organization (WHO) [83].
Pair-wise correlation between noise map indicators (airport, traffic and railway) were calculated and the association between noise levels and hypertension investigated using a logistic regression model. The odds ratio (OR) and 95% Confidence Intervals (CIs) for each effect estimate were estimated as results of this analysis.
The possible relation between environmental noise levels and BP, expressed as SBP and DBP separately, was assessed with mixed linear regression models and associations expressed with both day-time and night-time noise levels, obtaining risk beta coefficients and 95% CIs.
The analysis in categories made of intervals equal to 5 dB (A) suggested a linear relation, thus continuous exposure data have been used to assess the effect estimate in order to increase statistical power.
Potential covariates were evaluated in non-adjusted analysis: those with a p < 0.20 in order to avoid exclusion of important adjustment variables due to stochastic variability [84,85] and those already known in literature as risk factors for hypertension [86] (sex, age, BMI, educational status) were selected. The final model included sex, age (as continuous), educational status (elementary, medium, high school, university), alcohol (never drinker, former drinker and actual drinker), physical activity (less than 1 time a week of moderate exercise, between 1 and 3 times a week, more than 3 times a week), BMI, and use of pre-cooked foods (at least once a week, less than 1 meal at week). Smoking was included only in the model for BP, as a well-known risk factor for heart disease, but not for hypertension, as confirmed by the p-value, therefore not relevant in the preliminary analysis.
In order to investigate the differential susceptibility to noise exposure in subgroups of the study population, a stratification of the analysis was performed by sex, age, noise sensitivity (<50th percentile (P50) vs. ≥50th percentile), house noise protection (yes vs. no), windows closed to prevent noise exposure (never, few vs. often, always), living room exposition (noise source vs. side of noise source vs. back of noise source), bedroom exposition (noise source vs. side of noise source vs. back of noise source) and annoyance (few, moderately annoyed vs. very annoyed).
3. Results
A total of 517 participants (228 men and 289 women), aged between 35 and 72 years, at the time of visit, participated to the present study. The response rate in the study was medium-low (29.1%). In order to assess the potential selection bias, the authors compared the source population and the sample by sex and age, finding no statistically significant difference.
The mean age of participants was 57.3 years old (standard deviation 8.7) and 44.1% were males. Mean SBP and DBP expressed in mmHg during the visit were 126.9 and 81.1, respectively, while means for self-measured blood pressure were 125.6/79.2 and 121.5/77.7 respectively, for evening and next day morning. The overall hypertension prevalence was 37.5% (to be compared with the Italian population, in which there is a prevalence of 33% and 31% respectively among males and females [87]); of all subjects, 20.1% were treated for hypertension and had normal values of BP, 11.0% were treated but presented hypertensive values of SBP or DBP, and 11.2% without a medical prescription for hypertension presented abnormal values of BP. The prevalence of hypertension was higher in males (44.6%) than in females (32.7%).
Table 1 describes the variables considered in the study and stratified by hypertensive condition expressed as the WHO classification. Statistically significant differences between the two groups arose. Among those with hypertensive condition, higher values of SBP and DBP, BMI, alcohol consumption, lower level of education, actual workers, less than one time/week of moderate exercise, use of precooked foods and lower attitude to close windows were found.
The mean noise levels of the main noise source considered in this study are 61.7 dB (A) (standard deviation 7.6) of Lden and 49.4 dB (A) (standard deviation 13.6) of Lnight.
Multiple associations between covariates and prevalence of hypertension are shown in Table 2. The results represent the relationships between single parameters and risk of hypertension, net of all the other covariates included concurrently, without the main exposure of noise. Variables such as sex (male), higher age, smoking, higher BMI showed significant positive associations with a higher risk of hypertension. Educational level, stability of work conditions and physical activity showed a protective effect, in a significant association with a lower risk of hypertension.
Table 3 shows correlation coefficients between environmental noise exposure levels by day and night. Values display a different correlation for each noise source (r = 0.22 for airport noise, 0.99 for both railway and traffic exposures). In addition, significant correlation values between airport noise and railway noise during nighttime were detected, whilst for railways, this seems to be at the boundary of significance during daytime.
The regression model shown in Table 4, indicates that a 5 dB (A) increase in nocturnal environmental noise corresponds to a significant increase in blood pressure, especially in DBP (DBP and night-time noise: β = 0.50, 95% confidence intervals (CIs): 0.18, 0.81). Considering the hypertensive outcome, associations are almost significant especially during night-time in the full adjusted model (OR = 1.07, 95% CI: 0.99–1.15). Night-time noise is involved too in the association with SBP, showing a nearly significant association (β = 0.47, 95% CI: −0.05, 1.00).
Stratifying the main characteristics, the effects estimates were higher in participants who showed a higher noise sensitivity (based on Weinstein’s noise sensitivity method). Association between hypertension and environmental nocturnal noise were found in males (OR = 1.13; 95% CI: 1.01, 1.26), in persons older than 65 years of age (OR = 1.18; 95% CI: 1.02, 1.37) and those with higher noise sensitivity (OR = 1.12; 95% CI: 1.01–1.24).
Relations between DBP and environmental nocturnal noise showed some significant results too, among all participants, females (β = 0.40; 95% CI: 0.00, 0.79), people aged over 65 years (β = 1.03; 95% CI: 0.43, 1.62), people moderately annoyed by noise (β = 0.66; 95% CI: 0.05, 1.27) and other categories, shown in Figure 1, as noise sensitivity below and above the 50th percentile (45 in a scale from 10 to 60), structural changes for house noise protection (yes vs. no) and the habit of closing windows (never, few vs. often, always).
Noise could be quite different in terms of frequency, amplitude and duration of exposure. Figure 2 reports β for an increment of 10 dB(A) in Lden, stratified by main noise exposure: only railway exposure has a positive value (β = 0.68; 95% CI: −1.36, 2.72), although it does not reach a statistically significant level of risk.
4. Discussion
The present study investigated the impact of exposure to multiple noise sources on the blood pressure and on onset of hypertension in the wake of the HYENA study. Significant positive exposure–response relationships, especially to night-time noise exposure, were found in males; people aged over 65 years old and with a high sensitivity to noise in association with hypertension,; people aged over 65 years old and who never close windows at home due to noise in association with increase in systolic blood pressure; and for all participants, females, people aged over 65 years old, moderately annoyed by noise, high sensitivity to noise, without house noise protection and who never close windows due to noise, in association with an increase in diastolic blood pressure.
Significant differences were found in the hypertensive outcome between the various noise sources, considered to be road, railway and airport traffics and recreational noise. The exposure-response relationships between sound levels and cardiovascular outcomes showed different ORs depending on the sound sources analyzed; railway noise showed highest ORs. It should be noted that railway and road traffic noise were highly correlated between day and night, unlike aircraft noise. A possible explanation is that aircraft activity in Pisa is limited during the night. Nevertheless, the Lnight indicator (10 p.m.–6 a.m.) includes the so-called “shoulder hours” of the late evening and early morning, where some planes fly in an environment with a background noise lower than that in the day-time.
It is reasonable to believe that the relationship highlighted between nocturnal noise and hypertension can be motivated by the fact that the participants spent the night inside their houses compared to daytime hours, since the noise level assigned to the home address was used. This procedure would also explain the lower misclassification exposure during night hours, compared to daytime. Indeed, it is therefore reasonable to assume that during night hours the participants were actually subjected to the sound levels shown and that therefore there may be a correlation with cardiovascular effects, as emerged from the analyzes [88].
Smoking and alcohol are historical risk factors for hypertension, although smoking is still under investigation for its effect on blood pressure. For this reason, subjects were asked to refrain from smoking during the 30 min before the interview and BP measurement. As detailed in the methods section, smoking was included as a variable in the model, even if its impact on estimate of the exposure–response was not relevant.
The exposure–response association for hypertensive risk was more relevant among men, in accordance with previous evidence on males and hypertension [89,90,91]. However, the studies mentioned only investigated the relation between road traffic noise and hypertension. The present study aimed to consider a larger number of noise sources in a city like Pisa, where citizens are often exposed to a mixture of noise pollutants. Even when transportation noise seems to be absent, such as in the city center, anthropogenic noise could play a role among the determinants of cardiovascular and sleep health.
In all the investigated outcomes (hypertension, SBP and DBP), variable “age” gave the same indication of higher risk for people aged over 65 years, given that this category is likely to spend more time at home, and consequently its exposure should be less commonly misclassified.
Age always shows positive values and reaches significance in all night-noise analysis for 5 dB(A) increase in Lnight (Hypertension OR = 1.18; 95% CI: 1.02–1.37; SBP β = 1.41; 95% CI: 0.08–2.73; DBP β = 1.03; 95% CI: 0.43–1.62).
Gathering together some of the subcategories detected in the questionnaire, as reported in Figure 1, it emerged that, in the relation between DPB increase and Lnight noise, significant risks were found in subjects moderately annoyed ((0–7 in a 11-point scale) β = 0.66; 95% CI, 0.05–1.27), or with lower noise sensitivity, beyond 50th percentile, (β = 0.54; 95% CI, 0.13–0.94), or living in a house free of noise protection (β = 0.74; 95% CI, 0.26–1.21) or who never close windows because of noise (β = 0.82; 95% CI, 0.40–1.23). Apparently, people who not protecting themselves from noisy sources for personal reasons are more at risk than those who, concerned about the possible effects of noise on their health, strives to protect themselves from this specific exposure.
A potential weakness of this study is the medium-low response rate. However, a descriptive analysis showed that response rate is not different by sex, age and exposure zones, the only exception being the aircraft noise group showing a higher response rate. This can be partially explained by taking into account the limited population of the city (almost 90,000 residents) with a high component of students, and the airport, which is very close to the city, represents the major environmental concern of citizens.
Another weakness of the study could be the different exposure assessment of recreational noise, involving no initial “pedestrian data flow”, several microphones in specific areas and a subsequent model. A misclassification and a problem of comparison between noise sources could exist, as no data on recreational noise outside of the city center of Pisa were available. On these bases, the recreational group resulted in a non-significant and negative relation in all analyses, therefore the results, including all areas, could be underestimates.
At the same time, the present study focused not on a single type of noise, but shifted attention towards a more comprehensive approach to noise exposure that involves citizens in several ways, each with its peculiarities (frequency content, amplitude, individual perception, etc.). In addition, the completeness of the questionnaire helped to clarify certain factors and their roles in the associations investigated.
5. Conclusions
Statistically significant positive relation between night-time noise and diastolic blood pressure was found. The subcategories majorly involved in the relation between night-time noise and diastolic blood pressure were people aged older than 65 years, moderately annoyed, noise sensitive, without noise protections in house and residents who usually do not close windows when exposed to high levels of noise. Among various noise sources, railway noise showed the strongest association with the outcomes of the study. Hypertension is a major independent risk factor for events such as myocardial infarction and stroke and this study demonstrated an increase of risk in association with environmental noise.
Author Contributions
Conceptualization, D.P. and M.A.V.; methodology, D.P., G.L., M.A.V. and L.F.; software, D.P. and L.F.; validation, D.P., G.L., M.A.V. and L.F.; formal analysis, D.P. and L.F.; investigation, D.P. and L.F.; resources, D.P., G.L., M.A.V. and L.F.; data curation, D.P. and L.F.; writing—original draft preparation, D.P. and L.F.; writing—review and editing, D.P., G.L., M.A.V. and L.F.; visualization, D.P. and L.F.; supervision, M.A.V.; project administration, M.A.V.; funding acquisition, M.A.V. All authors have read and agreed to the published version of the manuscript.
Funding
This research received no external funding.
Institutional Review Board Statement
The present study protocol was evaluated and accepted by local ethics commission (Comitato Etico Scientifico dell’Azienda Ospedaliera Universitaria di Pisa, Protocollo 3486 del 2012).
Informed Consent Statement
Informed consent was obtained from all subjects involved in the study.
Data Availability Statement
The data presented in this study are available on request from the corresponding author.
Acknowledgments
The research was supported by Italian Ministry of Health. We thank our colleagues of Clinical Physiology Institute in Pisa who assisted our research. The authors wish to thank Lara Ginevra Del Pizzo for providing proof reading.
Conflicts of Interest
The authors declare no conflict of interest.
Publisher’s Note: MDPI stays neutral with regard to jurisdictional claims in published maps and institutional affiliations.
Figures and Tables
Enlarge this image.Figure 1. Estimated ORs/β per increment of 5 dB(A) of night-time noise by subgroups of population. in prevalent hypertension (A), estimated change of SBP (B) and estimated changes of DBP (C).
Enlarge this image.Figure 2. Estimated ORs/β per increment of 5 dB(A) of noise by main noise exposure. in prevalent hypertension (A), estimated change of SBP (B) and estimated changes of DBP (C).
Characteristics of subjects included in the study, variables divided in continuous and categorical variables.
| Characteristics | Total (n = 515) | Non-Hypertensive (n = 313) | Hypertensive (n = 194) | p-Value a |
|---|---|---|---|---|
| Continuous variables [median (IQR)] | ||||
| Systolic blood pressure (mmHg) | 123.1 (20.0) | 117.5 (16.0) | 136.5 (20.5) | <0.001 * |
| Diastolic blood pressure (mmHg) | 78.5 (12.1) | 76.0 (9.25) | 86.8 (13.25) | <0.001 * |
| Age (years) | 58.2 (14.2) | 54.8 (12.8) | 62.7 (11.3) | <0.001 * |
| Main noise source LDEN [dB(A)] | 62 (10.0) | 61.6 (10.6) | 62.5 (10.2) | 0.066 |
| Main noise source LNIGHT [dB(A)] | 53.5 (18.0) | 53.1 (15.4) | 54.1 (18.3) | 0.254 |
| Noise sensitivity score (10–60) b | 39.0 (12.0) | 39.0 (12.0) | 39.0 (11.0) | 0.874 |
| Categorical variables [n (%)] | ||||
| Male sex | 228 (44.1) | 124 (39.6) | 101 (50.2) | 0.042 |
| BMI (Kg/m2) | <0.001 * | |||
| <18.5 | 9 (1.7) | 8 (2.6) | 1 (0.5) | |
| 18.5–24.9 | 251 (48.6) | 178 (56.9) | 73 (36.3) | |
| 25–29.9 | 201 (38.9) | 97 (31.0) | 103 (51.2) | |
| 30+ | 56 (10.8) | 30 (9.6) | 24 (11.9) | |
| Educational level | <0.001 * | |||
| University or similar | 241 (46.6) | 166 (53.0) | 73 (36.3) | |
| Secondary | 174 (33.7) | 103 (32.9) | 70 (34.8) | |
| Primary | 66 (12.8) | 31 (9.9) | 35 (17.4) | |
| Illiterate | 33 (6.4) | 12 (3.8) | 21 (10.5) | |
| Smoking | 0.501 | |||
| Professional Status | ||||
| Unemployed | 58 (11.5) | 34 (10.9) | 24 (12.5) | |
| Retired | 157 (31.1) | 78 (24.9) | 79 (24.9) | |
| Actual worker | 290 (64.6) | 201 (64.2) | 89 (64.2) | <0.001 * |
| Physical activity (moderate exercise) | ||||
| Less than 1 time/week | 45 (8.9) | 20 (6.4) | 25 (13.0) | |
| Between 1 and 3 times/week | 134 (26.5) | 91 (29.2) | 43 (22.4) | |
| More than 3 times/week | 326 (64.6) | 202 (64.5) | 124 (64.6) | 0.020 |
| Never smokers | 235 (45.5) | 148 (47.3) | 85 (42.3) | |
| Smokers | 116 (22.4) | 72 (23.0) | 44 (21.9) | |
| Former smokers | 166 (32.1) | 93 (29.7) | 72 (35.8) | |
| Drinking c | 0.009 * | |||
| Non-drinkers | 146 (28.2) | 98 (31.3) | 48 (23.9) | |
| Casual drinkers | 187 (38.2) | 117 (37.4) | 68 (33.8) | |
| Regular drinkers | 183 (35.4) | 98 (31.3) | 84 (41.8) | |
| Diet, use of pre-cooked foods | 208 (40.2) | 142 (45.4) | 64 (31.8) | 0.009 * |
| Living room orientation, noise source d | 128 (24.8) | 77 (24.6) | 51 (25.4) | 0.882 |
| Bedroom orientation, noise source d | 134 (25.9) | 84 (26.8) | 48 (23.9) | 0.571 |
| Closing windows, yes e | 162 (31.3) | 107 (34.2) | 54 (26.9) | 0.081 |
| Protections, yes f | 333 (64.4) | 207 (66.1) | 124 (61.7) | 0.395 |
| Noise annoyance g | 0.878 | |||
| Moderate (0–7) | 201 (39.0) | 119 (45.9) | 75 (45.2) | |
| High (8–10) | 231 (44.9) | 140 (54.1) | 91 (54.8) | |
| Not exposed | 83 (16.1) | 54 (67.5) | 26 (32.5) | |
| Air pollution annoyance, high h | 281 (54.4) | 170 (54.3) | 110 (54.7) | 0.200 |
| Noise groups | 0.018 | |||
| Aircraft | 100 (19.8) | 59 (18.9) | 41 (21.4) | |
| Road traffic + Aircraft | 80 (15.8) | 40 (12.8) | 40 (20.8) | |
| Road traffic | 74 (14.7) | 42 (13.4) | 32 (16.7) | |
| Railway | 118 (23.4) | 85 (27.2) | 33 (17.2) | |
| Recreational | 53 (10.5) | 33 (10.5) | 20 (10.4) | |
| Reference group | 80 (15.8) | 54 (17.3) | 26 (13.5) | |
a Chi-square test and Kruskall-Wallis test for strata of hypertension with categorical or continuous variables, respectively. b Higher noise sensitivity with higher values. c Casual: less than 2 glasses/week. (1 missing observation) d Control group not included. e Yes: always close windows (vs. no: never, only on summer or winter season). f Sound-proofed windows or changes in structure due to noise. g Referred to the main noise source; in case of aircraft/traffic group, the higher annoyance is selected. h Score from 6 to 10 in a 0–10 scale. * Category with a significant association with hypertension.
Table 2Multiple associations between covariates and the prevalence of hypertension (HYENA definition).
| Variable | Categorization | OR a (95% CI) | p-Value |
|---|---|---|---|
| Age | Per 1 year | 1.08 (1.05–1.10) | <0.001 |
| Gender | Male | 1 | |
| Women | 0.70 (0.46–1.08) | 0.107 | |
| Alcohol | Never drinker | 1 | |
| Casual drinker | 1.25 (0.75–2.10) | 0.394 | |
| Regular drinker | 1.30 (0.76–2.20) | 0.338 | |
| Smoking | Never smoker | 1 | |
| Former smoker | 0.79 (0.49–1.26) | 0.321 | |
| Actual smoker | 0.69 (0.41–1.17) | 0.169 | |
| Professional status | Unemployed | 1 | |
| Retired | 0.38 (0.19–0.75) | 0.006 | |
| Actual worker | 0.49 (0.26–0.92) | 0.027 | |
| BMI | Per kg/m2 | 1.07 (1.02–1.13) | 0.010 |
| Noise sensitivity | Per scale unit | 1.01 (0.99–1.03) | 0.225 |
| Educational level | Illiterate | 1 | |
| Primary | 0.91 (0.36–2.32) | 0.844 | |
| Secondary | 0.61 (0.26–1.41) | 0.284 | |
| University or similar | 0.47 (0.20–1.09) | 0.117 | |
| Physical activity | None | 1 | |
| Moderately or strenuous 1–3 times a week | 0.43 (0.20–0.91) | 0.028 | |
| Moderately or strenuous > 3 times a week | 0.57 (0.28–1.13) | 0.108 |
a Odds Ratio are mutually adjusted.
Table 3Descriptive statistics and results of Spearman’s correlation of the different environmental noise exposures.
| Mean ± SE | Percentile | Air Traffic | Railway | Road Traffic | ||||||
|---|---|---|---|---|---|---|---|---|---|---|
| 10th | 50th | 90th | Day | Night | Day | Night | Day | Night | ||
| Air Traffic (day) | 57.00 ± 0.20 | 54.5 | 57.4 | 59.3 | 1 | |||||
| Air traffic (night) | 27.78 ± 0.87 | 20 | 25.6 | 41.1 | 0.22 | 1 | ||||
| Railway (day) | 59.53 ± 0.78 | 46.2 | 61 | 70.3 | −0.12 | 0.24 | 1 | |||
| Railway (night) | 52.49 ± 0.78 | 39.2 | 54.3 | 63.1 | −0.12 | 0.25 | 0.99 * | 1 | ||
| Traffic (day) | 68.04 ± 0.36 | 63.9 | 68 | 72 | 0.05 | 0.00 | −0.07 | −0.07 | 1 | |
| Traffic (night) | 59.15 ± 0.37 | 55.3 | 59.2 | 63.4 | 0.05 | 0.02 | −0.06 | −0.06 | 0.99 * | 1 |
| Recreational (day) a | 70.03 ± 0.66 | 64.2 | 71.2 | 74.2 | ||||||
| Recreational (night) a | 63.80 ± 0.72 | 57.5 | 65.6 | 68.4 | ||||||
a Recreational noise information are missing for the other types of noise. * Significant value.
Table 4Associations between hypertension and blood pressure with environmental noise by day and night; estimated risk for hypertension and change in blood pressure (mmHg) for a 10 dB (A) increment during the day or for a 5 dB (A) increment during night.
| Outcome | Night | Day | |||
|---|---|---|---|---|---|
| OR/5 dB(A) (95% CI) | p -Value | OR/10 dB(A) (95% CI) | p -Value | ||
| Hypertension | Non-adjusted | 1.03 (0.96, 1.10) | 0.386 | 1.23 (0.97, 1.57) | 0.091 |
| Full model | 1.07 (0.99, 1.15) | 0.070 | 1.27 (0.97, 1.67) | 0.085 | |
| β/5 dB (A) (95% CI) | β/10 dB (A) (95% CI) | ||||
| SBP | Non-adjusted | 0.11 (−0.47, 0.69) | 0.715 | −0.31 (−2.38, 1.76) | 0.768 |
| Full model | 0.47 (−0.05, 1.00) | 0.078 | −0.08 (−1.97, 1.81) | 0.934 | |
| DBP | Non-adjusted | 0.28 (−0.05, 0.61) | 0.101 | 0.30 (−0.88, 1.48) | 0.615 |
| Full model | 0.50 (0.18, 0.81) | 0.002 | 0.91 (−0.23, 2.06) | 0.118 | |
© 2021 by the authors.
Details
; Vigotti, Maria Angela 3 ; Fredianelli, Luca 4
1 Department of Biology, University of Pisa, 56126 Pisa, Italy;
2 Institute for Chemical-Physical Processes, National Research Council, 56124 Pisa, Italy
3 Department of Biology, University of Pisa, 56126 Pisa, Italy;
4 IPool S.r.l., Via Cocchi 7, 56121 Pisa, Italy